Effects Of Barapukuria Coal Mining On Environment Environmental Sciences Essay

The over increasing gap between supply of and energy is problem for many countries around the world. Governments are forced to examine different sources of energy in an attempt to create secure energy supply. The results of these examinations cover a large range of energy sources, not only traditional ones such as oil and gas, also nuclear-power and renewable resources. In addition governments are looking at increasing energy efficiency Because of the pressing need; there has also been a strategic shift in some countries back to using traditional fossil fuels. This has become more prevalent and widespread in developing countries where coal is the most dominant of traditional options used. There are two key reasons for this choice: first, there is abundant supply of coal; it is one of the cheapest ways to create electricity (Jaccard, 2005).

The resurgence coal as an energy source may come as a shock to some because of environmental impacts it has had in the past .However, some countries that have remained dependent on coal for energy, such as the United States, have mitigated the environmental impacts with new technologies stringent regulation. The economic development of the country requires different types of fuels and energy. Because of deforestation, supply of traditional fuels are decreasing and becoming expensive day by day. Significant portion of export earning is being used for import of petroleum products and coal (Hamilton 2005).

The key to creating reliable sources of energy is diversification. Since there are significant reserves of coal located in the northwest region of the country, and a belief within industry that further exploration may lead to the discovery of additional coal fields, this is a source of energy to consider. However turning to coal brings important concerns of policy makers, particularly about how to balance coal development with environmental concerns. The total national reserves of coal in 5 coal fields are estimated about 2.9 billion metric tons. Recovery rate of coal from reserves depends on the availability of technology and method of mining. Modern mining technology can ensure up to 85% recovery of coal from different reserves (Hamilton, 2005).

Coal is a very important but dirty fossil fuel. Coal mining has severe environmental, ecological, human-health consequences. If not done properly, coal mining has potential to damage landscape, soils, surface water, groundwater, air during all phases of exploration and use. Coal mining has some unavoidable negative impacts on humans and the environment. In its review of the mining industry of Bangladesh, the U.S. Geological Survey states that the country has “small reserves of coal, natural gas, and petroleum”. In May 2011, the country’s overall coal production was around 3,000 tons a day, from the lone operational state-owned Barapukuria coal mine in Dinajpur. There are five coal field discovered such as Khalashpeer, Rangpur (1995) coal field depth at 257-483 meter which is about 12 Km2 in area and proven reserve coal is 143 (GSB), 685 (Hosaf) in million tones. Phulbari, Dinajpur (1997) coal field which is about30 Km2 in area and depth at 150-240 meter and reserve coal is 572 million tones. Jamal gong, Jaipurhat (1965) coal field which is about 16 Km2 in area and depth at 900-1000 meter and proven reserve coal is about 1050 million tones .Dighirpar, Dinajpur (1995) coal field is at 327 meter depth and area not yet to known and reserve coal is about 200 (partly evaluated) million tones. The major findings were as under about Barapukuria, Dinajpur Coal Field Reserve of coal 390 Million tones, Depth of coal is 118-509 meter, Nos. of coal layer is 6, Average thickness of coal seam is 36 m, Composition of coal: ash 12.4%, Sulphur 0.53%, Moisture 10%, Rank of coal is Bituminous (high volatile), Calorific value of coal is 25.68 MJ/KG (11040 BTU/lb), Yearly Production is 1 million tones, Coal extraction method is Multi-Slice Long wall, During development of Barapukuria Coal Mine as well as load testing /trial run , coal as obtained from the mine, on the chemical analysis, confirmed composition of coal, Rank of coal and Calorific value of coal as predicted (Petrobangla, Govt. Bangladesh, 2005).

The state-owned company, Bangladesh Oil, Gas and Mineral Corporation, which is commonly known as Petrobangla, is involved in oil and gas exploration, production, and distribution. It is also “involved in the exploration for and production of such minerals as coal, granite, and limestone for the manufacture of cement”. Nearly half the Bangladeshi population is food insecure, and nearly one quarter severely food insecure. Local food production should be strengthened, not sacrificed for industrial projects,” said the Special Rapporteur on the right to food, Olivier De Schutter. The land under threat is located in Bangladesh’s most fertile agricultural region where production of staple crops such as rice and wheat allows subsistence farmers to feed their families, and supports the entire country’s food needs. In addition to the destruction of agricultural land, waterways supporting over 1,000 fisheries and nearly 50,000 fruit trees may be destroyed. The water table may be lowered by 15-25 meters over the life span of the mine. “Access to safe drinking water for some 220,000 people is at stake,” stated Catarina de Albuquerque, the Special Rapporteur on the human right to safe drinking water and sanitation. The mine would cause noise and dust pollution through dynamite explosion. Coal dust will pollute the air. Water will be polluted from washing the coal, risking pollution of surrounding water bodies. Bangladesh has networks of hundreds of small rivers, meaning that water pollution in one area can spread over a large area (Petrobangla, Govt. Bangladesh, 2005).

To prevent the mine from flooding, huge pumps would run 24 hours a day for the 30 years of the mining project, pumping up to 800 million liters of water a day out of the mine. Groundwater in an area covering about 500 square kilometers would be lowered. Wells would no longer provide enough water for farmers. Asia Energy’s solution is to distribute the water pumped out to farmers. Once the mining is finished, Asia Energy plans to create a huge lake, providing fresh water, fisheries and recreation, according to the company. But after 30 years of digging, the water will be toxic. As the civilization has advanced tremendously over the last century, the alternative source of power generation came in effect like nuclear power, which certainly replaced coal in the west. Assessing the coalmine and its versatile impact over the industrial revolution time, the researcher, end of the 20th century revealed that there is huge risk of health, potential air pollution, noticeable change in landscape, political and social problem, overall sustainability of the environment could get seriously affected by coal mine operation. Therefore, it is obvious that an assessment of the local environment should go prior and along the project of Barapukuria before any unexpected consequence over whelms this project. Energy is vital element of our daily lives, no matter where one lives (Petrobangla, Govt. Bangladesh, 2005).

Regionally, the Barapukuria coal basin is located in the Dinajpur Shield of Bangladesh and is surrounded by the Himalayan Fore deep to the north, the Shillong Shield/Platform to the east, and the Indian Peninsular Shield to the west. The geologic and structural conditions of the basin were illustrated in details by Islam and Hayashi (Khan, 1991; Khan and Chouhan, 1996; Alam et al., 2003; Islam and Hayashi, 2008a; Islam et al., 2009).

