Post on 01-Jan-2017
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2.0 ENERGY SCENARIO IN WORLD
Energy is one of the major inputs for the economic development of any
country. The major sources of energy in the world are oil, coal, natural gas, hydro
energy, nuclear energy, renewable combustible wastes and other energy sources. The
contribution of different energy sources to the total supply of energy in the world are:
Oil-35.1%, Coal-23.5%, Natural gas-20.7%, Renewable combustible wastes-11.1%,
Nuclear-6.8%, Hydro-2.3% and Other sources-0.5%. World electricity demand is
expected to continue more strongly than any other form of Energy. The total world
energy use rises from 505 quadrillion British thermal units (Btu) in 2008 to 619
quadrillion Btu in 2020 and 770 quadrillion Btu in 2035 (International Energy
Outloook, 2011). As it is expected to grow by 2.2% per year between 2008 and 2035,
with more than 80% of the increase occurring in non-OECD countries (World Energy
Outlook, 2010).
Out of total global power demand, coal based thermal power is meeting about
2/3rd
of the total requirement. Increased demand is most dramatic in developing
countries like China and India. By 2030, both the countries together will be the
world’s largest energy consumers (B.P.2012). Coal power generation is an established
part of the world's electricity mix providing over 44.7% of world electricity (nuclear
20.6%, oil 1.1%, natural gas 22.3% and hydro & other 11.3%). It is especially suitable
for large-scale, base-load electricity demand. The coal power is in increase demand in
all over the world and over the next decade is still the largest contributor to the growth
of power fuels accounting for 39% (B.P.2012). The share of coal energy in the global
electricity production is given in Figure 2.1.
2.1 ENERGY SCENARIO IN INDIA
Power sector in India has grown at a phenomenal rate during the last four
decades to meet the rapidly growing demand for electricity as electricity has become
an integral part of our day-to-day life and India is the fifth largest producer of
electricity in the world.
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Figure 2.1 Share of Coal Energy in Global Electricity Generation
India’s current installed power generation capacity as on 31 March 2012 is at
2,02,979.03 MW as against 1, 50,324 MW during 2009. The share of hydro is
about 19.24 percent, while share of nuclear and renewable are 2.35 percent and
12.07 percent, respectively (Central Electricity Authority, 2012) (Table 2.1). The
share of coal is maximum i.e., 56.54 percent while for gas and oil are 9.18 and
0.59 percent, respectively.
Table 2.1: Share of Energy in India
Fuel MW Percentage
Total thermal 13,4635.18 66.32
Coal 114,782.38 56.54
Gas 18.653.05 9.18
Oil 1,199.75 0.59
Hydro (Renewable) 39,060.40 19.24
Nuclear 4,780.00 2.35
*Renewable Energy
Resources
25,503.45 12.07
Total 2,02,979.03 100%
The Power ministry has set a target of adding 76,000MW of electricity capacity in the
12th
plan (2012-2017) and 93,000 MW in the 13th
plan Five-year plan (2017-2022).
Despite significant increases in total installed capacity during the last decade, the gap
between electricity supply and demand continues to increase. The resulting shortfall
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has had a negative impact on industrial output and economic growth. However, to
meet expected future demand, indigenous coal production will have to be greatly
expanded.
India’s energy consumption has been increasing at one of the fastest rates in
the world due to population growth and economic development, although new oil and
gas plants are planned, but coal is expected to remain the dominant fuel for power
generation. In India the demand of electricity is always more than the supply and the
coal reserves in India is in better condition than other fossil fuels, thus the power
production is totally dependent on the coal, which is responsible to a large extent.
Hence, it can be said that increasing demand of power with a very slow pace
of capacity addition requires that the power plants must operate with highest possible
power availability and reliability. Environmental problems associated with thermal
power plants start with transportation of coal from mine, feeding it to boiler, and the
emission of flue gases and particulate matter. Now-a-days, the environmental
problems of energy use are related with environmental cost, which have been rising,
reinforcing the effect of increased monetary costs in creating incentives for increasing
the efficiency with which energy is used.
2.2 COAL MINING IN INDIA
Mining of coal as well as other minerals is generally considered to be an
environmentally unfriendly activity as all the components of environment are affected
by various operations in mining and associated activities. In India, coal deposits are
chiefly located in Jharkhand, Orissa, Chhattisgarh, West Bengal, Madhya Pradesh,
Andhra Pradesh and Maharashtra (Provisional coal statistics, 2011-2012). While,
major portion of coking coal is produced by Jharkhand (Figure 2.3) only 0.75 MT is
collectively produced by West Bengal, Chhattisgarh and Madhya Pradesh. Table 2.2
shows the coal reserves of India up to the depth of 1,200 meters have been estimated
by the Geological Survey of India at 2,93,497 Million Tonnes. Out of the total
resources, the Gondwana coalfields account for 2,92,005 MT (99.5%), while the
Tertiary coalfields of Himalayan region contribute 1493 MT (0.5%) of coal resources
(GSI,2012).
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Figure 2.3: Coal production by various states
Table 2.2: Coal Reserves of India
Depth Range
(in Metre)
Proved
(Mt)
Indicated
(Mt)
Inferred
(Mt)
Total
(Mt)
%
Share
0-300 92251.33 70830.45 10760.74 173842.52 59.23%
300-600 10422.74 57244.92 16255.52 83923.18 28.59%
0-600
(For Jharia
Only)
13710.33 502.09 0.00 14212.42 4.84%
600-1200 1760.42 13591.39 6167.22 21519.03 7.33%
Total 118144.82 142168.85 33183.48 293497.15 100.00%
(Source GSI, 2012)
2.2.1 Jharia Coalfield (JCF)
From the very beginning of Indian coal mining history the JCF was a highly
attractive area for mining mainly because it has one of the highest concentrations of
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thick coal seams in the world, ranging from 50 cm to 30 m in thickness, at relatively
short depths. The JCF contains the only remaining reserves of prime coking coal in
India, it is responsible for 50% of the coking coal produced in India, and supports
80% coking coal requirement of the Indian Steel Industry (CIL,1976).
The coal production was increased by 3 MT as it was estimated as 42.65 MT
in the year 2016-2017 while it was 39.65MT in the last year (2010-11). The power
utility increases form 15.29 MT to 28.60 MT from 2006- 07 to 2011-12. Similarly, the
production of coal for the steel plant increases from 4.24 to 4.60 MT in the 2006-07 to
2010-12 and estimated to increase as 7.00MT (2016-17), 8.25MT (2020-21) and
9.00MT (2026-27) (www.bccl.gov.in).
2.3 SOURCES OF AIR POLLUTION
Sources of air pollution can be categorized according to the source type,
emission and their spatial distribution. These are of mainly two types viz., natural and
anthropogenic (man-made). Natural sources of air pollution are lightning generated
forest and grassland fires, sea salt spray, desert and soil erosion, dust storm, biogenic
emissions (pollen, spores, bacteria and debris), windblown dust and volcanic
eruptions (Seinfield,1986). While, manmade sources include transportation vehicles,
industrial processes, power plants, municipal incinerators and others. These sources
lead to generation of several pollutants and they further be classified as either primary
or secondary. Primary pollutants are substances directly emitted from a process, such
as ash from a volcanic eruption, carbon monoxide gas from a motor vehicle exhaust
or sulphur dioxide released from factories. Secondary pollutants are not emitted
directly. Rather, they form in the air when primary pollutants react or interact in
presence of sunlight. An important example of a secondary pollutant is ground level
ozone-one of the many secondary pollutants that make up photochemical smog.
