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1.0 Introduction
The Green Revolution has resulted into a surplus production of grains world over
including India (1, 2). This revolution in agriculture, on the contrary has revealed various
other issues to address like the soil deterioration, fertilizers and pest control
management and crop residue management. Crop residue management is of utmost
relevance because of the impact on soil organic matter (SOM), local and regional air
pollution and essential contribution to global Warming phenomenon. The main
contributors to the global crop residue generation are Wheat, rice, maize, barley, millet
and sorghum (3), of these rice and wheat are the main crops grown in Asian countries
and approximately 748 million tons (MT) residue from rice (623 MT from rice straw and
125 MT from rice husks) (4) and approximately 228 MT wheat residues are generated
each year. Generally, most of the wheat crop residue is used as feed for livestock; only
7%-25% of wheat residue is reported to be burnt in the field (5). However, in case of rice
straw because of its higher silica content, reduction in milk yield of cattle (6), massive
residue generation (1.37 tons per ton grain production) (7), early seedbed formation for
next crop and combined harvesting technology lead to no other alternative for the rice
crop residue than to be burnt in the field or at the most left in the field for microbial
degradation (3). Thus, open crop residue burning (CRB) is a very common practice which
leads to the release of various air pollutants including nonmethane hydrocarbon
compounds (NMHCs) and particulate matter (PM2.5 and PM10) consisting primarily of ash,
polycyclic aromatic hydrocarbons (PAH), and soot (organic carbon & black carbon) in the
atmosphere (8), and also lead to loss of soil fertility by changes in soil C\N ratio, nutrient
loss and killing of friendly pests and bacteria (9). Black carbon (BC) and organic carbon
(OC) emissions lead to weakening of the radiative-convective coupling of the atmosphere
and decrease global mean evaporation and rainfall and are also considered as the most
important cause of the formation of Asian Brown Clouds (ABCs) (10).
These detrimental effects of CRB lead to shift towards a crop residue management (CRM)
system for attaining the sustainability in Agriculture. Although, CRM has received less
space in R&D community but its probable contribution to soil fertility, soil organic matter,
soil structure and soil health will lead towards sustainable agriculture with substantial
carbon sequestration (11). Several alternatives have been suggested for CRM
categorized under physical methods, chemical methods, biochemical and
thermochemical conversion processes which include combustion, gasification and
pyrolysis (12, 13). Thermo-chemical technologies have significant role in CRM and are
preferably promoted over other technologies because these technologies also lead to
carbon sequestration and the by-products can be used as a fuel source having higher
calorific value and cleaner fuel in comparison to fossil fuel (14).
Some recent thermo-chemical technological advancement in crop residue management
is the utilization of crop residue for bio-ethanol (15), bio-oil, syn-gas and bio-char
1
production (16). Bio-oil production from the crop residue is recently getting more
recognition because of rising prices of fossil fuels and their pollution issues and also
because bio-oil has a potential to be used as a fuel directly (17). Thus, it is considered as
one of the most reliable technology for crop residue management. The bio-oil production
technology is based on the pyrolysis of the lignocellulosic crop residue in absence of
oxygen in a closed pyrolytic chamber. The pyrolysis conditions have a major role in
determining the yield of the bio-oil. In the pyrolysis of crop residue, along with bio-oil,
syn-gas and some solid Carbon-rich charred material are also produced (17). Bio-gas can
be used as an energy source because of its higher calorific value and less polluting
property (18).
Biochar can be defined as a carbon-rich crystalline graphene structured product obtained
by thermally decomposing the biomass such as wood, manure, leaves or crop residue in
closed pyrolysis chamber at a temperature < 700 0C, in absence of air (14). Biochar is
used as a potential adsorbent material for wastewater, for C sequestration, as energy
source and as a potential soil ameliorating agent in agriculture as it has a good capacity
to improve the soil’s physical, chemical and biological properties. The bio-char has
carbon-negative effect and so it can hold a massive amount of CO2 in the form of soil-C
for centennials to millennial (14, 19).