Structurally, the Barapukuria basin is a long, narrow, and shallow Permo Carboniferous rift basin. The basin trends approximately north-south for over 5 km, ranges from 2 to 3 km wide, and is over 550 m deep. Below a prominent unconformity, covered by an unstructured Pleistocene through Tertiary classic sequence, steeply dipping normal faults bound tilted half graven fault blocks. The northern, western, and southern boundaries of the basin are also truncated by several small-scale normal boundary faults. The faults and igneous dyke decrease the cohesion and friction angle and reduce the shear strength through fault plane and filling materials. The overall structures of the Barapukuria Basin imply a tectonically active highly disturbed zone (Wardell Armstrong, 1991; Bakr et al., 1996; Islam, 2005; Islam and Hayashi, 2008a; Islam et al., 2009).

The Barapukuria half-graven basin is assumed to be related to its tectonic origin. The basin area is very close (about 200 km) to the convergence boundary of the Indian and Eurasian plates. As a consequence, the far field tectonic stress field is highly significant to the structure of this basin. A 5 km long Eastern Boundary Fault of the Barapukuria basin is the best structural evidence for recent tectonic activity. However, the basin geometry and its stress field are directly related to the tectonic displacement gradient. Usually, the Barapukuria type intracrationic half graben basin in a convergent regime is developed due to local crustal weakening, where archeology strongly affects the dynamics of basin formation (Buck, 1991; Cloetingh et al., 1995).

In a gross sense, for the Barapukuria type half graben basin, displacement is greatest at the center of the fault and decreases to zero at the fault tips. The displacement of an initially horizontal surface that intersects the fault is greatest at the fault itself and decreases with distance away from the fault . This produces footwall uplift and hanging wall subsidence, the later which creates the sedimentary basin (Gibson et al., 1989; Contreras et al., 1997).

It is apparent that the basin geometry is affect-ted by fault propagation and displacement is accumulated on the boundary fault. About 200 m vertical displacement occurred with 73oC dipping. Along the basin the fault length is about 5 km. The fault length: vertical displacement ratio is about 25:1. About 60 m horizontal displacement indicates recent tectonic activity and the basin is developed due to 60 m horizontal displacement of the boundary fault towards the east (Islam et al., 2009).

The objectives of the research were:

To know the chemical properties of the of the coal, coal water and nearby agriculture field and

To know that whether these chemical parameters are polluting the environment of the area or not.

Chapter 2

Review of Literature

Global Coal Management policy continued to wait for approval from the Government for its Barapukuria coal project’s plan of development. The project’s environmental impact and feasibility studies had been completed, and mining operations could be done by open pit method. After coal preparation, the final product would be coking coal and thermal coal for both export and domestic use. The bituminous coal resource of 572 million metric tons was large enough for the mine to last more than 30 years at a mining rate of 15 Mt/yr. There are major environmental issues in the mining of coal that include land disturbance, water pollution, and impacts on air quality (World Coal Institute, 2007).

There are number of environmental issues linked to both underground and surface mining and they concerns mostly the impacts on water and air quality. First acid mine drainage (AMD). It is caused by the “oxidation of pyretic sulphur due to exposure of pyrite (FeS2) to air and water, it can cause acidity (or a decrease in the pH of water) and subsequent elevated concentrations of metals that are associated with sulphide mineralogy” (Management Brent, 2005).

AMD causes contamination if it gets into the water system. A second environmental concern related to mining is the leaching of metals into the water in the area. AMD and leaching of metals result in fish dying and negatively impact the plant life in the water .A third concern is the emissions of particulates from the mining process that degrade air quality. The primary causes of these particulates are dust due to the movement of vehicles used at all stages of the mining process. A fourth concerns is methane. Methane is a potent greenhouse gas released from the coal seams. Technology has been developed that captures and uses methane for heating or electricity generations (The Coal Authority, 2007). As of 1994, the Ministry of Environment and Forest (MoEF) requires that Environmental Impact Assessments (EIA) be completed (Rajaram et al., 2005).

These EIA consist of a two-stage clearance. First, a site clearance, followed by an environmental clearance. The complete process includes the following components: screening; scoping and consideration of alternatives; base line data collection ;impact prediction; assessment of alternatives; outlining of mitigation measures and an environmental impact statement; public hearings; environmental management plan; decision making; and monitoring (MoEF, 2001).

In addition to conducting an EIA prior to operations, environmental statements must be submitted on an annual basis. Guidelines for reclamation activities are supplied under the EIA process, and reclamation is expected to proceed concurrently with mining operations. Although the planning of mine closure and reclamation is recognized as important, and thus should be incorporated into the mining plan, in India this is still at the “embryonic stage” (Rajaram et aI., 2005).

The permission of the surface landowner must be sought prior to leasing of the subsurface minerals. There are two main options to obtain this consent: through written consent from the surface owner or a bond posted by the mine operator to cover any damages that might occur to the surface of the land (Hamilton, 2005).

Evaluation of possible environmental impacts for Barapukuria thermal power plant and coal mine: In this study, an attempt was taken to conduct environmental impact assessment of Barapukuria thermal power and coal mining project through environmental, socio-economical and meteorological study. The analysis showed that, the Mn concentration was found in the satisfactory range. The pH was found slightly alkaline and surface water was bacteria contaminated. SO4 concentration was in the range of WHO standard. Calculated Sox loading was almost same of monitored emission. Corresponding estimated concentration of Sox was in acceptable range, which may not bring any matter of concern. In the study, an attempt was also made to evaluate the health impacts of SPM (suspended particulate matter) emitted from the combustion of coal in the power plant. The socio economic condition was also considered a dominating factor, for the EIA along with the chemical parameters since increased employment for the project (Alam et al., 2011).

Analysis of orientation of maximum horizontal tensional stress of the Gondwana Barapukuria coal basin, NW Bangladesh: By means of finite element modeling: This paper uses two-dimensional Finite Element Method (FEM) numerical modeling to analyze the orientation of maximum horizontal tensional stress of the Barapukuria coal basin in Bangladesh. An elastic plane stress model incorporating elastic rock physical properties for the coal basin area was used consisting of 2916 elements with a network of 1540 nodes (Md.Rafiqul Islam, 2009).The stress field at any point of the model is assumed to comprise gravitational and tectonic components. The tectonic component is assumed to act entirely in the horizontal plane in the far-field and at the model eastern boundary. Modeling results are presented in terms of four parameters, i.e. orientation of maximum horizontal tensional stress, displacement vector, strain distribution, and maximum shear stress contour line within the model. Results show that the orientation of the maximum horizontal tensional stress axis is almost N45oE, which coincides with the regional stress field as studied by Gown et al. (1992).

Coal mining impact on land use/land cover in jainta hills district of Meghalay, India using remote sensing and GIS technique: K. Sarma and S.P.S. Kushwaha conducted their study was undertaken to analyze the process of human-induced landscape transformation in the coal mined affected areas of Jaintia Hills district of Meghalaya, northeast India by interpreting temporal remote sensing data using geographic information system. The study revealed that most of the areas were dominated by grassland/non- forest in all the time sequence period of the study.