Emissions may be categorized mainly as stationary and mobile sources which include
all the activities in an urban environment.
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Source categorization according to number and spatial distribution includes single
and point sources (stationary), area or multiple sources (stationary or mobile) and line
sources as briefed below.
2.3.1 Point, Area, Line and Fugitive Sources:
a) Point Sources
A point source is a single, identifiable source of air pollutant emissions
(for example, the emissions from a combustion furnace flue gas stack). Point
sources are also characterized as being either elevated or at ground-level. A point
source has no geometric dimensions. Point sources of air pollution include
stationary sources such as power plants, smelters, industrial and commercial
boilers, wood and pulp processors, paper mills, industrial surface coating
facilities, refinery and chemical processing operations, and petroleum storage
tanks. Large, stationary sources of emissions that have specific locations and
release pollutants in quantities above an emission threshold are known as point
sources.
b) Area Sources
An area source is a two-dimensional source of diffuse air pollutant
emissions (for example, the emissions from a forest fire, a landfill or the
evaporated vapours from a large spill of volatile liquid). Area sources of air
pollution are the air pollutant emission sources which operate within a certain
locale. The U.S. Environmental Protection Agency has categorized 70 different
categories of air pollution area source (www.epa.gov).
Locomotives operating within a rail yard are an example of an area source of
pollution. Other area sources of air pollution are:
� Multiple flue gas stacks within a single industrial plant
� Open burning and forest fires
� Evaporation losses from large spills of volatile liquids
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c) Mobile Sources
A line source is one-dimensional source of air pollutant emissions (for
example, the emissions from the vehicular traffic on a roadway). They can be
divided into on-road sources and non-road sources. On-road sources include
vehicles such as cars, motorcycles, trucks, and buses. Non-road mobile sources
include trains, aircraft, boats and ships, lawn and garden equipment, snow blowers,
industrial equipment, and construction vehicles and equipment. Mobile sources
pollute the air as a result of burning fuel and through evaporation of fuel during
fill-ups and on-board fuel storage and handling. Pollutants released from mobile
sources include carbon monoxide, volatile organic compounds, nitrogen oxides,
particulate matters (especially from diesel engines-black smoke), and hazardous air
pollutants/air toxics such as benzene, formaldehyde and acetaldehyde. Mobile
sources contribute greatly to air pollution nationwide and are the primary cause of
air pollution in many urban areas.
d) Fugitive Sources
Fugitive emissions mean the emissions of any air contaminant into the open air
other than from a stack or air pollution control equipment exhaust. Simply put,
fugitive dust is a type of nonpoint source air pollution - small airborne particles that
do not originate from a specific point such as a gravel quarry or grain mill. Fugitive
dust originates in small quantities over large areas. Significant sources include
unpaved roads, agricultural cropland and construction sites.
2.4 IMPACT OF AIR POLLUTION
The impact of air pollution are diverse and numerous. Air pollution can have
serious consequences for the health of human beings, climate change, agriculture and
also severely affects natural ecosystems (Molina and Molina, 2004; Decker et al.,
2000). As a result, air pollution is a global problem and has been the subject of global
cooperation and conflict.
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2.4.1 Impact on human health due to particle size
The health effects of particulates are strongly linked to particle size. The
extent to which air borne particles penetrate into the human respiratory system is
mainly determined by the size of the penetrating particles (Balachandran et al., 2000).
Small particles, such as those from fossil fuel combustion, are likely to be most
dangerous, because they can be inhaled deeply into the lungs, settling in areas where
the body's natural clearance mechanisms cannot remove them. The constituents in
small particulates also tend to be more chemically active and may be acidic as well
and therefore more damaging. Atmospheric particles with an aerodynamic diameter
smaller than 10 µm (PM10) have been put under scrutiny in the past, being easily
inhaled and deposited within the respiratory system (Pope et al., 1995). Studies show
that PM10 play a role in the incidence and severity of respiratory diseases (Brunekreef
and Holgate, 2002; Pope and Dockery, 1999) and have significant associations with
decline in lung function and cardio-vascular pathologies. Recent studies of health
effects of PM associated with heavy metals have mainly investigated the
concentration of metals in total suspended particles (TSP), PM10 (less than or equal to
10µm) and PM2.5 (less than or equal to 2.5µm).
There are several epidemiological studies present in the literature (Harrison
and Yin, 2000; Samet et al., 2000; Dockery, 1993; Hoek et al., 1997), which have
demonstrated a direct association between atmospheric inhalable particulate matter
and respiratory diseases, pulmonary damage, and mortality especially in the urban
areas. Exposure to elevated levels of PM increases the rate of respiratory problems,
hospitalizations due to lung or heart disease, and premature death (Asgharian et al.,
2001 a, b; Holberg et al., 1987). Fuel combustion, industries, and power plants are the
main sources of particles in urban and industrialized areas (Zhang et al., 2007).
Depending upon the atmospheric conditions, the health risks can be aggravated
(Cheng et al., 2009).
In several studies it was found that the existence of fine particles in the air is
associated with cardio vascular diseases and mortality (Sunyer et al., 1996; Zmirou et
al., 1996,). In particular, fine particles (PM2.5 and PM1.0 fractions with aerodynamic
diameter less than 2.5 µm and 1.0 µm, respectively) have a strong correlation with
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morbidity and/or mortality due to pulmonary and cardiac disease (WHO, 2003; Pope
et al., 2002; Samet et al., 2000). Fine particles can penetrate the human respiratory
tract and lungs, and several epidemiological studies have reported a link between
elevated particle concentration and increased mortality and morbidity (Ostro et al.,
1999; Abbey et al., 1999; Wilson and Suh, 1997). Hospital admissions indicating the
number of patients admitted into hospitals are a marker for an adverse health event
(Delfino et al., 1997; Burnett et al., 1995). Moreover, these particles may have wide-
ranging potential effects on agricultural and natural ecosystems, and they may reduce
visibility affecting transportation safety and aesthetics (Yuan et al., 2006).
Numerous studies associate particulate pollution with acute changes in lung
function and respiratory illness (Dockery et al.,1996; USEPA,1996) resulting in
increased hospital admissions for respiratory disease and heart disease, school and job
absences from respiratory infections, or aggravation of chronic conditions such as
asthma and bronchitis (Shprentz,1996). But the more demonstrative and sometimes
controversial evidence comes from a number of recent epidemiological studies. Many
of these studies have linked short-term increase in particulate levels, such as the ones
that occur during pollution episodes, with immediate (within 24 hours) increases in
mortality. This pollution-induced spike in the death rate ranges from 2 to 8% for
every 50-µg/m3 increase in particulate levels.
A focus on the occupational hazards and overall condition prevailing in
Indian coalmines are felt to be important. Simple Coal Workers’ Pneumoconiosis
(SCWP) and Progressive Massive Fibrosis (PMF) are the major occupational
respiratory diseases of coal miners caused due to exposure to respirable dust
generated during various mining operations. The concentration of respirable coal dust,
the period of exposure and free silica content are important factors associated with
pneumoconiosis risks. Assessment of respirable dust in coalmines and its control are
of primary importance to undertake preventive measures.
