Effects of acid mine drainage on groundwater quality: a case study from an open-pit copper mine in eastern Turkey M. Irfan Yesilnacar & Zekiye Kadiragagil
Bulletin of Engineering Geology and the Environment The official journal of the IAEG ISSN 1435-9529 Volume 72 Combined 3-4 Bull Eng Geol Environ (2013) 72:485-493 DOI 10.1007/s10064-013-0512-5
1 23
Your article is protected by copyright and all rights are held exclusively by SpringerVerlag Berlin Heidelberg. This e-offprint is for personal use only and shall not be selfarchived in electronic repositories. If you wish to self-archive your article, please use the accepted manuscript version for posting on your own website. You may further deposit the accepted manuscript version in any repository, provided it is only made publicly available 12 months after official publication or later and provided acknowledgement is given to the original source of publication and a link is inserted to the published article on Springer's website. The link must be accompanied by the following text: "The final publication is available at link.springer.com”.
1 23
Author's personal copy Bull Eng Geol Environ (2013) 72:485–493 DOI 10.1007/s10064-013-0512-5
ORIGINAL PAPER
Effects of acid mine drainage on groundwater quality: a case study from an open-pit copper mine in eastern Turkey M. Irfan Yesilnacar • Zekiye Kadiragagil
Received: 7 June 2012 / Accepted: 7 August 2013 / Published online: 16 November 2013 Springer-Verlag Berlin Heidelberg 2013
Abstract This study was undertaken to determine the variation in groundwater quality of an open-pit copper mine in Maden (eastern Turkey) which has been in operation since 2000 BC, and with modern methods since 1939. Physical and chemical parameters (including pH, temperature, electrical conductivity, concentrations of Na, K, Ca, Mg, Cl, HCO3, SO4, NO3, Fe, Co, Cr, Mn, Ni, Cu, Zn, Al, Cd, and Pb) of the groundwater and spring water samples from the study area were measured on a seasonal basis between October 2009 and July 2010. The groundwater quality was hydrochemically assessed in order to determine its suitability for human consumption and agricultural use. The measured and analyzed parameters in all the water samples were below the maximum admissible concentrations set out in international and national standards, guidelines, directives, and regulations for human consumption and for agricultural purposes. In addition, the results of previous studies on the possible effects of the mine site on soil, stream sediment, plants, and surface water in the same area are discussed. Keywords Acid mine drainage Groundwater contamination Drinking water Irrigation water Maden Turkey
Introduction Metal-containing acid mine drainage (AMD) is created by the interaction of air and water with sulfides such as pyrite M. I. Yesilnacar (&) Z. Kadiragagil Department of Environmental Engineering, Harran University, Osmanbey Campus, 63190 S¸ anlıurfa, Turkey e-mail:
[email protected];
[email protected]
(FeS2) found in overburden piles and also in mine shafts consisting of sub-commercial grade mining material left over from mining operations. Other sulfide minerals are oxidized in a similar way as pyrite, releasing metals and sulfate in solution and, therefore, AMD may contain several metals such as Cu, Fe, Zn, Al, Pb, As, and Cd in high concentrations. AMD is acidic in nature and generally has low organic carbon content. If uncontrolled, AMD flows into local streams, lakes, and rivers, contaminating soil and groundwater and destroying plant and animal biota (Szczepanska and Twardowska 1999; Equeenuddin et al. 2010). Furthermore, some effluents generated by the metal mining industry contain large quantities of toxic substances such as cyanides and heavy metals, which have serious human health and ecological implications (Akcil and Koldas 2006). The formation of acidic wastewater can continue even tens and hundreds of years after mine closure if the conditions remain favorable (Sahinkaya et al. 2011). The adverse effects of AMD on groundwater