Impact of surface coal mining on three Ohio watersheds ground water chemistry: Bonta et al. (1992) conducted a study to determine the effects of surface mining and reclamation on ground-water chemistry in three saturated zones in each of three small East Central Ohio water-sheds. The extensive disturbances of mining and reclamation: i) caused more changes in constituent’s concentration in the upper zone than the lower zone. Most of which were statistically significant increases, ii) affected ground-water chemistry in lower zones – those that were not physically disturbed, iii) tented to increases the frequency of exceedance of regulated constituents in all saturated zones and (4) affected the chemistry of surface base flow water at the watershed outlets. Several constituents were still changing at the end of the project within all sites and zones (Anhaeusser and Maske, 1986).

Mine-water chemistry: the good, the bad and the ugly: The mine discharged water and wastes for several times. They collected huge amount of water samples from different mine discharge and worked on them. They found that the discharged water could be useful sometimes but most of the times the nature is ugly (Banks, 1997).

Trace elements emission factors from coal combustion: A research on increase in the mobilization of trace elements in the environment especially in the atmosphere. An accurate knowledge of factors related to the mobilization, particularly the enrichment mechanism of trace elements in the emitted particulate, is of fundamental significance for environmental impact assessment studies. In this work an analytical method is presented to calculate the trace element emission factors taking into account the enrichment of trace element (Cernuschi, 1987).

Trace metals from coal-fired power plants: Derivation of an average data base for assessment studies of the situation in the European communities. The potential impact on different part of the ecosystem and man from the release of trace element from the coal fired power plants, they use twenty nine coal samples for their research, using the derived main values as well as taking into account of coal to be burnet in power plant of EC. The average trace element mobilization was predicted for fifteen elements for the year 1990, the global release so estimated range from 66.5 to 19,420 metric tons from Hg Zn, respectively (Sabbioni, 1983).

Criteria for determining when a body of surface water constitutes a hazard to mining: Kendorsky et al. discussed that there are various criteria for determining the quality of surface water body. They worked hard in determining the water constituents that are exposed in mining activities (coal mining). The surface drainage (acid mine drainage, heavy metal contamination etc.) causes several environmental impact (Molinda, 1999).

Various research work carried out on hydrogen ion concentration and nutrient status in soil: Soil pH varied widely from one soil series to another. Soil pH ranged from 4.32 to 7.64 in 0 – 15 cm depth and the soil pH ranged from 4.55 to 7.81 in 15 – 30 cm at Sonatala series (Huq, 2005).

In dry season the soil pH of coastal areas of Bangladesh were recorded between 6.25 to 8.34 and in the wet season the soil pH of coastal areas were recorded between 5.74 to 7.96 respectively (Alam, 2004) The soil pH of Taras series under AEZ-5 ranged from 5.54 to 5.90 and the pH of Jaonia series were ranged from 4.82 to 6.09 under AEZ-6. Both of the series were in acidic in nature (Alam, 2005).

The pH of the old Brahmaputra Floodplain soil ranged from 6.02 to 7.10 and that of Madhupur tract from 6.99 to 7.02 under different cropping patterns and tillage (Hossain et al., 2003).The optimum soil pH for crop production was considered to be between 6.5 to 7.0 (Tisdale et al., 1999).

The pH of the soil class high land and medium high land under soil series Amnura was 4.2 to 5.7 and 4.7 to 6.3 respectively in upland which was acidic than wet land (SRDI, 1999). The soil pH of the high, medium high and medium low under Sathi upazila ranged from 7.4 to 7.9, 7.3 to 7.6 and 5.0 to 7.8 respectively (SRDI, 1992).

The organic carbon content of soil at Sonatala series ranged from .58% to 1.08% in 0 to 15cm depth the organic carbon content of soil at the same series ranged from 0.58% to 0.89% in 15 to 30cm (Huq (2005). The organic matter content of soil of the Taras series under AEZ-5 ranged from 1.26% to 2.42% and the organic matter content in the Jaonia series were ranged from 1.68% to 2.52% under AEZ-6 (Alam, 2005).

In the dry season the organic matter content of the coastal area of Bangladesh was recorded at the ranged between 0.29 to 1.08% and in the wet season the organic matter content in the same areas were ranged from 0.34 to 1.27% respectively (Alam, 2004).

Organic matter values of the old Brahmaputra floodplain ranged from 0.64 to 1.77% and that of Madhupur tract from 0.21 to 1.69% under different cropping patterns and tillage’s (Hossain et al., 2003).The organic matter content of high land, medium high land and medium low land under Singra upazila values from 1.31%, 1.89% and 2.59% respectively (SRDI, 2001a). The organic matter content of high land, medium high land and medium low land under Madhupur upazila values from 2.45%, 1.24% and 2.31% respectively (SRDI, 2001a).

The organic matter content in varied from 0.58 to 2.13% of BAU Agriculture farm and also found that the organic matter contents were relatively higher at the surface layer but decreased at soil depth (Mondol, 1998).The organic matter content varied from 0.79 to 2.35% in ten selected soil series of Bangladesh and also observed that the organic matter contents relatively higher at the surface but decreased at soil depth (Fakir, 1998).Present organic Carbon of some non- irrigated soils of Madhupur upazila ranged from 0.5 to 0.85% (Zaman and Nuruzzaman, 1995).

The available P content ranged from 9.8 to 12.75ppm at 0-15cm in depth in Sonatala series and the same series the available P content ranged from 5.75 to 9.24ppm at the depth of 15 to 30cm (Huq, 2005). The available P content of the Taras series under AEZ- 5 ranged from 5.04 to 24.9 mg/kg and the available P content of the Jaonia series under AEZ- 6 ranged from 6.48 to 8.58 mg/kg (Alam, 2005).

Available P values of the old Brahmaputra floodplain soil varied from 7.0 to 20.0 µgg-1 under different cropping patterns and tillage’s (Hossain et al., 2003). The available P content ranged from 6.7 to 10.4 mg/kg in Barkol series, 8.0 to 11.9 ppm in khadimnagar series, 9.6 to 13.2 ppm in Subalong series, 13.9 to 16.2 ppm in Tejgaon series, 16.2 to 17 ppm in Belabl series, 10.1 to 17.4 ppm in Sonatala series and 11.9 to 17 ppm in Silmondi series (Ahamed, 2002).

The available P content of high land, medium high land and medium low land under Mymensingh Sadar upazila values from 32 µgg-1, 410 µgg-1 and 1150 µgg-1 respectively (SRDI, 2001a). The available P content of high land, medium high land and medium low land under Singra upazila values from 7.33, 7.20 and 60 µgg-1 respectively (SRDI, 2001a). Available P content of high land, medium high land and medium low land under Madhupur upazila values from 6, 5 and 8 µgg-1 respectively (SRDI, 2001a).