Several epidemiological studies conducted in different countries reported a
reducing trend of pneumoconiosis mortality since last two decades due to gradual
reduction in dust levels at work faces through stringent control measures (HEI, 1995;
Ostro, 1993). There are number of scattered studies reported in Indian coalmines by
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different agencies and the prevalence of the disease varied widely from one another to
draw any definite conclusion on the prevalence, distribution and determinants of the
disease (Bertollini et al., 1996). Roy, 1956 first reported pneumoconiosis cases in
bituminous coal mines of Madhya Pradesh prior to that it were presumed occupational
diseases like silicosis, pneumoconiosis were not properly diagnosed in India.
During major pollution events, such as those involving a 200-µg increase in
particulate levels, an expert panel at the World Health Organization (WHO) estimated
that daily mortality rates could increase as much as 20 percent (Shaheen, 2007). In the
aggregate, pollution-related effects like these can have a significant impact on
community health. WHO estimated that short-term pollution episodes accounted for 7
to 10 percent of all lower respiratory illnesses in children, with the number rising to
21 percent in the most polluted cities. Furthermore, 0.6 to 1.6 percent of deaths were
attributable to short-term pollution events, climbing to 3.4 percent in the cities with
the dirtiest air (Bertollini et al., 1996).
Health effects are not only restricted to occasional episodes when pollutant
levels are particularly high. Numerous studies suggest that health effects can occur at
particulate levels that are at or below the levels permitted under national and
international air quality standards. In fact, according to WHO and other organizations,
no evidence so far shows that there is a threshold below which particle pollution does
not induce some adverse health effects, especially for the more susceptible
populations (Shaheen, 2007). Therefore, the estimation of the levels of respirable
particulate and its major toxic constituent present in the urban atmosphere is a prime
requirement of epidemiological investigation, air quality management, and air
pollution abatement (Chow et al., 2002; Querol et al., 2001). This situation still has
prompted a vigorous debate about whether current air quality standards are sufficient
to protect public health.
2.4.2 Impact of Airborne Trace Metals on Human Health
With the developing industry of mining, smelting and metal treatment, heavy
metal pollution becomes serious (Wang et al., 2001; Guo, 1994; Su et al., 1994; Wu et
al., 1989; Liao, 1993). Most severe is that this kind of pollution is covert, long term
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and non-reversible. They can cause acute and chronic health effects (Amdur, 1980).
These pollutants are emitted into the atmosphere continuously through various human
activities, especially in large cities where inhabitants and industrial activities are
concentrated.
Thus, there is an increasing concern about the hazardous effects of metals and
metalloids present in airborne particulate matter on humans and other living
organisms in populated areas (McClellan, 2002) and thus many monitoring and
analysis programs on PM have been conducted in several parts of the world. Heavy
metals are potentially toxic, even at low exposure levels (Bosco et al., 2005). Air
pollutants, especially airborne trace metals in PM, have been associated with both
short-term and long-term adverse health effects including chronic respiratory disease,
heart disease, lung cancer, and damage to other organs (Niu et al., 2008; Williams et
al., 2007; Lingard et al., 2005; Rasmussen, 2004; Osonio-Vargas et al., 2003; Prieditis
et al., 2002; Allen et al., 2001; Vincent et al., 2001; Ghio et al., 1999;Costa et al.,
1997).There are several investigations on trace metals (Pb, Cd and Hg) in air and their
toxic effects (Onder and Dursun, 2006) have been studied which are described below-
Lead (Pb) is considered as critical pollutant in air. Modern
industrialization, with the introduction of Pb in mass produced plumbing, Solder,
paint, ceramic ware and countless other products resulted in marked rise of Pb in air
though it is not contributed by vehicles as use of leaded gasoline is banned since 2001
in India. The annual worldwide production of Pb is approximately 5.4 million Tones
and it continues to rise. Sixty percent of lead is used for the manufacturing of the
automobile batteries while the remainder is used in the production of pigments,
glazes, solders, plastics, cable sheathing, ammunitions, weights, gasoline additives,
and a variety of other products that continue to pose threat environment risks arising
from anthropogenic sources (Hu, 2002).The general body of literature on lead toxicity
indicates that, depending on the dose, lead exposure in children and adults can cause a
wide spectrum of health problems, ranging from convulsions, coma, renal failure, and
death at the high end to subtle effects on metabolism and intelligence at the low end
of exposures (US Agency for Toxic Substances and Disease Registry, 1999).
Children (and developing foetuses) appear to be particularly vulnerable to the
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neurotoxic effects of lead. A plethora of well-designed prospective epidemiologic
studies has convincingly demonstrated that low-level lead exposure in children less
than five years of age (with blood lead levels in the 5-25 mg/dL range) results in
deficits in intellectual development as manifested by lost intelligence quotient points
(Banks et al.,1997). Among the most important is the risk posed to the foetus posed
by mobilization of long lived skeletal stores of lead in pregnant women (Silbergeld,
1991). Several studies has clearly demonstrated that maternal bone lead stores are
mobilized at an accelerated rate during pregnancy and lactation (Gulson et al.,1997)
and are associated with decrements in birth weight, growth rate, and mental
development (Gonzalez-Cossio et al.,1997). Since bone lead stores persist for decades
(Hu et al., 1998), it is possible that lead can remain a threat to foetal health many
years after environmental exposure had actually been curtailed.
High levels of mercury exposure that occur through, for example,
inhalation of mercury vapours generated by thermal volatilization can lead to life-
threatening injuries to the lungs and neurologic system. At lower but more chronic
levels of exposure, a typical constellation of findings arises, termed erethism-with
tremor of the hands, excitability, memory loss, insomnia, timidity, and sometimes
delirium that was once commonly seen in workers exposed to mercury in the felt hat
industry (“mad as a hatter”). Even relatively modest levels of occupational mercury
exposure, as experienced, for example, by dentists, have been associated with
measurable declines in performance on neurobehavioral tests of motor speed, visual
scanning, verbal and visual memory, and visuo motor coordination (Bittner et
al.,1998). Small amount of mercury released from dental amalgams during chewing is
capable of causing significant illnesses, such as multiple sclerosis, systemic lupus, or
chronic fatigue syndrome (Grandjean et al., 1997). Methyl mercury also crosses the
placental barrier and causes damage to the foetus in pregnant women.
Arsenic undergoes some accumulation in soft tissue organs such as the liver,
spleen, kidneys and lungs once absorbed into the body, but the major long-term
storage site for arsenic is keratin-rich tissues, such as skin, hair, and nails making the
measurement of arsenic in these biological specimens useful for estimating total
arsenic burden and long-term exposure under certain circumstances. Acute arsenic
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poisoning is infamous for its lethality, which stems from arsenic’s destruction of the
integrity of blood vessels and gastrointestinal tissue and its effect on the heart and
brain. Chronic exposure to lower levels of arsenic results in somewhat unusual
patterns of skin hyper pigmentation, peripheral nerve damage manifesting as
numbness, tingling, and weakness in the hands and feet, diabetes, and blood vessel
damage resulting in a gangrenous condition affecting the extremities (Col et al.,1999).
Chronic arsenic exposure also causes a markedly elevated risk for developing a
number of cancers, most notably skin cancer, cancers of the liver (angiosarcoma) (US
Department of Health and Human Services; 1991), lung, bladder, and possibly the
kidney and colon. Arsenic affects skin, lungs, liver, cardiovascular system, nervous
system, haematopoietic system and reproductive system.
Manganese has become a metal of global concern because of the introduction
of methyl cyclopentadienyl manganese tricarbonyl (MMT) as a gasoline additive
(Lyzincki et al., 1999). Proponents of the use of MMT have claimed that the known
link between occupational manganese exposure and the development of a Parkinson’s
disease-like syndrome of tremor, postural instability, gait disorder, and cognitive
disorder has no implications for the relatively low levels of manganese exposure that
would ensure from its use in gasoline. However, this argument is starkly reminiscent
of the rationale given for adding lead to gasoline, and what little research that exists
from which one can infer the toxicity potential of manganese at low-levels of
exposure is not particularly comforting.
