III Chapter 3 – Affected Environment and Environmental ...a123.g.akamai.net/7/123/11558/abc123/forestservic...Overlap in soil and vegetation geography is summarized in complementary

Jakabe Restoration Project EA Final Copy Chapter 3

Chapter 3 – Affected Environment and Environmental Consequences_________ This chapter summarizes the physical and biological environments of the affected project area and the anticipated changes to those environments due to implementation of the alternatives. It also presents the scientific and analytical basis for the comparison of alternatives. The chapter is separated by resources. The current condition of each resource is described first followed by the environmental consequences of each action on that resource. Acreage differences between sections are due to rounding differences or how the Geographic Information System (GIS) was applied during spatial analysis, and should not be considered significant. The current condition of the area is the result of past actions or inactions across the watershed. The management has interconnected with natural processes to produce conditions that now lead to the need for vegetative treatments. A list of past actions is contained in Appendix E. The effects of these actions (current conditions) and the effects of the proposed alternatives have been analyzed in this section. Other activities concurrent with this project and analyzed as part of this project, are the Jakabe Juniper/Aspen Meadow Projects (Decision Memo signed June 9, 2004), Jakabe Road Closures (Decision Memo signed June 21, 2004), Jakabe Stream Enhancement Projects (Decision Memo signed July 22, 2004), the Jakabe Prescribed Burn Project (Decision Memo signed March 10, 2005), and the Chewaucan Fuels Treatment Area (Bureau of Land Management, Decision Record signed 2002). I. Soils Jakabe Soils Report, Watershed and Aquatics Specialist Report/Fisheries Biological Evaluation and Jakabe Soils Specialist Report, October 17, 2005 – Jakabe Watershed Enhancement Project, Jakabe Restoration Project Analysis File Addresses: Issue 2. Juniper encroachment – Loss of wildlife, riparian, and deciduous plant habitat; reduced water quality; and increased soil movement has resulted with the advance of juniper woodlands. Issue 4. Restoration of riparian habitat – reduced riparian habitat due to encroachment, road densities and locations, and loss of stable upland vegetation. Most of the soils lying beneath the forest and shrub litter are derived from volcanic rocks ejected from small volcanoes that fractured into fault blocks which dominate the geomorphology of the Chewaucan Watershed. The underlying rocks are blanketed in part by sandy ash and pumice deposits. The underlying pyroclastic and rhyolite rock yield sandy subsoil material, while underlying andesite and basalts rock weathers to loamy soil material. Individual soil map unit details are identified in the Fremont National Forest Soil Resource Inventory (Wenzel, 1979). Overall, most sites proposed for treatment within the Jakabe project area occur on pyroclastic rocks with low to moderate slopes. Erosion risk

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Erosion risks are apt to be low from management activities that open up the forest and yield a ground cover response, because background erosion rates are associated with open forest. Background erosion and sediment estimates are 0.00 to 0.02 ton per acre using local climate and soil data estimated with Water Erosion Prediction Project technology (WEPP 2001). Water Erosion Prediction Project technology is a computer model based on the Green-Amp infiltration equation that


uses local climate data sets, soil texture, vegetation type, ground cover, and topography (WEPP 2001). Map unit information in the Soil Resource Inventory (Wenzel, 1979) is used to estimate erosion and sediment with WEPP technology. Erosion rates vary with vegetation cover, soil conditions, and local climate for objective soil erosion and hydrologic estimates. If wildfire were to burn through the dense fuels in this area, the result would be erosion rates between 0.6 and 0.9 tons per acre. Wildfire can cause certain soil types to become water repellant. Evidence from the 2002 Toolbox Fire complex suggests that post-fire water repellency is uncommon in pumice and ash deposits like those found here. In spots where soils do become water repellant and the only down wood is burned trees, erosion can be as high as 1.72 tons per acre. As crown cover and fuel loads increase (Alternative 1), the risk of wildfire and therefore the risk of erosion increase. Generally, however, erosion rates in Jakabe are well below the 1.0 ton per acre recognized as accelerated erosion. Past forest practices, which are described in some detail in the Vegetation Section, have yielded a fleeting or short lived ground cover. Transects show ground cover is currently deficient, which is unfortunate since ground cover such as grass waterways is best known for erosion control. There should be abundant sagebrush/grass steppe cover, in the dry ponderosa pine or relevant ground gasses, forbs and shrubs for mixed conifer or lodgepole pine forest, as identified in the reference conditions. Primary sources of sediment within the watershed are roads, especially new roads. Road erosion is highlighted in the 1998 Dairy/Elder & South Creek Watershed Analysis. The detailed road segment analysis for the adjacent 2002 Toolbox project showed the primay erosion risk is roads along streams. Yet, like all erosions surfaces, roads tend to “harden” and limit erosion, especially if the road ditches are graveled or grassed. Roads without rolling dips or with poor alignments, past logging skid roads that have yet to grass over, and stream banks at poor culverts locations may yield chronic erosion. Roads are a primary concern as they are the link between sediment source areas and stream channels. Compaction Soil compaction and vegetation cover are principal factors for monitoring changes in forested watersheds and streams (Ziemer, 1998). The factors consider the effects of heavy equipment used with some forest practices and recovery of soils with well rooted vegetation—ground cover. Using aerial photographs, past harvest forest openings were grouped in three categories of low (less than 20 percent), moderate (21 to 34 percent), and high (greater than 35 percent) management activity. Without recovery, the high opening should have the most compaction and the low should have the least. On the other hand, given sandy soil and well rooted ground cover, a high area may recover rapidly from traffic. In forest traffic studies over several growth cycles, sand texture soils are less apt to compact or have adverse growth effects than soils with loam and clay loam textures (Gomez et al. 2002). Soil compaction transects were stratified by soil map units and harvest openings. Current conditions were assessed along 51 transects. The four dominant soil map units (SMU) received 5 or more transects. The dominant rock and soils are: the pyroclastic SMU 57 and SMU 76; rhyolite SMU 41; and the andesite and basalt SMU 37. Of 126 stands proposed for treatment in the Jakabe project area, 15 were estimated as high logging compaction with 1980’s heavy equipment-type logging.

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Most of these sites were sampled.. On transects, soil features were sampled at 20 points and the features were ranked on a scale from 1 (soft soil tilth) to 6 (thick growth-limiting plates). The protocol is consistent with Region 6 methods used to assess the 20 percent compaction. The findings are shown below. Transects in Jakabe project area across the range of soil map units; the common soil and tallies in high harvest openings are highlighted. Transects with more than 20 percent compaction are identified and explained with asterisk.

Material Loam, Rocky

Sandy, Rocky

Sand & Loam

Sandy, Rocky

Sandy, Rocky

Map Unit No. 37 41 57 76 other Total Transects 9 14 8 8 12 High Transects 4 2 0 2 5 Transect with compacted over 20 percent

0 0 0 0 0* see below

Most transects, 50 of 51, have suitable soil tilth. One transect exceeded the Pacific Northwest Region’s disturbance guideline of 20 percent (Forest Service, 1998). Compaction above 20 percent (*) was on found on site 44 with 4 of 20 samples on the engineered bed of Road 079. On a second transect excluding the road bed, this high harvest area met the standard and also had ground cover grasses that approach historic norms. An additional 25 sites that span all soil map units were sampled for ease of shovel penetration. In these soils with common rocky subsoil, several sites including high logging sites 35, 44, and 49 were found to have lower soil resistance than anticipated. On spot check, the untreated site 46 and the adjacent plantation both had garden-like ease of shovel penetration. Minimal compaction effects in areas harvested is apt to be due to the nature of the sandy and rocky soil material that limits compaction as well as a period of ground cover recovery. Looking at the roots within the upper foot (25cm) the field crew speculated the roots are declining as the forest openings are declining. Soil biology Soil erosion and compaction mostly look at soils as physical systems, but soils are mostly biological systems. Soil biology is intertwined with the kind and condtion of the vegetation. The forest coditions identified in the Vegetation Section affect soil biology because soils provide a historic record of vegetation conditions. Overlap in soil and vegetation geography is summarized in complementary soil and vegetation forming factors (Jenny 1941; Majors 1951). Soils record the influences of five factors: biota, climate, geologic material, topography, and time (Jenny 1941) and in turn vegetation records the influences of: soil, climate, geologic material, topography, and time (Majors 1951). Soil vegetation formation can be identified by slowly adjusting processes, such as mineral weathering over several centuries or rapidly adjusting processes over several decades (Yaalon 1983), such as the seral progression after recurring ground fires.

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Vegetation plays a dominant role in soil formation and it leaves its fingerprints as distinctive features in the soil. For example, fire suppression, which has driven the most drastic changes within ponderosa pine stands as explained in the Vegetation section; also alters ground cover and in turn soil litter re-supply. In a practical way, soil and vegetation forming factors are used to organize local or regional patterns of plant species and their environments. The patterns are found in local guides and survey such as Hopkins’ Plant Association (1976). The factors are applied to characterize distinctive ecological regions or plant geography. For example, the eastern and western Cascades in Oregon are separated into ecological regions by their distinctive climate, topography, geologic material, and vegetation (Thorson et al 2003). The Jakabe project area occurs in the Eastern Cascades ecological region which is characterized by a rain shadow for a dry snowy climate, pumice flats and plateau, and open ponderosa pine and lodgepole pine forests adapted to drought with frequent creeping ground fires (Thorson et al 2003). While the Western Cascade, is an ecological region characterized by a wet temperate rain and snow climate with eroded steep sided valleys and dissected mountains where hemlock and fir forests are common. The project area is on the dry eastern edge of the Eastern Cascades and grades into the semiarid upland of the Northern Basin and Range with low mountains, rocky soils, and juniper steppe woodlands, and sagebrush steppe Idaho fescue grass cover. The Atlas of Oregon amplifies the distinctive qualities of the state’s ecological regions in a series of charts of soil, vegetation, climate, geology, and topography (Loy et al. 2000). For example, the Atlas shows a model local for landslides and mass wasting is the H.J. Andrews Experimental Forest in the Western Cascades. The H.J. Andrews occurs on a band of tuff geologic material which has weathered to clay that slips as the rain saturates the steep ground. On the other hand, landslides and mass wasting are essentially absent in the Eastern Cascades, because slips are unlikely on semiarid, sandy, pumice plateaus and rim rocks. Comparisons of specific soils or ground cover conditions are uncertain, because experiment projects at H.J. Andrews have yet to find correlated soil surveys and guides for context about forest soil or nutrient processes. The local Fremont soil inventory records the details of the Eastern Cascades edge with thin volcanic ash and pumice deposits. The underlying sandy soil material from pyroclastic and rhyolite rock amplify the summer drought conditions in the historic open ponderosa pine and lodgepole pine forest. Frequent creeping ground fires yield an open pine forest that grade to a sagebrush steppe savanna. The Entisol soil order with a thin dark surface layers in sandy and sandy-rocky matrix is common (Wenzel, 1979). Underlying andesite and basalts rock that weather to loamy soil material are less common within the Jakabe project area. The loam retains moisture better than the sand and yields Mollisol soil order as grass and shrub litter decay accumulates. Fire suppression alters ground cover. It reduces litter accumulation by shifting away from grass and shrub cover in the open forest to closed stands. Since ground fire and post-fire nitrogen fixation by ground cover plants are dominant nutrient processes in semiarid eastside pine forests (Johnson et at. 1998), fire suppression reduces the seral progression that re-supplies nitrogen rich organic material. Post fire recovery through lupine blooms or ceanothus shrub seral progression over a few decades is important for nitrogen conservation.

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The decadal time line is well illustrated in the Eastern Cascade ecoregion in a 35 year study, with and without ground cover (Busse et al. 1996) and with vegetation samples after the local 1992 Lone Pine burn (Sexton 1998; Malaby, 2002). Ponderosa pine elongation was greater without ground cover in the first decade, but by the second decade growth advantage began to shift to sites with ground cover. In the third decade the pines sustained their growth advantage and their ground cover litter had enriched the sandy soil with nitrogen. This time line shows succession is more complex than the simple forbs to tree plant succession models used in introductory ecology. Post fire succession has been followed since the 1992 wildfire at Lone Pine. Post fire forb blooms have progressed to grass and shrub ground cover (Sexton 1998; Malaby, 2002). These local soils have developed soft dark granular structures, associated with effective water infiltration and nutrient conservation. Alternative 1 Currently the majority of units proposed for mechanized treatments are within the Jakabe project area occur on pyroclastic rocks that form sandy rocky soils on moderate slopes. Most sites have received past activity as identified in aerial photograph for low, moderate and high logging evidence. So ground cover and compaction was assessed in 51 transect across the common soils with additional spot checks across other soils. Consistent with geotechnical expectations in a sandy and rocky material, compaction occurred at 0 to 5 percent rate, well below the regional standard of 20 percent. And ground cover response from past logging openings were muted even where cut stumps were common. The no action alternative is apt to have direct and indirect effects of sustaining a deficient ground cover, and with fuel loading, wildfires may affect the aquatic habitat or aquatic species cumulatively. Compaction seems to recover or does not pose a chronic issue, yet the lack of ground cover may affect the water infiltration and percolation through the soils. This could negatively affect ground water recharge and therefore critical summer flows. Continued ground cover deficiency can also affect the hydrograph by increasing overland flows, which can cause erosion and possible sedimentation into the streams. This could negatively impact aquatic habitat and aquatic species such as the redband trout. Alternative 2 At a site scale, grass and shrub litter decay within the open semiarid forests drive the food webs. Currently there is a decline in the amount of open forest. The proposed treatments for late and old structures (LOS) recover or yield more characteristic open forest. With the proposed action there will be direct, indirect, and cumulative effects. Direct effects include recovery of ground cover with forest openings for improved nutrient litter cycles. The LOS also facilitates soil values that vary with ground cover, plant species, and litter. Chronic compaction effects from heavy logging equipment are apt to be minor. The minor ills may be offset by positive ground cover indirectly and cumulative effects that would increase the amount of water able to infiltrate along grass and shrub channels and be stored for forest growth. The creation of forest openings facilitate soil water storage and a longer season of forest growth within this dry environment. In a secondary way, openings may yield ground cover, as in grass waterways best known for increases in sub-surface flow, and could positively affect ground water recharge and therefore, critical summer flows. Relative to seasonal soil water storage and use for

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forest growth, recharge effects are apt to be minor. Like the Vegetation analysis, the relative the effects of the action alternatives may be measured by the acres of old growth (OG) treated, additional acres of late and old sturcture (LOS) development, and the acres of mid-seral treatments which would be the first steps in development of future LOS and inturn positive ground cover respone for gaiins in soil water use efficency. Over all, ill effects and impacts would be minimal when following Best Management Practices. Alternative 3 This alternative would have the same outcome as Alternative 2 with less LOS structure and therefore ground cover treated. There would be the same direct, indirect, and cumulative effects with this alternative; however, the effects and impacts would be minimal when following Best Management Practices. Alternative 5 This alternative would have essentially the same outcome as Alternative 2 with even less LOS and ground cover affected. II. Hydrology Watershed and Aquatics Specialist Report/Fisheries Biological Evaluation – Jakabe Watershed Enhancement Project – Jakabe Restoration Project Analysis File. Adresses: Issue 2. Juniper encroachment – Loss of wildlife, riparian, and deciduous plant habitat; reduced water quality; and increased soil movement has resulted with the advance of juniper woodlands. Issue 4. Restoration of riparian habitat – reduced riparian habitat due to encroachment, road densities and locations, and loss of stable upland vegetation. During the summers of 1998, 1999, and 2000, survey crews and resource professionals collected data across the analysis area obtaining current condition information about various watershed elements so that an assessment of watershed and aquatic resources could be performed. Information was gathered and summarized on a stream reach basis. In general, a reach is a segment of stream of similar gradient, valley type, etc. Only the primary perennial streams within the watershed were surveyed (Bear Creek, Coffeepot Creek, Ben Young Creek, Swamp Creek, and Chewaucan River). Within the 84,300 acres of the five subwatersheds, forested land covers 55,451 acres, approximately 66% of the subwatersheds. Of the forested acres, 51% or 27,984 acres have canopy densities exceeding the historical range of variability (HRV). When over 50% of forested communities are outside recommended canopy ranges, the forest stands are functioning inappropriately. Three of the five individual subwatersheds are functioning inappropriately and include the following: Ben Young (69%), Swamp Creek (60%), and the Chewaucan River (52%). The remaining two subwatersheds, Bear Creek and Coffeepot Creek, are functioning appropriately but-at-risk with nearly 40% of forest canopies exceeding HRV.

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Conifers have expanded into nearly every meadow and most riparian areas throughout the watershed, promoting competition with riparian vegetation (willow, aspen, cottonwood, alder) that is necessary to maintain proper stream types and bank stability. In addition, dense and vast juniper stands have become established throughout the landscape as a result of fire exclusion, especially in the Chewaucan River and Ben Young Creek subwatersheds. Approximately 99% of the juniper stands became established after 1860, the time of European settlement. These juniper woodlands have and are replacing numerous vegetation types, leaving the soils prone to erosion and reducing late summer stream flows. The increased conifer densities are likely contributing to lower base flows, but the extent is unknown. Fire suppression is the main reason for the watershed rating. The frequent and low intensity ground fires that maintained open stands of ponderosa pine have been suppressed since the early 1900s, allowing conifers to grow in higher densities than occurred historically in both forested and meadow sites. To a lesser degree, past silvicultural treatments, which emphasized clear-cutting, usually moved forest stands away from HRV. There are 372 miles of roads within the 84,306 acres of subwatersheds resulting in a road density of 2.82 mi/mi² (using the Forest Geographic Information System). Consequently the subwatersheds as a whole are functioning appropriately but-at-risk. Along with the 314 miles of stream channels within the five subwatersheds, an estimated 223 of the 372 miles of roads are hydrologically integrated with the stream network, thus increasing the drainage network by 71%, based on Wemple’s (1994) study results. Three of the subwatersheds have increased drainage networks that exceed this value – Swamp Creek (163%), Bear Creek (119%), and Ben Young (94%). The remaining two subwatersheds are below this value – Coffeepot (70%) and Chewaucan (43%). By 1946, 120 miles of roads (0.9mi/mi²) were constructed in the five subwatersheds. From 1947 to 1960, an additional 36 miles were built, raising the road density to 1.18 mi/mi². One hundred fifteen miles of roads were constructed between 1961 and 1969 bringing the road density to 2.05 mi/mi². Then, from 1970 to 1979, another 88 miles of roads were built – increasing the road density to 2.7 mi/mi². From 1980 to 1988, 11 miles of road were constructed, resulting in the current road density of 2.8 mi/mi². Most roads were built in association with high levels of timber harvest, especially after the Lakeview Sustained Yield Unit was implemented in 1950. It is believed the effects of the increased drainage network throughout the eight subwatersheds, from roads, have increased the number of days the Chewaucan River exceeds bankfull flows. Besides altering peak flows, roads also increase the sediment delivery into streams. Of the 372 miles of roads, 71 miles (19%) are within 300 feet of perennial and intermittent streams. Furthermore, roads cross channels at 304 locations – sites where direct sediment introduction occurs. Numerous sites along the thirty-three stream reaches were measured to determine Rosgen stream types (Appendix D). Of the 33 reaches 26 (79%) were functioning appropriately in terms of their potential stream type – as the shape and size of the stream channel is in balance with its setting. Twenty-one percent of the reaches are functioning appropriately but-at-risk, and none are functioning inappropriately. The three dominant stream types are E (42%), B (36%), and C (21%). Most stream reaches that are functioning appropriately (79%) are B and E stream types found throughout the watershed, while those that are functioning appropriately but-at-risk (21%) are mostly C stream types (and one E) that have width-to-depth ratios greater than expected.

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The Rosgen B stream types are usually located in forested reaches and within canyons, areas which are inherently stable. For this reason, forest management activities (such as timber harvest and grazing) have been conducted away from these stream reaches, leaving them relatively unaffected. However, the lack of fire continues to promote higher densities of mixed conifer and ponderosa pine in riparian areas along B stream types, creating a minor shift in relative plant species abundance. In addition, the E stream types found throughout the watershed are characterized and maintained by late-seral vegetation, resulting from grazing management which is conducive to late-seral plant composition. The majority of stream reaches that are not functioning appropriately are the C stream types and are located in large meadow reaches along the Chewaucan River. One stream reach that is not functioning appropriately is an E channel in Coffeepot creek which is also in a meadow. Early land management activities have influenced the current water table elevations and floodplain widths for the C and E stream types throughout the watershed. Beaver trapping and historical livestock grazing have led to downcut stream channels in low gradient meadows, converting C and E stream types with wide floodplains into F stream types with little to no floodplain. This resulted in lowered water tables with less water storage and lower base flows. As a result of improved livestock grazing strategies continually promoted on the watershed, E stream types have reclaimed many meadow sites, resulting in the reestablishment of floodplains dominated with late-seral riparian plants. However, the floodplains and areas of water storage are less extensive than they were prior to down cutting. This has likely reduced base flows within the watershed. Furthermore, beaver dams are not present in their historic numbers, further reducing the lateral extent of bank saturation and groundwater storage essential for maintenance of base flows during summer months. Stream temperatures were found to exceed state standards at numerous locations, and in all five of the streams. The Chewaucan River, Bear Creek, Coffeepot Creek, Ben Young Creek, and Swamp Creek are all listed on the State’s “303d” list of water quality limited streams, due to high stream temperatures. Because stream temperature affects fish habitat, and is an important factor regulating aquatic life within these streams, it is considered to be a limiting factor that may be affecting fish populations. Increased width-to-depth ratios (larger surface area being heated) in stream channels are generally considered to be the primary cause of elevated temperatures, the extent of which is unknown. It is also unknown if State stream temperature standards can be achieved even under natural or desired riparian and stream channel conditions in the Jakabe project area. Current hydrologic conditions, by reach or subshed, are summarized in the table below. Additional detailed information is contained in the Watershed and Aquatics Specialist Report/Fisheries Biological Evaluation in the analysis file.

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Indicators Functioning Appropriately

Functioning at Risk

Functioning at Unacceptable

Risk Bear Creek subshed

Upland forest vegetation (stream flow) Whole subshed

Road Density Whole subshed Riparian veg. & bank stability All reaches surveyed

Rosgen stream type All reaches surveyed

Ben Young Creek subshed Upland forest vegetation (stream flow) Whole subshed

Road Density Whole subshed Riparian veg. & bank stability All reaches surveyed


Chewaucan River subshed Upland forest vegetation (stream flow) Whole subshed

Road Density Whole subshed Riparian veg. & bank stability 2-4,8 6,11,13,16,18,19

Rosgen stream type 2-4,8 6,11,13,16,18,19

Coffeepot Creek subshed Upland forest vegetation (stream flow) Whole subshed

Road Density Whole subshed Riparian veg. & bank stability 1,4,6,7,9

Rosgen stream type 1,4,6,7 9

Swamp Creek subshed Upland forest vegetation (stream flow) Whole subwatershed

Road Density Whole subwatershed Riparian veg. & bank stability 2-6,8 1


a. Upland Forest Vegetation (stream flow): Alternative 1 (no action) Not implementing any management activities addressed in the proposed action (commercial and precommercial thinning in conjunction with juniper removal and prescribed burning) the current conditions within these subwatersheds could potentially degrade. This is due to increasing high

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canopy densities; juniper encroachment; and lack of fire, which results in decreased shrub and grass density decreasing soil cover and infiltration rates. Because of decreased soil cover and infiltration rates, increased overland flow and soil erosion often occur. Therefore, there is a potential loss of water available for stream flow during dry summer months due to unusually high amounts of water that are lost to overland flow and/or evapotranspiration due to high canopy densities and encroaching juniper. If current conditions degrade in reference to uplands, then habitat for aquatic species could also degrade, not meeting the need of protection and improvement of aquatic and terrestrial habitat. Furthermore, by perpetuating unusually high stand densities the probability for catastrophic fire increases. A catastrophic fire has the potential to decimate a stream and its aquatic species by leaving no shade adjacent to the stream (increased stream temps) and by denuding subwatersheds of vegetation thereby leaving exposed soils (increased sediment in streams). There would be no direct effects to the aquatic habitat with this alternative; however there will be indirect effects such as decreasing soil cover and infiltration rates and increasing overland flow and soil erosion. In the long-term there would be the cumulative effects discussed above (encroaching junipers, decreasing soil cover and infiltration rates, increasing overland flow and soil erosion) further deviating from the project need. Alternative 2 (proposed action) Implementing the proposed action, the Forest Service will begin to restore the upland plant communities by thinning and prescribed burning to reduce canopy densities and improve shrub/grass density, soil cover, and infiltration rates as addressed in the Chewaucan Watershed Analysis. By restoring the densities of shrubs and grasses and restoring infiltration rates, overland flow would lessen and therefore potential sedimentation into the stream would be reduced. With a potential increase in infiltration rates there could be an increase in stream flow during the critical dry summer months. Infiltration restores lost ground water that recharges the streams in late summer. Riparian vegetation would increase, providing natural, beneficial shade. Although there could be short-term adverse effects after thinning/harvesting the uplands by using heavy equipment (potential soil compaction), the long-term and cumulative effects of reduced canopy densities, shrub/grass density and soil cover, and improved infiltration rates would be beneficial. Also, by restoring the historic low intensity fires, fuel levels will be kept at a minimum thereby reducing the possibility of a catastrophic fire. Therefore, this action would be in compliance with the Riparian Management Objectives identified in INFISH, would benefit stream habitat for aquatic species, and meets the need for the project. In addition to these effects, there will be both positive and negative indirect effects. Indirectly, there is potential for exposed soils to erode after rainfall and eventually enter the streams after an area has been treated using heavy equipment. However, soil compaction levels would not go above current conditions by using selected BMPs (existing skid trails and roads). Alternative 3 This alternative would have the same outcome as Alternative 2 (restore reference conditions). Therefore, this alternative would be in compliance with the Riparian Management Objectives identified in INFISH. Alternative 5 This alternative would have the same outcome as Alternatives 2 & 3 (restore reference conditions), but to a lesser extent. Therefore, this alternative would be in compliance with the Riparian Management Objectives identified in INFISH.