The available P content of the non-irrigated surface sub surface soil of Ghatail and Kalihati upazila were 4 to 4.2 ppm and 2 to 26 ppm respectively (Razzaque et al., 1998) The P content of high land, medium high land and medium low land under Shahzadpur upazila values from 7 µgg-1, 9 µgg-1 and 6 µgg-1 soil, respectively (SRDI, 1997). Available P contents in Soan River valley soils of lower Shiwaliks of Himachal Pradesh were 2.0 to 29.0 mg Kg-1 (Kumar et al., 1995). The P content of high land, medium high and medium low land under Sathi upazila values from 34µgg-1, 34 µgg-1 and 17 µgg-1 soil, respectively (SRDI, 1992).

The Exchangeable Potassium content ranged from 0.09 to 0.93me/l00gm soil at 0-15 cm depth in the Sonatala series and the same series the Exchangeable Potassium content ranged from 0.08 to 0.71me/l00gm soil at the depth of 15-30 cm (Huq, 2005). The Exchangeable K of the Taras series under AEZ-5 ranged from 0.14to 0.27cmol/kg soil and the Exchangeable K of Jaonia series were ranged 0.33to 0.50cmol/kg soil under AEZ-6 (Alam, 2005).

In dry season, the potassium concentration of coastal area of Bangladesh were recorded at the ranged between 0.20 to 1.17me/l00g soil and in wet season the potassium concentration of the same areas were recorded at the ranged between 0.08 to 0.83me/ l00g soil respectively (Alam, 2004). The available K content of the Brahmaputra flood plain soil varied from 0.10 to 0.27meq 100-1 soil and that of Madhupur Tract soil from 0.10 to 0.21meq 100-1 soil under different cropping patterns tillage’s and depth (Hossain et al., 2003).

The K content of high land, medium high land and medium low land under Singra upazila values from 0.27meq l00g-1 soil, 0.30meq l00g-1 soil, and 0.34meq l00 g-1 soil, respectively ( SRDI, 200la). The K content of high land, medium high land and medium low land under Madhupur upazila values from 0.21meq l00 g-1 soil, 0.13meq l00g-1 soil, and 0.16meq 100 g-1soil, respectively (SRDI, 200Ib).The K content of high land, medium high land and medium low land under Singra upazila values from 0.16meq l00g-1 soil, 0.19meq l00 g-1 soil, and 0.13meq l00g-1 soil, respectively (SRDI, 200Ic).

The exchangeable K of old alluvial soils of some basin was 0.04 to 0.87meq l00g-1 soil (Singh et al., 2000). The series with high clay content required higher level of exchangeable K than a sandy soil to reach the same concentration of soil solution (Ray chaudhuri and Sanayl, 1999). An experiment on some soil properties and found that the water soluble K positively and significantly correlated with exchangeable K (Yadav et al., 1999).

The available S content of the Taras series under AEZ-5 ranged from 16.8 to 17.8 mg/kg and the available S content of Jaonia series were ranged from 12.8 to 19.8 mg/kg under AEZ-6 (Alam, 2005). The available S ranged from 4.20 to 33.9 ppm at 0-15 cm depth in the Sonatala series and the same series the available S content ranged from 1.30 to 30.70 ppm at the depth of 15-30 cm (Huq, 2005). The available Sulphur (S) of soil decrease with increasing the depth of soils. The available S of the Old Brahmaputra Floodplain soil varied from 4.00 to 20.00 µgg-1 (Hossain et al., 2003).

A laboratory experiment conducted on selected ten soil I series and reported that the available S of Barkol, Khadimnagar, Subalong, Tejgaon and Belabo series ranged from 12.11 tol3.39 ppm, 11.55 to 13.85 ppm, 13.00 to 15.76 ppm (Ahamed, 2002).The S content of high land, medium high land and medium low land under Mymensingh upazila values from 16µgg-1, 16 µgg-1and 13 µgg-1 soil, respectively (SRDI, 200Ic).

The S status of the non-irrigated surface and sub-surface soils of Ghatail and Kalihati upazila were 2.5 to 47.5 and 2.0 to 30.00 mg/kg, respectively (Razzaque et al., 1998). The S content of high land, medium high land and medium low land under Shahzadpur upazila values from 13µgg-1, 23 µgg-1 and 7 µgg-1 soil respectively (SRDI, 1992).

The Exchangeable Ca2+ content ranged from 5.74 to 8.23me/l00gm soil at 0-15 cm depth in the Sonatala series and the same series the Exchangeable Ca2+ content ranged from 4.13 to 6.16 me/l00gm soil at the depth of 15-30 cm (Huq, 2005). The Exchangeable Ca content of the Taras series under AEZ-5 ranged from 5.50 to 14.7cmol/kg soil and the Exchangeable Ca content of Jaonia series were ranged 12.7 to 14.0cmol/kg soil respectively under AEZ-6 (Alam, 2005).

The exchangeable Ca content of higher land, medium high land and medium low land under Singra upazila values from 10.20meq l00g”1, 15.21meq l00g’l and 19.41meq 100g”! soil, respectively (SRDI, 200la). The exchangeable Ca content of higher land, medium high land and medium low land under Madhupur upazila values from 0.8meq l00/g, 1.3meq l00/g and 1.3meq l00/g soil, respectively(SRDI, 2001b).

The Ca content in non-irrigated surface and sub-surface soil of Ghatail and Kalihati upazila were 1.34 to 6.66meq l00/g and 1.9 to 5.62meq l00/g soil, respectively (Razzaque et al., 1998). Available calcium (Ca) content in some non-irrigated soils of Madhupur ranged from 0.37 to 3.73meq l00/g soil and the mean value was 2.52meq l00/g soil (Zaman and Nuruzzaman, 1995). The cation such as Ca2+ and Mg2+ at the concentrations of 0.68 to 1.98meq l00/g and 0.62 to 3.45meq l00/g soil, respectively (Matin and Anwar, 1994).

Exchangeable Mg content in the non irrigated surface and sub surface soils of Ghatail and Kalihati Thana were 0.53-1.35 and 0.5-1.16emol/kg respectively. Portch and Islam (1984) reported that 21% soils of Bangladesh contain Mg below critical level and 25% below optimum level (Razzaque, 1995).

Sewage sludge containing domestic wastes can have significant amount of Zn and Cu. The accumulation of Zn was found to affect microbial pollution in soils (McGrath et al., 1995). The range of available Zn content in some non-irrigated soils of Madhupur was 1.05-3.57 µgg-1and the mean value was 1.94µgg-1 (Zaman and Nuruzzaman, 1995).

The Fe status of some soils of Rajasthan (Udaipur district) was 1.32-20.5 ppm (Mehra, 1994). An observed that 8% soils of Bangladesh contain Fe below optimum level (Porch and Islam, 1984).

A general and specific investigation conducted across China soil and crop heavy metal contamination. He investigated Cd level in soil in contaminated areas throughout 15 provinces of the country. The results indicated that levels of Ch, Hg and Pb in soils were greater than the governmental standards. Cadmium ranged from 0.45 to 1.04 g/kg on average in the four cities and was as high as 145 mg/kg in soil (Wang et al., 2001).