Like crop residue management, fly ash management has been drawing attention of the
policy makers for a long time because of its massive production from combustion of coal
in various Thermal Power Plants (TPPs) for electricity generation. The combustion of coal
produces a sufficient amount of energy along with various coal combustion by-products
(CCPs) or coal combustion residues (CCRs) like fly ash, bottom ash and boiler slag,
fluidized bed combustion ash and other solid fine particles (20, 21). The major fly ash
generating countries are U.S., Russia, China and India with a fly ash generation potential
of these countries contributing about 750 MT/yr (22). The fly ash utilization potential of
fly ash is greater in developed countries as compared to developing one. U.S., Europe,
and Japan have fly ash utilization potential of 39%, 47% and 82% [23] respectively,
whereas rest countries fly ash utilization potential averaged around 25% (24).
As estimated by MoEF (2007), fly ash production in India was 112 MT in year 2005-06
and was expected to increase upto 170 MT/yr and 273 MT/yr till the end of 2012 and
2020, respectively (25). Usually fly ash is utilized in cement and concrete industries,
brick formation, road making, landfill and as value added materials like adhesives,
adsorbent, wood substitutes, zeolite and importantly in soil amelioration (21). Fly ash
management through its utilization for ameliorating cultivable as well as non-cultivable
soil is applied for a long time because of the potential of fly ash to provide the major
macro and micro nutrients to the plants and related microbial communities (24, 26). Fly
ash has the capacity to decrease soil aggregation capacity, increase water holding
capacity, moisture content, porosity, electrical conductivity, etc. India has around 175
2
Mha non-cultivable land area because of water logging, higher sand proportion, salinity,
acidic nature and alkalinity which have a greater scope for utilization of fly ash (21, 24,
26, 27). Likewise fly ash, biochar also improves soil properties by increasing CEC,
improving pH, increasing porosity and permeability, decreasing soil bulk density,
increasing surface area, water holding capacity (28), and also increasing microbial
activities by providing them a source soil-C, soil-N and soil-P (Earthworm, Mycorrhizal and
bacterial activities) after its incorporation into the soil (29, 30).However, high toxic metal
content of the fly ash are one of the major constrain in its utilization as a soil amendment
agent, but the toxicity varies with soil types (21, 24, 26, 27).
A few studies have reported that the use of zeolites like alumina has increased the bio-oil
production from the crop residue (31, 32). Fly ash has a natural zeolytic properties (33,
34), thus it can be used along with crop residue to produce bio-oil and the solid remains
of this process i.e., biochar mixed fly ash can be used as for soil amendment. Also,
biochar is reported to decrease the leaching properties of various metals in soil (19), thus
it might be beneficial to use this combination of fly ash and biochar which might give an
overall synergistic positive effect to soil.
2.0 Review of Literature
2.1 Biochar from Crop Residues
All carbon-rich residues derived from fossil fuels and biomass by fire or heat are
considered as black carbon which includes solid combustion residues as well as
condensation products like char, charcoal, biochar, soot, graphite black C and graphite
(35). The exact chemical nature of a biochar produce depends upon the type of biomass
used and pyrolysis condition (14). Various studies from different parts of the world
accounts the biochar formation from different crop residues like from olive kernels (36);
straws of canola, corn, soybean and peanut (37); rice straw and rice husk (38), wheat
straw (39), rape and sunflowers residues (40); and also from residues of sugarcane,
sorghum, millet, coconut, oil palm, coffee, cocoa, maize, etc. (41). Also, earlier reports
suggested the formation of biochar from poultry litter (42) wood, municipal biowastes
(43), yard wastes, etc. which are in practice for a long time for soil amendment (14).
Various studies have reported that the yield of biochar production from crop residue is
twice to that of the wood (44).
2.1.1 Physiochemical Characteristics of Crop Residue Biochar
2.1.1.1 General Biochar Properties
The biochar characteristics are very much variable and they depend mainly upon the
biomass source and operating pyrolysis conditions like highest treatment heat (HTT),
3
pressure, reaction residence time, vapour residence time, moisture content of biomass
source, reaction vessel, pre-treatment, flow rate of gas /air and post treatment. Biochar
has large surface area, high pore space (micropores, mesopores and macropores) and
permeability, lower bulk density and high water holding capacity (WHC) (28).