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b. Road density: Alternative 1 (no action) Not obliterating or permanently closing a road, the drainage network of a stream significantly increases, as identified in the first issue of the Chewaucan Watershed Analysis. Roads directly affect the channel morphology of streams by accelerating erosion and sediment delivery and by increasing the magnitude of peak flow. The current conditions of these subwatersheds could potentially degrade by not obliterating roads. Indirectly, if current conditions degrade then habitat for aquatic species will also degrade. The more roads and stream crossings the more easily sediments can enter the streams via the roads, cumulatively affecting the hydrologic function. In addition, roads affect the hydrograph and drainage density, increasing peak flows and decreasing low flows. This alternative does not meet the need for protection and improvement of aquatic and terrestrial habitat. Alternative 2 (proposed action) By implementing the proposed action, the Forest Service will begin to restore the hydrologic flow and reduce sediment transport into the streams within the subwatersheds as stressed in the Watershed Analysis. Although the road densities will decrease if the proposed action is implemented, the amount of roads obliterated will not change the functioning rating for the subwatersheds. There are 22 miles of roads proposed for obliteration within the proposed action. Most of these roads run parallel to the streams and/or have stream crossings. Although there will be potential short term adverse effects by an initial increase of sediment entering the streams after ripping of the roadbed, the long-term effects would be beneficial and would move to restore the subwatersheds to functioning appropriately. Therefore, this action would be in compliance with the Riparian Management Objectives identified in INFISH and would benefit stream habitat and consequently benefit aquatic species. Indirect and cumulative effects would be improved hydrologic function over time as the roadbed settles and vegetation re-appears. Alternatives 3 and 5 These alternatives would have the same outcome as Alternative 2 (restore current condition). Therefore, they would be in compliance with the Riparian Management Objectives identified in INFISH and would have the same direct, indirect, and cumulative effects and determinations as Alternative 2. c. Riparian Vegetation and Bank Stability: Alternative 1 (no action) Not implementing any management activities addressed in the proposed action (obliterating roads, reducing canopy densities, prescribe burning, reducing encroaching juniper) there is potential for the current conditions to degrade, thereby not meeting the project need. Riparian vegetation and bank stability would decline due to high tree and road densities (less water available for subsurface flow, increased overland flow, and potential for accelerating erosion, sediment delivery, and increasing magnitude of peak flows). Increasing magnitude of peak flows, an issue identified in the Watershed Analysis, typically down cut the stream channel thus creating unstable banks and altering riparian vegetation. Riparian vegetation would reflect conditions that are suited towards a dryer climate (lower water table due to incised stream channel) such as grasses and sage. Grass and sage species have less root mass than riparian species and therefore do not have the ability to stabilize the incised stream banks. Consequently, the no action alternative would be detrimental to the aquatic habitat and therefore detrimental to aquatic species. The more roads and stream crossings

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the more easily sediments can enter the streams via the roads. If current conditions degrade, then habitat for aquatic species would also degrade. Alternative 2 (proposed action) Implementing the proposed action such as obliterating roads, reducing canopy densities, prescribe burning to reduce risk of catastrophic fire, along with the reduction of juniper; the Forest Service will move the watershed toward hydrologic restoration. By restoring the watershed to desired conditions, the indirect and cumulative effects would be more water available for subsurface flow, decreased overland flow, a decrease in potential erosion, decrease in sediment delivery, a decrease in the magnitude of peak flows, and more water available to the stream during periods of low flows. These decreases will benefit and help restore the riparian vegetation by not scouring and downcutting the channel. Therefore, the proposed action is in compliance with the Riparian Management Objectives identified in INFISH and consequently will help to improve stream habitat for fish and other aquatic species, meeting the project need. There would be short-term indirect effects with this alternative due to the potential for sedimentation to enter the streams. Alternatives 3 and 5 The effects of these alternatives would have the same outcome as the proposed action, Alternative 2 (restore current conditions). Therefore, these actions would be in compliance with the Riparian Management Objectives identified in INFISH. d. Rosgen Stream Type: Alternative 1 (no action) Not implementing any management activities addressed in the proposed action there is potential for the current conditions to degrade. Riparian vegetation, bank stability and therefore stream type could degrade because of high tree and road densities. Increasing magnitude of peak flows could cause the stream channel to incise thus creating unstable banks, altering riparian vegetation, and changing the functioning stream type to one that does not function appropriately; again outside the need for the project and issues identified in the Watershed Analysis. Riparian vegetation would reflect conditions that are suited towards a dryer climate such as grasses and sage. Grass and sage species have less root mass than riparian species and therefore do not have the ability to stabilize the incised streambanks. Consequently, the no action alternative would be detrimental to the aquatic habitat and aquatic species. If current conditions degrade, then habitat for aquatic species will also degrade. Indirectly, the more roads crossing streams the more easily sediments can enter the streams and alter stream substrate characteristics. Furthermore, the roads have a tendency to deliver water through a system faster than if they were not in the system adding to the cumulative effect of poor water quality. Alternative 2 (proposed action) Implementing the proposed action the Forest Service will move toward restoring stream channel functions. Restoration of the watershed to desired conditions will make more water available for subsurface flow, decrease overland flow, decrease potential erosion, decrease sediment delivery, decrease the magnitude of peak flows, and provide more water to the streams during low flows. Therefore, the proposed action is in compliance with the Riparian Management Objectives identified in INFISH and consequently will help to improve stream habitat for aquatic species and meets the need of the project. Short-term, adverse, direct effects would be due to the potential for sedimentation to enter the streams.

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Alternative 3 and 5 The effects of these alternatives would have the same outcome as the proposed action, Alternative 2 (restore current conditions). Therefore, they would be in compliance with the Riparian Management Objectives identified in INFISH. Determinations would be the same as for Alternative 2. III. Vegetation a. Forested Stands Upland Forest Vegetation (an overview), Chewaucan Watershed – Ecosystem Analysis at the Watershed Scale, 1999; Jakabe Vegetation Management Report, December 12, 2002 with updates; Addendum August 2, 2004 Addresses: Issue 2. Juniper encroachment – Loss of wildlife, riparian and deciduous plant habitat;

reduced water quality; and increased soil movement has resulted with the advance of juniper woodlands.

Issue 3. Aspen stands – Conifer encroachment of aspen stands has resulted in lost stands, reduced quality of stands, and reduction of aspen stand habitat dependent species.

Issue 4. Restoration of riparian habitat – reduced riparian habitat due to encroachment, road densities and locations, and loss of stable upland vegetation.

Issue 5. Improve sustainability of late and old structure stands – LOS stands are diminishing because of increased stocking and a shift of species composition

Three basic forest plant community types occur within the Chewaucan watershed. They are ponderosa pine, true mixed conifer, and high elevation lodgepole pine types. It is critical to consider that in the following discussion, “mixed conifer” discussions refer to the current conditions of a stand. Many of the areas currently discussed under “mixed conifer” were ponderosa pine dominated, frequent fire communities until the period of fire exclusion. The ecoclass typing system currently used in this area is based on plant community "typing". The plant community type represents the current plant assemblage. Community typing classification on some sites can change, from a CP to CL or CW, depending on the plant assembly present at the time of classification. Plant community types do not well represent either the climax type, as a habitat typing system would, or the site condition under a natural fire regime. The ponderosa pine (Pinus ponderosa) type is by far the most dominant forest plant community within the watershed. Estimates from the Forest's geographic information system (GIS) identify approximately 27,400 acres (73% of forest capable lands) to be ponderosa pine type communities. Ponderosa pine plant communities exist and thrive at the drier, warmer end of the climatic spectrum of forest types. These stands are the dominant conifer type up to 6000' elevation, as well as southern and western exposures at even higher elevation. Ponderosa pine stands will include white fir and lodgepole pine, displaying a "mixed conifer" phase or plant community type, then lodgepole pine with increased elevation. The mixed conifer phase (sometimes called “pine associated”) in these types is a white fir and lodgepole pine expansion as a result of fire exclusion. Without fire exclusion, these types are a frequent fire regime, LOS ponderosa pine stand with components of white fir and other species. Large ponderosa pines are scarce in the true mixed conifer type. On the very dry end, at lowest elevations or on excessively drained soils, western juniper (Juniperous

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occidentalis) makes up a portion of the tree layer. Most of this juniper type has also developed as a result of juniper expansion as a result of fire exclusion. Prior to fire exclusion Juniper was a very minor component of these types, and totally absent from some areas. At the more moist end, at higher elevations, and northern exposures, white fir (Abies concolor) will appear in the stand which is the beginning of a grade into the true mixed conifer type. The past fire management strategy of prevention, detection, and suppression has altered the fire ecology which forced the development of the open park like stands. With fires not playing a role, ponderosa pine stands are becoming multistory structures. Stocking levels have become drastically elevated compared to historic conditions. The speed at which stands have shifted from single to multistory structures has been remarkable until one realizes that due to fire exclusion, up to ten fire cycles may have been missed. Because of this lack of maintenance fires, wildfires in this type today will often produce stand replacement conditions. Fire prevention strategy has driven the most drastic changes within ponderosa pine stands. Understories of ponderosa pine, and in many cases lodgepole pine and white fir, have developed in the absence of frequent, low-intensity fire. Increases of stocking, and expansion of juniper, lodgepole pine and white fir has resulted in major changes in vegetative types. These changes are outside the range of adaptability for sustainability of the reference area structure and composition. These multistory stands are taxing the growing space provided on most sites. Only where fire has been carefully prescribed under the natural fuels program have a few stands been maintained in a single story structure which was historically the norm. Even in these stands the density has increased above the historical norm and threatens the resiliency of these stands to stand replacement mortality from insect and disease agents. Management practices this century have defined the structural stage and species distribution within the watershed. Management within the ponderosa pine types has been more extensive than intensive. Early activities were designed to conserve and protect the resource while capturing mortality. Fire prevention programs coupled with "high risk" removals across the whole watershed have left many stands deficient in snags, leaving overstocked understories and symptoms of multiple entries and multi storied structure. Where overstories have been mostly removed and the advanced regeneration managed, stands yield most of today’s mid-seral component. In the 1960s and 70s, dwarf mistletoe control was implemented within the Coffeepot and Ben Young Creek subwatersheds resulting in extensive, mosaic-like plantations and a few large stands which had most large and many mid-sized PP removed. Clear-cutting blocks became more common across the whole watershed in the 1970s and 80s. All these areas were planted at typical densities of 300 to 400 trees per acre. The largest diameter early seral, along with the mid and later seral areas exhibit densities that predispose the stands to attack by bark beetles, particularly mountain pine beetle.

Current Seral Stage Distribution in the Ponderosa Pine Type Early (unstocked to sapling size) 15% (all single story and within mosaics) Mid (post, poles and small saw timber) 30% (75% single story, 25% multi story) Late (medium sawtimber and greater) 55% (5% single story, 95% multi story)

Mixed conifer stands occur across approximately 7,530 acres (20% of forest capable lands) of the Chewaucan watershed. Relative to the ponderosa pine types, these stand types exist at higher

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elevations and northern exposures. With fire exclusion, ponderosa pine is the early-mid seral dominant species while white fir is the dominant climax species. Within these plant communities, ponderosa pine and white fir will dominate with highly variable cover percentages that range from 5 to 75%. Lodgepole pine can also become a component in the stand but is not usually in a dominant or codominant position, though it will be an early pioneer following disturbance. Species composition depends upon the position of the stand within the landscape, past disturbance regimes, and moisture/site relations. In most cases within the Chewaucan watershed, ponderosa pine will be the dominant species in the overstory. Ponderosa pine in the understory is out-competed when shade tolerant white fir or fast growing lodgepole are present. Most mixed conifer stands today exhibit abundant white fir in the understory, which relates to the area's fire ecology. Most mixed conifer stands in the Chewaucan watershed exhibit abundant white fir in their understory. The fire free period experienced this century has led mixed conifer stands, which evolved similar to open ponderosa stands, into dense stands of true fir at unprecedented stocking levels. Even on the south/southwest aspect of upper Bear Creek, young white fir is present and if left undisturbed will persist, eventually dominating this site until the next fire event occurs. That event, which was historically a maintenance intensity fire, will likely be a stand replacement event. Two other conifer species grow within mixed conifer stands in the Chewaucan watershed. Incense cedar (Calocedrus decurrens), and sugar pine (Pinus lambertiana) make up only a small portion of the overall composition of the tree layer but can be a common part of a given stand. Sugar pine tends to be a seral species while incense cedar will be climax. These two species occur at the most northern and eastern extent of their natural range. It is important to note that although threats by insects and diseases seem numerous, they tend to be species specific. Mixed conifer stands often offer a complexity of species distribution, which lends to a resiliency within the stand. This resiliency does not mean that a particular structural component, such as large old trees, will be maintained. It does mean that some species will be capable of regeneration and maintenance of some level of stocking on the site at most times. Management within the mixed conifer stands began much as it had with the ponderosa pine type. Protecting and capturing mortality of the valuable pine overstory was paramount. By far, most of the intensive forest management practices occurring on the Fremont National Forest were implemented in these relatively productive mixed conifer types. Due to the management imposed fire exclusion period allowing white fir encroachment, partial overstory removals became practical and common. Valuable ponderosa was harvested and the fast growing white fir understory was retained and managed as advanced regeneration thus avoiding the cost of artificial regeneration. Clear-cutting became a common practice in the 1970s and 80s when the fir understory was deemed too suppressed to be released. Just as in the ponderosa pine types, these plantations were planted at densities that will require precommercial thinning. To date, very little prescribed underburns have occurred in mixed conifer types. The natural fuels underburn project plan addressed only treating ponderosa pine types. In 1994, some acres of mixed conifer were underburned between drainages that feed Long Hollow. This burn demonstrated how fire can differentially thin white fir and pine. White fir mortality exceeded the ponderosa mortality, due to both white fir’s greater susceptibility to fire kill and its generally smaller size.

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Current Seral Stage Distribution in the Mixed Conifer Type

Early (not stocked to saplings) 20% (all single story) Mid (post, poles and small saw timber) 5% (25% single story, 75% multi story) Late (medium sawtimber and greater) 75% (all multi story)

Lodgepole pine (Pinus contorta ssp. murrayana) has the widest adaptive amplitude of any conifer on the Fremont. It is found growing space across the watershed at all elevations, but climax lodgepole pine stand types occur on only 2,465 acres (7% of forest capable lands) within the Chewaucan watershed. These are the acres where lodgepole is either climax or the persistent seral species. This species is the most cold-hardy of all the conifers on the Fremont occurring at the highest elevations within the watershed. Lodgepole pine is also found along edges of ponderosa pine and mixed conifer stands where the stands reach down into low laying areas where cold air becomes restricted (frost pockets) or in any concave topographic feature where cold air may become trapped. Between disturbances, lodgepole pine will frequently encroach into areas such as aspen and grass meadows. These areas tend to be too cold or wet for other conifers. Lodgepole pine is a seral species where it interfaces with most other conifers and will establish itself quickly following a disturbance. Being relatively short-lived it cannot successfully compete long-term with ponderosa or white fir. The current bark beetle activity was active first in the lodgepole pine and has resulted in high degrees of activity, especially in the lodgepole that has expanded into other types. Currently there is almost no mortality in the true high elevation lodgepole type. Management within the Chewaucan watershed of the lodgepole pine type came late and was intense. In 1978 approximately one half of the lodgepole pine in upper Bear Creek was regenerated under the Bear Creek Lodgepole project. The intent was to convert these late and old stands to younger more productive conditions. The least productive sites were excluded from treatment. The seed tree system was employed and regeneration was established by natural regeneration. Some ponderosa pine was planted on this site. The ponderosa grew well on the ridges but received frost damage elsewhere. The areas became well stocked with over 500+ trees per acre. In 1995-1997 most of these areas were precommercial thinned to approximately 200 trees per acre. No prescribed burning has occurred within any pure lodgepole pine types within the Chewaucan watershed.

Current Seral Stage Distribution in the Lodgepole Pine Type Early (not stocked to saplings) 35% (all single story) Mid (post, poles and small saw timber) 0% Late (medium sawtimber and greater) 65% (all multi story)(see fire & MPB)

Historic Conditions Stand information collected by Thorton T. Munger (Yellow Pine in Oregon, 1917) on similar types north of the project area showed stands ranging from 8-20 trees per acre greater than 16” dbh. The majority of the trees were between 16-32” dbh. Munger’s observations probably represent the high end of the historic range of variability (HRV) as these stands were measured just before a long period of bark beetle mortality that resulted in 50-70% or higher large tree mortality. To compare this

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data to the Jakabe proposals, HRV by basal area (BA) is estimated to range from 30-70 for these stands at the high end of the range, and potentially 10 to 30 BA for the low end of the range. The additional significance of these numbers is a strong indication of the vegetative conditions that the native species adapted to, within normal climactic variations, for many generations. Munger’s observations were also made at the end of a very wet period, notable in several ways including the homestead era in the Ft Rock Valley due to the success of dryland farming at that time. The Forest Service Pacific Northwest Region Interim Old Growth Definition for the Ponderosa pine series indicates a potentially higher maximum Range. Hopkins (1992) identified old-growth ponderosa pine stands in Oregon and Washington in the Ponderosa type as containing:

• For areas of low site productivity: per acre, 10 to 30 trees of 21”(or greater) dbh with a BA range of 24-72+, and two to six trees of 31” (or greater) dbh with a BA of 11-32+, for a total stand basal area of 35 to 104+.

• For areas of moderate-high site productivity: per acre, 13 to 45 trees of 21” (or greater) dbh with a BA range of 31-110+, and three to eight trees of 31” (or greater) dbh with a BA of 14-40+, for a total stand basal area of 45-150+.

The above categories describe the HRV applicable to late and old ponderosa pine stands. Most of the ponderosa pine stands within the project area would be classified as being at low site productivity area, with a BA range of 35 to 104+. These upper ranges were estimated with large diameters, which may not be representative, and resulted in these higher total basal area numbers. A few stands on the more productive sites, such as those on higher, wetter sites with inclusions of white fir, are n the HRV BA range of “45-150+”. The moderate to high productivity range situation is found on only a small number of the stands in the project area and few of them are planned for treatment. These stands at best should be classified in the moderate site productivity, with an estimated high HRV BA range of 40-120.

The low end of the range is indicating that the stands do meet the regional definition of old growth, not that the number indicates the low end of variability of the stand type. However, the lower number is not a bad surrogate for a value near the low end of the range.

Historically, the seral stages in all community types were distributed with more acres in the single-storied late and old structure, less acres in the mid-seral condition, and relatively few acres in the multi-storied late and old structure. Acres taken from the Chewaucan Watershed Analysis, for the Chewaucan Watershed, not broken down by subshed, as all would be below HRV Early Seral Mid Seral Late Seral

Single Story Late Seral Multi Story

Current Condition 6500 16,400 20,650 Estimated HRV 0-7000 0-7000 28-35,000 0-2500

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Reference Seral Stage Distribution in the Ponderosa Pine Type Early to Mid (nonstocked to small sawtimber) 20% (95% single story, 5% multi story)

Late (medium sawtimber and greater) 80% (95% single story, 5% multi story) Data interpreted from the 1994 REAP Report and the 1947 timber type map.

Reference Seral Stage Distribution in the Mixed Conifer Type Early to Mid (nonstocked to small saw timber) 40% (95% single story, 5% multi story) Late (medium sawtimber and greater) 60% (5% single story, 95% multi story)

Data interpreted from the 1994 REAP Report and the 1947 timber type map.

Reference Seral Stage Distribution in the Lodgepole Pine Type Early to Mid (nonstocked to small saw timber) 40% (0ne to ten acre patches) Late (medium sawtimber and greater) 60% (all multi story)(see fire & MPB)

Data interpreted from the 1994 REAP Report and the 1947 timber type map. Treatments and Historic Range of Variability These prescriptions are designed to move the area through the range of historical variability and develop a sustainable stand condition resistant to stand replacement events such as fire and insect and disease. It is not intended, however, that the stands will become more homogenized. On the contrary, especially if the entire spectrum of vegetation is considered, over time the stands will develop more diversity than currently present. The one exception would be that the small tree component will universally be reduced. However, it will recover rapidly and indeed only the presence of frequent underburning will limit that component. Irrespective of HRV, there are multiple analysis tools available that point to the targets used to develop the desired condition post treatment. These are also all developed with the objective of developing sustainable stands independent of need for frequent harvesting/thinning interventions. The Forest Vegetation Simulator (FVS) run with Continuous Vegetation Survey (CVS) plots from the area show that these stands are currently at high, or in a few cases moderate, risk of mortality from bark beetles. A more local guide, Cochran’s Plant Association Average Stocking Curves is also used for representative ecoclasses. Cochran’s suggested stocking levels are referenced for two ecotypes, CPS211 and CPS217. These two ecotypes are representative of the average acres in the planning area. It is well recognized that due to the large area covered in this project, there are stands planned for treatment that cover the full spectrum of types in the low fire intensity ponderosa pine type. But most of the acres fall close to the average range. For the CPS211 type the upper management zone is identified at a stand density index (SDI) of 116. For example, a SDI of 116 equates to 116 - 10” dbh trees (63 BA), 41 - 18” dbh trees (72BA), 31 - 21” dbh trees (75BA), or 16 – 30” dbh trees (81BA). In general, the target leave BA for this entry will be approximately one half of the upper management zone rounded up to the next high 10 BA, or about 40 BA leave, except in areas of many large diameter trees. Another exception is that the target leave stand will be prescribed to not exceed 40 leave trees per acre. Therefore in the few areas of very small leave trees, the leave BA could be as low as 20.

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For the CPS217 type the upper management zone is identified at a SDI of 124. This type is slightly more productive, but not enough to change the desired leave density on an average site. For example, an SDI of 124 equates to 124 - 10” dbh trees (68 BA), 44 - 18” dbh trees (77BA), 33 - 21” dbh trees (80BA), or 18 – 30” dbh trees (87BA). In general, the target leave BA for this entry will be approximately one half of the upper management zone rounded up to the next high 10 BA, or about 40 BA leave except in areas of many large diameter trees. Another exception is that the target leave stand will be prescribed to not exceed 40 leave trees per acre. Therefore in the few areas of very small leave trees, the leave BA could be as low as 20. Within both of these types there is a range of variability that can result in leave stands ranging between 20-60+ BA; and clumps within those areas that may be 100+ BA, due to large numbers of trees greater than 21” dbh that will not be cut. Unit-by-unit treatments are identified in Appendix F. Old Growth Treatment The relative effects of the action alternatives may be measured by the acres of old growth (OG) treated, additional acres of late and old sturcture (LOS) development and the acres of mid-seral treatments which would be the first steps in development of future LOS.

Treatment Alternative 2, ac Alternative 3, ac Alternative 5, ac OG treated to LOS Rx 2859 2422 1195 Additional LOS 4591 3946 2462 Mid seral 2745 2516 2145 10195 8884 5802

Alternative 1 Conditions in the Chewaucan Watershed would remain the same, short-term but long term effects would be increased risks affecting ecosystem sustainability because of conifer encroachment in riparian and meadow areas, loss of LOS conditions through stress on the larger trees with increased occurrence of early and mid-seral stage trees, and a shifting of desired species composition and stocking levels. The risk of catastrophic fire would increase with the added ladder fuels and increased stress-related mortality. Aqautic and terrestial habitat would not be protected by these vegetative changes. There would be no opportunity for economic return to the local communities from vegetation management. Alternative 2 treats the most acres (10170) across the landscape and in the long run would produce the most acres of old growth in a landscape condition offering more protection from large scale wildfires and other stand replacement risks. Vegetation management in the uplands would provide more watershed stability thereby improving hydrologic functions and overall watershed health. Alternative 3 treats about 13% fewer acres than Alternative 2. Leave areas are scattered throughout the project area. The leave areas would continue to lose large trees to stress related mortality, and could serve as breeding zones for increased bark beetle populations, causing increased mortality in the proximity of the leave areas. The landscape condition should produce some protection from large wildifres.

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Alternative 5 treats about 44% fewer acres than Alternative 2, but more significant now is the amount of untreated stands in the area. 85% of the old growth stands are untreated and very little protection is provided, at the landscape level, from large scale wildfire and insect and disease population development. The treatments in the goshawk stands, connectivity corridors, and RHCA areas are far less intensive than the rest of the treatment prescriptions. They will help to maintain the exisiting condition of the small amount of old growth treated, but are not expected to provide substantial long term benefit.

• All alternatives maintain or enhance old growth resource. Vegetative prescriptions are designed to develop single story LOS structure development at a lower density, which should greatly increase the longevity of LOS structure. Losses to fire and stress related mortality due to insect and disease agents should be greatly reduced as the individual trees respond to the change. The duration of this individual mortality may vary from 10-30 years or longer if conifer and surface vegetation regeneration is controlled through either use of fire or mechanical methods. The shorter duration of vigor is a result of the presence of localized high density of trees greater than 21” DBH and/or trees not cut to the desired stocking level for a resource or regulation issue.

• The planned enhancement prescriptions do, in the short run, somewhat reduce the

decadent aspect of the old growth habitat. The degree this occurs depends on the stand conditions, and is not a deliberate act but a byproduct of the culturing and fire application following treatment. The exeption is where the decadent aspect is produced by white fir encroachment. White fir will be removed in order to develop a more sustainable ponderosa pine stand.

• Not all acres of identified OG are planned for treatment for a variety of reasons. These

stands will, for a time, contribute to the old growth habitats and contain especially high percentages of dead, dying and rotted wood to provide those habitats. The most likely prognosis for the sustainability of most of these stands is short, about 1-2 decades. There is a large block of OG in the Bear Creek drainage which is still in one large block and at high risk to loss from wildfire or stress related mortality. The remainder of the old growth blocks are more scattered and so while individually are still at high risk for loss, collectively they are not at high risk from loss from a single event.