are more profound compared to surface water (Paschke et al. 2001; Eary et al. 2003). Significant concentrations of sulfate, metals, metalloids, and other contaminants have been found in groundwater plumes migrating from mine workings and sulfide waste repositories and impoundments. If not rectified, a plume of contaminated water will migrate over time downgradient, spreading beyond the mine workings and waste repositories, surfacing at seepage points, and contaminating surface water (Lachmar et al. 2006). Contamination levels depend on the interaction between the soil, sediment, or rock through which the contaminated water flows and the contaminant in the water (Lottermoser 2007). The study area is well known due to its copper deposit, the most important in Turkey (Go¨ymen and Aslaner 1969). The deposit was one of the most ancient copper mining
123
Author's personal copy 486
centers. According to some researchers, the deposit has been known since 2000 BC. The modern era of copper production at Maden began in 1939 when Etibank, a state mining organization, started exploiting the ore (Bamba 1976). The ore mining and processing plant produces 10,000 tons of blister copper per year. This amount of copper is produced from 30,000–35,000 tons of slag, and around 6,650 m3 of flotation waste with a solid content of 10 % is generated (Boybay and Arslan 1992). Over the years, overburden, slag, flotation waste, and wastewater resulting from the mining activities have been discharged into the Maden Cayi (stream) without any treatment. Hence, the contamination of surface water, plants, soil, and stream sediment in the vicinity of the mine area has been reported in several studies (Gu¨r 1993; Ozdemir and Sagiroglu 2000; S¸ as¸ maz and Yaman 2008; Kırat and Bo¨lu¨cek 2010). This study aims to evaluate the adverse effects of mining activity in the study area (Maden, Elazıg˘) on groundwater quality. For this purpose, the groundwater quality of the study area was monitored over 1 year on a seasonal basis and the results were compared with previous studies on the same area.
M. I. Yesilnacar, Z. Kadiragagil
Fig. 1 The study area
of submarine volcanism and they are hosts for Cyprus-type pyritic copper deposits (Griffitts et al. 1972; Bamba 1976; ¨ stu¨ntas¸ and Sag˘ırog˘lu 1993; Aktas¸ and Robertson 1984; U Ozdemir and Sagiroglu 2000). Methodology
Materials and methods Study area The study area is located 78 km southeast of the city of Elazıg˘ and within the town of Maden (Fig. 1). The area is thinly populated and has very rough morphology where peaks of around 1,500 m are separated by deep valleys with mainly seasonal streams. Vegetation is sparse and only stream valleys are conducive to plant growth. The region has a semi-arid climate type. The long-term mean annual precipitation is 434 mm and the temperature is 14 C. Geology Geological units in the studied area and their main geological properties are described below, and a simplified geological map of the area is given in Fig. 2. There are two main geological units in the study area: the Guleman Ophiolites and the Maden Complex. The Upper Cretaceous aged Guleman Ophiolites are composed of peridotites, gabbros, sheeted dykes, and pillow lavas, and bear many alpine-type chromite bodies. The Eocene Maden Complex overlies the ophiolites unconformably. The complex is composed of rocks that are sedimentary (sandstone, marl, limestone, and mudstone), volcano-sedimentary and volcanic-subvolcanic (diabase, diabase breccia, andesite, and basaltic andesite). The main volcanic bodies are products
123
Between October 2009 and July 2010 on a seasonal basis over a period of 1 year, groundwater and spring water samples were taken from three observation points to represent the entire study area (Fig. 3). Sampling and measurement procedures were carried out in accordance with: • • •
D4448-01 Standard Guide for Sampling Ground-Water Monitoring Wells (ASTM 2001), Water Quality-Sampling-Part 2: Guidance on sampling techniques (TSE 1997) and Groundwater Well Sampling (EPA 1995).