Acute high-dose exposures to cadmium can cause severe respiratory
irritation. Occupational levels of cadmium exposure are a risk factor for chronic lung
disease (through airborne exposure) and testicular degeneration (Benoff et al., 2000)
and are still under investigation as a risk factor for prostate cancer (Ye et al., 2000).
Lower levels of exposure are mainly of concern with respect to toxicity to the kidney.
Cadmium damages a specific structure of the functional unit of the kidney (the
proximal tubules of each nephron) in a way that is first manifested by leakage of low
molecular weight proteins and essential ions, such as calcium, into urine, with
progression over time to frank kidney failure (Satarug et al., 2000). This effects tends
to be irreversible (Roels et al, 1997) and recent research suggests that the risk exists at
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lower levels of exposure than previously thought (Suwazono et al., 2000; Jarup et al.,
2000). Even without causing frank kidney failure, however, cadmium’s effect on the
kidney can have metabolic effects with pathologic consequences.
Copper is an essential element for normal biological activities in humans.
Copper is mainly available in the coalfield environment due to burning of coal,
fertilizer, iron and steel production. Airborne copper is absorbed through duodenum
and causes irritation of the respiratory tract and metal fume fever. Above 14g of
copper intake causes gastrointestinal disorder haemolysis, heptotoxic and nephrotoxic
effects. Disease like thalassemia, haemacromatosis, cirrhosis, tuberculosis and
carcinoma encourage enhancement of the copper content in liver (Dara, 1993).
Higher concentrations of Nickel produce respiratory problems like
asthma, neoplasm of lungs. It also produces the gastrointestinal problems, problems of
Central Nervous System and headache (Gupta, 2004; Asante-Duah, 1993). Nickel
dust is also accounted as carcinogenic.
Aluminium contributes to the brain dysfunction of patients with severe kidney
disease who are undergoing dialysis. High levels of aluminium have been found in
neurofibrillary tangles (characteristic brain lesions in patients with Alzheimer’s
disease), as well as in the drinking water and soil of areas with an unusually high
incidence of Alzheimer’s disease. Nevertheless, the experimental and epidemiologic
evidence for a causal link between aluminium exposure and Alzheimer’s disease is,
overall, relatively weak, thus more research is needed on this topic.
Chromium, in its hexavalent form, which is the most toxic species of chromium,
is used extensively in some industries such as leather processing. As a result,
chromium has become a major factory run-off pollutant that is beginning to become a
global trend. The toxicity of chromium stems from its tendency to be corrosive and to
cause allergic reactions.
For a clearer picture of the potential risk of the heavy metals that in-coming
air pollution it may contribute, an extensive study is highly recommended.
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2.4.3 Effect on Properties
Air pollution affects material by soiling the painted surfaces, clothing
and structures. It is also attributed to the chemical deterioration. The smoke and
particulates are mainly responsible for such soiling phenomenon. Acidic and alkaline
particles corrode materials such as textiles, paints, machinery etc. SO2 is responsible
for weakening of leather, textiles and metallic corrosion due to its acidic nature. Metal
corrosion is accelerated by formation of sulphuric acid either in atmosphere or on
metal surface, which is highly corrosive in nature. NO2 and ozone affects the
discoloration of paints, clothing, dyes etc. due to its oxidizing nature. Smoke and
sticky aerosols which are generated as a combined effect of particulate and gaseous
pollutant are responsible for damage of building materials including stones and other
building surfaces (Stern, 2006; Kali, 1996). Solar radiation, fog formation and
precipitation (acid rain), alteration in temperature are the atmospheric phenomena that
directly affect the material (Seinfeld and Pandis, 1998).
2.4.4 Impact on Vegetation
The primary effect of particulate matter on vegetation is reduced growth
and productivity due to inference with photosynthesis process. The mechanisms of
action are through smothering of leaves, physical blocking of stomata, and
biochemical interactions, indirect effect through soil forest nutrient cycling due to
atmospheric deposition of pollutants on the plant canopy has been reported (Agrawal
and Singh, 2000; Amundson et al., 1990). Air pollution causes damage to large
number of food, forage and ornamental crops through halogen compounds such as
Hydrogen Fluoride (HF) and Hydrogen Chloride (HCl). Photochemical compounds,
sulphur compounds and nitrogen compounds also contribute to agricultural damage
(Chen et al., 2010; Chauhan and Joshi 2010; Li et al., 2007; Agrawal et al., 2006). The
curtailed value results from various types of leaf damage, stunting of growth,
decreased size and yield of fruits and vegetables, and destruction of flowers. SO2
results in significant decrease in photosynthetic pigments, phenolics and amino acid in
Spinach (Irshad et al., 2011; Agrawal and Agrawal, 1991). Several field experiments
have shown reductions in root and shoot lengths, leaf area and number of leaves, ears,
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seeds and yield of plants due to SO2 exposure (Agrawal et al., 2006; Agrawal and
Deepak, 2003).
2.5 AIR QUALITY AND EMISSION STANDARDS
Ambient air quality standard is acceptable concentrations of pollutants in the
atmosphere, while emission standards are allowable rates at which pollutants can be
released from a source. National Ambient Air Quality Standards (NAAQS) have been
adopted and followed by several environmental protection agencies throughout the
world at two levels: primary and secondary. Primary standards are required to be set
at levels that will protect public health and include an “adequate margin of safety”,
regardless of whether the standards are economically or technologically achievable.
Primary standards are projected for even the most sensitive individuals, including the
elderly and those already suffering from respiratory disorders. Secondary air quality
standards are more stringent than primary standards. Secondary standards are
established to protect public welfare (e.g., buildings, crops, animals and fabrics, etc.)
(Brimblecombe and Grossi 2010; Dockery and Pope, 1997)
In India the protection of environment and sustainable use of natural resources
received serious attraction from various committees of The Government and Planning
Commission in early 1970. The 5-year plan (1968-73) gave explicit recognition for
integrating environmental dimensions into the planning and developmental processes.
On the basis of the recommendation of the Tiwari Committee in 1980, Govt. formed
Dept. of environment for promoting and coordinating programs for environment and
related issues. Later in 1985, Ministry of Environment and Forest (MoEF) was formed
for formulating policies and their implementation. The CPCB is a statutory authority
under the purview of the MoEF.
From 1970 to 1981 several comprehensive Environmental Protection Acts
were passed and they continue to be amended from time to time to plug loopholes and
incorporate new concerns. Although existing laws dealing directly and indirectly to
the matters. As such, it is necessary to have a general legislation. In view of this fact
on 23rd
MAY 1986 the Comprehensive Environment (Protection) Act, also known as
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Umbrella act was enacted in order to implement effective environmental protection
and pollution control.