An experiment conducted on the status of separate components of natural ecosystems in the impact zone of the Nizhnekamsk industrial complex in the Tatar Republic, Russia. It was found that the contents of heavy metals in soils and plants of the impact zone were low. However, negative effect of heavy metals on the growth of lichens was observed. Changes in the degree of moistening of the study the Nizhnekamsk industrial complex have resulted in the transformation of the plant cover structure (Changes in species composition of the grass dwarf shrub later, appearance of hygrophytes, increasing role of mesohydrophytes in the phytocenosis, and the decay of trees) and in changes of population characteristics of common red backed vole (Morozkin et al., 2001).

The total and available Pb concentrations of road dusts at city areas varied from 57.7 to 212 mg/kg and 0.030 to 2.03 mg/kg but from rural areas 6.2-1.7 mg/kg and 0.02-0.06 mg/kg, respectively. Usually, low Pb was observed from rural areas (Sattar and Blume, 1999).

An studied on 30 soil samples from different parent materials in Bangladesh to determine the usual range of the quantities of trace elements and reported that DTPA extractable copper and iron ranged from1.0 to 14.2 mg/kg and 7 to 296 mg/kg respectively (Khan et al., 1997). An investigation on incidence of heavy metals in the application of inorganic fertilizers to rice field. They found that soil surface horizon contains 1.83, 45.96, 55.80 and 20.35 mg/kg for Cd, Pb, Zn and Cu respectively (Gimeno et al., 1996). Slightly contaminated soils contaminated with 10-20 ppm Cu on average. He also reported that mean Cu concentration in paddy soils in about 12 ppm (Sattar, 1996).

Cabrera et al. (1995) describe a method for the direct determination of lead in irrigation and waste waters. The range of lead concentration in the samples tested ware 6.3-103.7 and 10.0-63.5 µg/ litre in irrigation water and waste water respectively. An increased metal uptake was commonly observed when certain levels of metals in the growth medium were exceeded. This is related mainly to Zn, Cd and Ni. They also mentioned that legumes were more promising for indicating soil pollution with metals than monocotyledonous plants, particularly cereals but under higher polluted conditions even the cereals respond to metal levels in the growth media (Pendias et al., 1993).

The heavy metals may cause soil pollution to a great extent by their accumulation. The heavy metals may be defined as the metals which show a specific gravity great than 4.5 g/cm3 (Market, 1993).An experiment conducted on Cadmium, iron, zinc, copper and nickel in agricultural soils of the United States of America. They found that the mean value of surface soils for Pb, Zn, Cu in the 11 agricultural production area of the USA are 10.6 mg/kg, 42.9 mg/kg respectively within the range from <1 to 135 mg/kg, <3 to 264 mg/kg, 0.6 to 495 mg/kg respectively (Holmgren et al., 1993).

The influence of soil properties on the distribution of zinc in polish soils and found that 16.2% and 55.2% of total Zn was distributed between the Mn and Fe bound zinc and the residual Zn fraction, respectively. Water soluble Zn and nonspecifically adsorbed exchangeable Zn, organically bound zinc fractions were 1.1, 2.4, 7.4 and 12.8% of total zinc respectively. Acid soils contained a greater share of specifically adsorbed Zn, Mn and Fe bound Zn and residual Zn (Bogacz, 1993). Zinc(Zn) uptake occurs readily as hydrated organic chelates and also adsorbed on Fe and Mn oxides. It is rather soluble in soil solutions and very mobile in acid soils (Bedok et al., 1988).

The effect of domestic sewage sludge applied to farm fields at a rate of 44.9 kg/ha in a mixture with lime and sawdust. They found to increase the soil levels of Cd, Cu, Pb, Hg, Ni and Zn. The average levels in sludge treated soil were 0.11, 0.56 (MacLean et al., 1987). The up-take of heavy metals by plants depends on their concentrations in soils. But these metal ions are not always in available forms for plants. It was reported that once the metals are in the soil they are held by soil particles and there is little removal by plant uptake. The availability of such metals are depended on some factors like pH of the soil, organic matter, clay content, cation exchange capacity (CEC) and supply of atoms from other external sources (Me Grath, 1987).

The heavy metals enter into the agro-ecosystem in two major routes; aerials and applications, the aerials include the aerosols, re-suspended particulate matter, re-suspended air borne dusts etc. and application comprises fertilizers, pesticides, industrial wastes, industrial effluents and other soil amendments (Ariano, 1986). Application of untreated municipal waste water led to elevated extractable Cu in the cultivated layer and increase of total Cu with depth (Schirado et al., 1986). Intake of relatively low doses of Pb over a long period can lead to malfunction of organ and chronic toxicity. They also mention this toxic trace element is partly ingested with edible parts of agricultural and horticultural crops (Wierma et al.., 1986).

A study carried out within Matlab Upazila within the range 6.88 to 8.02 with the mean values of 7.408. Individually, the ranges of pH of pond, tube-well and river and canal water were 6.88 to 7.88, 7.21 to 8.02, 7.24 to 7.38 and 6.90 to 7.70, respectively. Out of 50 samples 90% pH values were higher than 7.0 i.e. most of the water were alkaline in nature and only 10% samples were recorded below pH 7.0 i.e. 3 samples were slightly acidic in nature. The lowest (6.88) and highest (8.02) pH value were recorded in pond and tube well water, respectively. The standard deviation and co-efficient variation were 0.28 and 3.82%. 2.2.2 (Basher, 2005).

pH is an important factor that determines the suitability of water of various purposes, including toxicity to plant and animals. In the fields of water supplies it is a factor that is considered in chemical coagulation, disinfection, water softening and corrosion control. pH must be controlled within a range favorable to the particular organisms involved. Chemical process used to coagulate sewage or cyanide ion requires that the pH be controlled within rather narrow limits (Huq and Alam, 2005).

Hydrogen ion concentration (pH) is one of the most important characteristics of water quality may be acid, neutral or alkaline in reaction. Water pH influences the other properties of water body activity of organisms, potency of toxic substances present in the aquatic environment (Rouse, 1979).

Temperature is one of the most important parameter for aquatic environment because of all physical, chemical, biological activity is governed by temperature. The life cycle and natural process of aquatic organisms are closely related to water temperatures. Sudden increase in water temperature may result in the decrease of dissolved oxygen and increase in chemical reaction in water. Normal life patterns of aquatic organisms may be completely disrupted by artificial changes in, water temperature. The standard temperature in the river varies between 20°-30.2° Celsius (Stoker, 1976).

Color of the water depends on the humus content of the decaying vegetative matter and industrial waste and by any other elements. Collected Water samples from the pond, mine drain, ground water had different color ranging from transparent to blackish color.