Riparian Treatments

Approximate Acres treated within Riparian areas: Alternative Acres of RHCA treatments2 2609 3 2417 5 1767

The table above shows the relative gross amounts of proposed riparian treatment by alternative. For this issue, acres of treatment are not as valuable a measure of response. While there are acres of treatment proposed, the proposed treatments are very light. They may help retard futher loss of riparian dependent resource values, but they will do little to enhance them. These riparian areas are

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those capable of growing conifers; which are also those most capable of producing the more valuable riparian dependent values. These areas can produce the riparian hardwoods valued by wildlife, the deepest shade that can help maintain cooler water temperatures, and the vegetative buffers that can best protect the water from adjacent hillside erosion. Alternative development to address this issue is limited by the current need to maintain shade on most of the perennial streams. Much of the shade currently present on these riparian areas is contributed by conifer encroachement into the riparian environment. Due to these conditions, the restoration of riparian areas will be a long term proposition. All action alternatives achieve a small level of riparian area improvement, and will improve the upland vegetative condition. This will provide for instream improvement, which should result in increased streamflow that maintainance of the existing shading on much of the area will become less of an issue for future treatments. Watershed/Ecosystem Enhanced Functioning Acres treated is the most appropriate measure of watershed/ecosystem enhanced functioning, with a focus on the early, LOS, and mid-seral treatments as the acres contributing most. The current condition of most of the vegetation in the conifer and juniper types is not functioning as the species have evolved to optimize their ability to persist and reproduce, and is not functioning in a manner consistent with the pre-fire suppression system for the type. Due to a combination of factors, predominantly fire suppression and to a lesser degree past harvest, the ponderosa pine stands have changed from a low density, low number of trees per acre, predominantly mature single story stands of ponderosa pine to a high density, very high number of trees per acre, multi story stand which may be still dominated by ponderosa pine or a mix of white fir and ponderosa pine. In a few cases, the ponderosa pine is nearly absent. Past harvest in some cases has removed the ponderosa pine large tree component and has aided the shift to white fir. Insect and disease agents, considered stress related mortality, have also contributed in the reduction of the large ponderosa pine component. The major significance of this shift is that the trees no longer function as individual trees in response to a damaging agent, such as fire, insects or disease, but respond much more as a stand. Wildfires burn with much greater intensity and in the higher stocked stands may easily cause 100% mortality. This condition is outside of the range of adaptation for ponderosa pine to reproduce and survive, considering reproduction is a key element of fitness. Insect and disease agents are less dramatic than wildfires, but the combination of their mortality, understory ponderosa pine competition, and surface litter conditions may also severely limit reproduction success. The severely supressed small ponderosa pine layers do not seem able to develop out of that condition unless some outside agent releases individual trees from the supressed condition. The vegetative conditions in the LOS and mid-seral stands are designed to facilitate effective and economical use of fire immediately after treatment. Presribed fire use in these areas can be of an intensity that greatly reduces the potential for intense fire behavior for 5-10 years following treatment. Implementation Strategy to Minimize Snag Falling Implementing only units that fit into a category of low risk for hazard trees in reforestation areas would reduce the number of snags cut for safety purposes. Units, or portions of them, may not meet

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the project objective of sustainable LOS development and reintroduction of fire where pockets of mortality in large trees occur. These areas will need to be protected from underburning. Only ground-based acres are included due to assumed hazard associated with helicopter and cable units.

Condition 1: Alternative 2, 3, or 5; approximately 2200 acres These are ponderosa pine stands that have had understory thinning and should develop/retain more ponderosa pine LOS. While this structure can lead to a reforestation with hazard tree felling need, they are not at risk if entered soon. Most of these stands are in Alternative 5. Condition 1a consists of few snags in the stand and assumes all activities are completed within five years to avoid further mortality. This condition covers approximately 1100 acres. Condition 2: Alternative 2 - 1300 acres, Alternative 3 - 900 acres, Alternative 5 – 0 acres These are stands, or portions of stands, with a stocked understory that has not been thinned. Stands should retain/develop some ponderosa pine LOS at a moderate risk if entered soon. Condition 3: Alternative 2 – 1600 acres, Alternative 3 – 1400 acres, Alternative 5 – 900 acres This condition includes stands with a stocked understory level of more than 80% of the area. These are most of the stands containing lodgepole pine and white fir along with ponderosa pine. Stands in this condition will develop/retain little ponderosa pine LOS while maintaining a stocked small tree stand of white fir/lodgepole pine.

The goshawk and corridor treatments will create a vegetative condition more compatable with a low intensity prescribed burn. The burning prescription for these areas, especially the connectivity corridors, will be designed so there is almost no mortality in the 10” dbh and greater size classes. This burning will be of lower effectiveness and higher cost than the burning in the LOS and mid seral prescription areas. There should be some reduction in wildfire intensity should a wildfire burn through these areas after precribed burning. However, depending on the fire weather at the time a wildfire may cause either minor or significant mortality in these stands. One reason is the canopy will be closed enough to retain heat and under some conditions carry a wind driven fire. The post treatment underburning is not expected to be hot enough to remove much more than the fine fuels and a small portion of the larger fuels. This should result in a short term reduction in fire intensity as the fuel ladder will be somewhat disrupted, but as surface vegetation regrows and litter increases the flamability of the surface layer will also increase. Economic Response

Estimated volume production for each alternative Estimated Total sawtimber volume.

Alt 2 Alt 3 Alt 5

MMBF 37.3 33.7 19.9 Additional fiber volume may be included in all alternatives, depending on demand.

The potential for utilization of small trees in this project by a biomass plant would contribute to achieving project objectives and would have no additional impacts. Determination of the amount of

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available biomass is problematic due to both a lack of a definite, site-specific plant and the fact that biomass opportunities are not well defined and are rigidly controlled by economics. Biomass production would not be a project objective but rather a method of achieving the project objectives. In that light, it is important to understand that the stands selected for treatment were not selected to maximize biomass output but rather to meet the project objectives. A result of this is the selected treatment areas would not necessarily produce as much biomass as might be expected from the area based on forest-wide or even localized projections. The following tables estimate Jakabe biomass potential output by alternative. Because this project is in the Lakeview Sustained Yield Unit, assumed commercial harvest includes the 9-20” dbh component and the biomass component would be the 4” to 9” dbh material and the unmerchantable portion of the commercial component. The bone dry tons/acre (BDT/ac) were developed using CVS plots in the Jakabe and Upper Sycan planning areas and stratifying by ecoclass. Ecoclasses not represented by Current Forest Vegetation Survey (CVS) plots were estimated from other types. The number of available plots is short of any statistically sound estimate. Therefore, another assumption is that while the total may be representative of the area and in general, the lodgepole and fir types produce much higher biomass output, the accuracy of any individual ecoclass BDT/ac is limited. Alternative 2

Ecoclass Total Acres

Ground based logging system acres

Average est. BDT/ac on

ground-based acres

Total BDT

Lodgepole pine types 257 251 12 3579

Ponderosa pine types 7432 3543 4 10062

White fir/mixed conifer types 2714 1682 12 22901

Totals 10403 5476 36542

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Alternative 3




ground-based acres

Total BDT




Totals 9000 4835 32166 Alternative 5




ground-based acres

Total BDT




Totals 5614 3141 18831 Cumulative effects The activities which have had the most profound effects on the conifer vegetation in the Jakabe watershed have been timber harvest, thinning, tree planting, fire suppression and prescribed burning. Grazing has potentially had a lesser effect.

Past activities on Forest Service managed lands: Harvest activities fall into two categories for cumulative effects analysis; those activities which have resulted in a current changed condition to the vegetation and those which have not. Most acres outside of the lodgepole pine type have had some minor level of harvest as described in the preceding section. Approximately 10,784 acres, of the 57,293 acres of Forest Service lands, have had a timber harvest or silvicultural activity that has had the effect of an identifiable stand change from adjacent stands.

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The Decision Memo for Jakabe Juniper has authorized additional acreage for juniper and associated species cutting. Approximately 4000 acres is in implementation stage. The amount of activity by type and sale name where applicable, is displayed in Appendix E. Industrial Forest and Other Private Land Ownership Approximately 15,984 acres of private industrial forest ownership is within the Jakabe Analysis Area. About 90% of this type has had past timber harvests that have resulted in significant stand changes, removing most of the large and mid-sized trees. The remaining stands are dominated by advanced reproduction approximately 20+ years old. Approximately 5755 acres are in other private ranch or individual ownership; predominantly non-forested grazing land. Of the forested areas, small holdings have been harvested.

b. Proposed, Endangered, Threatened, or Sensitive (PETS) Plant Species Jakabe Watershed Enhancement Project, Botany Report, June 7, 2002 Jakabe Restoration Project Analysis File There are both protected and managed populations of Penstemon glaucinus (PEGL) and Castilleja chlorotica (CACH) along the north and west boundary of the project area. Three populations of PEGL in the project area were designated protected in the 1994 Conservation Strategy for Blue-leaved Penstemon. Treatments in protected populations will be designed to maintain or enhance blue-leaved penstemon. Treatments in managed populations should have design and sampling criteria that will enable managers to determine treatment effects on the species. The 3 protected PEGL sites are locted along the north boundary of the project area. The sites straddle the watershed break with a portion of each site in the Summer Lake Watershed. At the time the sites were first surveyed in 1990, the sites were discreet populations with unoccupied habitat occurring between these populations. A followup survey in 1997 found penstemon had spread into previously unoccupied habitat and the protected populations were no longer discreet, making the protected boundaries difficult to distinquish on the ground. A mitigation measure designed into the 1997 Hadley/Lakes Salvage considered all populations of PEGL in the Hadley Butte area protected. For this project, the core areas of the 3 protected populations will continue to be considered protected. Treatments will maintain or enhance the species. Treatments known to maintain or enhance the species include reducing canopy closure of conifers and maintaining the natural disturbance regimes which provide conditions for reproduction. Treatments outside these core areas but in areas occupied by PEGL will be considered managed. The eleven managed populations, designated in 1994, will continued to be evaluated by Forest Service personnel for treatment effects on the species.

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c. Noxious Weeds Jakabe Noxious Weed Report, July 7, 2001, Updated Report February 16, 2006, Jakabe Restoration Project Analysis File Addresses: Issue 2. Juniper encroachment – Loss of wildlife, riparian and deciduous plant habitat;



The Fremont Land and Resource Management Plan (Fremont Forest Plan) directs that noxious weeds be controlled or eradicated to the extent that funding is available. In 1998, the Environmental Assessment for the Management of Noxious Weeds (the 1998 EA) was completed for the Fremont National Forest in accordance with the 1988 Regional EIS for Managing Competing and Unwanted Vegetation and the 1989 Mediated Agreement (USDA Forest Service, 1998, 4). The Decision Notice from the 1998 Environmental Assessment selected an alternative that allows a variety of noxious weed treatments, including herbicides (USDA Forest Service, 1998, 4). A summary of the objectives found in the 1998 EA include, to establish and increase awareness of noxious weeds, promote long-term health and productivity of forest and range land ecosystems, and implement treatments that move the Forest towards 100 percent control of invader species (USDA Forest Service, 1998, 2). The 1998 EA analyzed the effects of various treatment methods including manual, biological, cultural, mechanical, and chemical methods. The 1998 EA emphasized that the first and most important aspect of noxious weed management, is a prevention strategy. Prevention means to detect and ameliorate the conditions that cause or favor the presence of competing or unwanted vegetation. Rangelands in functioning conditions resist invasive plants. Disturbance from roads, grazing, logging, and recreation has resulted in portions of the project area being susceptible to noxious weed invasions and establishment. The increases in motorized vehicle use within the project area as well as the dispersal of noxious weed seeds by recreational vehicles are problematic contributors. On October 11, 2005, the Regional Forester for the Pacific Northwest Region (Region 6) signed a Record of Decision that will guide the invasive plant management program on National Forests in the Region (USDA Forest Service, 2005). The decision amends the Fremont National Forest Land and Resource Management Plan (FLRMP) through Amendment 26. The 2005 Record of Decision (ROD) amends all National Forests Plans in the Region by adding new direction but does not vacate existing invasive plant management direction beyond the 1988 Record of Decision for Managing Competing and Unwanted Vegetation (ROD) and 1989 Mediated Agreement for invasive plant management (USDA Forest Service, 2005). Parts of the 1988 ROD and 1989 Mediated Agreement that apply to unwanted native vegetation were not affected by this decision. Invasive plant management direction stemming from the 1988 ROD and 1989 Mediated Agreement will be replaced by new direction, in the form of:

• Desired Future Condition (DFC) statement • Goals and objectives statements • Standards for preventing the introduction, establishment and spread of invasive plants • Standards for invasive plant treatment and site restoration

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• An inventory and monitoring framework The purpose of the new management direction is to facilitate subsequent actions to eliminate or control invasive plants so that: (1) desired conditions on National Forest System lands can be attained; (2) federal land managers’ ability to provide goods and services from the National Forest System lands is maintained; and (3) the Forest Service’s ability to cooperate with similar efforts across other ownerships is improved (USDA Forest Service, 2005). Site-specific treatment decisions will be based on location, biology, size of the infestation, site conditions, and integrated resource objectives as analyzed under the Fremont-Winema National Forests Invasive Plant EIS, or specific projects as needed. The Fremont-Winema National Forests is the process of writing this new Invasive Plant EIS to tier to the 2005 ROD. Until a Record of Decision becomes effective on this new Invasive Plant EIS, noxious weed treatments will continue on the Fremont portion of the Fremont-Winema National Forests, as directed under the existing 1998 Environmental Assessment for the Management of Noxious Weeds. In December 2005, the revised version of the Fremont-Winema National Forests Invasive Species Prevention Practices was produced. These prevention practices can be found in Appendix D. The items in italics are standards required by the 2005 ROD. The other items are guidelines to follow at various times during project planning and project implementation phases. This project is located within the Lakeview Federal Sustained Yield Unit. The Lakeview Federal Stewardship Group (LSG) Strategy discusses two guidelines concerning noxious weeds. The Prevention Practices cover both of these guidelines and provides additional precautions not listed in the LSG Strategy. Therefore, no additional guidelines would be needed for this project due to its location within the Lakeview Federal Sustained Yield Unit. Existing Condition Past ground disturbing activities such as extensive logging, road construction, and grazing have created habitat for noxious weed invasion and expansion. Noxious weeds can be found in the Chewaucan watershed and within the Jakabe project analysis area in a variety of habitats including riparian, roadsides, campgrounds, rock pits and scattered among forested and non-forested plant associations (Environmental Assessment for the Management of Noxious Weeds, USDA Fremont National Forest 1998). The presence and potential for spread of this unwanted vegetation threatens species diversity; threatened, endangered, or sensitive plant and animal species; overall range vegetation condition; and forage production. Currently, there are no known noxious weed populations occupying R-6 sensitive plant habitat on the Fremont National Forest. A total of 148.6 acres of noxious weeds (128 sites) have been located within the project area during Forest surveys. These weed sites are primarily located along forest system roads, plantations, on log landings, dispersed campsites and other disturbed areas. Listed below is the existing condition by species for the project area.

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Noxious Weeds within the Jakabe Project Area Species Number of Sites Acres

Canada thistle 73 99.8 musk thistle 24 95.8 Mediterranean sage 12 5.1 tansy ragwort 4 1.6 spotted knapweed 13 3.5 diffuse knapweed 1 0.1 Dalmatian toadflax 1 0.1

Four of the sites within plantations contain both musk thistle and Canada thistle. Therefore, the infested acres within the project area are 148.6. Canada thistle (Cirsium arvense), musk thistle (Carduus nutans), spotted knapweed (Centaurea maculosa), diffuse knapweed (Centaurea diffusa), whitetop (Cardaria draba), Mediterranean sage (Salvia aethiopsis), Dalmatian toadflax (Linaria dalmatica), and tansy ragwort (Senecio jabobaea) have been inventoried in the Jakabe project area. This inventory is updated annually as new infestations are discovered. Many of the stream corridors in the Jakabe project area have not been surveyed although major travel corridors and some units in the project area have been rudimentarily surveyed. Noxious weeds know no boundaries and control measures are more successful at the watershed scale. Some noxious weed populations in the watershed have been treated under the Paisley Ranger District’s noxious weed control program, based on the Forest-wide direction from the 1998 Environmental Assessment for the Management of Noxious Weeds on the Fremont National Forest. Approximately 20 acres of infestation are being treated in the project area through a performance based herbicide treatment contract. Manual treatment of musk thistle and Mediterranean sage is an integral part of the control program as well. Weed infestations and effectiveness of control measures can be assessed annually during the field season, recognizing that treatment timing and effectiveness varies depending on the species. Priority for treatment has followed such criteria as degree of detrimental effects, reproductive and dispersal capabilities, distribution and difficulty of control of the targeted weed species. Noxious weed control will promote the health and productivity of forest and rangeland resources and is integral to other watershed restoration objectives that improve the watershed toward reference conditions. Environmental Consequences Direct and Indirect Effects Common to All Alternatives The consequences of noxious weed infestation can include alteration of the structure, organization, or function of ecological systems (Olson, 1999). Noxious weeds have the ability to deplete soil, water, and nutrients to levels lower than native plant species can tolerate, allowing noxious weeds to out-compete native vegetation (Olson, 1999). This happens because they produce abundant seed, have fast growth rates, have no natural enemies, and are often avoided by large herbivores. Some noxious weeds also produce secondary compounds, which can be toxic to other native plant species, or animals. Weed infestation can therefore lead to a decrease in native plant species, which can alter the ability of wildlife and livestock to find suitable, edible forage.

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At the watersheds level, noxious weeds can alter the seasonal water flow (Olson, 1999). They create more erosion than native plant species because they have fewer shallow roots, which soak up and hold water. Noxious weeds also have less canopy closure than native plants, increasing the amount of sunlight directly hitting the soil and the amount of water evaporated at the soil surface. This creates a hard crust on the soil, which becomes difficult for additional moisture to penetrate leading to increased soil surface run-off. The moisture held by the soil helps maintain stream levels throughout the summer. When noxious weeds are present, there is an increase in erosion and surface run-off, leading to deterioration in watershed conditions. The Jakabe Restoration Project area will be monitored for noxious weeds under all of the alternatives. With the 1998 Environmental Assessment for the Management of Noxious Weeds (the 1998 EA) and the Forest Service noxious weed treatment contract in effect, regardless of which alternative is chosen for the Jakabe, noxious weed sites on National Forest Systems lands will be treated in accordance with funds available. In the short term, the alternatives would affect the potential for noxious weed infestation in the project area in two main ways. First, ground disturbing treatment activities, such as harvest activities, fuels treatments, underburning, and temporary road construction, would increase the amount of open disturbed habitat available for infestation. Second, increased activity and traffic would heighten the chance for introduction of noxious weed seeds from vehicles and equipment. The potential for noxious weed infestation would therefore increase with the amount of ground disturbing activity in each alternative. In the long term, the alternatives canopy reducing activities have the potential to increase native herbaceous plants in the understory that may out-compete exotic vegetation establishment. Likewise, road decommissioning and lowering road density would reduce disturbed habitat and corridors for weed infestation. Long-term impacts also include the potential for future high severity fires, which would create additional area at risk to weed infestation. This risk decreases as the amount of fuel reduction activities increase, as would happen with the action alternatives. Timber sale contracts, road packages, stewardship pilot projects, and service contracts are now required to include provisions to minimize the introduction and spread of invasive plants, pursuant to Executive Order 13112 dated February 3, 1999 (Joyner, 2002). This requirement is also discussed in Appendix D. These requirements will reduce the potential for introduction of weed seeds during implementation of the action alternatives. Alternative 1 The No Action Alternative would leave the proposed activity area in its current condition. Without ground disturbing activities occurring, noxious weed habitat and the potential for new introductions would not be increased above the existing condition. Predicted fuel accumulations would be the highest for Alternative 1, with management activities not occurring within the project area. Higher fuel accumulation would increase the probability for future high severity fires, which would create additional noxious weed habitat.

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In the No Action Alternative, roads would be left in their current condition. Closing and revegetating roads as proposed in all other alternatives would assist in preventing noxious weed spread. Noxious weed spread may occur in the project area if Alternative 1 is chosen. However, because of the lack of ground disturbance, Alternative 1 has the lowest probability of spreading and introducing noxious weeds when compared to Alternatives 2, 3, and 5, as shown below.

Risk of Noxious Weed Infestation in the Jakabe Project Area

Alternative Acres of Proposed Treatment

Miles of Temporary Road Construction*

Comparative Risk

Alternative 1 0 0 Low Alternative 2 16,010 11.78 (8.81) High Alternative 3 14,367 10.06 (7.31) High Alternative 5 10,072 8.30 (6.56) Moderate

* The miles of temporary roads proposed would vary depending upon the logging system used. In the Coffeepot Creek and Chewaucan River Subwatersheds, cable logging is proposed in some units. If the cable logging proves to be infeasible, then the areas would be helicopter logged or not harvested at all. The number outside the parentheses is the miles of temporary roads if cable logging is chosen. The number inside the parentheses is the miles of temporary roads if cable logging is not chosen. Alternatives 2, 3 and 5 Alternatives 2, 3, and 5 are the proposed action alternatives, with Alternative 2 as the Proposed Action. Alternative 2 would treat the most acres across the watershed when compared to the other alternatives.

Acres of Proposed Activies by Alternative Alternative Acres of Vegetation

Treatment without the Use of Prescribed Fire

Acres of Prescribed Fire with Pretreatment

Total Acres of Proposed Activities

Alternative 2 7,724 8,286 16,010 Alternative 3 6,676 7,691 14,367 Alternative 5 4,841 5,231 10,072 The tables below shows the number of noxious weed sites and corresponding acreage for the action alternatives. These sites are located within the areas of proposed activities.

Noxious Weed Sites within Proposed Treatment Area for Alternative 2 Species Number of Sites Acres

Canada thistle 30 65.8 musk thistle 11 59.9 Mediterranean sage 8 4.8 tansy ragwort 2 1.4 spotted knapweed 8 4.3

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If Alternative 2 is chosen, 59 known noxious weed sites exist within proposed areas of activities. Two of the 59 sites contain both musk thistle and Canada thistle. Therefore, the infested acres within proposed areas of activities are 91.1.

Noxious Weed Sites within Proposed Treatment Area for Alternative 3 Species Number of Sites Acres

Canada thistle 30 65.8 musk thistle 11 59.9 Mediterranean sage 8 4.8 tansy ragwort 1 1.3 spotted knapweed 8 4.3

If Alternative 3 is chosen, 58 known noxious weed sites exist within proposed areas of activities. Two of the 58 sites contain both musk thistle and Canada thistle, making 91 infested acres within proposed areas of activities.

Noxious Weed Sites within Proposed Treatment Area for Alternative 5 Species Number of Sites Acres Canada thistle 18 63.1 musk thistle 7 58.9 Mediterranean sage 7 4.6 tansy ragwort 1 1.3 spotted knapweed 8 4.3

If Alternative 5 is chosen, 41 known noxious weed sites exist within proposed areas of activities. Two of the 41 sites contain both musk thistle and Canada thistle, resulting in 87.2 infested acres within proposed areas. Constructing temporary roads is a proposed activity for Alternatives 2, 3, and 5. This would increase noxious weed habitat in the short-term by creating ground disturbance and providing access to previously inaccessible places. When the activities behind the temporary and re-opened roads are completed, the roads would be either closed or decommissioned. Until the native vegetation recovers, these areas would continue to be potential noxious weed habitat. If cable logging is determined to be unfeasible within the Coffeepot Creek and Chewaucan River Subwatersheds, then the miles of temporary roads would be reduced in all action alternatives. Watershed improvement projects, such as decommissioning existing roads, assist in eliminating noxious weed habitat and corridors for seed dispersal. Design criteria listed on pages 19-21 of Chapter 2 would also be used to prevent spread from known or newly discovered noxious weed sites if project implementation occurs for Alternatives 2, 3, or 5. Cumulative Effects Alternative 1 Alternative 1 would not contribute to cumulative ground disturbing activities in the Jakabe project area, and therefore would not contribute to increased noxious weed habitat or increased risk of weed

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introductions. This alternative would not contribute to cumulative fuel reduction in the Jakabe project area, and therefore would result in a higher risk of future severe fires, creating additional noxious weed habitat, compared to the action alternatives. In addition, Alternative 1 would not have watershed improvement projects, such as decommissioning existing roads, to assist in eliminating noxious weed habitat and corridors for seed dispersal. Alternatives 2, 3, and 5 Overall, Alternative 2 would have the most cumulative ground disturbing activities, followed by Alternative 3, then Alternative 5. Alternatives 2 and 3 would result in increased potential for weed infestation on approximately a fourth of the project area (25-28 percent). Alternative 5 would result in increased potential for weed infestation on approximately a fifth of the project area (18 percent). As described in the Direct and Indirect Effects section, early detection and treatment along with mitigations to prevent seed spread would be used to help reduce the risk of weed invasion on National Forest System lands. As described under Direct and Indirect Effects, Alternatives 2, 3, and 5 would contribute to cumulative fuel reduction activities in the Jakabe project area, and would result in a lower risk of future high severity wildfire than Alternative 1. Future high severity fires could create additional weed habitat. In addition to the miles of road closures addressed in the EA, approximately 22 miles of road closures within the project area have occurred or will occur. These additional closures were addressed under a separate Decision Memo. The additional 22 miles would further help to reduce noxious weed habitat and corridors for seed dispersal. There is the potential for the spread of noxious weeds under all action alternatives in the Jakabe Watershed Restoration Project proposal. Invasive species are not predicted to expand in areas where no forested vegetation treatment is planned, although current weed populations should be controlled and monitored in these areas. Thinning without burning is proposed and would have limited effects depending on the extent of the disturbance and equipment used. Using fire alone as a maintenance tool is proposed for portions of the project area and these areas generally have either been previously entered with fire or have some degree of conifer encroachment that can be mitigated with prescribed fire. In general, noxious weed expansion has not resulted from burns conducted in the watershed that had similar objectives to those proposed with this project. However, precommercial and noncommercial thinning combined with prescribed burning may have the greatest potential to invite the spread of noxious weeds in the watershed. The amount of fuels to be removed to meet stand management objectives and provide for safe and effective burning varies with this proposal. Site disturbance is generally associated with thinning, which can create habitat for new noxious weed invasion or provide sites for the expansion of existing populations. Alternatively, canopy reducing activities have the potential to increase native herbaceous plants in the understory that may out-compete exotic vegetation establishment. These objectives are compatible with recommendations for non-forested vegetation management identified in the Chewaucan Watershed Analysis. There is the risk of expanding current weed populations through mechanical and prescribed burn treatments on conifers, road obliteration, and other potentially

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ground disturbing activities, especially through the use of heavy equipment, which can transfer weed seed from one site to another. These potential impacts to weed distribution in the watershed could be mitigated with more aggressive control of known weed populations prior to treatment and with routine assessment of disturbed sites within the project area, depending on the intensity of the treatment in terms of ground disturbance. Overall, thinning and prescribed burning can restore habitat and reduce the risk of catastrophic fire, which poses a greater threat to exotic species management than can be predicted with planned vegetation control. The effect of burning on native vegetation and the potential degree for invasive species to become established will depend on the timing and intensity of the burn, and the amount, if any, of slash left after mechanical pretreatments. Pretreatment and burning in juniper woodland creates a high potential for the spread of weeds as opposed to pre-commercial thinning and burning. Thinning/logging and other harvest activities may cause site disturbance conducive to the establishment of noxious weeds. Any alternative selected should follow the guidelines, goals and objectives outlined in the 1998 Environmental Assessment for the Management of Noxious Weeds on the Fremont National Forest and the 1989 Fremont National Forest Land and Resource Management Plan. IV. Range Jakabe Range Report, 5/14/02 Jakabe Restoration Project Analysis File The Jakabe project area includes pastures in the Bear/Lakes (East Bear, Mill Creek, Corral Creek, Coffeepot, Long Hollow, East River and Round Pass), Drum Hill (West and East), Paradise (Brattain Butte), Buck/Doe (West Buck and East Doe) Swamp Creek (Moss Pass and Ben Young) and Whiterock allotments. These areas have been grazed since before the Fremont was established. The primary grazing was sheep until the mid-1950s when the allotments were converted to cattle. The grazing strategy for the Mill Creek, Corral Creek, Coffeepot, Long Hollow, East River and Round Pass pastures of the Bear/Lakes Allotment is early use, 5/28-6/30, combined with deferred rotation or rest rotation. The East Bear pasture is the entry pasture, 7/1, every other year for the high intensity, low frequency summer pastures. Drum Hill Allotment is managed to complement the strategy on the Bear/Lakes Allotment. Years with entry into the South Lakes pasture of the Lakes Allotment , approximately 200 head use West Drum from June 1 to June 30. One hundred forty head are permitted in East Drum from September 20-October 1. The years with entry into the East Bear pasture of Bear Creek Allotment, 242 pairs are permitted in the allotment, both West and East Drum. The Brattain Butte pasture of the Paradise Allotment is used as an early season pasture. Grazing strategy in the Buck/Doe Allotment is a two pasture deferred rotation with rotated pasture entry every year. Season of use is May 28 through September 8. Swamp Creek is a three pasture allotment with a high intensity/low frequency system. The Ben Young pasture is used mid season and the Moss Pass and Shoestring pastures will be alternated as the entry pasture every other year. The pasture has had significant non-use in the recent past. The Lakeview Ranger District administers the Whiterock Allotment. The grazing strategy is season long.