Electrical conductivity (EC), temperature, and pH were measured with a SevenGo pro-SG7 conductivity meter and a portable pH meter immediately after sampling in the field. The water samples collected in the field were analyzed for chemical constituents such as sodium, potassium, calcium, magnesium, chloride, bicarbonate, sulfate, nitrate, iron, cobalt, chrome, manganese, nickel, copper, zinc, aluminum, cadmium, and lead. Analyses were conducted in the laboratory using the standard methods as suggested by the American Public Health Association (APHA-AWWA-WEF 1999). Metal concentrations were measured with an inductively coupled plasma (ICP) combined with atomic emission spectroscopy. Concentrations of chloride, sulfate, and nitrate were determined with a Merck Nova 60 photometer. Concentration of bicarbonate was analyzed by volumetric titrations. All measurements were done at least in duplicate. The accuracy of
Author's personal copy Effects of AMD on groundwater quality
487
Fig. 2 Geological map of the study area (adapted from MTA 2010) Fig. 3 Study area showing topography and the location of the sampling sites in relation to mine areas
the chemical analysis was verified by calculating ion-balance errors, which were generally below 5 %. Results and discussion The physical and chemical parameters for each sampling point are provided in Table 1. The quality of the groundwater in the studied area was assessed hydrochemically so as to
determine its suitability for human consumption and agricultural purposes. In addition, hydrochemical facies of all the groundwater samples were determined (Kadiragagil 2011). In terms of the quality of water intended for human consumption, the results were evaluated in accordance with: •
Standard 266 of the Turkish Standards Institution (TSE) regarding the quality of water intended for human consumption (TSE 2005),
123
Author's personal copy 488
M. I. Yesilnacar, Z. Kadiragagil
Table 1 Mean values of physical and chemical parameters of groundwater in the sampling sites Sampling periods
Fall
Sampling site no.
1
Temperature (C)
Winter 2
3
1
Spring 2
3
1
Summer 2
3
1
2
3
17.00
19.90
14.10
11.00
15.00
12.00
14.00
16.40
13.00
14.00
23.40
pH
8.13
7.00
7.17
7.57
7.00
7.17
7.85
7.00
7.16
7.85
7.00
7.17
EC
783.00
303.00
210.40
480.00
303.00
210.40
631.50
308.00
162.80
631.50
298.00
258.00
HCO3
15.00
90.00
167.50
142.50
97.50
167.50
142.50
93.75
165.00
155.00
93.75
170.00
130.00
199.00
16.89
15.19
105.08
16.89
15.19
152.04
16.96
16.13
152.04
16.81
14.25
Cl
2.50
1.11
1.14
0.77
1.11
1.14
1.59
1.31
1.48
1.59
0.90
0.79
NO3 Na
1.00 3.32
1.07 4.93
0.99 4.17
2.55 1.33
1.07 4.93
0.99 4.17
1.73 2.33
1.19 4.94
1.04 4.13
1.73 2.33
0.95 4.91
0.94 4.22 0.80
SO4
K
2.59
0.76
0.72
0.76
0.76
0.72
1.68
0.74
0.64
1.68
0.78
Mg
70.40
6.90
4.81
36.91
6.90
4.81
53.66
6.98
4.95
53.66
6.82
4.68
Ca
37.93
54.04
47.28
14.89
54.04
47.28
26.41
53.85
45.83
26.41
54.23
48.72
Fe
0.28
0.58
0.58
0.10
0.58
0.58
0.59
0.27
0.26
0.59
0.10
0.10
Co
0.02
0.01
0.01
0.02
0.01
0.01
0.02
0.01
0.01
0.02
0.01
0.01
Cr
0.03
0.01
0.01
0.02
0.01
0.01
0.03
0.01
0.01
0.03
0.01
0.01
Mn
0.02
0.10
0.10
0.02
0.10
0.10
0.02
0.10
0.10
0.02
0.10
0.10
Ni
0.03
0.01
0.01
0.02
0.01
0.01
0.02
0.01
0.01
0.02
0.01
0.01
Cu
0.20
0.01
0.01
0.02
0.01
0.01
0.11
0.01
0.01
0.11
0.01
0.01
Zn
0.41
0.10
0.10
0.02
0.10
0.10
0.19
0.10
0.10
0.18
0.10
0.10
Al
0.05
0.10
0.10
0.01
0.10
0.10
0.03
0.10
0.10
0.03
0.10
0.10
Cd
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
Pb
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
Concentrations are expressed in mg/l, EC in lS/cm
• •
•
The World Health Organization (WHO) Guidelines for Drinking-Water Quality (WHO 2004), Directive 98/83/EC of the EU (European Union) regarding the quality of water intended for human consumption (EU 1998) and The Turkish Water Pollution Control Regulations (Ministry of Environment and Forestry 2004).