Conductivity is a measure of the ability of an aqueous solution to carry an electric current. This ability depends on the presence ion; on their total concentration, mobility and valence; and on the temperature of measurement (Huq and Alam, 2005). It is the measurement of concentration of mineral constituents present in water. In any water body higher electrical conductivity means higher pollution.

Electrical conductance or conductivity is the ability of a substance to conduct an electric current. Specific electrical conductance (SEC) is the conductance of a body of unit length and unit cross section at a specified temperature of 25° C. This term is synonymous with volume conductivity and is reciprocal of volume receptivity. The presence of charged ionic species in solution makes the solution conductive. The conductance measurement provides an indication of ion concentration.

The volatile compounds produce odor (Khopkar, 1995). The odor can be relatively described as Medicinal (phenolic), Fishy (due to algae), Earthy (decaying matter) or Chemical (Chlorine).

Oxygen is essential to all forms of aquatic life including those organisms for the self-purification processes in natural waters. Without free dissolved oxygen (DO), the rivers, streams and lake become uninhabitable to gill breathing aquatic organisms (Vesilina et al. 1990). In drinking water DO varies from 4-6 ppm (De. A, K 2005)

The waste from various sources falling into the river has biochemical oxygen Demand, which also decreases the dissolved oxygen. The incensement of biochemical oxygen demand decreases the dissolved oxygen.

BOD is an index of the biodegradable organics present (Clesceri et al., 1998). The rate of oxygen used by organism in the aquatic systems while stabilizing decomposable organic matter is commonly referred to as BOD. It is important to understand that BOD is not a measure of some specific pollutant but it is very important phenomenon for limn logical studies (Vesilind et al., 1990).

The total dissolved solid (TDS) denote mainly the various kinds of minerals present in water. TDS do not contain any gas and colloids. Total dissolved solids in pond water samples ranges from 188 ppm, ground water samples ranges from 85 ppm. TDS standard in drinking water are 500 ppm (De. A, K 2005).TDS in water mainly consist of ammonia, nitrite, nitrate, phosphate, alkalis, some acids, sulphate, metallic ions etc. the variations in the concentrations of TDS in river water due to discharge of effluents and wastes (Moore et al., 1960).

Coal mining and it’s the environmental impacts: There are four types of mining around the world: Surface mining, commonly referred to as either “strip-mining” or “open pit mining”, is a technique used when the coal seam has a relatively small amount of soil above it, is relatively horizontal, and i8s located in low relief areas. The economic viability of this type of mining depends on the value of the coal reserve, the depth of the coal seam as well the make-up of the soil above the coal (Buchanan and Brenkley, 1994).

The process of open pit mining is to blast the soil overlying the coal to loosen it and then remove it, following by stripping the coal out of the ground. This type of mining assures the highest recovery rate of coalfield, so long as the coal seam is located sufficiently close to the surface. Among the most environmental impacts associated with the planning stages of surface mining are large-scale land use, transportation and traffic issues (Buchanan and Brenkley, 1994).

Many of the environmental issues of concern during the primary stages of the mining process continue throughout the entire process. For example , the transportations and traffic issues on roads in the area are present during the extraction phases ( i.e bringing in equipment ,removing coal and soil).Finally, during the reclamation stage there is still traffic to and from the site .Impacts from the extraction phase include removal and disposal of soil ,disturbance of hydrology, blast vibration ,fly rock, and high wall stability ( Buchanan and Brenkley,1994).

The reclamation stage mining involves restoring soil fertility, recreating ecosystem diversity, and recreating landscape. Erosion may lead to an increase in sediment in surface water resulting in the degradation of water quality (Buchanan and Brenkley, 1994). Concerning land disturbance, there is disrupted and can cause the land to be less productive after mining; soil erosion may also develop (Mangena and Brent, 2005).

Underground mining is generally used where the coal is located well below the surface. The environmental impacts associated with underground mining are numerous. During the pre mining phase of the operations, determining the appropriate site can disrupt the land and cause dust. During the extraction process, the impacts are much greater. They include spoil disposal, aquifer disturbance, mine water drainage /disposal, methane emissions, dust and land disturbance (Buchanan and Brenkley, 1994).

These impacts continue after the closure of the mine if proper reclamation and rehabilitation are not completed and can become increasingly harmful .The major land disturbance after exploitation is subsidence, sinking of overlying land due to the hollowing out below. Whether it is surface or underground mining, environmental impacts are inevitable as mining is by its very nature an intrusive industry. The focus should be on mitigating these impacts and on reclamation of the land. What is important to remember in regards to mining is that the sue of land is temporary .Coal mining can help to create energy security, and once mining operations are completed, a gradual process of reclamation and rehabilitation of the land can be undertaken. The reclamation process includes the reshaping contouring of spoil piles, replacing top soil, replanting, relocating valuable resources. Reclaimed land can have many users, including agriculture; forestry recreation (World Coal Institute, 2007).

This is a high volume mining technique for low value products near a plentiful source of water. Scoops/buckets are used to extracted material from shallow water. A high-tech variation of this undersea mining, where material is sucked from the seafloor (although the only successful application of this to-date has been for gem diamonds in shallow water)’ .This mining process is usually combined with the processing (typically drying and concentration) on a floating barge, which is anchored in the middle of the lagoon.

There are two main types of in-situ mining: solution and thermal. Solution-Involves the injection of water down drill holes into soluble deposits (most commonly salt).The material-rich solution is then pumped back to the surface. From mining to coal cleaning, from transportation to electricity generation to disposal, coal releases numerous toxic pollutants into our air, our waters and onto our lands. Nationally, the cumulative impact of all of these effects is magnified by the enormous quantities of coal burned each year – nearly 900 million tons. Promoting more coal use without also providing additional environmental safeguards will only increase this toxic abuse of our health and ecosystems. The trace elements contained in coal (and others formed during combustion) are a large group of diverse pollutants with a number of health and environmental effects. They are a public health concern because at sufficient exposure levels they adversely affect human health. Some are known to cause cancer, others impair reproduction and the normal development of children, and still others damage the nervous and immune systems. Many are also respiratory irritants that can worsen respiratory conditions such as asthma. They are an environmental concern because they damage ecosystems. Power plants also emit large quantities of carbon dioxide (CO2), the “greenhouse gas” largely responsible for climate change. The health and environmental effects caused by power plant emissions may vary over time and space, from short-term episodes of coal dust blown from a passing train to the long-term global dispersion of mercury, to climate change. Because of different factors like geology, demographics and climate, impacts will also vary from place to place. For example, effects from coal mining may be the biggest concern in the coal-field regions of the country, while inhalation exposure may be the foremost risk in an urban setting and, in less populated rural America, visibility impairment and haze may be of special concern ( Keating, M, 2001).