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None of the alternatives of the Jakabe project would require a need to alter or change management of the allotments included in the project area. The grazing strategies and management plans for Bear Creek, Lakes, Drum Hill, and Buck/Doe Allotments were developed and approved with the Chewaucan Grazing Environmental Analysis and Decision Notice/Finding of No Significant Impact, July 26, 2001. Alternative 1, no action, could result in the continued loss of forage species due to canopy closure in forested communities and continued conifer encroachment on meadow and riparian communities. The following effects based on the treatment scenarios, (proposed action 5/9/00), are common to all action alternatives. The level of effects will be dependant on the size of treated and non-treated areas.

Scenario 1. No vegetative treatments of any type at this time No effect on current upland forage, meadow or riparian forage species. Scenario 2. Apply vegetation treatments without applying prescribed burning at this time. Thinning of white fir, small diameter trees and understory in snag habitats could increase upland forage species. Treatment of encroaching conifers in meadow communities could increase the meadow forage species. Felling and leaving conifers in aspen stands would allow grazing systems to continue as developed in the Chewaucan Grazing EA by discouraging use of specific areas while protecting aspen regeneration. Scenario 3. Apply prescribed fire without any pretreatment The Paisley Ranger District has successfully implemented prescribed fire projects with no changes to the grazing program on the district. Any need to increase fuel loads prior to prescribed fire treatments through maximum growth of forage species, as well as the need to discourage cattle use of areas after implemented prescribed fire treatments, would be determined on a site specific level. The grazing systems currently being used, as well as the use of topographic features and riding/herding, allow for flexible management in the allotments included in the project area. This flexibility would allow prescribed fire implemented through the Jakabe project to possibly increase the availability of upland and meadow forage species, without impacting the benefits of the grazing systems or the allowable use in the allotments. Scenario 4. Apply a pretreatment in order to facilitate prescribed fire Effects will be the same as prescribed fire without pretreatment (Scenario 3).

V. Fish & Wildlife Addresses: Issue 1. Mule deer habitat – The Chewaucan Watershed is already low in respect to deer

cover and habitat effectiveness. Issue 2. Juniper encroachment – Loss of wildlife, riparian, and deciduous plant habitat;



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a. Fish Watershed and Aquatics Specialist Report/Fisheries Biological Evaluation, November 4, 2002 Jakabe Restoration Project Analysis File Interior redband trout are the only Forest Service sensitive fish species found in the Chewaucan Watershed. There are no bull trout (the only federally listed species found on the Paisley Ranger District) within the Chewaucan Watershed. Bull trout are found within the Klamath Basin watershed. Interior redband trout (Oncorhynchus mykiss) are non-anadromous rainbow trout that occur in six desert basins throughout southeast Oregon and northeast California – Malheur, Catlow Valley, Fort Rock, Chewaucan, Goose Lake, and Warner Lakes (Behnke 1992). Previously, these fish have been petitioned for listing under the Federal Endangered Species Act; however, listing was found to be not warranted. Redband trout require four basic habitat types to accommodate life history requirements: spawning, rearing, adult and over wintering (Behnke 1992). Kunkel (1976) documented that redband trout in a southeastern Oregon stream spawned in April and May, with the highest spawning intensities occurring in the first part of May. Gravels free of sediments are optimum for spawning since sediment can smother eggs by impeding the free flow of oxygenated water and can trap alevins (Willers 1991). According to Bjornn and Reiser (1991) spawning is adversely affected when substrate fines (<6.4mm) exceed 25%. Intermittent streams are used for spawning and are effective when flow continues through emergence and downstream migration of juveniles into perennial tributaries (Behnke 1992). Within forested systems, large wood provides storage of sediment in the tributaries and contributes to the maintenance of water quality and productive fish habitat (Duncan et al. 1987) by both slowing water velocity upstream and trapping transported sediment. In low gradient systems, sediment is trapped on active floodplains during high flow events. After young trout emerge from the spawning gravel, they often rear in low velocity areas associated with stream margin habitats, high cover areas, and interstitial spaces. Adults require habitat for resting and feeding and thus are generally found in areas of abundant cover associated with deep pools, large organic material, undercut stream banks and overhanging vegetation. Over winter sites, characterized by low velocity areas with cover including large woody debris, are important to all age classes (Bjornn and Reiser 1991). Generally, water temperatures in excess of 21° C or 70°F, are unfavorable and may cause stress to all age classes (Sigler and Sigler 1991). Temperatures of about 15°C, or 58°- 60°F, are ideal for optimum growth of rainbow trout (Leitritz and Lewis 1980), while temperatures exceeding 29.4°C (84.9°F) can be fatal (Bjornn and Reiser 1991). Behnke (1992) states that redband possess a hereditary basis to persist at higher water temperatures (greater than 21°C or 70°F) than other species of trout and has captured (flyfishing) live redband in streams with temperatures of 28.3°C (82.9°F). b. Habitat for aquatic species Current conditions of the aquatic habitat, by reaches, are summarized in the table below.

Bear Creek subwatershed

Functioning Appropriately

Functioning at Risk

Functioning at Unacceptable

Risk

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Large Woody Debris 5 2,6,7,8 1,3

Pools 1,2,3,5,6,7 8

Large Pools 1,2,3 5,7 6,8

Spawning gravel fines 1 6

Stream temperature 5,6,7,8 1,2,3

Ben Young Creek Subwatershed

Large Woody Debris 5,6

Pools 3,4,5,6 8

Large Pools 3,4 5

Spawning gravel fines 3

Stream temperature 6,7 1,3,4,5

Chewaucan River subshed Large Woody Debris 3 2B,3A,4 2

Pools 2-4,6,8,11,13,16,19 8

Large Pools subshed

Spawning gravel fines 4,8 3 19

Stream temperature 16,18,19 2-4,6,8,11,13

Coffeepot Creek subshed Large Woody Debris 6,7,9 4

Pools All reaches surveyed

Large Pools 1,4,6,7 9

Spawning gravel fines 1,4

Stream temperature 4,9 1

Fish Passage 4,6,7 1,8,9 5

Swamp Creek subshed Large Woody Debris 2,6

Pools 6 1,5,8 2-4

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Large Pools 1-5 6

Spawning gravel fines 1 6

Stream temperature 5,6 1-4,8

1. Large Woody Debris (LWD) Reaches of stream within the project area were identified as functioning appropriately, functioning at risk, or functioning inappropriately. Those functioning at risk or inappropriately were identified as issues in the Chewaucan Watershed Analysis. Effects of large woody debris placement were analyzed with the Jakabe Restoration Project and on July 22, 2004, the Jakabe Stream Enhancement Projects Decision Memo was signed authorizing placement of native debris in designated reaches of streams within the Jakabe area. 2. Pools Pools were also analyzed with the Jakabe Restoration Project and incorporated into the July 2004 Stream Enhancement Decision Memo. The stream enhancement work, which includes the addition of LWD or large boulders in stream reaches where pools and large pools are below the 75th percentile, will restore the reaches to functioning appropriately in regards to pools. This action is in compliance with the Riparian Management Objectives identified in INFISH and would improve stream habitat for all aquatic species. 3. Spawning Gravel Fines Alternative 1 (no action) Currently several reaches of stream within the project area have been sampled for spawning gravel fines. Among these stream reaches, when looking at fines, some are functioning appropriately, some are functioning at risk, and some are functioning inappropriately. By not implementing any management activities within these subwatersheds the Forest Service could potentially degrade the current conditions in reference to fine sediments. This is due to the unusually high canopy densities, encroaching junipers and lack of fire, which results in shrub and grass density decreasing, decreasing soil cover and decreasing infiltration rates. As a result, overland flow and soil erosion often result. Also, by not decommissioning any roads within the subwatersheds (as would be the direction with the no action alternative), the sediment coming off of these areas has a higher chance of directly entering the streams. Fine sediment also enters streams from unstable banks. If current conditions degrade, in reference to increased spawning gravel fines, then habitat for aquatic species will also degrade. Short-term and long-term there would be direct, indirect, and cumulative effects with this action. Long-term determination call for this alternative would be “may impact individuals or habitat but will not likely contribute to a trend towards federal listing or loss of viability to the population or species”. Alternative 2 (proposed action) By implementing the proposed action, the Forest Service will begin to restore the upland plant communities by thinning and prescribe burning to reduce canopy densities, improve shrub and grass density, soil cover, and infiltration rates. Sedimentation will also decrease by planting willow to stabilize point bars and placing sedge mats on exposed soil. These management activities would help to decrease the amount of sediments entering the streams. The

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decommissioning of roads and thinning the uplands will also decrease the amounts of sediment entering the streams. Although there could be potential short-term adverse effects by an initial increase of sediment soon after decommissioning a road and putting heavy equipment in the uplands (soil compaction) the long-term effects would be beneficial. The use of existing skid trails would mitigate the effects. There would be short-term adverse effects with the instream work (willow and sedge planting), but long-term effects would be beneficial. Thus this action would be in compliance with the Riparian Management Objectives identified in INFISH and would benefit stream habitat for aquatic species. Short-term determination call would be “may impact individuals or habitat but will not likely contribute to a trend towards federal listing or loss of viability to the population or species”. Long-term determination would be “beneficial impact.” Alternatives 3 and 5 These alternatives would have the same outcome as Alternative 2 (restore current condition). Therefore, the actions would be in compliance with the Riparian Management Objectives identified in INFISH. The effects determination call would be the same as Alternative 2. 4. Stream Temperature Alternative 1 (no action) Among the stream reaches in the project area that have had temperatures measured, some are functioning appropriately, some are functioning at risk, and some are functioning inappropriately. By not implementing any management activities within these subwatersheds the Forest Service could potentially degrade current conditions in regards to stream temperatures. As discussed in the “Upland plant communities and their effect on amount of water and sediment reaching riparian areas and in Desired Road Densities,” by not managing the uplands, there could be potential detrimental effects to the streams. This is due to the unusually high canopy densities, encroaching junipers and lack of fire, which results in shrub and grass density decreasing and soil cover and infiltration rates lessening. As a result, there is less water absorbed into the soil for grasses, shrubs, and subsurface flow. Less water entering streams because of a lack of subsurface flow results in a loss of water available for stream flow during the dry summer months and higher water temperatures. Also, by not decommissioning any roads within the subwatersheds (as would be the direction with the no action alternative), the overland flow has a higher chance of directly entering the streams and increasing the water’s temperature. Degrading the stream habitat by potentially increasing the water temperatures will not benefit aquatic species. The long-term determination call would be “may impact individuals or habitat, but will not likely contribute to a trend towards federal listing or loss of viability to the population or species”. Alternative 2 (proposed action) By implementing the proposed action, the Forest Service will begin to restore the upland plant communities by thinning and prescribed burning to reduce canopy densities, improve shrub and grass density, soil cover, and infiltration rates. There would also be decommissioning of roads. These management activities would therefore, help to maintain or improve the temperatures of the streams within these subwatersheds. There could be short-term adverse effects to the stream when the uplands are being thinned due to impacted soils in the uplands and the combined possibility that there could be a short increase in overland flow. However, long-term effects of returning the uplands to properly functioning would be beneficial to stream temperatures. Soil compaction levels would not go above what is currently on site by using

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mitigation measures (use of existing skid trails and roads). Thus, this action would be in compliance with the Riparian Management Objectives identified in INFISH and would improve the stream habitat, which would benefit aquatic species. Short-term there could be direct, indirect, and cumulative effects with this alternative as described above. Long-term there would not be direct, indirect, or cumulative effects. Short-term determination call for this alternative would be “may impact individuals or habitat but will not likely contribute to a trend towards federal listing or loss of viability to the population or species”. Long-term determination call would be “beneficial impact.” Alternatives 3 and 5 These alternatives would have the same outcome as Alternative 2 (restore current condition). Therefore, they would be in compliance with the Riparian Management Objectives identified in INFISH. The effects determination call would be the same as Alternative 2. 5. Fish Passage Several culverts across the Chewaucan Watershed were identified as problems for fish passage due to excessive water velocities and/or waterfalls at outlets. In general, culverts that were installed at a slope greater than 1% and culverts that are narrower than bank-full pose a velocity barrier to fish passage. A significant drop at the outlet end of a culvert also presents a barrier. One possible solution to fish passage problems is to install bottomless arches, low water fords, or culverts designed to accommodate the stream width, slope, and water velocity of a specific creek. Another solution is removal of the culvert with road closure and restructuring of the stream bank. Bottomless arches are multi-plated structures that rest on concrete runners, while using the actual streambed for their bottom. A low water ford consists of concrete approaches to each side of the stream and then a small channel or dip for water flow. During high flow the water will spread onto the concrete approaches. By replacing culverts that are fish barriers, the Forest Service moves toward restoring current conditions and is in compliance with the riparian objectives identified in the Inland Native Fish Strategy (USDA Forest Service, 1995). Surveys of culverts were done during the summers of 1998, 1999, and 2000. Four culverts were slated for replacement during the in-water-work-window (July 1-August 15, 2001) under the Decision Memo (Categorical Exclusion) entitled, “Ben Young Creek, Swamp Creek, and Bear Creek Fish Passable Culvert Replacement Project.”. Additional problem culverts were identified in the Chewaucan watershed, with restoration recommendations, and analyzed by the interdisciplinary team as part of the Jakabe Restoration Project. These culverts were authorized for replacement with the Chewaucan Watershed Fish Passable Culverts Replacement Project Decision Memo, dated May 9, 2002. These included culverts on Little Bear, Dog, Coffeepot, Little Coffeepot, and Swamp Creeks. No other culvert replacements are currently proposed in the Jakabe area.

c. Wildlife Jakabe Analysis Area, Specialist Report and Biological Assessment/Evaluation, April 19, 2001 Revised March 2002, Addendums September 14, 2004 and March 15, 2006; Jakabe Restoration Analysis File

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1. Management Indicator Species (MIS) i. Mule Deer (MIS – Hunted Species) The Jakabe analysis area includes approximately 12,780 acres of winter and transition range, and 66,252 acres of summer range for the Interstate mule deer herd. Oregon Department of Fish and Wildlife management objective for this herd is 14,800 wintering deer. Based on the POPII population model the Interstate wildlife management unit wintering deer population in 2003/2004 was estimated at 48% and in 2004/2005 at 52% of management objective. The mule deer population has been below management objective since the severe winter of 1992/1993 but is stable around 50% of management objective. (M.J. Hedrick, ODFW, personal communication). The Jakabe analysis area provides fair to poor habitat for mule deer and other large ungulate species. Cover, both hiding and thermal, is limited on both winter and summer ranges. Patches of thermal cover are distributed throughout the area, primarily in thick stands of lodgepole pine and white fir and thickets of ponderosa pine regeneration, but not in arrangement or quantity to meet standards and guidelines. Additionally, mountain mahogony stands and juniper clumps and individual trees, although not meeting Forest Plan definition, may actually function as thermal cover. Fawning cover is plentiful, existing in perennial and seasonally wet drainages and near seeps and springs where adequate cover and forage exists. Riparian habitat conditions for fawning have been somewhat degraded since the turn of the century due to livestock and ungulate grazing, suppression of fire and a subsequent loss of deciduous vegetation and herbaceous and shrubby forage. Herbaceous forage, primarily grasses, forbs, and sedges, is highly variable over the landscape with excellent concentrations associated with riparian areas and openings and relatively none in some of the older, multi-storied stands. Shrubby forage is primarily mountain mahogony and a scattered few areas of bitterbrush. Ceanothus and manzanita is relatively plentiful in the upper elevations. Big sagebrush communities dominate much of the lower elevation open areas and may also provide some shrubby forage. However, concentrated browsing, grazing, and fire suppression have resulted in limited recruitment of new age classes, declining vigor, and browse lines on mahogony, diminishing the forage value. The forage to cover ratio (75.1:24.9) throughout the watershed is less than optimal and below Forest Plan standards and guidelines. Large areas of the analysis area are cover deficient and portions of the planning area could become forage limited as stands become increasingly dense and/or juniper establishes itself and understory herbaceous and shrubby forage declines. Fire suppression and the resultant increase in stand densities, invasive juniper and white fir, and decadent or less vigorous shrub species, while providing relatively good hiding cover in some subsheds, have created an ever increasing potential for large scale wildfire. The effect of such an event, while providing a flush of transient forage, could create large cover and shrubby forage deficient areas, resulting in potentially large decreases in effective habitat for mule deer. Habitat effectiveness in the Jakabe Analysis area is influenced primarily by the spatial arrangement of cover and forage and the cover:forage ratios. Additional effects from road densities and forage utilization by cattle occur as well. Effects Analysis The effects of the alternatives on mule deer habitat are as indicated in the tables below.

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Alternative comparison of hiding cover and habitat effectiveness for mule deer by subshed in the Chewaucan River watershed. The habitat effectiveness analysis encompasses all federal and private lands within the project area. Acres that were not capable of producing cover were not included in the final analysis. Bear Creek Subshed

Alternative Cover (S&G =30%)

Habitat Effectiveness (S&G = 50%)

1 37.% 32% 2 28% 26% 3 29% 29% 5 37% 39%

Ben Young Creek Subshed

Alternative Cover (S&G = 30%)


1 31% 37% 2 20% 13% 3 23% 24% 5 31% 47%

Chewaucan River Subshed



1 13% 8% 2 5% 2% 3 6% 4% 5 13% 9%

Coffeepot Creek Subshed



1 35% 40% 2 18% 17% 3 22% 25% 5 35% 47%

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Swamp Creek Subshed Alternative Cover

(S&G = 30%) Habitat Effectiveness

(S&G = 50%) 1 38% 21% 2 17% 12% 3 22% 22% 5 38% 58%

Entire Chewaucan Watershed

Alternative Cover Habitat Effectiveness (S&G = 50%)

1 26% 24% 2 14% 7% 3 16% 9% 5 26% 28%

Winter Range

Alternative Cover (S&G = 40-60%)


1 27% 27% 2 3% 0% 3 7% 2% 5 27% 32%

Transition Range



1 14% 6% 2 5% 1% 3 6% 1% 5 14% 7%

Summer Range



1 27% 27% 2 16% 9% 3 18% 11% 5 27% 31%

Although under current management, optimal habitat is defined as that which is within 600 feet (183m) of cover (cover being defined as a stand that is at least 60% cover), Gay did not find concentrated deer use within 600 feet of hiding cover (1998). In fact, fewer than 20% of study animals concentrated habitat within 600 feet of hiding cover (Gay 1998). Although the LRMP

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requires that we manage by using the current definition of cover (a stand in which >60% of the area can hide 90% of a deer at 200 feet), this omits less dense vegetation types which deer also recognize as cover (Gay 1998). Alternative 1, the no action alternative, would not have any immediate effect on mule deer habitat. Habitat effectiveness would remain below standards and guidelines in all subsheds as would cover in the Chewaucan River subshed. Long term effects could see a continued loss of forage as conifers mature and shade out understory species, shrubby forage continues to decline in vigor, and recruitment of new age classes is restricted. Thermal and fawning cover would show some minor fluctuations and hiding cover could decrease as young trees matured and crowded regeneration thinned itself naturally. The potential for large scale wildfire would remain. Alternatives 2 and 3, the action alternatives, will reduce habitat effectiveness and cover in all subsheds. Alternative 3 generates the least effects. Alternatives 2 and 3 will reduce habitat effecitveness and cover below standards and guidelines on all ranges and the analysis area overall. Alternative 3 was designed to lessen the effects on mule deer, however it does not increase cover and habitat effectiveness and thus will not meet standards and guidelines for habitat effectiveness in any subshed and will meet cover standard and guidelines only in the Bear Creek subshed. The net effects of both action alternatives will be an increase in herbaceous forage, fawning habitat, and habitat security and a decrease in cover and habitat effectiveness; more reflective of historic conditions. The effects of not meeting standards and guidelines for habitat effectiveness and cover with alternatives 2 and 3 could be a reduction in mule deer numbers. Oregon Department of Fish and Wildlife herd management objectives could be affected. The implementation of either of these alternatives would require a non-significant Forest Plan Amendment allowing the deviation from current cover reqiurements to meet the needs of a sustainable, healthy ecosystem. Cover will be greatly reduced across the watershed. Retaining small cover clumps within the harvest units should help mitigate the loss of cover in some areas. In areas where road densities are low, mule deer may find greater security and may continue to utilize areas where cover is lacking. In areas where road densities remain high, mule deer use may greatly decline. Alternatives 5: This alternative will increase habitat effectiveness and maintain existing cover in all subsheds and on all ranges. The net effects of this alternative will be an increase in herbaceous forage through underburning and opening up stands, fawning habitat through riparian enhancement, habitat security with road closures, an increase in habitat effectiveness, and the maintenance of existing cover. Although populations are expected to remain stable, mule deer habitat is expected to improve with this alternative. Cover will be maintained in all areas that are currently mapped as cover. Retaining small cover clumps within the harvest units should help mitigate the lack of cover in some areas. The action alternatives provide the opportunity to reduce the encroachment of juniper and white fir and reduce stand densities to those approaching pre-fire suppression levels. Herbaceous and shrubby forage would increase with the more open and favorable growing conditions. Prescribed fire under controlled conditions will provide the opportunity to regenerate herbaceous and shrubby forage while providing for a mosaic of different age classes. Riparian habitat conditions would improve with stimulated growth and regeneration of deciduous vegetation and herbaceous and

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shrubby forage from the flush of nutrients from prescribed fire and more open and favorable growing conditions. The burn objective for the action alternatives is a 40-60% unburned/40-60% burned mosaic. It is anticipated that regeneration of bitterbrush will not occur for several years in areas where bitterbrush is present. Reducing the duff layer, while minimizing the loss of down wood, will increase the opportunities for rodent caching. Burning with mechanical treatments would increase production and quality of the herbaceous forage that is particularly important in the spring on the transition range. Riparian habitat conditions would improve with stimulated growth and regeneration of deciduous vegetation and herbaceous and shrubby forage from the flush of nutrients from prescribed fire and more open and favorable growing conditions. Overall effects on forage with all action alternatives will be an increase in herbaceous forage and a decrease in shrubby forage. Distribution of cattle grazing is expected to improve as new grazing areas are created, relieving grazing pressure on riparian areas and other areas of concern. Road densities will decrease with proposed road closures and obliterations. The effects of road densities on habitat effectiveness will be diminished, thus increasing habitat security. The potential for large scale wildfire would decrease. Cumulative Effects Several factors affect mule deer populations. These include birth rate (productivity), sex ratios, longevity, mortality, body condition and harvest rate. Harvest rate, mortality by predation or accident, and sex ratios are factors independent from management of the national forest. Birth rate, longevity, mortality, and body condition are influenced by habitat quality and quantity, both of which are dependent on land management practices on federal, state, and private lands. Factors affecting the quality and quantity of mule deer habitat determined by management on the Fremont National Forest include cover/forage relationships, travel corridors, road density, habitat quality, harvest rate through manipulating access, water availability, and management of critical habitat areas such as fawning cover. Factors affecting habitat effectiveness are addressed in the analysis as described above. Travel corridors are located throughout the planning area, most frequently coinciding with riparian areas, timbered stringers, and ridgelines. Alternatives 2 and 3 will decrease cover throughout the planning area and thus decrease the suitablity of areas currently used as travel corridors. These alternatives will affect to varying degree those areas most frequently used as travel corridors. The Jakabe analysis area consists of summer, winter, and spring/fall transition range for the Interstate mule deer herd. The range of this herd encompasses approximately 1843 square miles west of state highway #31, south and west of the town of Paisley. Approximately 39% of this area is on public lands with the remainder on private lands. Environmental analyses for a variety of projects have analyzed HE and cover on approximately 170,254 acres of the summer, transition, and winter ranges of the Interstate herd on the district (including private land within district boundaries) within the last 3 years. The combination of all analyzed areas to date including the Jakabe Analysis area results in an HE of 41.2% with a total of 39.6% cover. Cumulative effects calculations are specific to the Interstate mule deer herd and only include the areas where a mule deer analysis has been completed on the Paisley Ranger District (approximately 170,291 acres).

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1 40 % 41% 2 34% 40% 3 35% 42% 5 40% 49%

Alternatives 2 and 3 cumulatively reduce mule deer cover and habitat effectiveness on all seasonal ranges. Alternative 5 represents the least cumulative effect on both cover and habitat effectiveness. Change on the Paisley Ranger District over the years including commercial harvest, fire suppression, wildfire, plant succession, livestock grazing, the road system, and recreational use have cumulatively affected mule deer. Commercial harvest that included overstory removal and fire suppression significantly increased desirable shrub species above historical levels. Over the long term, this has also led to a condition of decadent, less nutrient rich browse species and overstocked dense stands of timber in which forage is becoming limited. Livestock grazing created competition with mule deer for early green-ups, forbs, and winter browse. With increased road densities along with increased recreational use, mule deer security has been reduced. Although mule deer populations have increased from pre-settlement times, populations have declined from the high numbers experienced during the middle to late 1900s.