Temperature has a very important role in determining the characteristics and application
of biochar (Table 1) as biochar prepared at low temperature can be used for controlling
release of nutrients from fertilizers (45) and high temperature leads to the formation of
activated carbon like material (46). Chemically, biochar is a highly aromatic compound
that contains random stacks of graphitic layers (35) i.e., has high carbon content
followed by oxygen, hydrogen and nitrogen and has higher C\N, C\H, C\O ratios and
lesser volatile matter content than the parent material (47). Biochar is highly stable,
resistant to various erosion, having high cation exchange capacity (CEC) and a variable
range of pH (depends upon biomass source and heating temperature) (14). High cation
exchange capacity (CEC) of biochar is due to the presence of various functional groups
like pyranone, phenolic, carboxylic, lactone and amine (48). Several workers regard
biochar as a rich source of nitrogen alongwith carbon, which can be used to further
improve soil nutrient status (49). Because of its higher adsorption capacity in comparison
to soil, biochar is regarded as a better soil phosphorus retaining material (35). Further,
biochar favors microbial soil communities like N2-fixing bacteria (50), arbuscular
mycorrhizal (AM) fungi (51) and several other organisms like earthworms (29), by
providing them space and nutrients and protect them from predation and desiccation
(30, 52, 53).
2.1.2 Crop Residue Biochar Properties – A Comparative Statement
Various physicochemical properties of biochar produce from various crop residue sources
are summarized in Table-1. The effect of pyrolysis temperature can easily be generalized
from the data given in Table-1, as the rise in pyrolysis temperature leads to decrease in
nitrogen and oxygen content, increase in carbon, phosphorus, ash content and pH (37,
54) is reported. Surface area of biochar also increases with increase in pyrolysis
temperature; however it is 100 times substantially less than the surface area of activated
charcoal. Porosity of the biochar increases with increase in pyrolysis temperature
because of the loss of volatile matter, thus, in turn leading to decrease in bulk density.
2.1.3 Life cycle analysis of biochar
Biochar has been found as a very stable and resistive element in soil and so it has very
long life (thousand to millions of years) in soil, because the recalcitrance of biochar
depends upon biomass source, pyrolysis condition, soil properties and climate (55). Terra
Preta soil or Amazonian Dark Earths (ADE), regarded as a type of biochar, is considered
as an example for describing the longevity of biochar in soil (56). Various lab-scale
4
studies has predicted that biochar has a mean residence time of 1300-4000 years in soil
(57). Its degradation and mineralization is very slow and because of this property, it is
considered as a good method for mitigating Climate change by locking a huge amount of
atmospheric CO2 (15). Also, various studies suggested that a fraction of C (present as
mineral carbonates and organic molecules) from biochar, called labile carbon content, is
mineralized abiotically and biotically to CO2 within a short period of time (14). Rumpel et.
al., (2006) (58) reported that biochar amended soil in a steeply sloped area was more
prone to water erosion than the other soil organic matter because of its low density, less
mineral interactions and lesser biodegradability.
2.1.4 Biochar as a soil amendment agent: for Sustainable Agriculture
Enhanced mineralization of soil organic matter and depletion of soil nutrients are
currently considered as the two important limitations for the sustainable agriculture.
Biochar having high adsorption capacity and nutrient retention capacity as well more
stable nutrient source is considered as an effective soil amendment than compost and
organic manure (59). The amount of biochar incorporation in soil requires the
understanding of soil characteristics and climatic conditions. Although, after performing
various experiments of biochar application to soil, especially for crop production,
Lehmann concludes that: “crops respond positively to biochar addition up to 50 MgC/ha and may
show growth reduction only at very high applications”. Crop residue biochar as a soil amendment
agent for sustainable agriculture, can be described in following sub headings:
5
Table 1. Chemical characterization of biochar from different sources
% dry weight basis
SourcePT (0C) pH
SA (m2/gm) C N O H P C/N H2O Ash References
Corn stover 500 8.90 4.20 25.00 0.60 5.00 1.10 n/a 41.67 9.1 69.00 54
Corn stover 515 9.50 4.40 45.00 0.50 1.00 1.70 n/a 90.00 11.5 55.00 54