The Clean Air Act (US-EPA) requires that the list of criteria pollutant be
reviewed periodically and that standard be adjusted according to latest scientific
information. Past review have been modified both the list of pollutants and their
acceptable concentrations. Standard may be absolute and such these should estimate
the probability of causing harm to receptor (plants or animal in contact with the
pollution) by acknowledging dilution, attenuation, types and numbers of receptors,
likely doses, and possible effects. Then the decision on an acceptable concentration
may be calculated from the acceptable risk. The later remains a subjective or political
decision. Sources of air quality data available for general use are extremely
heterogeneous throughout the world. In general, measurements of air pollution are
made by one or more agencies at all levels of government, national, provincial, city
and town as well as by public and private laboratories, institutes and universities in
many instances. Primary departmental responsibility at the national level usually
resides in the Central pollution Control board (as in India), in the federal health
service (as in Pakistan, USA, USSR) or in a science and technology ministry (as in
Japan and the United Kingdom). Detailed air quality monitoring and survey on the
local level are carried out by Municipal hygiene laboratories (as in Paris), by town
planning commissions (as in Liege), and sometimes by a complex by a complex of
agencies (as in Milan).
In exercise of the power conferred by Sub-section (2) (h) of section 16 of the
Air (Prevention and control of Pollution) Act, 1981 and in suppression of the
NAAQS, 1994, the Central Pollution Control Board (CPCB) of India has stipulated
and notified the ambient air quality standards in the year 2009 (Table 2.3) by
classifying the different areas into two categories: -
(i) Industrial, Residential, rural and other areas
(ii) Ecologically Sensitive area (notified by Central Government)
Chapter 2 Literature Review
23
Table 2.3: National Ambient Air Quality Standards, CPCB 18th
November, 2009
Source: CPCB under section 16(2) of the Air Act: 2009
*Annual arithmetic mean of minimum 104 measurements in a year at a particular site taken twice a
week 24 hourly at uniform intervals.
**24 hourly or 08 hourly or 01 hourly monitored values, as applicable, shall be complied with 98% of the time in a
year. 2% of the time, they may exceed the limits but not on two consecutive days of monitoring.
Pollutant Time
weighted
average
Concentration in ambient
air
Methods of Measurement
Industrial,
Residential
, Rural &
Other Area
Ecologically
Sensitive
Area
(notified by
Central
Government)
Sulphur Dioxide,
(SO2), µg/m3 Annual *
24 hours**
50 20 - Improved West and Gaeke
-Ultraviolet fluorescence
80 80
Nitrogen Dioxide
(NOx), µg/m3
Annual *
24 hours**
40 30 - Jacob & Hochheiser
Modified(Na-Arsenite)
- Chemiluminescence. 80 80
Particulate Matter
(size less than 10 um)
or PM10 µg/m3
Annual *
24 hours**
60 60 - Gravimetric
- TOEM
- Beta attenuation 100 100
Particulate Matter(
Size less than 2.5 um)
or PM2.5 µg/m3
Annual *
24 hours**
40 40 -Gravimetric
- TOEM
- Beta attenuation 60 60
Ozone(O3), µg/m3 Annual *
24 hours**
100 100 -UV photometric
- Chemiluminescence.
- Chemical Method 180 180
Lead (Pb) Annual *
24 hours**
0.50 0.50 AAS method after sampling
Using EPM 2000 or equivalent
filter paper 1.0 1.0
Carbon Monoxide
(CO) mg/m3
8 hours*
1 hour**
02 02 -Non Dispersive Infra Red
(NDIR) spectroscopy 04 04
Ammonia (NH3)
µg/m3
Annual *
24 hours**
100 100 -Chemiluminescence
400 400
Benzene (C6H6)
µg/m3
Annual * 05 05
-Gas chromatography based
continuous analyzer
-Adsorption and Desorption
followed by GC analysis
Benzo(a)Pyrene
(BaP)-paticulate
phase only, ng/m3
Annual * 01 01
-Solvent extraction followed by
HPLC/GC analysis
Arsenic (As), ng/m3
Annual * 06 06
-AAS/ICP method after
sampling on EPM 2000 or
equivalent filter paper
Nickel (Ni), ng/m3
Annual * 20 20
-AAS/ICP method after
sampling on EPM 2000 or
equivalent filter paper
Chapter 2 Literature Review
24
Internationally, the maximum permissible limits (in µg /m3) of pollutants in the air set
by WHO are given in the Table 2.4
Table 2.4 : WHO Maximum Permissible Limits of Air Pollutants
Pollutant Time Weighted Average (µg/m3) Exposure Time
SO2 (WHO: 1979, 1987) 500
350
100-150*
40-60*
10 minutes
1 hour
24 hours
1 year
CO 30
10
1 hour
8 hours
NO2 (WHO : 1977, 1987) 400
150
1 hour
24 hours
Ozone (WHO : 1978, 1987) 159-200
100-120
1 hour
8 hours
Total suspended particulates 150-230*
60-9*
24 hours
1 year
(Source: WHO, UNEP 1996, Urban Air Pollution in Megacities of the World, Washington, DC: WHO & UNEP)
Note. * Guidelines values for combined exposure to SO2 and SPM (they may not apply to situations where only one of the
components present).
Dust particles are the main concerning issues in mining sector. Table 2.5 displays
standards provided by the different countries and India for respirable fraction of mines
dust.
Table 2.5 :Respirable Dust Standards for Coal Mines in Different Countries
(Source: Coal Mines Regulations 123 of 1957)
The Ambient Air Quality Standards in India for existing as well as new Coal Mines
lay down and notified by MOEF, GOI in September 2000 are given in Tables 2.6, 2.7
and 2.8 respectively.
Name of the
Country
Stipulated maximum dust concentration at different points Recommended instrument
for Monitoring
USA At working place :
- 2 mg/m3 where dust contains less than 5% free silica.
- 10mg/m3 (% free silica) where dust contains more than 5%
free silica
Personal
Gravimetric
Sampler
United
Kingdom
- At coal face – 7 mg/m3
- At heading 5mg/m3
- At face intake – 5 mg/m3
Gravimetric Dust
Sampler
Former USSR - 10 mg/m3 when free silica content is more than 10%
- 2 mg/m3 when free silica content is more than 10%
Not specified
Germany - At coal face – 7 mg/m3
- At heading 5mg/m3
- At face intake – 5 mg/m3
Gravimetric Dust
Sampler
India (DGMS) - 3 mg/m3 where face silica content is less than 5%
- 15 mg/m3 (% free silica) where free silica content is more
than 5%)
Gravimetric Dust
Sampler
Chapter 2 Literature Review
25
The Ambient Air Quality Standards in India for existing as well as new Coal Mines
lay down and notified by MOEF, GOI in September 2000 are given in Tables 2.6, 2.7
and 2.8 respectively.
Table 2.6 :Ambient Air Quality Standards for Existing Coal Mines
(Source:MoEF, Govt.of India Notification,Sep 2000)
Table 2.7 : Ambient Air Quality Standards for New Coal Mines
(Source:MoEF, Govt.of India Notification,Sep 2000
Category
Pollutant Time weighted average Concentration in
Ambient Air
Method of
Measurement
Existing coal
fields/mines given
below:
Karampura,
Ramgarh,
Gandih Rajhara,
Wardha,
Nagpur, Silewara,
Pench Kanhan,
Patharkhera,
Umrer, Korba,
Chirimiri, Central India
Coalfields, (including
Baik-unthpur,
Bisrampur)
Singrauli, Ib Vally,
Talcher, Godavary-
Valley and any other.
Suspended
Particulates
Matter
(SPM)
Annual
Average*
24 hours**
430 µg/m3
600µg/m3
High Volume Sampling
(Average flow rate not
less than 1.1m3/minute)
Respirable
Particulate
Matter (size less
than 10 (RPM)
Annual Average*
24 hours**
215µg/m3
300µg/m3
Respirable Particulate
Matter sampling and
analysis
Sulphur Dioxide
(SO2)
Annual
Average*
24 hours**
80µg/m3
120µg/m3
1 Improved West and
Gaeke method
2. Ultraviolet
fluorescence
Oxide of
Nitrogen as NO2
Annual
Average*
24 hours**
80µg/m3
120µg/m3
1 Jacob &
Hochheiser
Modified (Na-
Arsenic) Method
2 Gas phase
Chemilumines-
cence.