Private lands within and adjacent to the analysis area have, for the most part, been harvested and additional activities are not expected to substantially affect mule deer habitat. Forseeable potential future actions that could additionally affect deer and their habitat include the Baja and Headwaters prescribed burning projects and restoration projects within the Upper Sycan watershed. All projects will additionally reduce cover and increase forage availability. Opportunities to improve riparian habitats through vegetation manipulation and reintroduction of fire will be pursued. Travel and access management will also be considered within the Upper Sycan watershed. The cumulative effect on deer will be an increase in foraging and fawning habitats and an improvement in habitat security, with a net loss of cover and effective habitat. ii. Trout Family (MIS – Riparian/stream ecosystems) See Fish Section, page 67. iii. Three-toed Woodpecker (MIS – Overmature/mature Lodgepole Pine) This area of the Fremont N.F. is considered to be outside of the range of three-toed woodpeckers. Since black-backed woodpeckers have similar habitat requirements, the North Zone has substituted this species for three-toed woodpecker. Although black-backed woodpeckers are most commonly seen in lodgepole pine habitat, suitable foraging and nesting habitat exists throughout the analysis area. Black-backed woodpeckers, described as irruptive after catastrophic events by Yunick (1985), have been sighted within the planning area during field reconnaissance. Sightings have been primarily associated with pockets of newly dead lodgepole or ponderosa pine from burning, insect activity or disease. Foraging activity may have recently increased across the watershed in association with increased bark beetle. Overstory mortality occurring in large diameter pine and fir in recent years from drought, overstocked

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stands, and an increase in disease and insect activity have created additional snag habitat to improve nesting habitat conditions and foraging opportunity. Sanitation and salvage logging, however, have limited the availability and abundance of this habitat. Local movements and concentrations of birds in response to areas of beetle activity may reflect more a change in distribution of foraging activity rather than an increase in population numbers. Approximately 263 acres of old growth habitat for three-toed (black-backed) woodpeckers have been designated within the Jakabe analysis area. Another 1327 acres of late and old seral (LOS) lodgepole pine are available as suitable habitat with about 800 acres of younger seral lodgepole pine available for future potential habitat. Several thousand acres of less preferred although suitable LOS pine or fir habitat with scattered individuals and/or patches of lodgepole pine are available as well. Alternative 1 would provide the greatest amount of habitat for this species. As increases in understory densities continue to affect overstory health, small population irruptions of this species will respond to mortality from drought, overstocked stands, and an increase in disease and insect activity throughout the analysis area. Populations are expected to show a gradual increase over time corresponding with increased mortality in the overstory. In addition, increasing susceptibility to catastrophic wildfire within the analysis area provides the potential for large population irruptions of this species in response to such an event. All action alternatives will decrease habitat for black-backed woodpeckers. Although no treatments in lodgepole pine habitat have been prescribed, an unknown amount of lodgepole pine will be treated within mixed conifer stands. The major effects will occur with the reduction of densities throughout the analysis area. This effect will have more impact across the landscape with alternative 2, and less so with alternative 3 and 5 due to there being less acres identified for this type of treatment. The expected resultant improvement in overstory health will diminish the potential for small population irruptions over time in response to insect outbreaks. Populations are expected to decrease with the decline in insect activity. Some level of maintenance will occur as recruitment of new dead occurs as the result of prescribed fire. Recruitment of new dead will be minimal however and maintenance levels of black-backed woodpeckers will be below what currently exists. Cumulative Effects: Salvage activities of disturbance including beetle-kill and fire on the Paisley Ranger District have likely decreased black-backed woodpecker populations from historical levels. Ongoing prescribed fire on the Paisley Ranger District is expected to increase foraging habitat for black-backed woodpeckers through understory mortality and increase the nesting habitat through individual and clumps of overstory mortality. Due to the uncertainty of disturbance and what kind of activities will result from future disturbance, it is unknown how black-backed woodpeckers populations will cumulatively be affected over time. If fire suppression intensifies and intensive salvage logging occurs following fires, local and regional black-backed woodpecker populations may consequently decline (Murphy and Lenhausen 1998; Johnson and O’Neil 2001). However, unharvested snags from the Toolbox, Winter, and Grassy fires along with current bark beetle infestations in the area of Slide Mountain have incresed black-backed woodpecker habitat across the Forest.

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iv. Red-naped Sapsucker (MIS – Aspen and Deciduous Riparian Ecosystems) Red-naped sapsuckers are closely associated with aspen and deciduous riparian or forest stands. Sapsucker species require older trees with heart rot for nesting as well as adjacent conifers or mountain mahogony for sapwell feeding. Although sapsucker species have been documented within the analysis area’s late and old aspen clones, the preferred habitat of both red-naped and Williamson's sapsuckers has limited distribution throughout the watershed with about 792 acres of aspen identified. Many clones are generally in a mature, overmature, to declining/decadent condition with little regeneration evident. The limited regeneration that does occur shows light to severe damage from cattle grazing and/or ungulate browsing. Many clones are being overtopped and outcompeted by conifers, further contributing to the decline of the stand. The distribution and total acres of aspen have undoubtedly declined since the turn of the century. This loss of preferred habitat for sapsuckers, several neotropical migrant bird species, beaver and other deciduous riparian vegetation dependent species is a contributing factor limiting population numbers and distribution of these species across the landscape. The effects of alternative 1 could be a gradual reduction in suitable habitat for this species. Continued grazing and browsing may affect regeneration and vigor of aspen and other deciduous vegetation. Conifers will continue to out-compete and overtop deciduous vegetation, particularily aspen, until many clones die out and eventually topple. Population numbers for red-naped sapsuckers and other riparian deciduous vegetation dependent species will decline. Alternatives 2, 3, and 5 present the opportunity to increase the quality of potential habitat by reducing conifer competition in aspen habitats. A total of 363 acres of aspen habitat have been identified for treatment to stimulate regeneration and reduce competition. Riparian habitat conditions would improve with stimulated growth and regeneration of deciduous vegetation and herbaceous and shrubby forage from the flush of nutrients from prescribed fire and more open and favorable growing conditions. Distribution of cattle grazing is expected to improve as new foraging areas are created with more open and favorable conditions, relieving grazing pressure on riparian areas and other areas of concern. As habitat quality increases, population numbers for red-naped sapsuckers and other riparian deciduous vegetation dependent species will show a corresponding increase. Cumulative Effects: On the Paisley Ranger District, some aspen has gradually been replaced by conifers over time as a result of the change in forest structure to dense conifer stands from fire suppression and timber management, and regeneration is limited due to the impacts from grazing by cattle and big game. Where stream channels have been downcut and/or widened and the water table lowered, site potential for aspen has been reduced. With the reduction of aspen, and in some cases the entire loss of clones, population levels and distribution of red-naped sapsuckers have likely declined from historical levels. Forseeable potential future actions that could affect aspen habitats include the Baja and Headwaters prescribed burning projects and restoration projects within the Upper Sycan watershed. Prescribed fire and silvicultural treatments designed to promote aspen stimulation and regeneration, are expected to improve aspen habitat for sapsuckers. Thinning encroaching conifers within aspen will open up stands and allow for expansion and growth, prescribed fire will stimulate regeneration, and improved riparian conditions will eventually improve water tables. Large scale prescribed burning is likely to improve the distribution of cattle and big game with increased foraging opportunities.

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Cumulatively, it is anticipated that red-naped sapsuckers and other riparian dependent species populations will increase immediately as aspen expands and regenerates across the landscape. v. Primary Excavators/Cavity Dependent Species (MIS – Dead Trees) Fremont Forest Plan standards and guidelines for snags and downed wood are assumed to represent the minimum required for 100% of potential population levels of primary cavity excavators. The optimum level for these species may be somewhat higher, while the desired condition should be somewhere between the minimum and optimum. Cavity dependent species that may be present in the Jakabe analysis area include Lewis' woodpecker, northern flicker, black-backed woodpecker, hairy woodpecker, downy woodpecker, white-headed woodpecker, Williamson's sapsucker, red-breasted sapsucker, mountain chickadee and the red-breasted, white-breasted and pygmy nuthatches. Additional bird, amphibian, and mammal species that utilize snags and down wood for some portion of their life histories may be present as well. Snag and large woody debris (LWD) densities for the forested portion of the analysis area are variable with higher numbers in areas of light or little management activities and relatively low numbers in areas of intensive management. This is the result of several factors including salvage actvities, past fire prevention activities, and an inadequate number retained or loss of snags and replacements in previously harvested units. Insect and disease activity, drought, and overstory mortality due to high stand densities have reslulted in new snags and down wood but are generally less than required by standards and guidelines primarily in ponderosa pine and mixed conifer stands. Lodgepole pine stands appear to have more than adequate numbers of snags and large down wood. Snag and down wood surveys based on proposed regional protocols were conducted in the watershed during the 1998 and 1999 field season within stands and previously harvested units of all species. The mean number of snags and LWD for the watershed in all stands except lodgepole pine types is 3.0 snags and .9 pieces (> 6’ long, 12” dbh on small end) per acre. In harvested units, the mean numbers are .5 snags and .4 pieces per acre. These numbers are below the standard and guidelines. Generally, lodgepole pine types are assumed to at least meet the standards and guidelines. Initial counts in Bear Creek indicated numbers well over the Forest Plan requirements . Alternative 1 will provide the greatest amount of snags and large down wood for cavity dependent species. Additional snags and large down wood will be created as overstory mortality increases and dead trees eventually fall creating new foraging and nesting habitat. Population numbers are expected to increase with the additional nesting and foraging habitat. Alternatives 2, 3, and 5 will harvest much of the potential future habitat for these species. Alternative 3 and even more so alternative 5 generates the least effects due to the mitigating effects of leaving clumps and untreated stands. Snags and downed wood would be retained at the levels assumed to maintain the current population of cavity dependent species. However, because current numbers do not meet the desired conditions or standards and guidelines, all snags and LWD would have to be retained in ponderosa pine and mixed conifer stands to maintain the current population. Usually safety concerns will not allow this. Therefore, the following mitigation measure will be inluded:

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In order to insure that existing snag numbers are maintained, any snags felled for safety reasons during project implementation would be mitigated by creating a replacement snag or snags. This would be achieved through topping, inoculation, girdling or other methods.

Population numbers for cavity dependent species are expected to decline until some level of maintenance will occur as recruitment of new dead occurs as the result of prescribed fire. Recruitment of new dead will be minimal however and maintenance levels of cavity dependent species will be below what currently exists. It is expected that any snag recruitment over time that is within 200’ of a road will be lost due to hazard tree removal or firewood cutting. Application of DecAID for the Jakabe Dead Wood Analysis It is assumed that if snag numbers and distribution are similar to “reference” or “natural” conditions, we would be meeting the snag needs of cavity nesting birds under the historic range of variability. Currently, it appears as though snag distribution across the landscape is very similar to “reference” conditions for snag >20” dbh and that there is currently a greater amount of the area with 0-10 snags per acre >20” dbh then there is in the “reference” conditions. There are some differences in snag distribution across the landscape for snags >10” dbh. There is less area in the subwatersheds with 0 snags per acre and more area in the subwatershed with 0-10 snags per acre then there is in the “reference” conditions. This likely means that snags are better distributed and more evenly distributed cross the watershed then there is in the “reference” conditions. The habitats that are rare in the subwatersheds and may below “reference” conditions are the areas of very high snag densities of 10+ snags per acre which are created by disturbance. This means that habitat may be lacking for those species that depend on high densities of snags such as black-backed woodpeckers and pileated woodpeckers. However, when looking at the watershed locally and comparing it to 1930’s and 1947 vegetation mapping, none to very little of the watershed was represented as post-fire condition. There is currently 0% of the Watershed in a post-fire condition; similar to what is represented in 1930’s and 1947 data that is available. This may indicate that this local area may have actually had less of the area with high densities of snags then what is represented in the PPDF inventory data in DecAID which represents a very large area across Oregon and Washington. However, it is very important to recognize that the “reference” condition, 1930’s, and 1947’s data individually provides only one point in time. With the variability of fire under historical conditions, certainly at some point in history, some of the ponderosa pine type within this watershed was in a post-fire condition. It was likely in small patches and appears to have been very infrequent within this Watershed.

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Percent of the Chewaucan Watershed in a Post-fire Condition

0 0 00

0.5

1

1930's 1947 current

YearPe

rcen

t of

Land

scap

e

Use of inventory data from unharvested plots to mimic “natural” conditions admittedly may be misleading in this wildlife habitat type due to decades of fire exclusion, harvest, climate changes, and other factors. Therefore, below is a summary of 3 other sources of information on snag densities in "presettlement" or historic times, each with its own assumptions and limitations. They are not specific to any Structural Condition Class. Harrod et al. (1998) estimated historical snags densities in ponderosa pine-dominated, dry forests. Harrod estimated that densities of snags greater than 6 inches dbh ranged from 5.9 to 14.1/acre in pre-European settlement landscapes. Their estimates were derived by calculating growth in basal area from pre-1930 growth rates, holding forest stand structure relatively constant (i.e. as a new live tree is recruited another one becomes a mortality), and applying published snag fall rates (Bull 1983, Keen 1929, Raphael and Morrison 1987, Schmid et al. 1985) to calculate basal area of snags every 10 years. They assumed that historic frequent, low-intensity fires did not accelerate snag fall rates.

Agee (2002) estimated lower snag densities than Harrod et al. for the ponderosa pine/Douglas-fir forest series by estimating number of trees in 0.1ha clumps of 16 age classes and assuming that the oldest patch is killed by insects every 25 years. He assumed fire helped to decompose snag patches and that after 5 fires at 10-year intervals the snags would be completely consumed. His estimated historical snag density was 2 per acre. Agee (2002) compares his estimates to Harrod et al. (1998) but states a different assumption about dbh of snags; Agee assumes an average snag dbh of 75 cm (30 in) when calculating biomass, while Harrod et al. estimated densities for size classes as small as 15 cm (6 in) dbh. Results from regional studies in Eastern Washington and Oregon (of all ownerships) by Ohmann and Wadell suggest there are currently 2.025 total snags per acre greater than 10 inches dbh of which 0.405 snags were greater than 20 inches dbh (2002).

There is a ponderosa pine site in Idaho that has never been harvested and that has undergone wildfires over the past decades. Recent snag data from this site reveals that there are approximately 3.6 snags per acre > 12” dbh. Overall, current average snag densities based on 1998 snag inventory data reflects that there is an average of 2.15 snags per acre >10” dbh in the ponderosa pine communities across the Watershed. This is within the range of snag densities predicted by Harrod and Agee; similar to the regional studies by Ohmann and Wadell; and slightly less than the site in Idaho which had 3.6 snags per acre.

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LRMP Standards and Guidelines, as amended by the Regional Forester’s Amendment #2, require that “all sale activities (including regeneration, select cutting, thinning, or salvage harvest) will maintain snag and green tree replacement/roost trees greater than 15 inches dbh at 100 percent population potential levels of primary cavity excavators. The LRMP as amended directs this to be done “using the best available data on species requirements as applied through current snag models or other documented procedures.” In keeping with the direction to use the best available information on species requirements, the data available in DecAID, or “the decayed wood advisor for managing snags, partially dead trees, and down wood for biodiversity in Washington and Oregon” (Mellen et al. 2003) was used as a reference to discuss the effects of this project.

The current direction of managing for 100 percent population potential levels of primary excavators may not represent the most meaningful measure of managing for cavity-nesters and that these snag levels, under certain conditions, may not be adequate for some species. DecAID was used as a source because it is a culmination of the most recent science and data available. As stated by Johnson and O’Neil (2001), DecAID is based on a thorough review of the literature, available research and inventory data, and expert judgment.

Primary excavators, such as woodpeckers and nuthatches, are forest dwelling birds that are specialized for foraging on and nesting in decaying wood. They require trees with rotted heartwood for excavating nest holes and for a foraging substrate (Jackman 1974). This foraging substrate consists of insects such as bark and wood boring beetles on the surface of trees. Their impact is sometimes great enough to prevent insect outbreaks (Jackman 1974). The most significant role primary excavators play in the forest community is the provision of nest holes for small mammals or for cavity nesting birds that do not excavate their own holes (Jackman 1974). Approximately 31 percent of the total bird fauna use snags for nesting and denning, foraging, roosting, communicating, and as hunting and resting perches (Raphael and White 1984). Rose et al. identifies 96 wildlife species associated with snags and 86 species associated with down wood (2001). Most snag using wildlife species are associated with snags greater than 14.2” dbh with about a third of these using snags greater than 29.1” dbh. Mountain pine beetles, mistletoe, and root disease are some of the mortality agent within the Jakabe Project Area. DecAID can help managers decide how much snag and down wood of different sizes should be retained to meet wildlife management objectives for a particular project or area (Mellen et al, 2002). The information contained in DecAID is based on published scientific literature, research data, expert judgment, and professional experience. It is primarily a statistical summary of published research data for wildlife presence (mainly cavity-nesting birds) and inventoried forest conditions (Mellen et al, 2003). Assessments about the potential effects of this project on species viability are based on site-specific information, local experience, and professional judgment, along with data from the DecAID analysis. DecAID was not intended or designed to be a stand-alone method of predicting effects on species viability.

DecAID presents information on the range of “natural conditions” (as represented by unharvested plots within the plots sampled) “current conditions” (all plots sampled, including both unharvested and harvested plots) and wildlife use, with respect to densities (abundance) of snags and down wood, and sizes of snags and down wood.

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How the data in DecAID was reviewed specific to this project For this project, DecAID was not used to determine appropriate snag levels across the project area. Because this project will have a minimal effect on snag habitat (snags will only be felled if they pose a safety hazard during logging operations), there was not a need to determine snag numbers. DecAID was used to compare existing conditions to “reference” conditions (as represented by the inventory data in DecAID) for the effects anaysis of this project. Although there is some mixed conifer and lodgepole pine type in the watershed, the ponderosa pine vegetation type was the only vegetation type analyzed for snags for this project because this is the predominant vegetation type in the watershed. Lodgepine pine was also not analyzed for this project because currently there is no data available in DecAID for this vegetation type. The Silviculturist on the interdisciplinary team determined that historically, the ponderosa pine type in the Jakabe Project Area would have fit either the ponderosa pine/Douglas fire (PPDF)_ Small/Medium, PPDF_Large, or the PPDF_Open Trees Vegetation Condition. The Chewaucan Watershed Analysis was referenced to determine historically about what percent of the forested landscape in the ponderosa pine type was in the early to mid and late category.

The Chewaucan Watershed Analysis states that the reference seral stage distribution in the ponderosa pine type is:

Early to Mid (nonstocked to small sawtimber) PPDF_Open

20% (95% single story, 5% multi story)

Late (medium sawtimber and greater) PPDF_Small/Medium

80% (95% single story, 5% multi story)

For information on how the following charts were developed, please refer to DecAID - Jakabe Snag Analysis - Application of DecAID, July 11, 2005 on file at the Paisley Ranger District. Chart 1. Distribution of Snags >10” dbh

Distribution of Snags >10" dbh

Comparison of "Reference" Conditions Based on DecAID Inventory Data and Existing Conditions From Snag Surveys

57%

25%

4% 4%

60%

2% 0%

9%

0%

39%

0%

10%

20%

30%

40%

50%

60%

70%

0 0-10 10-20 20-30 30+

Number of Snags per Acre >10" dbh

Perc

ent o

f Lan

dsca

pe

"Reference" Condition

Existing Condition

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Chart 2. Distribution of Snags >20” dbh

Distribution of Snags >20" dbh

Comparison of "Reference" Conditions Based on DecAID Inventory Data and Existing Conditions From Snag Surveys

71

26

2 0 0

59

42

0 0 00

1020304050607080

0 0-10 10-20 20-30 30+

Number of Snags per Acre >20" dbh

Perc

ent o

f Lan

dsca

pe

"Reference" Condition

Existing Condition

It is assumed that if snag numbers and distribution are similar to “reference” or “natural” conditions, that we would be meeting the snag needs of cavity nesting birds under the historic range of variability. Therefore, by comparing the above charts it appears as though snag distribution across the landscape is very similar to “reference” conditions for snag >20” dbh. It appears that there is currently a greater amount of the area with 0-10 snags per acre >20” dbh then there is in the “reference” conditions. There are some differences in snag distribution across the landscape for snags >10” dbh. There is less area in the subwatersheds with 0 snags per acre and more area in the subwatershed with 0-10 snags per acre then there is in the “reference” conditions. Overall, current average snag densities based on 1998 snag inventory data reflects that there is an average of 2.15 snags per acre >10” dbh in the ponderosa pine communities across the Watershed. This is within the range of snag densities predicted by Harrod and Agee; similar to the regional studies by Ohmann and Wadell; and slightly less than the site in Idaho which had 3.6 snags per acre. Cumulative Effects: Due to past harvest management including roadside hazard, fire suppression, snag removal, and overstory removal, snag and down wood numbers have declined from historical levels. Excavators associated with open late/old ponderosa pine, such as the white-headed woodpecker and Lewis woodpecker, have likely experienced a decline in habitat suitability, bird distribution, and populations. This decline is a result of forest succession from an open pine forest to a dense mixed conifer dominated forest, and from the direct removal of snag habitat. Forseeable potential future actions that could affect cavity dependent species habitats include the Baja and Headwaters prescribed burning projects and restoration projects within the Upper Sycan watershed. Prescribed fire and silvicultural treatments designed to promote the development of LOS

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habitat with a snag and down wood component, are expected to improve habitat for cavity dependent species. Prescribed fire is expected to increase replacement snag and down wood numbers and reduce the fuel loading thereby protecting stands from wildfire. Cumulatively it is expected that with the action alternatives and the expected future activities on the Paisley Ranger District, that as LOS habitat develops across the landscape (150-200 years), primary and secondary excavator populations would increase over time. Additional data discussion regarding DecAID can be found in the analysis file. iv. Goshawk (MIS – Overmature/mature Ponderosa Pine, Mixed Conifers) The northern goshawk is the largest North American accipiter and was chosen as a MIS species due to its association with mature and LOS ponderosa and mixed conifer forest structural stages for nesting. The goshawk's home range encompasses about 6000 acres and is composed of a nest core area, post-fledging area, and a foraging area. Suitable goshawk habitat exists throughout much of the analysis area. Approximately 993 acres have been designated as old growth habitat for goshawk or goshawk and pileated woodpecker. Another 2580 acres have been designated as goshawk post-fledging areas (PFAs) and nest sites. Six active goshawk nest sites and 2 alternate nests have been identified within the watershed. Suitable habitat for goshawks currently exists in all subsheds. Habitat for prey species and foraging has improved where the removal of late and old seral forest has increased the area of open and early seral forest cover types. Foraging habitat quantity and quality has declined where open, parklike LOS pine stands have been replaced by dense, multi-story LOS stands. Habitat quality has declined since the 1940's with increased disturbance from higher road densities, increased commercial logging activity, and greater recreational use. Goshawk sightings have been documented on several occasions within the Jakabe analysis area. Many of these sightings are associated with known or suspected nesting areas. Alternative 1 would have the least effect on goshawk nesting habitat. However, foraging habitat for goshawks would remain as is and over the long term would gradually decline as understory densities increased. Population numbers would not be affected initially, although gradual loss of foraging habitat in the long term could result in a corresponding decline in the number of goshawks. Alternatives 2, 3, and 5 could result in a loss of potential nesting habitat for goshawks due to the opening up of stands through density reduction. While foraging habitat for goshawk would increase due to increased amount of open area, available habitat for small mammal and bird species (goshawk prey species) could be limited by the amount of large down wood and shrubs retained and available for future recruitment. Goshawk numbers will be dependent upon the availability of prey species, although habitat quality should improve with the creation of additional open areas. If prey species respond favorably to increases in herbaceous forage, goshawk numbers could increase, otherwise no change in goshawk population numbers is anticipated. Existing known goshawk PFAs and designated old growth stands managed for goshawks will have a modified treatment designed specifically to improve the stands as goshawk habitat. The silvicultural treatment includes a mosaic of three stand types: 1) untreated dense areas; 2) a 50:50 mix of treated/untreated areas; and 3) open conditions. This is expected to provide a mix of foraging, prey habitat, and nesting conditions preferred by goshawks.

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Other raptors will be addressed with the following mitigation measure: If an active raptor nest is found during operations, at least 300 yards around the nest site will be left untreated until young have fledged (usually around 7/30-8/15). Cumulative Effects: Forseeable potential future actions that could affect goshawk habitats include the Baja and Headwaters prescribed burning projects and restoration projects within the Upper Sycan watershed. All projects will open stands providing increased foraging opportunities for goshawks. Opportunities to improve riparian habitats through vegetation manipulation and reintroduction of fire may be implemented which will also improve foraging habitat. Road closures and obliterations could improve habitat security. The cumulative effects on goshawk and their habitats from these actions would result in a net decrease in nesting habitat and an improvement in the quantity and quality of foraging habitat. vii. Pine Marten (MIS – High Elevation Forests, Lodgepole Pine and Mixed Conifers) The American marten was chosen as a MIS species due to its close association with late successional mixed conifer and lodgepole pine forests. Martens prefer late successional stands of mesic mixed conifer forests, particularly those with complex physical structure near the ground (Ruggiero et. al. 1994). Openings greater than 2 acres are generally avoided due to marten susceptibility to predators and the lack of forest structure for maintenance of prey species. Potential marten habitat exists in the Bear Creek subshed north and west of forest road 3315, and in the Ben Young and Swamp Creek subsheds. The only documented occurrence of marten within the watershed is just north of Moss Pass Butte (1997). Both habitat availability and continuity have declined within the last 50 years. Habitat suitability however, may have increased in patches of LOS forest habitat where mixed conifer has replaced or invaded ponderosa pine stands providing the dense conditions, increased overstory mortality and down wood that provide suitable pine marten habitat. Sanitation and salvage logging, however, have limited the availability and abundance of this habitat. Habitat security has declined since the 1940's with increased disturbance from higher road densities, increased commercial logging activity, and greater recreational use. No old growth management areas for pine marten or pine marten/three-toed woodpeckers (black-backed) have been designated within the Jakabe analysis area. Alternative 1 would have the least effect on pine marten habitat. As ever increasing stand densities affect overstory health and tree mortality occurs, habitat quantity and quality increases for pine marten in the form of new denning and foraging sites. If increased foraging and denning opportunities are utilized by pine marten, a gradual increase in population numbers for this species could occur corresponding to increased overstory mortality and resultant changes in stand structure. Alternative 2, 3, and 5 result in the loss of potential denning and foraging habitat for pine marten. Snags and downed wood would be retained at the levels assumed needed to maintain the current population of pine marten. Proposed road closures and obliterations will increase habitat security. Riparian area treatments could improve foraging habitat quality by stimulating deciduous growth and where creating small openings. However, loss of structure, canopy closure, and potential denning and foraging sites in treatment areas will reduce suitability of habitat for pine marten. The

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opportunity for a gradual increase in population numbers for marten is foregone with reduced habitat suitability. Cumulative Effects: Lodgepole pine and mixed conifer LOS habitat that contained a large amount of snag and down wood habitat has decreased on the Paisley Ranger District. This is largely due to timber harvest and a lesser degree to wildfire, firewood cutting, and hazard tree removal. These disturbance agents have removed snag and down wood, reduced patch sizes and connectivity, and diminished the amount of high quality LOS interior habitat and overstory canopy cover all required for pine marten habitat. It is anticipated that pine marten populations have likely decreased from historical levels. Forseeable potential future actions that could affect pine marten habitats include the Baja and Headwaters prescribed burning projects and restoration projects within the Upper Sycan watershed. All projects will open stands reducing habitat suitability for marten. Silvicultural treatments designed to promote LOS character including a large tree component, snag and down wood development, and a multistructure in the mixed conifer stands is expected to increase habitat quality for pine marten and most importantly, improve the continuity of LOS across the landscape in the long term. Opportunities to improve riparian habitats through vegetation manipulation and reintroduction of fire may be implemented which could improve foraging habitat. Road closures and obliterations could improve habitat security. Cumulatively, pine marten populations are not expected to change in the short term, but may increase in lodgepole pine or ture mixed conifer types as continuous LOS habitat containing heavy amounts of snags and down wood develops across the landscape in the long term (150-200 years). viii. Pileated Woodpecker (MIS – Overmature/mature Mixed Conifer Forests) Pileated woodpeckers are the largest woodpeckers in North America and were chosen as a MIS species because of its close association with old growth conifer forests. Of the woodpeckers, the pileated is the most likely to be affected by timber management practices due to its large size and resultant need for large dead trees for nesting, large hollow trees for roosting, and dead woody material for foraging (Bull et. al. 1990). The pileated is also responsible for creating nest holes for numerous larger secondary cavity nesters. Approximately 90% of the diet of these birds consists of carpenter ants, which are associated with large standing and downed wood. Pileated sightings, vocalizations, and foraging habitat have been recorded in the Bear Creek and Chewaucan River subsheds. None of the watershed has been surveyed for presence of pileated woodpecker. Areas of suitable habitat occur primarily in mixed conifer stands in the upper elevations of the Bear Creek and Swamp Creek subsheds. Suitability decreases within the mid to lower elevations of the watershed where ponderosa pine dominates. The amount of newly created dead tree habitat due to stressed overstories, especially where white fir has established itself under ponderosa pine, provides increasing foraging and nesting opportunities for pileated woodpeckers. Overall, habitat conditions have improved where mixed conifer has replaced or invaded ponderosa pine stands providing the dense conditions and increased overstory mortality that provide suitable pileated habitat. Sanitation and salvage logging, however, have limited the availability and abundance of this habitat. Habitat security has declined with increased disturbance from higher road densities, increased commercial logging activity, and greater recreational use.