Coconut shell 550 8.90 15.10 80.10 0.50 2.50 n/a n/a 160.20 12.4 n/a 54
Peanut hulls 481 8.00 1.00 59.00 2.70 12.00 2.30 n/a 21.85 7.2 18.00 54
Corn cob 400 9.00 < 0.1 80.10 0.60 8.80 3.70 n/a 133.50 3.1 3.70 54
Sugarcane bagasse 350 5.00 n/a 75.20 0.66 15.80 4.60 n/a 113.94 3.42 3.60 54
Poultry litter 400 10.30 n/a 42.30 4.20 n/a n/a n/a 10.07 n/a n/a 54
Cottonseed hull 500 8.50 <0.1 78.70 2.50 6.90 2.50 n/a 31.48 6.5 7.90 54
Cottonseed hull 800 7.70 322.00 84.30 0.60 6.60 0.60 n/a 140.50 5.9 9.20 54
Rape residue 550 n/a n/a 72.20 1.30 25.60 0.90 n/a 55.54 3.2 21.80 40
Sunflower residue 550 n/a n/a 63.40 1.60 34.30 0.70 n/a 39.63 4.73 28.90 40
Wheat straw n/a n/a n/a 43.20 0.61 39.40 5.00 n/a 70.82 n/a n/a 47
Rice hulls n/a n/a n/a 38.30 0.83 35.45 4.36 n/a 46.14 n/a n/a 47
Olive kernel 800 n/a n/a 75.68 1.35 12.18 0.79 n/a 56.06 n/a n/a 36
Canola straw 500 9.39 n/a 63.40 0.04 n/a n/a 0.301585.00 n/a 18.40 37
Canola straw 700 10.76 n/a 54.90 0.04 n/a n/a 0.501372.50 n/a 28.55 37
Soyabean straw 500 10.92 n/a 62.60 0.40 n/a n/a 0.40 156.50 n/a 17.85 37
Soyabean straw 700 11.10 n/a 57.90 0.10 n/a n/a 0.60 579.00 n/a 23.70 37
Corn straw 500 10.77 n/a 41.90 0.90 n/a n/a 0.40 46.56 n/a 50.70 37
Corn straw 700 11.32 n/a 24.50 0.80 n/a n/a 0.70 30.63 n/a 73.30 37
Peanut straw 500 10.86 n/a 48.50 1.50 n/a n/a 0.10 32.33 n/a 32.50 37
Peanut straw 700 11.15 n/a 47.00 1.50 n/a n/a 0.12 31.33 n/a 38.50 37(Here, PT= pyrolysis temperature; SA= surface area; H2O= moisture content; and n/a= data not available)
6
7
2.1.4.1 Direct use of Biochar
As biochar is a highly porous structure, so after its addition to soil it leads to increase in
the soil aeration, soil water holding capacity and decrease in soil aggregation, soil
strength and soil bulk density. The pH of biochar varies from slightly acidic to alkaline
range (mostly in alkaline range from pH = 8.0-10.0), so alkaline pH leads to better
functioning of soil microbial communities and resurrecting buffering capacity to soil after
its application (37). Also, biochar application can be beneficial in acidic soil reclamation
and the soil that has been degraded by long term continuous cultivation (60). Various
anionic functional groups of biochar (48) on its surface behaves as an cation exchange
resin leading to the retention of essential cations for exchange, thus increase the soil
CEC, leading to increased crop productivity (59, 61). Biochar application to soil increases
the soil organic carbon pool and soil-N. During the initial periods of its application,
biochar has less resistance and is more prone to degradation because a small fraction of
carbon is present in the labile form (62), so the microbial activities is enhanced during
this time period. Excellent nutrient retention property of biochar leads to longer retention
of nutrients in topsoil after fertilizer application. High porosity and larger surface area of
soil after biochar amendment would lead to the growth of microorganism thus leading to
better symbiosis of the crop with bacteria and fungi, which results in the dissolution of
nutrients and bioavailability of nutrients for the crop (30).
2.1.4.2 Indirect use of biochar
The nutrient retention capacity of biochar leads to the reduction of fertilizer use, so it
indirectly results in reduction production, energy and environmental cost. Also, biochar
application to soil leads to subdued release of N2O and CH4 like potent Green house
gases (43, 63). According to an estimation of Woolf (2008) (64), all the crop residues of
the world if converted into biochar, would sequester about 1 gigatonne of carbon to soil
and is assumed to be a better carbon capture and storage (CCS) alternative for
mitigating Climate Change. Biochar has a carbon negative effect on the atmosphere (15,
55). By-products of biochar production (syn-gas and bio-oil) from crop residue are cleaner
fuel with high calorific value, thus can be used as an alternative source of energy (38-
40).
2.1.5 Crop residue Biochar as an adsorbent material
Lou et al., (2011) (65) reported that the rice-straw biochar amended in soil sediments has
a significant sorption capacity for pentachlorophenol (PCP), a genotoxic material for seed
germination. Xu et al., (2011) (66) was reported significant adsorption of methyl violet
from aqueous solutions by various crop residue derived biochars due to electrostatic
attraction and specific interaction between dye and various negative charges on biochar
8
surface. Similarly, a comparative adsorption study of rice-straw biochar and fly ash by
Lou et al., (2012) (67) advocated biochar as a significant sorption material for FCP than
aged fly ash. However, fresh fly ash has greater sorption capacity for FCP.