Mining impacts both surface waters and groundwater. In underground mining, waste materials are piled at the surface creating runoff that both pollutes and alters the flow of local streams. As rain percolates through these piles, soluble components are dissolved in the runoff and cause the elevation of total dissolved solids (TDS) in local water bodies. The presence of TDS in a stream usually indicates that sulfates, calcium, carbonates and bicarbonates are present. While not a direct threat to human health, these pollutants make water undrinkable by altering its taste and can also degrade water to the point where it can’t be used for industry or agriculture. Acid mine drainage is a particularly severe byproduct of mining especially where coal seams have abundant quantities of pyrite. When pyrite is exposed to water and air, it forms sulfuric acid and iron. The acidity of the runoff is problematic by itself, but it also dissolves metals like manganese, zinc and nickel, which then become part of the runoff. The resulting acidity and presence of metals in the runoff are directly toxic to aquatic life and render the water unfit for use. Some metals bioaccumulations in the aquatic food chain. Additionally, bottom-dwelling organisms can be smothered by iron that settles out of the water (Buchanan and Brenkley, 1994).

Also of concern is the impact mining has on groundwater, including contamination and physical dislocation of aquifers. These are typically localized effects. Acid mine drainage that seeps into groundwater is a common cause of contamination. Physical disruption of aquifers can occur from blasting which can cause the groundwater to seep to a lower level or even connect two aquifers (leading to contamination of both). When a mine is located below the water table, water seeps into the mine and has to be pumped out. This can lower the water table and even dry up nearby wells. The process of mining, followed by reclamation, changes the permeability of overlying soil, alters the rate of groundwater discharge and increases flooding potential (World Coal Institute, 2007).

Underground mines not only impact groundwater hydrology, they are prone to subsidence. Subsidence occurs when the ground above the mine sinks because the roof of the mine either shifts or collapses. Subsidence can alter ground slopes to such an extent that roads, water and gas lines and buildings are damaged. Natural drainage patterns, river flows and aquifers can also be altered. The extent and severity of the subsidence depends on numerous factors including how thick the overlying soil and rock layers are and the mining method. These problems can be addressed by preventive methods such as leaving enough coal in place to provide structural support to the mine roof. Deliberately collapsing the mine after the coal is extracted causes subsidence to occur sooner, but more evenly. For existing mines, one “corrective” measure that has been used is backfilling the mine with either mine wastes or combustion wastes. While this approach may seem to solve both subsidence and waste disposal problems, it is actually expensive and dangerous and releases contaminants to the groundwater. In addition, these wastes often lack the structural strength to support the mine roof (World Coal Institute, 2007).

At the preparation plant (which is commonly located at or near the mine), impurities that are removed from the coal by screening and washing are placed in waste piles. As with the mining waste, rain percolates through these piles dissolving soluble components and elevating TDS in local water bodies. This runoff is also acidic and contains heavy metals. Trucks, rail, coal slurry pipelines and barges transport coal. All of these either directly or indirectly affect air or water quality. In addition to the ambient air and public health impacts from blowing coal dust, there is also the air pollution from the vehicles themselves. Constant heavy truck traffic damages roads, and clearing transportation of rights of way can increase sediment loading of streams and alter the local landscape. Maintaining rights of way by using herbicides can contaminate surface and ground waters. Waterways for barges require at least a 200-foot wide passage that may produce flooding over a much wider distance and require extensive areas for disposal of spoil from dredged areas. Slurry pipelines may also disturb large areas during construction. National dependence on coal as a fuel source also involves worker exposure to high-risk conditions at various stages during mining, processing and burning of coal (World Coal Institute, 2007).

Although increased mechanization and oversight of the mining industry has increased worker’s safety over the last century, workers whether unionized or not often work long hours under strenuous conditions. Some of the potential safety and human health hazards include: inhalation of dust containing crystalline silica during high wall drilling and mining which can lead to black lung disease; exposure to mercury through inhalation of vapors or mercury-containing dust; inhalation of toxic fumes and gases and exposure to ultraviolet and infrared radiation at welding operations; noise-induced hearing loss as a result of prolonged exposure to processing and mining equipment; as well as heat stroke and exhaustion. (Keating M, 2001)

Air emissions from power plants are subject to requirements of the Clean Air Act (CAA). Coal contains many trace elements that are released during combustion and end up in the atmosphere, in local surface waters and in combustion waste residues. Some of the trace elements in coal are metals, including nickel, mercury, arsenic, chromium and cadmium. Other contaminants are sulfur, nitrogen, chlorine and fluorine. Because of the enormous amounts of coal burned each year – nearly 900 million tons – all of these pollutants are released in significant quantities. Under the CAA, National Ambient Air Quality Standards (NAAQS) have been set for six so-called “criteria” pollutants: nitrogen dioxide (NO2), sulfur dioxide (SO2), particulate matter (PM), lead, carbon monoxide and ozone. In 1990, the CAA was amended to require additional cuts in SO2 emissions. However, despite steps underway to reduce emissions, a loophole in the CAA exempts many of the nation’s old coal-fired power plants from modern pollution standards for NOx and SO2. These “grandfathered” plants emit up to 10 times more pollution than modern coal plants (World coal Association, 2005).

In best practice, studies of the immediate environment are carried out several years before a coal mine opens in order to define the existing conditions and to identify potential problems. The studies look at the impact of mining on surface and ground water, soils, local land use, native vegetation and wildlife populations. Computer simulations can be undertaken to model impacts on the local environment. The findings are then reviewed as part of the process leading to the award of a mining permit by the relevant government authorities (World coal Association, 2005)

Mine subsidence can be a problem with underground coal mining, whereby the ground level lowers as a result of coal having been mined beneath. A thorough understanding of subsistence patterns in a particular region allows the effects of underground mining on the surface to be quantified. The coal mining industry uses a range of engineering techniques to design the layout and dimensions of its underground mine workings so that surface subsidence can be anticipated and controlled. This ensures the safe, maximum recovery of a coal resource, while providing protection to other land uses (World coal Association, 2005).

Mine operations work to improve their water management, aiming to reduce demand through efficiency, technology and the use of lower quality and recycled water. Water pollution is controlled by carefully separating the water runoff from undisturbed areas from water which contains sediments or salt from mine workings. Clean runoff can be discharged into surrounding water courses, while other water is treated and can be reused such as for dust suppression and in coal preparation plants (World coal Association, 2005).

Dust at mining operations can be caused by trucks being driven on unsealed roads, coal crushing operations, drilling operations and wind blowing over areas disturbed by mining. Dust levels can be controlled by spraying water on roads, stockpiles and conveyors. Other steps can also be taken, including fitting drills with dust collection systems and purchasing additional land surrounding the mine to act as a buffer zone. Trees planted in these buffer zones can also minimize the visual impact of mining operations on local communities. Noise can be controlled through the careful selection of equipment and insulation and sound enclosures around machinery (World coal Association, 2005).