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Approximately 525 acres of old growth designated at pileated woodpecker habitat exists within the planning area. These areas will receive no treatments so the habitat components required including high canopy closure, mixed dense stands, etc. will be retained. Alternative 1 would provide for the greatest amount of pileated foraging and nesting habitat. Populations are expected to show a gradual increase over time corresponding with increased stand densities and mortality in the overstory. Alternatives 2-3, the action alternatives, may result in the loss of future foraging and nesting habitat for pileated woodpecker within proposed harvest units in the ponderosa pine type. Habitat suitability will decline as the proposed treatments in the overstocked ponderosa pine type reduce canopy cover and convert the stands back to single story pine stands. However, existing snags and downed wood would be retained at current levels which are assumed to maintain the current population. A decrease in the number of pileated woodpeckers that currently use these areas could occur due to the change in stand structure. Within the areas identified for treatment in the mixed conifer type, it is expected that habitat will remain suitable for pileated woodpecker foraging and nesting as treatments provide for more sustainable conditions. Pileated woodpecker populations should remain stable within these areas. It is expected that the potential decline in pileated woodpecker population may be offset by an increase in habitat within the areas that are not identified for treatment. There are approximately 24,000 acres of forested type in the ponderosa pine and the mixed conifer type that are not identified for treatment. As stated above, these stands are at high risk for bark beetle attack and increased mortality is expected. This will lead to an increase in snag and down wood habitat providing optimal habitat for pileated woodpeckers. Although habitat may be lost in the areas proposed for treatment in the ponderosa pine type (approximately 8200 acres), and it expected that the woodpeckers will shift to the non-treated stands as the beetle epidemic shifts. Overall across the landscape, pileated woodepecker populations are expected to increase due to the large amount of area that is not identified for treatment. Cumulative Effects: LOS habitat that contained a large tree component and snag and down wood habitat has decreased on the Paisley Lake Ranger District. This is largely due to timber harvest and a lesser degree to firewood cutting and hazard tree removal. These disturbance agents have removed large diameter trees, snags, and down wood, reduced patch sizes and connectivity, and diminished the amount of high quality LOS interior habitat and overstory canopy cover all required for pileated woodpecker habitat. Succession of some true ponderosa pine sites towards a mixed conifer composition as a result of fire suppression may lead to increased habitat for pileated woodpecker as these stands develop LOS structural character. It is anticipated that pileated woodpecker populations have likely decreased from historical numbers within the true mixed conifer ecotypes, but have likely increased from historical numbers within overstocked ponderosa pine ecotypes. Forseeable potential future actions that could affect pileated woodpecker habitats include the Baja and Headwaters prescribed burning projects and restoration projects within the Upper Sycan watershed. Prescribed fire and silvicultural treatments designed to promote existing and future LOS habitat within true mixed conifer stands are expected to improve habitat for pileated woodpeckers. It

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is expected that the true ponderosa pine stands that have moved toward a mixed conifer composition will be converted back to true ponderosa pine forests thereby decreasing what may have been future habitat for pileated woodpeckers. Prescribed fire is expected to increase replacement snag and down wood numbers and reduce the fuel loading thereby protecting the stand from wildfire.

The current ongoing beetle epidemic in the Chewaucan Watershed is expected to create more habitat for pileated woodpeckers in the near future. This will likely lead to an increase in local populations and a shift in location for nesting and foraging. Cumulatively in the short-term, it is expected that pileated woodpecker habitat will remain above historical levels due to an increase in snag and down wood habitat largely due to the beetle epidemic in forested areas that are not treated. Cumulatively, it is expected that pileated woodpecker populations would return to historical levels in the long term (150-200 years) as continuous mixed conifer LOS habitat develops across the landscape, and ponderosa pine stands become more sustainable and less resistent to insect and disease outbreaks through mechanical and prescribed fire treatment. 2. Proposed, Endangered, Threatened, or Sensitive (PETS) Species The Jakabe analysis area contains habitat or documented occurrences of the below listed threatened, endangered, or sensitive (TES) animal species. No other TES animal species are known to occur or have suitable habitat within the analysis area. The Endangered species Act requires National Forests to manage for the recovery of threatened and endangered species (as identified by the U.S. Fish and Wildlife Service) and the ecosystems upon which they depend. In addition, the Regional Forester has identified sensitive species for each National Forest, where species viability may be a concern. The following table displays the federal and regional listings.

Threatened, Endangered, and Sensitive Species

Representative of:

Bald Eagle

Federally Listed Threatened Species

Canada Lynx

Federally Listed Threatened Species

Oregon Spotted Frog

Federally Listed Candidate Species R6 Sensitive Species List

Yellow-Billed Cuckoo

Federally Listed Candidate Species

Horned Grebe

R6 Sensitive Species List

Red-necked Grebe


Least Bittern


Bufflehead


Peregrine Falcon


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Western Sage Grouse R6 Sensitive Species List Yellow Rail


Upland Sandpiper


Gray Flycatcher


Tricolored Blackbird


California Wolverine


Pacific Fisher


Pygmy Rabbit


Northern Leopard Frog


Columbia Spotted Frog


Northwestern Pond Turtle


The following table displays the threatened and endangered species that would potentially be affected by the Jakabe Project (discussion follows).

Effects* No Action Alternative Action

Alternatives Species Name Status Species Habitat Specie

s Habitat

Bald eagle (Haliaeetus leucocephalus)

Threatened

NE

NE

NE

NE

Canada lynx (Lynx canadensis)

Threatened

NE

NE

NE

NE

Oregon spotted frog (Rana pretiosa)

Candidate

NI

NI

NI

NI

Yellow-billed cuckoo (Coccyzus americanus)

Candidate

NI

NI

NI

NI

*Effects Determination Code for Threatened or Endangered Species NE = No Effect from the project on the species or critical habitat. LAA = The project may affect and is likely to adversely affect the species or critical habitat. Formal Consultation with U.S. Fish & Wildlife Service is required. NLAA = The project may affect the species or critical habitat, but those effects are not likely to adversely affect the species or critical habitat. Informal Consultation is required with concurrence from the U.S. Fish & Wildlife Service. BE = The project would benefit a species or its habitat. Written concurrence from the U.S. Fish & Wildlife Service requested.

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*Effects Determination Code for Candidate Species NI = No Impact MIIH = May impact individuals or habitat, but would not likely contribute to a trend toward federal listing or loss of viability to the population or species. The following table displays the Region 6 sensitive species that would be affected by the Jakabe Project (discussion follows).

Effects* No Action Alternative Action Alternatives

Species Name Species Habitat Species Habitat Horned grebe (Podiceps auritus) NI NI NI NI Red-necked grebe (Podiceps grisegena) NI NI NI NI Least bittern (Ixobrychus exillis) NI NI NI NI Bufflehead (Bucephala albeola) NI NI NI NI Peregrine falcon (Falco peregrinus) NI NI NI NI Western sage grouse (Centrocercus urophasianus) NI NI MIIH MIIH Yellow rail (Coturnicops noveboracensis) NI NI NI NI Upland Sandpiper (Bartramia longicauda) NI NI NI NI Gray flycatcher (Empidonax wrightii) NI NI MIIH MIIH Tricolored blackbird (Agelaius tricolor) NI NI NI NI California wolverine (Gulo gulo) NI NI NI NI Pacific fisher (Martes pennanti) NI NI MIIH MIIH Pygmy rabbit (Brachylagus idahoensis) NI NI NI NI Northern Leopard Frog (Rana boylii) NI NI NI NI Columbia Spotted Frog (Rana luteiventris) NI NI NI NI Oregon spotted frog (Rana pretiosa) NI NI NI NI

Northwestern Pond Turtle (Clemmys marmorata marmorata) NI NI

NI NI

*Effects Determination Code for R6 Sensitive Species NI = No Impact MIIH = May impact individuals or habitat, but would not likely contribute to a trend toward federal listing or loss of viability to the population or species i. Bald Eagle (MIS – Threatened Species) Status: Federal Category - Threatened. WA/OR - Threatened. Findings: No Effect. PREFIELD REVIEW: Suitable trees for nesting and roosting exist within the planning area especially along the Chewaucan River. However, no active, potential or marginal nesting or roosting areas have been identified. Bald eagle sightings have been documented within or immediately adjacent to

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the Jakabe analysis area. The nearest know site is the Avery Creek winter roost located just to the east of the watershed boundary near Morgan Butte. Many of the bald eagle sightings documented within the analysis area may be associated with this site. Spring and summer sightings of adult bald eagles associated with the confluence of Bear Creek and the Chewaucan River suggest the possiblity of a nest in the area. FIELD RECONNAISSANCE: Ongoing field reconnaissance activities in the form of yearly monitoring activities and timber sale or other project reconnaissance have resulted in the bald eagle sightings above. Reconnaissance has taken place within the planning area during the wintering, courtship and nesting periods for bald eagles. A thorough search of the Bear Creek drainage and theChewaucan River area near the Bear Creek confluence in 1999 and 2000 resulted in no additional eagle sightings or nests located. No active, potential, or marginal nesting or roosting sites are known to exist in the panning area. Sightings have primarily been associated with foraging activities along the Chewaucan River. DETERMINATION OF EFFECTS: Bald eagle sightings within the Jakabe analysis area appear to be associated primarily with foraging activities as described above. Proposed harvest and burning operations and associated activities will not occur within 1 mile of the known roost site, activities will not occur during the time winter roosting occurs and nesting activities have not been documented within the analysis area. No direct, indirect, or cumulative impacts on bald eagles are anticipated. ii. Gray Flycatcher Status: R6 Sensitive Species List Findings: May impact individuals or habitat, but not likely to contribute to a trend toward federal listing or loss of viability to the population or species. PREFIELD REVIEW: No sightings of gray flycatchers have been documented within the Jakabe analysis area. FIELD RECONNAISSANCE: Neo-tropical migrant bird (ntmb) point count surveys and monitoring avian productivity and survivorship (maps) mist netting stations at three sites within the analysis area have not resulted in any gray flycatcher observations. Although gray flycatchers were not detected during the field reconnaissance performed for this project, habitat does exist in the ponderosa pine/mountain big sagebrush/bluegrass or juniper/low sagebrush/fescue ecotypes. DETERMINATION OF EFFECTS: Proposed activities will impact areas of possible habitat. Proposed juniper treatments are expected to impact potential nesting habitat. Prescriptions will be designed however to provide for a mosaic of juniper habitats with the potential for enhanced deciduous, shrub and herbaceous growth between patches of juniper. Proposed timber harvest treatments in dry ponderosa pine sites could also impact habitat for gray flycatchers especially where juniper is present, primarily by opening up stands for increased foraging opportunities but also reducing potential nesting habitat. Prescribed burning will also impact suitable habitat, resulting in a loss of potential nesting habitat and an increase in foraging sites. Burn prescriptions will be designed to provide for a mosaic of burned and unburned areas (see mitigation and resource protection measures) providing for both nesting/roosting habitat and new foraging sites. Spring burning and mechanical treatment implemented between May 1 and July 15 may impact nesting birds, potentially reducing the number of successful fledglings. Implementation of proposed activities

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will impact potential gray flycatcher habitat and may impact individuals, but are not likely to contribute to a trend toward federal listing or loss of viability to the population or species. iii. Pacific Fisher Status: R6 Sensitive Species List Findings: May impact potential habitat, but not likely to contribute to a trend toward federal listing or loss of viability to the population or species. PREFIELD REVIEW: No sightings of fisher have been documented within the Jakabe analysis area. Fisher habitat within the analysis area is marginal due to lack of suitable large tree habitat and fragmentation of forest types from past management activities. Potential, though marginal, habitat may exist within mixed conifer habitat types in the Ben Young, Bear Creek, Coffepot Creek, and Swamp Creek subsheds. FIELD RECONNAISSANCE: A survey designed specifically to detect the presence/absence of fisher has not occurred on the Paisley or Silver Lake Ranger Districts. Numerous site visits for project analysis and track surveys performed in 1994 and 1997 resulted in no detections of fisher. DETERMINATION OF EFFECTS: Proposed treatments will reduce canopy cover in potential fisher habitat. Where canopy closure in mixed conifer stands is reduced to less than 40-60% or stands are converted to single story stands, habitat suitability for fisher will decline or be lost. Since fisher are not documented as occurring within the analysis area proposed activities will have no direct, indirect, or cumulative impacts Pacific fisher but may impact their habitats. Proposed actions will not cause a trend toward federal listing or loss of viability. iv. Peregrine Falcon (MIS – Endangered Species) Status: Federal: recently downlisted from endangered, OR/WA: endangered, R-6 Sensitive Species List Findings: No impact. PREFIELD REVIEW: Potential peregrine nesting habitat has been identified at 17 cliff sites within the watershed (White, et al, 1980). An additional 5 sites have been identified on or immediately adjacent to the watershed boundaries. Only sporadic surveys of these potential sites have occurred. It is not known if any of these sites are occupied. None of these sites have been identified as Management Area 2 (emphasis on endangered and threatened species). There are no known active or historical nest sites. The number of potential sites in each subshed is listed below: Bear Creek 3 Ben Young Creek 0 Chewaucan River 13 Coffeepot Creek 0 Swamp Creek 1 Habitat for prey species and foraging has improved where the removal of late and old seral (LOS) forest has increased the area of open, early seral forest cover types. Foraging habitat quantity and quality has declined where open, parklike LOS pine stands have been replaced by dense, multi-story

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LOS stands. Habitat quality has declined since the 1940's with increased disturbance from higher road densities, increased commercial logging activity, and greater recreational use. A single peregrine falcon observation has been documented within the watershed near Parker Hills in 1998. FIELD RECONNAISSANCE: Field surveys for peregrine falcons were completed at the above mentioned potential habitat areas in 1998 and 1999. No additional peregrine falcons or evidence of nesting were observed. DETERMINATION OF EFFECTS: No known areas of occupied peregrine falcon habitat exist within the planning area therefore implementation of the proposed activities will not cause any impacts on peregrine falcons or their habitats. Activities will not cause cumulative impacts on peregrine falcons or their habitats nor lead to a loss of viability. v. Western Sage Grouse Status: Region 6 Sensitive Species List Findings: May impact individuals, but not likely to contribute to a trend toward federal listing or loss of viability to the population or species. PREFIELD REVIEW: Habitat is present for sage grouse in the northernmost sections of the analysis area, along the National Forest boundary, and on the eastside of the Chewaucan River. Anecdotal information suggests that sage grouse may have occurred historically in the Sage Hen Creek area. Historic numbers and lek locations are not known. No documented sightings occur within the watershed. There are no known currently occupied areas of western sage grouse habitat. The quality of existing habitat has declined with advanced plant succession and juniper encroachment within the watershed. The primary effect is the loss of open areas for breeding displays and rearing/foraging habitat for young chicks within large sagebrush dominant communities. FIELD RECONNAISSANCE: Field reconnaissance was conducted in this area during the 1998 - 2000 field seasons by general survey methods. No sage grouse or evidence of their presence was found. DETERMINATION OF EFFECTS: Alternative 1 would have no significant immediate effect on sage grouse or their habitat. Long term effects would be a continued decline in quality of existing habitat with advanced plant succession and juniper encroachment within the watershed and the resultant loss of open areas for breeding displays and rearing/foraging habitat for young chicks within large sagebrush dominant communities. Alternatives 2 and 3 could impact sage grouse if nesting or lek activities occur within the analysis area. Prescribed burning and mechanical treatments will enhance sage grouse habitat with treatments designed to minimize loss of winter and security cover by leaving a mosaic of burned and unburned islands of sagebrush, establishing a variety of sagebrush seral stages to meet the entire life cycle needs of sage grouse, and reducing conifer encroachment into sagebrush habitats. Sage grouse nesting and brood rearing habitat will be improved by providing dense nesting cover, enhancing forb production, and reducing loss of sagebrush habitats to conifer (juniper) encroachment. Proposed project activities are expected to be beneficial for sage grouse habitat, but

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may impact individuals if present during project implementation, but are not likely to contribute to a trend toward federal listing or loss of viability to the population or species. CUMULATIVE EFFECTS: Overall, past grazing practices and loss of habitat by conversion from sagebrush to pastureland has had the greatest effects on sage grouse. Habitat for sage grouse in the Chewaucan basin is located primarily along the "desert fringe" and is a relatively small percent of available sage grouse habitat. Much of western sage grouse habitat in this area is within Bureau of Land Management and other ownership lands of the the Great Basin. The proposed activities will not affect a significant amount of sagebrush habitat, therefore implementation should not cause any significant cumulative impacts on sage grouse or their habitats. 3. Other Species and Habitats of Concern i. Beaver Beaver are less numerous now in the Jakabe analysis area than they were historically. Many areas that show historic evidence of beaver activity are presently unoccupied. The initial decreases were associated with extensive trapping. Decline in habitat has acted as a more recent influence on decreasing beaver populations. Habitat for beaver has declined with the loss of deciduous shrub and tree species from the riparian ecosystem. Existing beaver sign indicates historical beaver presence in perennial systems and associated tributaries within the analysis area. This suggests that beaver abundance was historically higher than it is now. ODFW records tend to support this. Trapping and damage complaint records indicate active populations throughout the Chewaucan system. Trapping had been prohibited on Fremont N.F. lands by forest request since the 1977-78 season to allow beaver re-establishment to rehabilitate riparian areas. Trapping pressure prior to that time was relatively heavy with beaver taken most years. The only known active colony is at Bear Creek. ODFW has reopened trapping on the Fremont N.F. beginning with the 1998-99 season. Potential beaver habitat exists within the analysis area, where sufficient food, water and building sites are available to support additional colonies. These areas correspond primarily to areas of previous beaver activity. Habitat quality however has declined with the loss of deciduous vegetation mentioned earlier in this document. Alternative 1 would have relatively little impact on beaver populations within the analysis area. Population numbers may slowly increase if currently active colonies remain viable, reproduces, and offspring successfully disperse to potential habitat. Alternative 2, 3, and 5 present the opportunity to increase the quality of potential habitat by reducing conifer encroachment in riparian areas and stimulating deciduous growth. As habitat quality increases and beaver disperse into suitable sites, population numbers could show a corresponding increase up to a point of habitat saturation or successful colonization of all suitable sites. These additional colonies could then play a critical role in the establishment of new colonies in suitable habitat in adjacent drainages and by providing a seed source for recolonization through possible reintroduction or juvenile dispersal across the forest.

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ii. Neotropical Birds Neotropical migratory birds (NTMB) are those that breed in the U.S. and winter south of the border in Central and South America. Many passerine songbirds, hawks and owls fall into this category, as do many shorebirds commonly encountered. Nationwide declines in population trends for neotropical migrants have developed into an international concern. Efforts are now underway to examine population trends on wintering habitat in Central and South America as well as breeding habitat here in the United States. Neotropical migratory point count monitoring has taken place within the Chewaucan Watershed on Bear Creek and the Chewaucan River for eight years. Effects on neotropical birds from any of the action alternatives are variable. Species which prefer dense stand conditions, such as the hermit thrush and other ground nesting birds, will find better habitat conditions in Alternative 1, while those which prefer more open areas will find better habitat conditions in Alternatives 2-5. Alternative 5 generates the least effects to all species due to the mitigating effects of leaving untreated blocks of cover and unthinned clumps. Activities will reduce habitat for landbird species that are provided suitable habitat in mixed conifer forests with dense understories that are now present. These species invaded historic dry forest habitats which were formerly under a fire regime that controlled extensive understory development. Some examples of these species include Townsend’s warbler, red-breasted nuthatch, mountain chickadee, warbling vireo, American robin, spotted towhee, and Nashville warbler (Altman 2001). Reduction of shrubs associated with maintenance of the prescribed fire program and reduction of densities as proposed will negatively affect shrub and canopy nesting species. Some representative bird species that may be impacted from removal of shrubs, brush, and dense thickets are from those life forms occurring in mixed conifer, lodgepole and ponderosa pine forest types and that reproduce on the ground or in bushes and feed in those areas. Those species include dark eyed junco, MacGillivray’s warbler, chipping sparrow, green-tailed towhee, hermit and Swainson’s thrushes, dusky and Hammond’s flycatchers and some species of hummingbirds (Carey 2001). Mitigation designed to leave a mosaic of burned and unburned area (60% burned/40% unburned) will provide for a variety of habitats. Implementation of proposed activities during the courtship and nesting season (generally May 1 – July 15) for neotropical birds could impact nesting success resulting in some loss of that year’s cohort. Cumulative effects: Change on the Paisley Ranger District over the years including commercial harvest, fire suppression, wildfire, plant succession, and livestock grazing have likely changed neotropical bird species composition and abundance. Species that prefer dense conditions such as the hermit thrush and other ground nesting birds have likely increased, and species that prefer more open forests such as the white-headed woodpecker, chipping sparrow, and pygmy nuthatch have likely decreased. Livestock grazing over the years has increased brown cowbird populations resulting in nest parasitism of many neotropical migratory birds nests and a corresponding decrease in populations. It is likely that neotropical bird species diversity and abundance has decreased from historical levels. Activities that are expected to be implemented in the near future on the Paisley Ranger District including prescribed fire, understory thinning, and riparian improvements will likely increase species composition and abundance. Species that prefer more dense conditions may decrease, while species that prefer more open conditions may increase. Overall, the diversity in structure and

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ground vegetation as a result of these activities will likely increase species diversity immediately across the landscape. iii. Great Grey Owls Suitable habitat for great grey owls exists within the planning area in areas with mature, dense, primarily lodgepole pine stands adjacent to seasonally moist meadows. One sighting of a great gray owl has been documented within the planning area. No nest sites are known. Potential roost trees for this species may be lost with the proposed harvest and burning activities. However, proposed activities will increase foraging habitat providing adequate large woody debris is retained for prey habitat. Direct effects may occur if disturbance occurs during the breeding season to unknown nests. No other impacts associated with proposed activities are anticipated. Although some loss of potential nesting/roosting habitat will occur, no adverse effect on population numbers is expected. iv. Golden Eagles Suitable habitat exists within the planning area in more open conditons where cliffs or open-form ponderosa pine trees are present. All action alternatives are expected to improve conditons for golden ealges. Burning will improve foraging conditions and mechanical treatments are expected to improve potential nesting trees by allowing for open grown conditons. There may be direct effects if disturbance occurs during the breeding season to unknown nests. No other impacts associated with proposed activities are anticipated. This project will provide an opportunity to enhance foraging habitat and potentially increase population numbers. v. Osprey Suitable habitat for osprey exists within the planning area along the Chewaucan River. Osprey have been documented on several occasions along the Chewaucan River near Marster Campground and it is likely they could be nesting in that area. The only effects anticipated from the proposed activities would be the loss of potential nest snags through underburn activities. Direct effects may occur if disturbance occurs during the breeding season to unknown nests. No other impacts associated with proposed activities are anticipated. Although some loss of potential nesting/roosting habitat could occur, no adverse effects on population numbers is expected. vi. Prairie Falcon Suitable habitat for prairie falcons exists within the planning area where tall cliffs are adjacent to open habitat. The 17 cliff sites, and additional 5 sites adjacent to the planning area, that have been identifited as potential peregrine falcon habitat would also be potential prairie falcon habitat. Only sporadic surveys of potential sites have occurred. Prairie falcons have been documented on a few occasions in the planning area along with one nest. Habitat for prey species and foraging has improved where the removal of late and old seral (LOS) forest has increased the area of open, early seral forest cover types. Foraging habitat quantity and quality has declined where open, parklike LOS pine stands have been replaced by dense, multi-story LOS stands. Habitat quality has declined since the 1940s with increased disturbance from higher road densities, increased commercial logging activity, and greater recreational use. Proposed activities are expected to open up the overall conditon of the watershed, therefore improving foraging habitat. Direct effects may occur if disturbance occurs during the breeding season to unknown nests. No other impacts associated with proposed activities are anticipated. Activities will not cause cumulative impacts on prairie falcons or their habitats nor lead to a loss of viability.