2.1.6 Risk associated with biochar as a soil amendment agent
The following are the major limitations and risks associated with biochar application to
soil which limit its use as soil ameliorator (68):
1. Application rates: a standardized application rate is still needed.
2. Effect on agrochemicals: application of biochar increases the binding of various
agrochemicals on its surface, thus reduces killing of pests and enhances the
longivity of chemical in soil by avoiding them from microbila decay.
3. PAHs production from pyrolysis: various studies reported PAHs production during
slow pyrolysis of biochar which remain attached with the anioinc surfaces of
biochar and might be causing negative impact to soil and microbila diveristy.
4. Soil albedo: biochar decreases soil albedo by providing black surface to soil and
increases absorption of sunlight, thus indirectly leads to Global warming
phenomenon.
5. Soil residence time: the residence time of biochar in soil is estimated as centinnial
to millenial with an average residence time of 600 years.
6. Soil Organic Carbon (SOM): in the literature not any conclusive report is available
which signify that biochar either increases or decreases the SOM content.
7. Heterogeneous nature of biochar: the properties of biochar are not stable; they
vary with type of biomass, pyrolysis condition and its application.
8. Cost of production: it is also comparatively higher.
2.2 Fly Ash from coal combustion
An inorganic finely divided particulate material generated from the burning of pulverised
coal and collected from the flue gas or electrostatic precipitaors in thermal power plants
is considered as fly ash (34). It is mainly an alluminosilicate compound (analogous to clay
particles) with a potential amount of oxides of Mg, Ca, Fe, and Na alonwith various toxic
trace metals. On the basis of amount of CaO, SiO2, Al2O3 and Fe oxides, ASTM C618
procedure catagorised fly ash into two classes, viz., Class C and Class F. Combustion of
lignite and sub-bituminous coal leads to the formation of Class C fly ash which has a high
content of CaO (33%), Na2O (0.7%) and comparatively lower contents of SiO2, Al2O3 and
Fe oxides (Table 2). Higher content of CaO provides self cementing property of Class C fly
ash. The burning of harder and older bituminous and anthracite coal leads to the
production of Class F fly ash which is more finer than the Class C fly ash because of the
presence of higher contents of SiO2 (53%), Al2O3, and Fe2O3, a lesser CaO (9%) content
(Table 2), thus requires an activator e.g., lime liming property (25, 26).
9
Table 2. Basic Characteristics of Class C and Class F fly ash
Characteristics
Source CoalClass
CClass F Lignite and Sub-bituminous Bituminous and Anthracite
Major Producers
U.S., South African
countries Australia, Canada, China, India,
South Africa, U.S.
Basic Nature Cementious Pozzolonic
Typical Composition
(%)
SiO2 40 55
Al2O3 17 26
Fe2O3 6 7
CaO 24 9
SO3 3.3 0.6
Available alkalies(Na2O) 0.7 0.5
Fineness 8 14
(retained on 325 mess)
(Source: Yunusha et al. 2012 (26))
2.2.1 Morphology and Physical Properties of fly ash
Various SEM and XRD studies revealed that fly ash has a regular shape and size,
consisting of about 2% spherical, hollow and solid structures known as cenospheres and
pleurospheres. Collectively these structures are known as microspheres having very high
thermal and magnetic properties, spherical design and chemical inertness (20, 33, 34).
The bulky microspheres are mainly present as (a). crystalline monolith, (b). porous, (c).
Cenospheres: hollow spheres formed by alluminosilicate in which the particle diameter to
wall thickness ratio can reach more than 50, and (d). Plerospheres: in which a hollow
large sphere is filled with various small spherical particles (21, 34). Fly ash has a great
adsorption capacity for various gases and other chemicals like pesticides due to presence
of these hollow spheres (20). These hollow spheres are responsible for the natural
geolytic behaviour of fly ash (34), also for comparatively lesser bulk density, higher
porosity, water holding capacity (WHC), surface area and electroconductivity (EC) than
soil. Particle diameter of fly ash usually ranges between 1-150 µm, however 60% of fly
ash is constituted by particles having diameter < 3 µm (comprise only 10 wt.% of fly ash).