All the water quality parameters considered in all the water samples were below the maximum admissible concentration according to the above-specified international and national standards, guidelines, directives, and regulations. The analytical data plotted on the US salinity diagram illustrate that sample nos. 1 and 2 fall in the field of C2-S1, indicating medium salinity and low alkalinity hazard (Fig. 4). Also, sample no. 3 falls in the field of C1S1, indicating low salinity and low alkalinity hazard (Fig. 4). The EC and Na% values plotted on the Wilcox diagram illustrate that all the well water samples fall in the field of ‘‘very good to good’’ for irrigation (Fig. 5). The geochemical evolution of the groundwater was determined by plotting the concentrations of major cations and anions into a Piper (1944) trilinear diagram (Fig. 6), which was prepared using RockWare Aq.QA v.1.1 software. On the
123
basis of the chemical analyses of all water samples taken from the study area (during the period of sampling), the groundwater is divided into two facies. Sample no. 1 represents Ca–CI facies, while sample nos. 2 and 3 represent Ca–HCO3 facies. According to Schoeller’s diagram, the groundwater was classified as ‘‘very good quality drinkable water (S2 and S3)’’ and ‘‘good quality drinkable water (S1)’’ for human consumption (Fig. 7). Gu¨r (1993) and Gu¨r et al. (1994) did not observe significant heavy metal pollution in the upstream section of the Maden stream, while in the vicinity of the mining plant and downstream of the stream, significant heavy metal pollution was detected. The plant samples from 47 stations to analyze the contents of Cu, Fe, Mn, and Zn to determine the contamination level in plants growing along the Maden stream valley were collected by Ozdemir (1996) and Ozdemir and Sagiroglu (2000). Similar to the studies conducted by Gu¨r (1993) and Gu¨r et al. (1994), Cu, Fe, Mn and Zn contamination was detected in all the plant species. Studies on the soil and sediment pollution in the area have also been conducted previously (S¸ as¸ maz and Yaman 2008; Kırat et al. 2008; Kırat and Bo¨lu¨cek 2010). The mean
Author's personal copy Effects of AMD on groundwater quality
Fig. 4 Salinity and alkalinity hazard of irrigation water in USA salinity diagram with groundwater samples 1, 2, and 3 plotted
concentrations of Cu, Ni, Co, Cr, and Mn in the soil samples taken in the vicinity of the plant were 1,595, 489, 202, 305, and 1,406 mg/kg, respectively. The study results indicated that these soil samples had much higher metal concentrations compared to uncontaminated soil samples (106-fold for Cu, 25-fold for Ni, 10-fold for Co, 5-fold for Cr, and 3-fold for Mn). Furthermore, heavy metal accumulation was detected in most plants (S¸ as¸ maz and Yaman 2008). Similarly, Kırat et al. (2008) and Kırat and Bo¨lu¨cek (2010) reported that some heavy metals (including Cu, Pb, Zn, As, Cd, and Fe) were concentrated in the fine fraction of stream sediment. As seen from Table 2, AMD derived from the mine area is highly acidic, and the sulfate and metal concentrations are remarkably high. In addition, the composition of AMD is highly variable. The pH and sulfate concentrations in the first sampling point (AMD1) were 5 and 1,500 mg/L, respectively, while these values in the second sampling point (AMD2) were 3 and 3,200 mg/L, respectively. The reason for the decreasing pH and increasing sulfate concentration is that the AMD that is formed flows from the first sampling point (AMD1) to the second one (AMD2) as a result of the slope of the land (Fig. 3). AMD has very low
489
Fig. 5 Suitability of groundwater for irrigation in Wilcox diagram with groundwater samples 1, 2, and 3 plotted
pH and high concentration of metal and sulfate in the second sampling point as a result of the contact of sulfurcontaining ore with the water and air (Sahinkaya et al. 2011). The results of the aforementioned studies have revealed that the stream water, plants, soil, and sediment in the mine area and its vicinity face a very serious environmental problem as a result of the overburden, slag, flotation waste, and wastewater from the mining activities, and from the uncontrolled discharge of AMD and the discharged municipal wastewater without any treatment. However, the reason for not observing any serious contamination in the groundwater in the area is because of the geological structure of the area and natural processes. The study suggests that the concentration of contaminants is reduced to an acceptable level by natural processes. Gonza´lez-Cha´vez et al. (2009) defines the following mechanisms of attenuation: adsorption, biological uptake, cation and anion exchange reactions, dilution, filtration, and precipitation reactions; except for dilution, these mechanisms can be operative in unsaturated media. All the mechanisms except for biological uptake can be operative in the aquifer. Natural attenuation processes in the aquifer might also reduce the constituent concentrations to background levels in the pathway of the subsurface drainage
123
Author's personal copy 490
M. I. Yesilnacar, Z. Kadiragagil
Fig. 6 Chemical facies of all groundwater samples in Piper diagram
since the upper geological units include limestone and mudstone with clayey layers that more readily adsorb contaminants. Neutralizing minerals, such as carbonates, in the aquifers also buffer acidic groundwater.