Category Pollutant Time weighted
average
Concentration in
Ambient Air
Method of Measurement
New Coal
Mines (Coal Mines
commenced operation
after the date of
publication of this
notification)
Suspended Particulates
Matter (SPM)
Annual
Average*
24 hours**
360 µg/m3
500µg/m3
High Volume Sampling
(Average flow rate not less
than 1.1m3/minute)
Respirable Particulate
Matter (size less than
10 (RPM)
Annual
Average*
24 hours**
180µg/m3
250µg/m3
Respirable Particulate Matter
sampling and analysis
Sulphur Dioxide (SO2) Annual
Average* 24 hours**
80µg/m3
120µg/m3
1. Improved West and
Gaeke method. 2. Ultraviolet fluorescence
Oxide of Nitrogen as
NO2
Annual
Average*
24 hours**
80µg/m3
120µg/m3
3 Jacob & Hochheiser
Modified (Na-Arsenic)
Method
4 Gas phase Chemilumines-cence.
Chapter 2 Literature Review
26
Table 2.8: Ambient Air Quality Standards for Jharia, Raniganj and Bokaro
Category Pollutant Time weighted
average
Concentration in
Ambient Air
Method of Measurement
Coal mines
located in the
coal- fields of
Jharia
Raniganj
Bokaro
Suspended Particulates
Matter (SPM)
Annual
Average*
24 hours**
500 µg/m3
700 µg/m3
High Volume Sampling
(Average flow rate not less
than 1.1 m3/minute)
Respirable Particulate
Matter (size less than 10
µm) (RPM)
Annual
Average*
24 hours**
250 µg/m3
300 µg/m3
Respirable Particulate
Matter sampling and
analysis
Sulphur Dioxide (SO2) Annual
Average*
24 hours**
80 µg/m3
1.Improved West and Gaeke
method
2.Ultraviolet fluorescence
Oxide of Nitrogen as NO2 Annual Average*
24 hours**
80 µg/m3
120 µg/m3
1.Jacob & Hochheiser
Modified (Na-Arsenic)
Method
2.Gas phase Chemilumine-
scence
Note: * Annual Arithmetic mean for the measurements taken in a year, following the guidelines for frequency of sampling laid
down in clause 2.
** 24 hourly/8 hourly values shall be met 92% of the time in a year. However, 8% of the time it may exceed but not on two
consecutive days.
Unauthorised construction shall not be taken as a reference of nearest residential
or commercial place for monitoring.
2.6 AIR POLLUTION IN COAL MINING AREAS
Mining is one of the core sector industries, which plays a major and crucial
role of the process of country’s economic development but the environmental impact
of coal mining cannot be ignored (Singh et al., 1996; Chaulya and Chakraborty, 1995;
Wahid et al., 1995; Huchabee et al., 1983) and coal based industries may be
conveniently listed as the major polluters (Krishnamurthy, 2004). Coal mining, its
processing and utilization gives rise to air pollutants, particularly suspended and
respirable particulate matter. Operation of excavators, transporters, loaders, conveyer
belts, etc., result in massive discharges of fine particulates, which depends on
individual sites due to difference in geology, mineral, terrain and many other factors.
The extraction stage primarily produces larger particles with limited dispersion, which
have major effects on mineworkers and occasionally on local residents. Similarly,
operation of primary and secondary crushers in sizing the coal, handling and storing
of crushed coal, operation of screens, dispatching of washed coals, etc. all are
Chapter 2 Literature Review
27
expected to create degraded air quality in the surrounding area. Further, activities of
captive power plants including the discharge through stack within the mining complex
also create lots of air pollution problems in the locality.
Besides, PM, it also give rise to gaseous pollutants, such as, SO2, NOx and CO
and HC etc. The main sources of SO2 are the burning of sulphur containing fuel and
operation of diesel powered vehicles (Michal, 1990). NOx are formed in power
stations, automobile exhausts, burning of coal and refuse and in the use of explosives.
CO is produced from burning of fuel, automobile exhaust, furnaces and power
stations. These large scale mechanized opencast coal mining is associated with safety
and health hazards and associated negative effects on working efficiency through poor
visibility, failure of equipment, increased maintenance cost and lowering of labour
productivity (Prabha and Singh, 2006). The coal mining environment has been
deteriorated at a faster rate due to the enhancement of coal production in recent past.
Determination of the exposure to respirable dust among coal miners will help to
investigate relationships between such exposure and respiratory diseases (Naidoo et
al., 2006; Mukherjee et al., 2005; Donoghue, 2004).
Out of the various components of air pollution, dust problem seems to be
alarming. Mining process generates dust in every stage of its operation, i.e., drilling,
blasting, loading, transportation, washing, etc. The operational study carried out at
Korba Coalfield (Singh and Puri, 2004) reveals that drill operators are exposed to the
highest levels of dust followed by coal handling operators, pay loaders and feeder
breeder operators. SPM, the major threatening component in mining areas, is capable
of causing harm through a number of adverse impacts (Agarwal & Agarwal, 1994;
Sengupta, 1988). Jha and Kumar (2003) conclude that most importance needs to be
given on finer dust particles, i.e., respirable particulate matter as these can cause
significant health impact also emphasizes the need of accurate measurement of the
finer parts of dust as it behaves like gas molecules. Haul road seems to be the major
sources of dust emission in mine areas (Pathak, 2004; Chaulya et al., 2002). A study
conducted by Tan (1984) and Chadwick et al., (1987) reveals 5% and 25% of coal
dust generation during the dumper movement on unpaved haul roads and
Chapter 2 Literature Review
28
loading/unloading of dumpers respectively. It has been estimated that 10-100 gm of
dust having 5µm size is being produced per ton of coal production. These particles
can be suspended for a few seconds to several months.
Study conducted by Sharma and Singh (1992) in Tilaboni, Nakrakonda and
Jhanjhra block of Raniganj coalfield reported that open storage of coal in large
quantities responsible for higher dust fall rate in Nakrakonda colliery and
concentration levels of SPM in work zone were found much higher than their
corresponding level in ambient air. Similar study conducted by. Reddy and Ruj (2003)
in Raniganj-Asansol area also reported higher concentration of SPM (exceed the
norms set by CPCB) while below the standard for SO2 and NOX. D. Mal (1996)
recorded higher concentration of SPM, (80 to 406 µg/m3) at different locations of
Nandini mines in Chattisgarh, while for SO2 and NOX concentration varies from 7.8
to 26.7 µg/m3and 30.2 to 86.9 µg/m
3respectively.
Study conducted by various researchers (Ghose, 2002; Banerjee and Hussain,
1989; Sahoo, 1981) in Jharia coalfield reported higher SPM concentration exceeding
permissible limits. Kumar and Ratan (2003) found higher SPM concentration at
different zones viz., dust generating zone, non dust generating zone and residential
zone. Same result of higher SPM in residential and rural area were found by Sinha
and Sreekesh (2002) in mining Belt of Goa. A study for assessment and management
of air quality was carried out in the Ib Valley area of the Ib Valley coalfield in Orissa
state, India. The 24 h average concentrations of TSP, PM10, SO2 and NOx were
determined at regular intervals throughout one year at twelve monitoring stations in
residential areas and six monitoring stations in mining/industrial areas. The 24 h
average TSP and PM10 concentrations were124.6-390.3 µg/m3 and 25.9–119.9 in
µg/m3 in residential areas, and were 146.3–845.2 µg/m
3 and 45.5–290.5 µg/m
3 in
industrial areas. The air quality of Angul-Talcher area is deteriorated significantly due
to coal mining, thermal power plants, NALCO smelter and other allied activities.