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vii. Small Accipiters Suitable habitat exists within the planning area in areas of more dense woodlands. Two nests and one sighting of sharp-shinned hawks, and only one sighting of Cooper’s hawks have been documented within the planning area. Areas proposed for mechanical treatment would likely decrease nesting habitat for sharp-shinned and Cooper’s hawks with the more open conditions. The areas retained for cover under alternative 3 and 5 will maintain potential nesting habitat. Direct effects may occur if disturbance occurs during the breeding season to unknown nests. No other impacts associated with proposed activities are anticipated. Local populations may decline with alternative’s 2 and less so 3. Although some loss of potential nesting habitat could occur, no adverse effects on population numbers is expected. viii. Rocky Mountain Elk The Jakabe analysis area is within the herd range for the South Interstate and Winter Ridge elk herds. This herd ranges from the Sprague River Valley to the south to the Silver Lake lakebed to the north. No winter range or calving areas have been identified within the analysis area (C. Foster, 1994). However, elk sightings have occurred within the area during winter and within perennial drainages during the calving season. It is likely that portions of the area are used by elk for both wintering and calving. Current indications are that the elk populations within the planning area are stable to decreasing. Alternative 1 will have little affect on elk populations. The herd would continue to increase and expand it's area of use at the current rate. The action alternatives (2-3) however, are expected to create conditions highly favorable to elk primarily by increasing available forage. While the action alternatives may increase available elk forage, they would also have a negative impact on elk cover. ix. Cliffs, Caves, and Talus Slopes Cliff, cave and talus habitats are present throughout the planning area but primarily associated with perennial drainages. LRMP standards and guidelines require retention of 80% of the existing shade in these areas. All action alternatives will be designed to meet this requirement. Some loss of shade is expected. However, this loss of shade may stimulate shrub production which because of the rocky nature of the area will be less susceptible to burning or browsing. Shade loss to tree removal should be short term. A long term increase in shade from shrubby species is likely. x. Connectivity Between LOS Habitat The Regional Forester's Amendment #2 requires connectivity corridors designed to connect designated old growth areas and LOS habitat types across the landscape. Formal connectivity corridors have been mapped within the Jakabe analysis area. Adequate connectivity appears to exist within the planning area except where habitats are open and isolated clumps of LOS habitat exist. Retention or creation of adequate DWM and snags and prescriptions designed to maintain and/or enhance connectivity between LOS habitats over time within connectivity corridors will maintain those LOS habitats scheduled for entry.

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VI. Fuels Jakabe Fuels Specialist Report, March 3, 2005 Jakabe Restoration Project Analysis File Addresses: Issue 2. Juniper encroachment – Loss of wildlife, riparian and deciduous plant habitat;



Issue 4. Restoration of riparian habitat – reduced riparian habitat due to encroachment, road densities and locations, and loss of stable upland vegetation. Issue 5. Improve sustainability of late and old structure stands – LOS stands are diminishing because of increased stocking and a shift of species composition In the timbered portions of the Jakabe planning area, naturally occurring forest fuels have accumulated to an extent that they constitute a hazard outside the normal range of variability. This hazardous fuels buildup can be divided into two components: increased dead fuel loading and increased ladder fuels. Dead fuels consist of needles, twigs, limbs, and boles of fallen trees. Frequent, low-intensity fires (such as those recorded in the Jakabe area every 7—14 years) consume a portion of these fuels during each fire cycle, thus limiting their accumulation. Beginning in the 1870’s, intensive grazing removed much of the dry fall grass that formerly carried natural fires. By the early 20th Century, fires were being actively suppressed. Many stands have seen no fire over a time period equal to four to five natural fire cycles. The fire behavior effects of the resulting heavy fuel loading are longer flame lengths, higher intensities, and longer residence times, all of which contribute to increased mortality in overstory trees. Ladder fuels are defined as those providing “vertical continuity”; that is, an unbroken chain of flammable material from the surface of the ground to the crowns of trees. These ladder fuels make it easier for fires burning in surface fuels to make the transition to tree crowns, where they can torch—and kill—individual trees. When weather conditions are favorable and tree crowns are closely spaced, fire can spread from crown to crown and develop into a stand-replacement event. Ladder fuels are composed primarily of live fuels, brush (often needle-draped), and seedling and sapling-sized trees; but often include limbs and suspended boles of fallen trees. Frequent, low-intensity fires kill a large proportion of these younger trees and shrubs, limiting the development of ladder fuels over large areas of the landscape. Fire exclusion has removed this limiting factor, allowing understory trees and shrubs to sprout and grow through the equivalent of four to five natural fire cycles, producing ladder fuels over an extent of the landscape outside the normal range of variability. The Jakabe area is very dry in terms of both moisture regime and humidity. The existing canopy closure does not contribute greatly to increasing humidity and higher fuel moisture, and conversely, it does provide some snow interception that reduces potential fuel moisture. A more open canopy would not result in a noticeable change in humidity and fuel moisture. However, a more open canopy and understory reduction does contribute greatly to decreased fire behavior, lower flame heights, and greater ease of control or the option to manage as a monitor fire. While brush, grass, and seedling growth is expected to increase, none of these will begin to develop ladder fuels

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equivalent to those being removed. Maintenance burns would limit the development of future ladder fuels. Vegetative treatments in the Jakabe area are designed as a first step in reversing the trends associated with fire exclusion; to treat accumulated fuels with prescribed fire where it can be done safely, and to mechanically remove understory trees (ladder fuels) where this pre-treatment is necessary before prescribed fire can be safely applied. This analysis attempts to compare the various alternatives from the perspective of fire and fuels management. The forested areas within the Jakabe analysis area present a wide range of conditions, but for the purposes of this report, they will be divided into 4 types:

1. High-elevation, cold sites Primarily lodgepole pine/white fir above 6,000’. No fire treatment is prescribed for these stands, so they will not be discussed further. 2. Condition Class 1 Moderately stocked stand with light fuel loading; treated with prescribed fire within the past 5 years. The defining characteristic of Class 1 is that it presents a fuels profile that allows maintenance by fire. 3. Condition Class 2 Moderately stocked; probably treated or burned within the past 10-20 years The defining characteristic of Class 2 is that its fuels profile presents a hazard that can be safely and effectively treated with prescribed fire. 4. Condition Class 3 Overstocked/untreated ponderosa pine and pine-associated stands. The defining characteristic of Class 3 is that its fuels profile presents a hazard that cannot be safely and effectively treated with prescribed fire without pretreatment.

Fire exclusion has allowed a regime to develop under which stands move from Class 1 through Class 2 to Class 3 as natural fuels build up and seedling trees—often shade-tolerant/fire-intolerant species--grow into the understory. Reduced to simplest terms, the goal of fuels treatment in the Jakabe area is to:

o maintain stands in Condition Class 1 o treat stands in Class 2 moving them toward Class 1 and prevent their conversion to

Class 3, o modify stands in Class 3 toward Class 2 by mechanical treatment, at which point they

may be treated with prescribed fire. Fire behavior in the 3 condition classes may be predicted using the BEHAVE system, a standard tool for modeling Fire Behavior, after making a number of assumptions:

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o A “point source” fire, such as a lightning strike or a match. o A uniform, continuous fuel bed. o A free-running fire.

To differentiate fire behavior among the classes, different fuel models must be assigned. A typical ponderosa pine stand would usually be classified a Model 9, defined as: hardwood litter - closed stands of long-needled pine like ponderosa, Jeffrey and red pines. This model will be used for Condition Class 2. Stands in Condition Class 3 exhibit higher fuel loadings and much thicker understories, creating a fuels profile closest to a Model 10. This model is described as: timber (litter and understory) with greater quantities of 3-inch or larger limb wood resulting from overmaturity or natural events. Stands in Condition Class 1 have been burned recently enough that only a few years’ needle cast is present over the duff layer and fuels greater than ¼” diameter are light; a condition best represented by Model 8: closed timber litter; ground fires with low flame lengths, fire may encounter an occasional “jackpot” that may flare up, and a compact litter layer consisting mainly of needles, leaves, and occasional twigs. Environmental conditions used for comparisons are those of an “average worst day”:

Date/time Temperature Humidity Midflame Wind speed

1 hr fuel moisture

10 hr fuel moisture

100 hr fuel moisture

Live fuel moisture

Aug 10/1400 80 15% 5 mph 7% 8% 9% 90%

Elements of comparison shall be: Rate of Spread (ROS), Flame Length (FL), Scorch Height (Scorch), Size at Initial Attack (Size), Final Size, and Mortality (Mort). Mortality will be discussed in greater detail after comparisons. (BEHAVE runs producing the following outputs are attached.)

Element Class 1 Class 2 Class 3

ROS 2 ch/hr 8 ch/hr 9 ch/hr FL 1’ 2.8’ 5.2’* Size .1—1 acre 2.6—23.5 ac. 3.1—27.9 ac. Final Size 1 acre 5—41 ac. 6—74 ac. Scorch 1’ 8’ 29’ Mortality 6—16% 6—16% 56—81% Crown Scorch 0% 0% 68%

*Too intense for direct frontal attack w/handcrews; engines, dozers, aircraft may be effective. Comparison Rationale As shown by the chart, the differences between Conditions 2 and 3 are not in size or spread, but in intensity. Heavier fuel loadings create a fire too intense for direct attack, and much more damaging to the stand. Ranges of size are due to variability in elapsed time before initial attack (1 to 3 hours) and a reasonable range of attack level (from 2 engines to 4 engines plus a dozer arriving later).

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Final size may also be affected by other factors outside the scope of this comparison: accessibility, resource availability, other fires in response area, etc. If attack is delayed, final size increases dramatically. Scorch height is a direct output of stand type and temperature, but mortality is much more complex than the chart shows, and needs explanation. The BEHAVE system models a surface fire, and the mortality shown is that resulting from scorch of boles (varying by bark thickness) and crowns (varying by crown height). If this were a full representation of real fire behavior it would be a relatively simple matter to thin with fire: trees with thin bark and low crowns die; trees with thick bark and high crowns survive. The crowns of the smaller trees don’t just scorch, however. They torch, providing a short-lived but very intense heat source much closer to the crowns of the larger trees. This is the basis for the concept of “ladder fuels”. These ladder fuels produce much higher mortality in the overstory than the model predicts, and if crown closure is tight, provide the potential for crown-to-crown spread, which also is not predicted by the model. Mortality from an actual fire under the conditions above in a Condition Class 3 stand could approach 100%. Alternative 1 (No Action) This alternative would allow stands in Condition Class 3 to remain there and stands in Classes 2 and 1 to progress toward Class 3 conditions. Potential for catastrophic fire would increase over time as more acres achieved these conditions. A no-action alternative would allow the processes that created the current situation to continue. Mortality will continue in overstocked stands, fuel loadings will continue to increase, understory trees will continue to grow, and shade-tolerant seedlings will continue to generate, increasing vertical fuel continuity. Crown closure in plantations will continue, increasing horizontal fuel continuity. These trends will remain until interrupted by a disturbance, such as a stand-replacement wildfire. Alternative 2 This alternative would increase the acreage of stands in Condition Class 1 and 2 and reduce the acreage of stands in Condition Class 3. Potential for catastrophic fire would decrease over time as these changes occur. Alternative 3 Under this alternative most of the stands in Condition Class 1 would be maintained with prescribed fire, some stands in Condition Class 2 would be treated and some would not. Those Condition Class 2 stands not treated would progress toward Class 3 and most of those currently in Condition Class 3 would maintain that condition. Because there would be less progression toward lower fuel conditions classes and movement from class 2 to class 3, potential for catastrophic fire would increase slightly and gradually from its present level as compared to Alternative 2. Alternative 5 Under this alternative, stands in Class 1 would be maintained with prescribed fire. Stands in Class 2 would be treated with prescribed fire if not classified as “cover”. This would exclude more Class 2 stands from treatment than would Alternative 3. Those stands not treated would progress toward Class 3. Since almost all stands in Class 3 would be classified as “cover”, they would not be treated

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and remain in Class 3 conditions. Potential for catastrophic fire would increase over time as more acres achieve Class 3 conditions. VII. Roadless Areas The Brattain Butte Roadless Area is located within the Jakabe analysis area. This Semiprimitive Non-motorized Management Area consists of approximately 5,880 acres and lies along the eastern boundary. Aspen-lined draws, ponderosa pine stands, mountain mahogany patches, and juniper woodlands are interspersed among low sage ridges and scabrock flats. Fire suppression has led to encroachment of pine and juniper into the aspen stands and riparian draws. Juniper has also increased across the ridges over-taking ground stabilizing forbs and grasses. This situation has increased erosion resulting in higher sediment loads in the Chewaucan River, which lies to the west of the Brattain Butte Area. Portions of this area are included in the Jakabe Juniper/Aspen Meadow Projects Decision Memo (June 9, 2004) and the Jakabe Prescribed Burn Project Decision Memo (March 10, 2005). Approximately 1600 acres of the 9,039-acre Hanan Trail Roadless Area is within The Jakabe analysis area. This area consists of ponderosa pine, mixed conifer, and lodgepole pine stands along with aspen riparian areas, small meadows, and steep rock slopes. Past projects within the Hanan Trail Roadless Area include trail maintenance, and trail head improvements; clearing of down logs, installation of new outhouses at the trailheads, fence repair, and minor trail relocation. Past and continuing projects within the Brattain Butte Area are removal of juniper and conifer encroachment in riparian areas and aspen stands, placement of down junipers for bank stabilization, and prescribed burning. A recent Decision Memo based on the analysis work done for the Jakabe Restoration Project allowed the cutting of juniper and other encroaching conifers in the Brattain Butte area where necessary to carry fire. This activity will be followed by a prescribed burn designed to initiate the return of fire to the ecosystem. A moderate intensity fire would be used to create a 60%:40% mosaic of burned/unburned area (Decision Memo, Jakabe Juniper/Aspen/Meadow Projects, June 9, 2004; Paisley Ranger District). VIII. Other Unroaded Areas Unroaded areas are defined in the FEIS for the Roadless Area Conservation Final Rule as “any area, without the presence of a classified road, of a size and configuration sufficient to protect the inherent characteristics associated with its roadless condition. Unroaded areas do not overlap with inventoried roadless areas.” (USDA, 2000, FEIS Glossary, G-12) Unroaded areas have typically not been inventoried and are therefore separate from inventoried roadless areas (IRA). For the sake of clarity, the term “unroaded area” will be used in this section to differentiate these areas from IRAs. As stated, unroaded areas do not overlap with IRAs, which are considered in the previous section. During the 30 day public comment period on the proposed action contained in the review copy of the Jakabe Restoration Project EA, the Oregon Natural Resources Council (ONRC) submitted a map of unroaded areas they had identified in the project area (see Appendix A). Though void of system roads, these areas do contain evidence of past activities such as level 1 or 2 roads, skid trails, commercial logging, and landings. Some of these roads have been mapped and are in the analysis file. ONRC requested that uninventoried roadless areas greater than about 1,000 acres be protected from commercial logging and road building. The areas are named by ONRC on the map they submitted.

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There are no Forest-wide or Management Area standards specific to unroaded areas, although many of the resources that unroaded areas typically contain (i.e. wildlife, riparian resources and recreation opportunities) are specifically addressed by Forest Plan standards and guidelines or goals. The analysis area for the direct and indirect effects on the unroaded areas consists of the ONRC-mapped unroaded area within the Jakabe project area boundary. The analysis area for cumulative effects is the extent of these unroaded areas, both inside and outside of the project area boundary. These areas were not identified during the Roadless Area Review and Evaluation (RARE I), RARE II, or the EIS for the Roadless Area Conservation Final Rule as an eligible area of 5,000 or more acres in size. The analysis of effects on an unroaded area requires consideration of the activities that are proposed within it, weighed against the values or unique characteristics unroaded areas can provide or contribute to. Those values include:

• High quality or undisturbed soil, water, and air; • Sources of public drinking water; • Diversity of plant and animal communities; • Habitat for threatened, endangered, proposed, candidate, and sensitive species and for

those species dependent on large, undisturbed areas of land; • Primitive, semi-primitive non-motorized and semi-primitive motorized classes of dispersed

recreation; • Reference landscapes, including areas that are relatively at less risk from noxious weeds: • Natural appearing landscapes with high scenic quality; • Traditional cultural properties and sacred sites; • Other locally identified unique characteristics.

Effects of the proposed actions were determined using a qualitative discussion based on amount and type of proposed activities. Those activities that are included in all action alternatives that have the potential to have an effect on said unroaded areas include: commercial harvest, temporary road construction, road management, fuels treatments and prescribed fire. Other activities included in the action alternatives such as non-commercial juniper and small tree thinning, stream and water quality improvement would have minimal effect and are not considered further in this section. Information provided in the Vegetation, Hydrology, Fish and Wildlife, Fuels, Transportation, Recreation and Scenic, Soils, and Air Quality sections is also applicable to unroaded areas. Effects of Alternatives Alternative 1. The No Action alternative would not include any commercial harvest and associated road maintenance, temporary road construction, road decommissioning, fuels treatment, prescribed fire or other new activities associated with the action alternatives in the unroaded areas. There would be no direct effect on soil, water, air, sources of public drinking water, diversity of plant and animal communities, wildlife habitat, recreation opportunities, reference landscapes, noxious weed presence, natural appearance or scenic quality, or cultural resources. A potential indirect effect may occur because none of the road management activities that are included in the action alternatives would be implemented, leaving the areas in the conditions described earlier in Chapter 3. Only minimal ongoing road maintenance would occur, leaving many of the roads in poor condition. No

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action to decommission or close roads that are within the unroaded areas on the ONRC submitted map would occur. There would be no change in the preconceived roadless character of any of the areas. Common Effects of Alternatives 2, 3, and 5. High quality, or undisturbed soil, water, and air. Effects of the action alternatives on the potential for effects on these resources are discussed elsewhere in Chapter 3. Only those effects that differ or are specific to a particular unroaded area will be discussed here. The ONRC roadless areas generally do not contain classified roads shown on the district brownline transportation system maps. They do however, contain small segments of classified roads (levels 1 and 2) shown on the Forest GIS transportation layers. That does not mean these are wild areas devoid of transportation system features such as roads, skidtrails and landings. Nor does it mean these areas are pristine in the sense of either a lack of visible signs of human activities or they are in a “natural” or reference condition. These areas are generally very similar to the areas not included in the ONRC roadless designation except that they do not include upper level classified roads and/or roads which have received some level of ongoing road maintenance. Considerable past harvest activities have occurred within these areas. Visual review of the digital orthophotos show evidence of these past activities and associated roads/skidtrails. The vegetative condition has progressed through the same changes occurring as a result of fire suppression, harvest and time as the rest of the planning area. These areas are at the same risk of uncharacteristic fire and insect and disease activity as the rest of the area. Many of the timbered stands within these unroaded areas were previously logged through past timber sales. The table below shows past timber sales within identified unroaded areas.

ONRC mapped URA Past Harvest Sales

Temporary Road

construction BR 19 (Boulder Springs URA) Slide, Cub O' Coffee CO 55 (Elder Creek URA) Upper Coffeepot, Java, Caffeine 2400' BR 25 (Bear Creek URA) Hi Lo, Pup 0 CH 28 (Bear Creek URA) 0 BR 26 (Bear Creek URA) Pup 0 CO 6 & CH 104 (Parker Hills URA) Tine, Pad 2500' each CO 13 (Parker Hills URA) Pad 3000' CH 32 (Brattain Butte URA) 600' CH 37 (Meyers Canyon URA) 0 CH 43 (Buck Mtn URA) 0 CH 44 (Buck Mtn URA) 0 CH 45 (Buck Mtn URA) Fawn 1600' CH 46 (Doe Mtn URA) Cannonball, Buck-Doe helicoptor

Low standard temporary roads would be constructed to access several of the commercial harvest stands under the action alternatives. After harvest activities are completed the temporary roads would be rehabilitated. The construction of temporary roads would have a local, short-term impact on soil productivity as soil displacement and compaction would occur during the construction and use of these temporary roads. The BMPs for roads would be implemented, thereby mitigating potential sediment inputs to streams. The rehabilitation of temporary roads would include reshaping,

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subsoiling, and erosion control measures (such as J-hooks and waterbars) to promote recovery of soil conditions after they are used for harvest operations. Routine road maintenance on existing system roads, as a part of the timber sale, would improve existing drainage problems, moving water off of the roads and onto the land surface where runoff would have the opportunity to infiltrate into the soil. The specific design of the activities include resource protection measures (i.e. BMPs, RHCA buffers, Soil Productivity Guidelines, etc.), any project-generated sediment would be short-term in nature, and at an immeasurable, negligible level across the landscape. With the use of the protection measures, riparian and water quality goals and objectives described in the Forest Plan and other Regional plans and direction would be met. Although the vegetation treatments are expected to improve upland conditions, no significant increases in water yield or sedimentation are expected. See the Hydrology, Fish, and Soils sections of Chapter 3 for additional detail. Sources of public drinking water. The areas are not in a municipal watershed and there are no sources of public drinking water in any of the unroaded areas. Diversity of plant and animal communities. The unroaded areas identified range from ponderosa pine plant communities, to pine associated, to shrub-steppe communities. These are discussed in detail under Vegetation in Chapter 3 Habitat for threatened, endangered, proposed, candidate, and sensitive species and for those species dependent on large, undisturbed areas of land. Potential habitat for bald eagles, a federally listed threatened species, may occur within the project area. However, no direct, indirect, or cumulative impacts on bald eagles are anticipated. No other proposed, threatened, or endangered wildlife species are known to occur in these unroaded areas (Wildlife Species Specialist’s Report and Biological Evaluation, 2005). Potential effects to species on the Region 6 Sensitive Species list are discussed in the Forest Service Sensitive Wildlife Species section of Chapter 3. This project may have an effect on individual or habitat for gray flycatcher, Pacific fisher, and western sage grouse. In summary, the conclusion is that implementation of either action alternative will not cause a trend toward Federal listing or loss of viability for these species. Primitive, semi-primitive non-motorized and semi-primitive motorized classes of dispersed recreation. Other than the eastern portion of the identified Brattain Butte unroaded area, the unroaded areas are managed as roaded modified and roaded natural per Forest Plan direction. Non-motorized, dispersed recreation opportunities are available in undeveloped areas between and adjacent to existing roads in the project area. Implementation of the project would result in a short-term interruption in solitude as commercial logging, other thinning and underburn activities are occurring. In the long term, due to the decommissioning and closure of classified roads associated with each of the three-unroaded areas, the degree of “roadless character” may increase slightly on a local level. Reference landscapes, including areas that are relatively at less risk from noxious weeds. The forested and non-forested areas of most of the identified unroaded areas have been sufficiently altered, so that they no longer provide a reference landscape. While the most notable impacts are

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from road building, timber harvest and livestock grazing, other human influences have included fire suppression, firewood gathering, noxious weed treatment, and recreational activities. The potential risks of noxious weeds and other invasive non-native species within the unroaded areas would not differ from those described under the Noxious Weed section. A prevention strategy and resource protection measures that minimize the potential for spreading noxious weeds and other invasive non-native species are incorporated in the design of the action alternatives (see Chapter 2). Natural appearing landscapes with high scenic quality. Evidence of past management activities is present in each of the unroaded areas. Implementing the commercial harvest and other thinning activities would further decrease apparent naturalness while protecting the historic natural conditions. Implementation of thinning prescriptions would result in more open forested stands and allow increased sight distance and larger trees to develop. In the short term, the increased numbers of stumps and the open nature of the forested stands when viewed in the foreground would likely be the most apparent visual change resulting from implementation. Skidtrails and rehabilitated temporary roads would be noticeable in the short-term until vegetation becomes established. In the long term, due to their temporary use and subsequent obliteration, their return to natural appearance would be expected to proceed. Underburning would have the temporary visual effect of blackening some ground vegetation, scorching needles of low branches, or killing most small trees. Thinning and prescribed fire should result in long-term beneficial effects through improved vegetative health. This should be characterized by vigorous re-growth of forbs and grasses and sustainable large ponderosa pine trees in open stands. The resulting condition should more closely resemble a “natural” condition than do current conditions, which are partially the result of decades of fire suppression. Traditional cultural properties and sacred sites. There are no Traditional Cultural Properties in this area. Resource protection measures designed to protect all known or discovered cultural resources are included in all of the action alternatives (see Chapter 2). Therefore, there should be no short term or direct effects on any of the cultural resource sites that may occur within the unroaded areas. Other locally identified unique characteristics. There are no characteristics in the unroaded areas that would be considered unique relative to the rest of the Jakabe Restoration Project area and the Fremont-Winema National Forests. Cumulative Effects. On National Forest lands, vegetation management and road construction have occurred within all identified unroaded areas, though to a somewhat lesser extent than on many other areas within the Chewaucan subwatersheds. Harvest methods have included clearcuts, shelterwood cuttings, select tree removal, and overstory removals as the main management style. Precommercial thinning, reforestation, and animal damage control have also occurred. Looking at the direct effects of the action alternatives in the Jakabe Project, all activities within the unroaded areas would be the same with the exception of acres of commercial harvest proposed in each alternative. Alternatives 2 and 3 would result in about the same amount of commercial harvest activity in the unroaded areas. Alternative 5 would result in less commercial harvest. Apparent naturalness and solitude would be decreased in the short term by commercial harvest. Stumps would be visible in the foreground and the open nature of the forested stands would likely be the

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most apparent visual changes. Skidtrails and rehabilitated temporary roads would be noticeable in the short-term until vegetation becomes established again. In the long term, due to their temporary use and subsequent obliteration, their return to natural appearance would be expected to proceed. Underburning would have the temporary visual effect of blackening some ground vegetation, scorching needles of low branches, or killing most small trees. Other than timber harvest and road construction, the primary additional past activities that have occurred include livestock grazing within all areas for at least the past 100 years, fire suppression activity for approximately that same length of time, and dispersed recreation, including hunting. Continued grazing on National Forest lands may have minor long-term impacts on apparent naturalness, although effects would not be greater than past impacts. Future fire suppression would be expected to produce a long-term negative effect on the development of sustainable ecosystems. Fire suppression would have a short-term negative effect on solitude. Indirect effects associated with recreational use, including potential noxious weed spread, erosion, litter, off road vehicle use and evidence of fire rings, are expected to remain minor but could create localized long-term negative impacts on natural appearance. Cumulative effects of the alternatives, when considered with other past, present, and reasonably foreseeable future activities on the potential for spread of noxious weeds, are discussed elsewhere in Chapter 3. There are no specific cumulative effects relating to noxious weeds within unroaded areas, that differ from those described under the general Noxious Weed section. Effects of the alternatives on the potential for cumulative effects on soil, water, air, wildlife habitat for threatened, endangered, proposed, candidate, and sensitive species, sensitive plant species and dispersed recreation are discussed elsewhere in Chapter 3. There are no specific cumulative effects relating to these resources, within unroaded areas, that differ from those described under the appropriate sections found elsewhere within Chapter 3. In summary, of the action alternatives, Alternative 5 would have the least amount of negative short-term cumulative effects on natural appearance and solitude because it has the least amount of commercial harvest activity. All other activities would be the same with implementation of Alternative 2, 3, or Alternative 5. The road decommissioning and closures that are included in the action alternatives have the potential to have a long-term beneficial cumulative effect on natural appearance and solitude. Even under Alternative 1, the no action alternative, natural appearance and solitude have been affected by past activities such as road building, logging and grazing. It is unlikely these unroaded areas would be considered as potential wilderness due to their location in proximity to private industrial timberlands, the degree of existing development (classified roads), and past management activities.