3.
Conclusion and recommendations Based on the results of this study, the following conclusions can be drawn: 1.
2.
The stream water, plants, soil, and sediment in the mine area and its vicinity face a very serious environmental problem as a result of the overburden, slag, flotation waste, and wastewater from the mining activities and the uncontrolled discharge of AMD and the discharged municipal wastewater without any treatment. As a consequence of the geological formation of the study area and natural attenuation processes, contamination in the groundwater in the area has so far not been detected.
123
4.
Test results indicate that groundwater and natural spring water in the area are suitable for human consumption and for agricultural purposes. However, contamination as a result of continuous intensive mining activities is possible in the future. Hence, groundwater vulnerability maps for the delineation of protection zones in areas affected by groundwater contamination due to mining activities need to be prepared. Unless more care is taken to prevent contamination of stream water, plants, soil, and sediment, the problems may affect the entire region. Therefore, a continuous and systematic environmental monitoring network should be established to monitor the environmental and natural resources in the region.
It is hoped that the results of this study will contribute to the efforts of practitioners and scientists to better manage the possible effects of an open-pit copper mine on the environment and specifically groundwater quality in a semi-arid region.
Author's personal copy Effects of AMD on groundwater quality
491
Fig. 7 Classification of the groundwater analyses in the drinkable water diagram by Schoeller
123
Author's personal copy 492
M. I. Yesilnacar, Z. Kadiragagil
Table 2 Chemical composition of AMD water of the open-pit mine in Maden (Sahinkaya et al. 2011) Parameter
AMD1 (mg/l)
AMD2 (mg/l)
COD
\30
\30
pH
4.3
3.04
Sulfate
1,500
3,360
Al
0.155
54.37 ± 2.95
Ca
236
117.31 ± 6.30
Cd
0.0018
0.01 ± 0.01
Co Cr
2.189 0.029
8.99 ± 0.48 0.12 ± 0.03
Cu
3.976
44.91 ± 2.75
Fe
2.274
391.05 ± 60
K
1.889
19.34 ± 0.92
Mg
367.6
341.77 ± 20
Mn
6.476
6.05 ± 1.72
Na
10.69
11.24 ± 1.88
Ni
0.776
3.78 ± 0.2
Pb
0.99
6.90 ± 2.23
Zn
3.01
5.90 ± 0.84
Acknowledgments This study was funded by the Scientific ¨ BAK) under Research Projects Committee of Harran University (HU Grant No. 2009-081. The authors would like to thank Deniz Ucar, Nisa Kasar, and Omer Kotan for their assistance in the field and the laboratory.