Frequent movement of vehicles in this industrialized area caused significant air
pollution load to this area. Excess air pollution load considerably deteriorates the air
Chapter 2 Literature Review
29
quality and subsequently responsible for harmful consequences of the exposed
population (Suman et al., 2007).
As the production of coal by opencast mining is growing, it is essential to
evaluate its impact on the air environment and also to assess the characteristics of the
emitted airborne dust, which is harmful to human health.
2.6.1 Characterization of Particulate matter
Particle size is considered the most important parameter in characterizing the
physical behavior of particulate matter, as it affects removal processes, atmospheric
residence times and contribution of light scattering to visibility degradation. Particle
size is typically defined in terms of its diameter. Although liquid aerosol particles are
nearly always spherical but solid particles are often irregular in shape (Seinfield,
1986). Characterization of Airborne PM is very important because it consists of many
organic and inorganic compounds with a variety of size (Cheng and Lin, 2010).
Different sizes and compositions of particles cause different adverse health effects
and long-term exposure to high levels can cause significant risk to human health (Ny
and Lee, 2011).
Larger sizes are easy to eliminate from the respiratory system through
coughing, sneezing and swallowing, while particles less than 5 µm can reach the
pharynx tract. There have been a few studies to evaluate the association between the
size distribution of particulate matter and elemental concentrations in urban areas
(Fang et al., 2000, 2006). In the past, some researchers in Europe and Asia have
analyzed the size distribution of heavy metals in TSP and roadside environments.
Espinosa et al. (2001) and Allen et al. (2001) studied size distribution of metals in
urban area. In recent years, more importance has given on particulate matter of size
2.5µm (PM2.5) as reflected by a growing number of studies of this fraction, including
not only the measurements of its concentration but also the determination of its
chemical content (Yatkin and Bayram, 2008; Sudesh and Rajamani, 2006; Viana et
al., 2006; Wu et al., 2006;Braga et al., 2005; Fang et al., 2005; Giugliano et al., 2005;
Hueglin et al., 2005; Lonati et al., 2005; Viana et al., 2005). Fine particles with a
diameter less than 2.5 or ultra-fine particles can travel deep into the lungs with the
Chapter 2 Literature Review
30
potential to penetrate tissue and undergo interstitialization (GradeASteel, 2011). Fine
particles are not easily removed and can be deposited on the respiratory tracks from
the body, causing lung and heart problems, particularly if the particles contain toxic
materials. During the characterization of the fugitive dust, Organiscak and Reed
(2004) conclude that the unpaved mini haulage roads generate dust particle of all
sizes. At least 80% of the air borne dust generated by haul trucks is larger than 10 µm.
In fact, the chemical composition represents a key tool for understanding the origin of
particles, anthropogenic and/or natural, and for characterizing the atmospheric
processes in which they are involved (Karar and Gupta, 2007; Braziewicz et al.,
2004).
2.6.2 Influence of Meteorology on air pollution
The linkage between meteorological factors (wind speed, wind direction,
temperature, relative humidity, etc) and air pollutants are very old (Rajkumar and
Chang, 2000).Several cases occurred in past (1940’s, early 1950’s and 1986) in US
and Europe and India (Bhopal, 1984). There are several incidents of air pollution took
place in past they are as following- Donora (Harold et al., 1949), Nashville (Turner,
1961), Stockholm (Bringfielt, 1971), Bangi, Malaysia (Sani, 1987), California (Chow
et al., 1998), Turkey (Tayanc, 2000), Ahmedabad, India (Lal et al., 2000), Hong Kong
(Chan et al., 1998; Chan and Kwok, 2000), and Phoenix, AZ (Ellis et al., 1999, 2000).
� Donora, PA (1948) combination of particles and gaseous pollutants, lead to
the formation of thermal inversion layer in the lower atmosphere, which
prohibit the mixing of pollutants. Hence air pollution accumulated to such
levels that several thousand people become ill, many required hospitalization
and twenty died (Nebel and Wright, 2000; Kupchella and Hyland, 1989;
Battan, 1966; Hoecker, 1949).
� London (1952 and 1956) due to the mixing of smoke and fog in the
atmosphere, leads to death of several thousand people and it occurred due to
calm condition of the atmosphere which leads to poor dispersion of pollutants
by the wind. Because of the cold, residents of London began to burn more coal
than usual. The resulting air pollution was trapped by the heavy layer of cold
Chapter 2 Literature Review
31
air, and the concentration of pollutants built up dramatically. The smog was so
thick that it would sometimes make driving impossible. During winter, flow of
wind in the opposite direction (anticyclone condition) and the wind’s low
velocity (calm) held accumulated gases, ash, and unburned coal suspended in
the atmosphere (Battan, 1966; Kupchella and Hyland, 1989).
� Ukraine (26 April 1986) the disaster that took place is known as Chernobyl
disaster, it was a nuclear accident that occurred at the Chernobyl Nuclear
Power Plant in Ukraine (officially Ukrainian SSR), It is considered the worst
nuclear power plant accident in history. An explosion and fire released large
quantities of radioactive contamination into the atmosphere, which spread over
much of Western USSR and Europe and is one of only two classified as a
level 7 event on the International Nuclear Event Scale (the other being the
Fukushima Daiichi nuclear disaster)(Richard, 2011) .The battle to contain the
contamination and avert a greater catastrophe ultimately involved over
500,000 workers and cost an estimated 18 billion rubles, crippling the Soviet
economy (The battle of Chernovyl) .
� Bhopal, India (2-3 Dec.1984) a disaster took place in the night at the Union
Carbide India Limited (UCIL) pesticide plant in Bhopal, Madhya Pradesh,
India. A leak of methyl isocyanate gas and other chemicals from the plant
resulted in the exposure of hundreds of thousands of people leakage of MIC
from Union carbide factory known as Bhopal Gas Tragedy, considered as one
of the world's worst industrial catastrophes,(Bhopal trial, 2010, BBC News).
The official immediate death toll was 2,259 and the government of Madhya
Pradesh has confirmed a total of 3,787 deaths related to the gas release
(www.mp.gov.in). A government affidavit in 2006 stated that the leak caused
558,125 injuries including 38,478 partial and approximately 3,900 severely
and permanently disabling injuries.
Thus, prevailing wind direction has a certain role on the transport and
dispersion of dust particle (Aldrin and Haff, 2005; Wise and Comrie, 2005;
Marcazzan et al., 2002). Wind erosion also catalyses the process of dust generation
Chapter 2 Literature Review
32
(Sabre et al., 2000). Ghosh and Banerjee (2006) concludes that the actual contribution
of pollutants to air quality from opencast mining and their dispersion to the
surrounding locations can be successfully evaluated by factal analysis technique
where meteorological parameters (specially wind speed and wind direction) plays
crucial role. There is a strong seasonality in the meteorological factors that modulate
air quality levels (Espinosa et al., 2004). Ragosta et al., (2006) reported in their study
that correlation structures of metals vary under the condition of low relative humidity
and high wind speed and vise versa. The results agree with the spatial distribution of
the possible heavy metal industrial sources. Under mild wind speed a systematic
decrease of particulate matter concentration was also observed by Chen et al (2008) in
an industrial area of Sanghai, China.