10
A vast range of surface area and density is revealed by the fly ash ranging from 0.2
m2/gm to 0.8 m2/gm and 1.9 x 106 gm/m3 to 2.9 x 106 gm/m3 [34]. Colour of fly ash
depends upon the source material; however it is usually from greyish to black in colour
(21, 34).
2.2.2 Physico-chemical characacteristics of fly ash
Physico-chemical properties of fly ash depend upon the coal source and combustion
condition. In general, fly ash has an alkaline pH (8.0-11.48) due to presence of alkali and
alkaline earth metals compounds [33]; greater electrical conductivity (EC), mostly
composed of alumina, silica, and iron oxides (~87%); various macro and micro elements
(e.g., Fe, Mg, P, K, Si, Na, S, Ca, Mn, Al, etc.) and trace elements (e.g., As, Ba, B, Cd, Cr,
Cu, Co, Pb, Ni, Hg, Mo, Sc, Se, V, Zn, etc.). General chemical composition of fly ash is SiO2
> Al2O3 > Fe2O3 > CaO > MgO > K2O > Na2O > TiO2 (24). Trace metals (mainly heavy
metals) leaching like Zn, Cd, Pb, As, Se, and B are the major limitation for the use of fly
ash in the soil system which pollute the groundwater (69), but most of these metals are
reported in very less amount in Indian fly ash (70).
2.2.3 Use of fly ash
Fly ash is potentially used in cement industries, brick kilns, road formation, as adsorbent,
zeolyte formation which is further used for removal of heavy metals from wastewaters,
adhesives, wall board, paint, wood substitute, and as a potential soil amendment agent
(21,71-73). Singh et al. (2012) (74) reported a considerable amount of sorption of
metribuzin herbicide in fly ash amended soil, thus reduction of the runoff and leaching
losses from the soil. Use of fly ash in cement and soil amelioration also helps in carbon
sequestration (21). According to an study, 1 tonne fly ash can sequester 26 kg of CO2, i.e.
38.18 tonne fly ash will sequester 1 tonne of CO2, thus making the way for the utilization
of alkaline fly ash residue for CO2 mitigation (75). Fly ash has the capacity to adsorb some
volatile compounds like polynuclear aromatic hydrocarbons (PAHs) (76). The porous
nature of silicates and the surface embedded with activated carbon particles provides the
adsorbing capacity to the fly ash. The pore spaces formed by silicates show hydrophobic
nature and adsorb organic solvents from wastewater; and pore spaces formed by
aluminosilicates show hydrophilic nature and suitable for adsorption of water from organic
solvents [20]. Vitekari et al.,(2012) (77)viewed fly ash as a carrier for bio-pesticides and
bio-fertilizer formulations
2.2.4 Fly ash as a soil amendment agent
Class C fly ash is used for neutralizing the acidic soils. Calcium carbonate equivalent
(CCE) of fly ash is responsible for the neutralization of soil acidity mainly (26). Generally
all the soil macro and micro nutrients are present in fly ash except nitrogen (26). Thus, fly
ash amendment resulted into improvement of soil acidity, soil sodicity, nutrient supply,
concentration and loss, and adverse soil physical properties (26). Fly ash also has almost
similar soil improving properties as of biochar. Low rate fly ash application to soil is
11
reported to increase the VAM (vesicular arbuscular mycorrhiza) colonization (Glomus
aggregatum) in plant roots (Cajanus cajan) and at high rate of application, growth is
totally suppressed [78]. Singh et al., (2011) (79) performed various studies on
amendment of fly ash in three different cultivars of paddy in Indian soil and reported that
fly ash amendment at lower concentration (10%) enhanced the yield of rice.
2.2.5 Negative effects of fly ash
The following are some major negative effects of fly ash (80, 81):
1. High pH (from 8-12) resulting into reduction in bioavailability of a few nutrients.
2. High salinity.
3. High content of phytotoxic elements e.g., B, As, Mo, Se, etc. However, according to
a study by Love et al., (2009) (82) on Cassia occidentalis plant growing on
weathered fly ash suggests that fly ash prompts genotoxicity in plant. Wong and
Selvam (2009) (83) performed co-composting of fly ash with sludge and reported
that the heavy metal content of fly ash decreased with the increase in compost
ash content, however, B content was increased with the increase in ash content.
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12
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