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IX. Recreation and Scenic Values Jakabe Recreation Specialist Report, March 23, 2002 Jakabe Restoration Project Analysis File Recreation use in the Jakabe Planning Area is heaviest along Forest Road 33 as it follows the Chewaucan River south of Paisley. Fishing is the primary activity bringing both day visitors and campers to the area. Two developed campgrounds exist in this travel corridor: Marster Spring and Chewaucan Crossing, as well as “Forest Camps” at Jones Crossing and Upper Jones. Numerous dispersed campsites exist along the river and its tributaries, receiving moderate use throughout the warmer months and heavy use on holiday weekends. In contrast, mule deer hunting season, which normally runs for ten days around the first of October, disperses visitor activity over the entire planning area. During this time, dispersed camps may be found anywhere, not just along streams. The Fremont National Recreation Trail (NRT) passes through the Jakabe area from Moss Pass to the head of Bear Creek, crossing the Chewaucan River on the bridge at Chewaucan Crossing. Trail use is generally light, but organized equestrian groups and mountain bikers as well as hikers use it several times a year. Bird watching, small game and bird hunting, photography and sightseeing each bring their enthusiasts into the Jakabe area at certain times of year. Impacts on Recreation use by proposed management activities would range from minimal to moderate. Short-term increases in truck traffic on road 33 would create some noise disturbance and increased traffic hazards to campers along the River. Mechanical treatment would also present some noise intrusion into a normally quiet experience, and create changes in visual characteristics of treated areas that could be viewed negatively by some forest visitors. Logging activities might require the inconvenience of temporary road closures. Some proposed treatment areas are near or adjacent to the NRT trail; several more would be visible to trail users. Prescribed fire would also result in a short-term increase in vehicle traffic and possible intermittent road closures. The smoke produced could reduce visibility and present a nuisance in riverside campgrounds, particularly during night and early morning hours. Recreation use in the area is occasionally affected by wildfire. Effects have ranged from smoke intrusion, through disturbance by fire equipment, to precautionary evacuation of camps. A commonly voiced concern of forest visitors is that of a favorite recreation site being vulnerable to wildfire. Alternative 1 (No Action) This alternative would result in no increased disturbance to Recreationists, but would do nothing to abate the hazard of catastrophic fire. Alternative 2 This alternative would result in the highest level of short-term disturbance and potential visual impacts, but the greatest level of hazard reduction.

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Alternative 3 This alternative would result in a lower level of short-term disturbance and visual impacts and a lower level of hazard reduction. Alternative 5 This alternative would result in a lower level of short-term disturbance and visual impacts than any other treatment alternative and reduce the fire hazard only slightly. From the perspective of Recreation management, the threat of a catastrophic fire represents a much more serious problem than short-term disturbance by management activities. Adequate public notification, information boards, and public contact in the campgrounds can mitigate the negative impacts of these activities. Forest visitors have historically been supportive of prescribed fire, and given good information sharing, should continue to be so. Forest Service Road 33 is a Scenic Viewsheds (MA 6) within the project area. This travel route passes through many different landscapes, varying from intensively managed forest stands to dense old-growth forest and stream-fed meadows to sagebrush flats and distant rim rock bluffs. The road generally follows the Chewaucan River through the northern half of the project area until the river turns to the southeast. This area is managed to meet the Visual Quality Objectives of foreground retention- middleground partial retention (Forest Plan pages 153-158). Management within this area will be minimized through manipulation of the shape, scale, and distribution of treatments. When viewed as foreground or middleground, management treatments may not appear to completely borrow from naturally established form, line, color, or texture. Alterations may also be out of scale or contain detail that is inconsistent with natural occurrences. Only a few units are adjacent to the 33 road and prescriptions will minimize activities and follow the guidelines within the Forest Plan. Some level of activity will be noticeable, especially during implementation, but the long-term effects will be minimal. X. Cultural Resources Cultural Inventory Report, Jakabe Restoration Project Analysis File The archaeological record indicates that human occupation within the Jakabe project area probably extends back as far as 8000 years before present. These early aboriginal people focused their hunting and gathering activities around the Forest openings, along the streams and Chewaucan River and most noteworthy, in and around Coffeepot Flat. These same nomadic people probably wintered around the Great Chewaucan Marsh, situated in a lower desert setting some 10 miles to the east of the Jakabe area. The population of hunters-gathers in the region would have moved (transhumance) between the open areas of the Jakabe project setting and the Chewaucan Marsh to the east. The abundance of local obsidian, in the form of small nodules weathering out of nearby perlite deposits, was another major attraction of the Chewaucan watershed area. Previous on-the-ground surveys have been conducted in the proposed Jakabe project area. These surveys were conducted by a professional archaeologist or certified cultural resource technician. The on-the-ground strategy used the standards and guidance presented in the Fremont National Forest Inventory Plan.

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The proposed projects within the Jakabe Watershed Project area have the potential to be ground disturbing. Generally, the management strategy is to be light-on-the land as these various projects are being implemented. Therefore, site protection through avoidance and on-the-ground monitoring will be the tools used to address the stipulations of the PMOA (1995). Coordination is critical to the preservation and protection of these valuable cultural resources. Sale Administrators and Project Managers will need to work with the Forest Archaeologist and/or District Cultural Resource Technician. These projects will involve some ground disturbance. When projects are implemented, particular attention should be noted towards the possibility of cultural material coming out of any sub-surface excavation activities. In the event that previously undetected cultural resources are discovered during the course of the projects, work should be stopped while measures are developed which would allow for the mitigation of any adverse effects resulting from project implementation. If the above recommendations are followed, any of the action alternatives can be considered to be a no effect undertaking. Alternative 1 would have no effect on the cultural resources. XI. Transportation The IDTeam met July 27, 2000 to address road management with the Jakabe analysis area. Using the recommendations in the Chewaucan Watershed Analysis, the team identified roads affecting hydrologic functions with poor location. The team put together a map and list of potential roads to close and obliterate, and then posted this information at the Paisley Ranger District to solicit additional information. Using additional information received, the team put together the final proposal for road management in the Jakabe project. Road densities calculated by the engineering technician on the IDTeam identified the following information: 278 miles road (USFS Land) 114 miles road (Private Land) 392 total miles road in Chewaucan Watershed 20 mi. Open Road in Swamp Creek Subshed 20 mi. Open Road in Ben Young Creek Subshed 34 mi. Open Road in Coffeepot Creek Subshed 77 mi. Open Road in Chewaucan River Subshed 24 mi. Open Road in Bear Creek Subshed A total of 32 miles of roads were identified for closure in the Jakabe project area. Twenty-two of these miles were closed with the Jakabe Road Closure Decision Memo (June 21, 2004). An additional 10 miles are proposed for closure with all the action alternatives, and 22 miles of road would be obliterated. A complete list of affected roads is in AppendixC. Construction of temporary roads will be needed to accomplish treatments on identified units for each alternative. The following tables reflect the necessary temporary roads for a combination of tractor


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logging and cable logging options. However, at several sites in the Coffeepot Creek and Chewaucan River subwatersheds the temporary roads would be constructed only if cable logging is determined to be a feasible site-specific option. Access to an appropriate location for the cable system would be made possible by temporary roads. If the cable system was not used the unit would be logged with a helicopter system or not harvested at all. The second table shows the number of miles needed for each subwatershed and the total for the Jakabe planning area if cable systems were not feasible and the units were helicopter logged. Miles of temporary road by subwatershed and Alternative. Subwatershed Alternative 2 Alternative 3 Alternative 5

Chewaucan River 4.05 3.54 2.78 Bear Creek 0.72 0.51 0.44

Coffeepot Creek 3.90 3.84 3.30 Ben Young Creek 1.48 0.66 0.70

Swamp Creek 1.63 1.50 1.08 Total 11.78 10.06 8.30

Miles of temporary road if helicopter systems are used.

Subwatershed Alternative 2 Alternative 3 Alternative 5 Chewaucan River 2.50 2.21 2.21 Coffeepot Creek 2.48 2.42 2.13

Total 8.81 7.31 6.56 The total length of temporary roads shown in the tables is made up of several segments of temporary roads dispersed throughout the subwatersheds. The individual lengths of temporary roads vary from 200 feet (0.04 miles) to 6000 feet (1.14 miles). The average individual length of temporary road segments is 1728 feet, 1609 feet, and 1413 feet for Alternative 2, Alternative 3, and Alternative 5, respectively. Several units have temporary road segments that are greater than 2000 feet. Approximately 28%, 30%, and 26% of the units have temporary road segments that are greater than 2000 feet in length for Alternative 2, Alternative 3, and Alternative 5, respectively. Road building is a challenge in the hard ridgeline rhyolite and basalt lava geologic-soil units. Fortunately the principle Forest Roads have been installed. Current access to thin forest and treat fuel loads involve road maintenance, limited temporary road building, and road decommissioning. With the hard rock and soil rock, deep ripping to decommission roads is apt to daylight rocks. Scarification may cause less subsoil disturbance. And residual road compaction may be ameliorated with fibrous grass and shrub roots in forest openings. Effects of Alternative 1 (no action): There would be no temporary road construction under this alternative. There would be no additional erosion or sedimentation associated with temporary road building. Effects common to all action alternatives: Direct road erosion effects from system roads or temporary roads are small relative to crown or ground fire erosion effects. Unlike rainy western Oregon, road sediment is small. Local erosion was estimated using Water Erosion Prediction Project (WEPP) technology (WEPP 2001). The WEPP


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Fuel Management Erosion analysis facilitates the comparison of sediment from wildfires, prescribed fires, and roads. In the semiarid eastside environs, road sediments vary from 0.4 to 2.6 tons per square mile per year. It is a small value relative a sediment load in the inevitable wildfires from 86.1 tons per square mile per year or more historic ground fire of 6.6 tons per square mile per year. This WEPP estimate used climate station data at Hart Mountain and Mount Shasta and local soil survey information. Alternative 2 (proposed action): There would be approximately 12 miles of temporary road construction and 9 miles of temporary road construction if cable-logging systems were not used. Thirty-four percent of the temporary roads would be built in the Chewaucan River subwatershed and 33% would be constructed in the Coffeepot Creek subwatershed. Alternative 3: There would be approximately 10 miles of temporary road construction and 7 miles of temporary road construction if cable-logging systems were not used. Thirty-five percent of the temporary roads would be built in the Chewaucan River subwatershed and 38% would be constructed in the Coffeepot Creek subwatershed. Alternative 5: There would be approximately 8 miles of temporary road construction and 7 miles of temporary road construction if cable-logging systems were not used at two sites. Thirty-three percent of the temporary roads would be built in the Chewaucan River subwatershed and 40% would be constructed in the Coffeepot Creek subwatershed. XII. Air Quality Existing Conditions/Affected Environment Air Quality Regulatory Framework The Clean Air Act. The basic framework for controlling air pollutants in the United States is the 1970 Clean Air Act (CAA), as amended in 1990 and 1999 (42 U.S.C. § 7401 et seq.). The CAA was designed to protect and enhance the quality of the nations air resources. The CAA encourages reasonable federal, state and local government actions for pollution prevention. State Implementation Plans (SIPs) are developed to implement the provisions of the Clean Air Act. The State of Oregon Clean Air Act Implementation Plan (OAR 340-200-0040) has been developed. National Ambient Air Quality Standards. The EPA has established NAAQS for six criteria pollutants that have been determined to be harmful to the public and environment the following table lists the six NAAQS. Oregon has adopted most of these standards to form the Oregon Ambient Air Quality Standards (DEQ Ambient Air).


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Table 3-18. EPA National Air Quality Standards for Criteria Pollutants Pollutant Time Period Average Federal Oregon

Carbon Monoxide (CO) One-hour 8-Hour

35 ppm* 9 ppm*

35 ppm* 9 ppm*

Lead (Pb) Calendar Quarter (90 days)

1.5 µg/m3 1.5 µg/m3

Nitrogen Dioxide (NO2) Annual Arithmetic Mean 0.053 ppm* 0.053 ppm* Sulfur Dioxide (SO2) Annual Arithmetic Mean

24-Hour 3-Hour

0.03 ppm* 0.14 ppm* -----------

**0.02 ppm* **0.10 ppm* **0.50 ppm*

Ozone 8-Hour Hourly Average

0.08 ppm* 0.12 ppm*

---------- 0.12 ppm*

PM10 Annual Arithmetic Mean 24-Hour Average

50 µg/m3 150 µg/m3

50 µg/m3 150 µg/m3

PM2.5 Annual Arithmetic Mean 24-Hour Average

15 µg/m3 65 µg/m3

15 µg/m3 65 µg/m3

* ppm = parts per million µg/m3 = micrograms per cubic meter ** denotes more stringent standards than federal Prevention of Significant Deterioration. “The Prevention of Significant Deterioration (PSD) provisions of the Clean Air Act require measures “to preserve, protect, and enhance the air quality in national parks, national wilderness areas, national monuments, national seashores, and other areas of special national or regional natural, recreation, scenic, or historic value.” Stringent requirements are therefore established for areas designated as “Class I” areas (42 U.S.C. § 7475 (d)(2)(B)). Designation as a Class I area allows only very small increments of new pollution above already existing air pollution levels.” The Class I airshed of the Gearhart Wilderness is approximately 9 miles west of the Jakabe analysis area. Visibility Protection. The Clean Air Act establishes as a national goal, “the prevention of any future, and the remedying of any existing impairment of, visibility in mandatory Class I Federal areas which impairment results from manmade air pollution” (42 U.S.C. § 7491 et seq.). Visibility impairment is a basic indicator of air pollution. The EPA has determined that regional variation in visibility needs to be addressed. As a result, the EPA promulgated Regional Haze Regulations for Protection of Visibility in National Parks and Wilderness Areas in 1997. These regulations are intended to improve visibility, or visual air quality, in more than 150 Class I Areas across the country. Non-Attainment Areas. If a community does not meet or “attain” the NAAQS, the EPA designates it as a non-attainment area. The state must then demonstrate to the public and EPA how that area will meet the ambient air quality standards in the future based upon controlling emission sources, through a control plan that is part of the SIP. The emissions from prescribed fire may be considered as part of the demonstration. The nearest PM-10 non-attainment area is Lakeview, Oregon (DEQ Air Quality), which is approximately 24 miles south of the southern-most boundary of the Jakabe analysis area.


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Conformity. The general conformity provisions of the CAA (Section 176(c)), prohibit federal agencies from taking any action within a non-attainment area that causes or contributes to a new violation of the standards, increases the frequency or severity of an existing violation, or delays the timely attainment of a standard as defined in the area plan. Federal agencies are required to ensure their actions conform to applicable State Implementation Plans. The Jakabe Restoration Project is not subject to the conformity process since it does not occur within a non-attainment area boundary. Policies and Programs Interim Air Quality Policy on Wildland and Prescribed Fires. The “Interim Air Quality Policy on Wildland and Prescribed Fires” (EPA 1998) addresses public health and welfare impacts caused by wildland fires managed to meet resource objectives and prescribed fires. This policy complements the Natural Events Policy, which addresses public health impacts caused by wildland fires. The Interim Air Quality Policy urges states and tribal managers to collaborate with wildland owners and managers to mitigate the air quality impacts that could be caused by the increase of prescribed fires and wildland fires managed to meet resource objectives. The Interim Policy “urges wildland owners/managers to: (1) notify air quality managers of plans to significantly increase their future use of fire for resource management, (2) consider the air quality impacts of fires and take appropriate steps to mitigate those impacts, (3) consider appropriate alternative treatments, (4) and participate in the development and implementation of State and Tribal Smoke Management Plans”. The Jakabe Restoration Project meets the intent of the Interim Policy through the NEPA analysis process and the practices of the Forest Plan. Smoke Management Programs. Managing smoke from prescribed burning across agency lands is tracked and monitored by the USDA Forest Service and USDI Bureau of Land Management, Regional Air and Smoke Program located in Portland Oregon. The Interagency Monitoring of Protected Visual Environments (IMPROVE) program is one of the ways smoke is monitored across both Washington and Oregon through the use of fifteen receptor sites. The objectives of the Program are to:

1. Establish current visibility and aerosol conditions in mandatory Class I areas, 2. Identify chemical species and emission sources responsible for existing human-made

visibility impairment, 3. Document long-term trends for assessing progress towards the national visibility goals, 4. Provide regional haze monitoring representing all visibility-protected Federal Class I areas

where practical. The Oregon Airshed Group operates under the guidelines of the SIP. The intent of the SIP “is to minimize or prevent smoke impacts to communities while using fire to accomplish land and resource management objectives.” The SIP identifies the responsibilities of air regulatory agencies, and federal, tribal, state, and private land managers. The SIP provides accurate and reliable guidance and direction to the individuals doing the burning. This program is designed to meet the state’s regulatory needs as well as the Interim Policy mentioned above. Members of the Oregon Airshed Group report planned burns to the smoke Monitoring Unit in Salem. Burns are reported by “airshed” (geographical areas identified by the Airshed Group with similar topography and weather patterns) and “impact zones” (communities identified by the Airshed Group susceptible to smoke intrusions). The smoke Monitoring Unit meteorologist/program coordinator evaluates proposed burns, existing air quality, and forecasted weather conditions including atmospheric stability and transport winds.


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This information is used to issue daily burn restrictions for members of the Airshed Group. Burn restrictions are issued primarily from spring through fall. Oregon Department of Environmental Quality (DEQ) monitors planned prescribed burns and issues advisories when air dispersion is poor. Sources of Particulate Matter. Private debris burning, agricultural burning, and wood burning stoves all contribute smoke to nearby communities. There are no known large stationary point sources of air pollutants in the area. On the Fremont-Winema National Forests, prescribed burning is accomplished during spring and early summer when dilution, dispersal, and mixing conditions are generally good to excellent; and late summer and early fall when conditions may be more restrictive. Spring burning often uses existing snow packs as “check lines” to help limit fire spread thus facilitating controlled burning. Prescribed burning in the spring usually produces less particulate matter as fuel moistures are higher hence less smoldering combustion of fuels plus optimal atmospheric dispersion conditions are fairly prominent. Early fall burning conditions may include high fire danger, adverse weather, and fuel loading which limit controlled burning. Late fall often has weather patterns and cool nights with more frequent atmospheric inversion conditions which limit burning opportunities. Regardless of the season, atmospheric conditions are key factors in the decision making process as to whether or not conditions are favorable for burning. Effects of Alternatives Smoke sensitive areas near the Jakabe planning area include the Class I airshed of Gearhart Wilderness, the communities of Summer Lake and Valley Falls, and the city of Paisley. Smoke management is defined as: The management of fuel treatments from forest activities so that there is no or reduced effect to local areas surrounding the project. This primarily deals with impacts to people or air quality. The effects of smoke management from activity created fuels on the surrounding area are described below and the procedures and guidelines followed when utilizing prescribed fire as a management tool. All Forest Wide Standards and Guidelines for air quality (Forest Plan pg. 102) will be followed to minimize potential of burning activities to affect air quality in local communities. The Fremont National Forest complies with all applicable air quality laws and regulations, and coordinates with appropriate air quality regulating agencies. Currently, and in the future, all planned ignitions are and will be conducted according to the Operational Guidance for the Oregon Smoke Management Program (OSMP). The Operational Guidance contains the direction for meeting the terms of the OSMP. The Environmental Protection Agency has approved the OSMP as meeting the requirements of the Clean Air Act, as amended. The OSMP, which is administered by the Oregon State Forester, regulates the amount of forestry related burning that can be done at any one time. The amount of burning that can occur on any one day depends upon the specific type of burning, the tons of material to be burned, and the atmospheric conditions available to promote mixing and transportation of smoke away from sensitive areas. For each activity requiring prescribed fire, the Forest Service requires a written, site-specific prescribed burning plan approved by Forest Service management. The purpose of the plan is to ensure that resource management objectives are clearly defined and that the site, environment, or human health is not harmed. The plan contains a risk assessment to quantify the chance of fire


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escaping and develops a contingency plan for actions taken to prevent escape and if it does, quickly contain the escape. The plan would be implemented to minimize the possibility of the burn affecting Class I or other "smoke sensitive" areas in accordance with the OSMP. Air quality would potentially be affected by prescribed burning (underburning and pile burning) or from wildfire, or dust from equipment operation and road use. The principle effect, whether by prescribed fire or wildfire, relates to temporary visibility impairments and the potential effects on human health. Emissions from smoke or dust would result in release of pollutants into the atmosphere, possibly affecting the health of forest workers and residents/recreationists in the vicinity of the on-going project. The critical pollutants thought to affect human health include particulate matter, emitted in smoke or dust, which is equal to or smaller than 10 microns in size (PM10). Alternative 1. No treatment or activities are prescribed by this alternative. In the absence of fuel reduction treatments, the area is highly susceptible to a stand replacement fire. In the event of a wildfire, depending on fire size and intensity, air quality could be impaired for a three to four week period. The extent of effects on visibility and human health would likely be greater than effects from prescribed fire operations, which would be managed to minimize effects to air quality. Alternatives 2 and 3. In compliance with the Clean Air Act, the Forest Service is operating under the State of Oregon Administrative Rule OAR 629-43-043. The Forest Service is complying and would continue to comply with the requirements of the OSMP, which is administered by the Oregon Department of Forestry. The general public could obtain information about any proposed burns in the immediate area from local Ranger Districts, advertisements in local newspapers, radio, or television, and avoid areas being approved by the EPA. Table 3-19 shows the estimated amounts of particulate matter (PM) that would be created by the smoke from the prescribed burning contained in the alternatives. The acres of burning in the table are for the treatment of activity fuels and natural fuels. The particulate matter that is quantified in the table includes PM 10 and PM 2.5. Smoke is made up of suspended particulate matter and gases. Particulate matter is made up of soot, tars, condensed organic substances, and water droplets. Particulate matter less than 10 microns (PM10) is respirable into human lungs and considered a health hazard. Actual health effects depend on exposure time and concentration of smoke or dust. Data on human exposure to smoke from forestry burning is very limited. Table 3-19.—Estimate of Potential Volume of PM Created by Alternative Treatments

Prescribed Fire Treatment Alt. 2 & 3 Tons PM Alt.5 Tons PM Burn Hand Piles 0 acres 0 acres

Burn Landing Piles 1300 piles 4330 820 piles 2731 Underburning 2000 acres 205 1100 acres 113

The values in the table above are only estimates. The actual amount of particulate matter released is dependent on many variables (weather, fuel moisture, firing method, etc.). Burning would only be conducted when actual and predicted atmospheric conditions would minimize the possibility of smoke affecting the local communities and the Class I airshed of Gearhart Wilderness. All prescribed fire activities would be implemented in full compliance with Oregon DEQ programs through cooperation with the Oregon SIP. The project would meet the Forest Plan air quality standards, and management direction to “maintain existing air quality.” The Forest


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participates in the Oregon Smoke Management Program to meet National and State air quality standards for PM 10 and PM 2.5. The project would meet all criteria to protect air quality and would not result in any long-term effects to air quality. Daily particulate matter standards would be met by following the Oregon State Implementation Plan. That is, National Ambient Air Quality Standards for PM 10 and PM 2.5 would be met with all action alternatives. (The NAAQS standards are a complex mixture of concentration limits for air pollutants when measured over specified time limits.) Smoke from prescribed burning may result in short-term impacts on recreation and transportation in and near the project area. The size, location and type of prescribed burn and weather conditions (e.g., temperature, wind, atmospheric stability and mixing, and fuel moisture) determine how much and in what direction smoke travels. Dust and vehicle emissions could temporarily reduce air quality in the immediate vicinity of equipment operations. All alternatives involving commercial removal would require the application of dust abatement to roads used for haul. Impacts from dust and vehicle emissions would be short-term and temporary in nature. Cumulative Effects. Although the Fremont-Winema National Forests tries to conduct prescribed burning during periods of good or better smoke dispersion, there may still be some cumulative smoke impacts from concurrent private and forestry burning common to Alternatives 2, 3, and 5. It is assumed that all burning would likely occur over a brief period of time while conditions are appropriate, and smoke monitoring will be implemented, thereby reducing the potential cumulative effects. Other prescribed burns designated in the area are the Jakabe Prescribed Burn Project and the Headwaters Fuels Project. These will also contribute smoke effects over time, but not at the same time as any burning in the Jakabe Restoration Project. Public Safety Warning signs would be posted as required by the timber sale contract in commercial harvest activity areas. Public safety issues, including the need to abate dust on roads open to the public, would be addressed with contractors during contract prework sessions. A site-specific burn plan would be prepared prior to implementing prescribed fire. The plan would ensure that resource management objectives are clearly defined, and that site environment and human health are not harmed. The plan would contain a risk assessment and actions to prevent escape, and a contingency plan for actions to quickly contain an escaped fire. Warning signs would be posted during prescribed fire activities to provide for public safety in the project area. Information on prescribed fire activities would be provided to the public through Forest news releases, advertisements in local newspapers and radio or television announcements. There would be no significant effects to public health or safety as a result of implementing any of the alternatives of the Jakabe Restoration Project analysis. XIII. Irreversible and Irretrievable Effects The term "irreversible commitment of resources" describes the loss of future options. It relates primarily to nonrenewable resources, such as minerals or cultural resources, or to factors such as soil productivity that are renewable only over very long periods of time. For all alternatives there are no irreversible commitments of resources. The term irretrievable applies to the loss of production, harvest, or use of natural resources because of management decisions. Under active management, irretrievable resource commitments are


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unavoidable, because managing resources for any given purpose necessarily precludes the opportunity to use those resources for other purposes. The analysis revealed no significant irreversible or irretrievable commitment of resources associated with implementing the alternatives that are not already identified in the Forest Plan FEIS. XIV. Prime Farmland, Rangeland, and Forestland Adverse effects on prime farmland, rangeland, and forestland not already identified in the Forest Plan FEIS are not expected from implementing the alternatives. There are no prime farmlands within the project area. XV. Floodplains and Wetlands The proposed alternatives would have no impact on floodplains or wetlands as described in Executive Orders 11988 and 11990. XVI. Environmental Justice With the implementation of any of the alternatives, there would be no disproportionately high adverse human health or environmental effects on minority or low-income populations. The actions would occur in a remote area and nearby communities would mainly be affected by economic impacts as related to timber harvest or contractors implementing thinning and reforestation activities. XVII. Consumers, Civil Rights, Minority Groups, and Women The proposed alternatives would not adversely affect consumers, civil rights, minority groups, or women. Timber sale and other contract provisions include non-discrimination requirements. The proposed alternatives would not have a disproportionately high or adverse human health affect on any identifiable low-income or minority population.

Documents

III Chapter 3 – Affected Environment and Environmental ...a123.g.akamai.net/7/123/11558/abc123/forestservic...Overlap in soil and vegetation geography is summarized in complementary