Children living in the vicinity of power plants have the highest health risks. Adults are also at risk from contaminated groundwater and from inhaling dust from the facility. The poverty rate of people living within one mile of power plant waste facilities is twice as high as the national average and the percentage of non-white populations within one mile is 30 percent higher than the national average. Consequently, there may be other factors that make these people more vulnerable to health risks from these facilities. These include age (both young and old), nutritional status and access to health care. Also, these people are exposed to numerous other air pollutants emitted from the power plant smokestacks and possibly to air pollution from other nearby industrial facilities or lead paint in the home. Similar high poverty rates are found in 118 of the 120 coal-producing counties in America where power plant combustion wastes are increasingly being disposed of in unlined, under-regulated coal mine pits often directly into groundwater. Mineworkers and their families also often reside in the communities where the coal is being mined. Some of the additional health risks and dangers to residents of coal mining communities include injuries and fatalities related to the collapse of highwalls, roads and homes adjacent to or above coal seams being mined; the blasting of fly rock offsite onto a homeowner’s land or public roadway; injury and/or suffocation at abandoned mine sites; and the inhalation of airborne fine dust particles off-site. In summary, there is nothing clean about coal. Everything related to mining, combustion, waste disposal, and each activity in between, adversely affects public health and the environment. Coal-fired power plants cause a host of environmental harms; promoting increased reliance on coal without additional environmental safeguards is certain to increase those harms. The time is now for coal-fired plants to clean up their act (Keating M, 2001)

Acid mine drainage (AMD) can be a challenge at coal mining operations. AMD is metal-rich water formed from the chemical reaction between water and rocks containing sulphur-bearing minerals. The runoff formed is usually acidic and frequently comes from areas where ore- or coal mining activities have exposed rocks containing pyrite, a sulphur-bearing mineral. However, metal-rich drainage can also occur in mineralized areas that have not been mined. AMD is formed when the pyrite reacts with air and water to form sulphuric acid and dissolved iron. This acid run-off dissolves heavy metals such as copper, lead and mercury into ground and surface water. Mine reclamation activities are undertaken gradually – with the shaping and contouring of spoil piles, replacement of topsoil, seeding with grasses and planting of trees taking place on the mined-out areas. Care is taken to relocate streams, wildlife, and other valuable resources. As mining operations cease in one section of a surface mine, bulldozers and scrapers are used to reshape the disturbed area. Drainage within and off the site is carefully designed to make the new land surface as stable and resistant to soil erosion as the local environment allows. Based on the soil requirements, the land is suitably fertilized and re-vegetated. Reclaimed land can have many uses, including agriculture, forestry, wildlife habitation and recreation. Companies carefully monitor the progress of rehabilitation and usually prohibit the use of the land until the vegetation is self-supporting. The cost of the rehabilitation of the mined land is factored into the mine’s operating costs (World coal Association, 2005).

Chapter 3

Materials and Methods

Study area

The present study was carried out to study the possible environmental effects from coal mining from the Barapukuria coal mining industries, Dinajpur. It takes six months` to carry out the experiment. Regionally, the Barapukuria coal basin is located in the Dinajpur Shield of Bangladesh and is surrounded by the Himalayan Fore deep to the north, the Shillong Shield/Platform to the east, and the Indian Peninsular Shield to the west.

Parbatipur is an upazila of Dinajpur District in the Rangpur Division, Bangladesh. Parbatipur is located at 25.6533°N 88.9155°E . It has 53,146 households and a total area 395.1 km². Saidpur upazila on the north, Phulbari (Dinajpur) upazila on the south, Badarganj upazila on the east, chirir Bandar upazila on the west. Parbatipur Thana was established in 1800 and was turned into an upazila in 1983. It consists of 13 union parishads, 194 mouzas and 230 villages. As of the 1991 Bangladesh census, Parbatipur has a population of 270,904. Males constitute 51.46% of the population, and females 48.54%. Upazila’s population of people eighteen years old or older is 139,294. Parbatipur has an average literacy rate of 29.7% (7+ years), compared to the national average of 32.4%. Parbatipur has 10 unions, 1 paurasava, 194 mauzas / mahallas, 230 villages and 1 cantonment situated in it Structurally, the Barapukuria basin is a long, narrow, and shallow Permo Carboniferous rift basin. The basin trends approximately N-S for over 5 km, ranges from 2 to 3 km wide, and is over 550 m deep. The overall structures of the Barapukuria Basin imply a tectonically active highly disturbed zone (BBS, 2006).

Phulbari is an important business center and its importance grew significantly with the development of the Barapukuria coal mine and hard rock mine both located within a few kilometers from the town.

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Fig. 1. Map showing the location of Barapukuria coal mining area.

Sample collection

To accomplish the task of assessment the effect of Barapukuria coal mine and thermal power plant on surrounding environment, the effect of coal water on soil, plants and emissions from power plant had been evaluated. To qualify and elucidate this impact, relevant data were collected from these projects and from ‘relevant papers’ and ‘news papers’. An investigation on the chemical properties of coal, coal water, soil and plant samples were also conducted to find out the properties of coal and coal water and their effect on soil and plant.

Sampling:

Simple random sampling was used for the primary data collection. Then these data were edited and arranged in the form of qualitative data.

Preparation of sample for analysis:

Air-drying: The soil sample is placed in a thin layer on a clean piece of paper on a shelf in the room and left until it is air-dry. Visible roots and plant fragments were removed from the soil sample and discarded.

Grinding: For the preparation of the soil sample, soil was passed through the grinder and subsequently, a 2 mm stainless steel sieve.

Storing: The soil samples were kept in a clean polythene bag for chemical analysis.

Sample analysis

The methods followed for analyzing the coal, coal water, soil and plant samples are stated below:

Soil and coal sample

Soil reaction (pH): Soil pH was determined by soil pH and moisture meter ZD5PM 0909 made in Germany. Ten grams of air dried soil from each sampling depth was taken in 50 ml beakers separately and 25 ml of distilled water was added to each beaker. The suspension was stirred well for 20 minutes and allowed to stand for about 30 minutes, Then each samples was stirred for 2 minutes before reading. The position of the electrode was immersed into the partly settled soil suspension and pH was measured. The result was reported as soil pH measured in water (soil: water ratio being 1:2.5).

Electrical Conductivity (EC): The parameter EC was used to determine a conductivity meter. The model of EC meter was HM digital meter. The solution is 1:5 of soil water suspension. The methodology adopted in the study can be categorized in three classes: application of participatory rural appraisal (PRA) tools to get an understanding of the land and water use and management systems, including development potentials and constraints, collection of secondary data, and analysis of the information from PRA and secondary information in the context of research objectives. Two field visits were made to the study area for primary data collection through PRA as well as for secondary data collection. The data collected in the study area were mostly qualitative, and in a few cases, semi-quantitative.

Organic carbon: The percent of organic carbon was determined titrimetrically