2.6.3 Source Apportionment Study
Particulate matter originates from various natural and anthropogenic sources,
namely: resuspended surface dust, combustion of fossil fuels, windblown soil and
mineral particles, volcanic dust, sea salt spray, biological material such as pollen,
spores and bacteria and debris from forest fires etc, and traffic. From a toxicological
point of view, the most important particles are those with a diameter <10 µm (PM10),
so-called respirable fraction, which penetrate the human respiratory system deeply. It
is well established that fine particles (smaller than 2.5 µm) penetrate the pulmonary
region and tend to deposit in alveoli (WHO, 2000) causing adverse health effects
leading to pulmonary and respiratory diseases. anthropogenic activities sources like
Metallic elements originate from different anthropogenic sources and are associated
with different particles fractions. Those emitted during the burning of fossil fuels, i.e.,
V, Co, Mo, Pb Ni and Cr (Pacyna, 1986) is mostly associated with particles smaller
than PM2.5. As, Cr, Cu, Mn and Zn are released into the atmosphere by metallurgical
industries (Alastuey et al., 2006; Querol et al., 2001; Pacyna, 1986), and traffic
pollution involves a wide range of trace element emissions that include Fe, Ba, Pb,
Cu, Zn, and Cd (Birmili et al., 2006;Pacyna, 1986), which may be associated with the
fine and coarse particles.
Chapter 2 Literature Review
33
The geological distribution of As is varied in individual coal basins and exist
both in organic and inorganic form. Previous studies shows that most of As in coal is
associated with pyrite, most commonly as As rich inclusions in the pyrite lattice
(Coleman and Bragg, 1990) but sometimes associated with clay minerals, phosphate
minerals (Swaine, 1990) and arsenic minerals including orpiment realgar and
arsenopyrite (Ding et al., 2001). The world average As content of bituminous and
lignite are 9±0.8 and 7.4±1.4 ppm respectively whereas Mercury in coal is 0.1±.01
ppm. Several study conducted by various researches are given below
2.6.4 Aerobiological Study
Depending on physicochemical characteristics and the degree of pollution, air
can condense, disperse or carry many harmful agents such as aerosols, organic
particles, viruses, bacteria, fungi and volatile substances. This particulate matter can
adversely affect both human health and air quality standards (Macher et al. 1999).
Aerobiology deals with the study of airborne particles of biological origin including sources,
liberation, dispersal, deposition and impact on other living organisms and the effects of
environmental conditions on each of these processes (Reanprayoon and Yoonaiwong,
2012; Main 2003). Exposures to outdoor allergens are important in the development of
allergic disease. Understanding the role of outdoor allergens requires knowledge of
the nature of outdoor allergen-bearing particles, the distributions of their source, and
the nature of the aerosols (particle types, sizes and dynamics of concentrations) The
exposure to spores causing health problems is usually assessed by determining the
concentration of spores per cubic meter of air (CFU/m3). Particles of 10 µm are deposited
easily into the bronchial tree and are associated with immediate hypersensitivity responses,
while particles of 2.5 µm or less have the capacity to penetrate into the smaller airways and
are associated with delayed hypersensitivity mechanisms (Horner et al. 1995; Macher et al.
1999). An estimated 300 million persons suffer from asthma around the world. The Program
on Global Initiative for Asthma (GINA) suggests that this number increases each year. The
National Institute for Allergy and Infectious Diseases (NIAID) in the United States indicates
that more than 17 million people have been diagnosed with asthma; thus asthma is the sixth
most common chronic disease, affecting more than 4.8 million children.
Chapter 2 Literature Review
34
The association between airborne fungi and symptoms of respiratory allergy
and asthma is now well established (Malling, 1986; Strachan, 1988; Garrett et al.,
1998). More than 80 genera of fungi have been reported to be associated with
respiratory tract allergy (Latge and Paris, 1991; Horner et al., 1995) and more than
100 species of fungi are involved with serious human and animal infections and many
other species cause serious plant diseases (Cvetnic and Pepeljnjak, 1997).Sensitization
to fungal allergens is sometimes associated with life-threatening asthma (Black et al.,
2000) and death (Targonski et al., 1995). An important concern for the past studies on
the airborne fungi around the world is, most of the reports dealt with the urban and
sub-urban areas. Detailed long-term aerobiological studies in coal mining area are
largely lacking. However, the rural agriculture based areas are reported to carry higher
airborne load of fungal allergens and farmers are reported to get longer exposure of
outdoor airborne fungi compared to the people of all other professions.
2.6.5 Air Dispersion Modeling and Air Quality Indexing
Air quality dispersion modeling is a computer simulation that predicts air quality
concentrations from various types of emission sources (point, area and line). It
uses meteorological data such as temperature, mixing height, wind direction and
wind speed to calculate concentrations. In coal mining area fugitive dust generated
by various processes like drilling, blasting, overburden loading and unloading,
coal loading and unloading, road transport over unpaved roads and losses from
exposed overburden dumps, coal handling plants and exposed pit faces (Huertas,
2012). Temporal and spatial variation of surface level TSP and PM10
concentrations to assess the impact of the mining operations on air quality in the
region and identify areas within the mining region that should be classified as
highly, fairly and moderately polluted based on national legislation.
Transportation of materials has been identified as the main source of TSP and
PM10 pollution (Huertas et al., in press; Trivedi et al., 2009; Chaulya, 2004; Ghose
and Majee, 2000; Cowherd, 1988). TSP and PM10 in open pit mining regions
reduce air quality and can cause silicosis, black lung (CWP) and increased
mortality. They also reduce visibility and affect surrounding flora and fauna
Chapter 2 Literature Review
35
(Wheeler et al., 2000; NIOSH, 2005). Holmes and Morawska (2006) conducted a
review of the different particle dispersion models available, including Box,
Gaussian, Lagrangian/Eulerian, CFD and aerosol dynamic models. They
concluded that the major weakness in particle dispersion modeling was a lack of
validation studies that compared the predicted and actual values. Chaulya et al.
(2002) compared FDM (Fugitive dust model) and PAL2 (point, area and lines
sources model) during a winter season in a coal mining region in India. They
found a coefficient of correlation (R2) of 0.66 for PAL2 and 0.75 for FDM when
experimental data from 3 high volume samplers was compared with model results.
Trivedi et al. (2009) modeled TSP using FDM and obtained an R2of 0.71 using
data from 5 monitoring stations. This information would enable the environmental
authority to implement new decontaminating measures based on the pollution
classification. Also, the results of the study could be used to estimate the
contribution of each mine to the pollution in each population center within the
mining region, thereby allowing the environmental authority to determine the
appropriate contribution of each mining company toward financing
decontamination measures. As of December 2006, the American Meteorological
Society (AMS)/U.S. Environmental Protection Agency (EPA) Regulatory Model
with Plume Rise Model Enhancements developed by the AMS/EPA Regulatory
Model Improvement Committee (AERMIC) replaced the Industrial Source
Complex Short Term Version 3 (ISCST3) dispersion model as the EPA preferred
regulatory model. AERMOD accounts for several PBL effects not accounted for
by ISCST3 (Faulkner et al., 2008). Perry et al.(2005) compared several existing
air dispersion models in terms of modeled and observed concentration
distributions and concluded that with few exceptions the performance of
AERMOD is superior to that of the other applied models.