References Akcil A, Koldas S (2006) Acid mine drainage (AMD): causes, treatment and case studies. J Clean Prod 14:1139–1145 Aktas¸ G, Robertson HF (1984) The maden complex, SE Turkey: evolution of a Neotethyan active margin; the geological evolution of the Eastern Mediteranean. Spec Publ Geol Soc Edinburgh 17:375–402 APHA-AWWA-WEF (1999) Standard methods for the examination of water and wastewater (20th ed.). Am Publ Health Assoc, p 1325 ASTM (The American Society for Testing and Materials) (2001) Standard Guide for Sampling Groundwater Monitoring Wells. D4448-01, 17 Bamba T (1976) Ophiolite and Related Copper Deposits of the Ergani Mining District, Southeastern Turkey. Bull Miner Res Explor Inst Turk 86:36–50 Boybay M, Arslan M (1992) Elazıg˘ ve C¸evresinde Endu¨striyel Kirlenme. Ekoloji 4:2667–2671 Eary LE, Runnells DD, Esposito KJ (2003) Geochemical controls on ground water composition at the Cripple Creek mining district, Cripple Creek, Colorado. Appl Geochem 1:1–24 EPA (U.S. Environmental Protection Agency) (1995) Groundwater well sampling, SOP#:2007, 01/26/1995, USA Equeenuddin MS, Tripathy S, Sahoo PK, Panigrahi MK (2010) Hydrogeochemical characteristics of acid mine drainage and
123
water pollution at Makum Coalfield, India. J Geochem Explor 105:75–82 EU (European Union) (1998) Council Directive 98/83/EC of European Communities on the quality of water intended for human consumption (p 32). European Union Council Gonza´lez-Cha´vez MC, Carrillo-Gonza´leza R, Gutie´rrez-Castorena MC (2009) Natural attenuation in a slag heap contaminated with cadmium: the role of plants and arbuscular mycorrhizal fungi. J Hazard Mater 161:1288–1298 Go¨ymen G, Aslaner M (1969) Dog˘u anadolu’da bulunan Ergani maden bakir yatag˘inin ve bilhassa yantas¸ larinin maden mikroskopik incelenmesi. MTA dergisi 72:176–188 ¨ ner O ¨ (1972) Massive sulfide copper Griffitts WR, Albers JP, O deposits of the Ergani-Maden area, Southeastern Turkey. Econ Geol 67:701–716 Gu¨r F (1993) Pollution potential of flotation wastewaters of Ergani copper plants on Maden brook. MSc Thesis. Firat University, Graduate School of Natural and Applied Sciences Department of Chemical Engineering, p 81 (in Turkish with English abstract) Gu¨r F, Tu¨men F, Bildik M (1994) Ergani Bakır I˙s¸ letmeleri Flotasyon ¨ . Fen ve Artıklarının Maden C¸ayı’nın Kirlenmesindeki Rolu¨, F.U Mu¨h. Bilimleri Dergisi 6(1):67–87 Kadiragagil Z (2011) Effect of acid mine drainage on groundwater quality: a case study from Ergani-Maden copper facility. MSc thesis, Harran University (in Turkish with English abstract) Kırat G, Bo¨lu¨cek C (2010) The effect of the dissolution on metal distribution in the stream sediments in the vicinity of Maden (Elazıg˘). Fırat Univ. J Eng 22(2):147–155 (in Turkish with English abstract) Kırat G, Bo¨lu¨cek C, Kalender L (2008) Maden (Elazıg˘) C¸evresinde Dere Kumlarinda Cu, Pb, Zn, As, Cd ve Fe Dagilimi. Geosound 53:203–217 (in Turkish with English abstract) Lachmar T, Burk NI, Kolesar PT (2006) Groundwater contribution of metals from an abandoned mine to the North Fork of the American Fork River, Utah. Water Air Soil Poll 173:103–120 Lottermoser BG (2007) Mine wastes: characterization, treatment and environmental impacts (2nd edition). Springer, Berlin, p 304 Ministry of Environment and Forestry (2004). The Turkish water pollution control regulations. The Turkish Official Gazette of 31 Dec 2004, n. 25687, Ankara, Turkey MTA (2010) The geological map of L43-a2 sheet (1:25.000 scaled). General Directorate of Mineral Research & Exploration, Ankara, Turkey Ozdemir Z (1996) Investigation of biogeochemical anomalies along Maden C¸ayı (Maden-Elazıg˘). PhD thesis. Firat University (in Turkish with English abstract) Ozdemir Z, Sagiroglu A (2000) Salix acmophylla, Tamarix smyrnensis and Phragmites australis as biogeochemical indicators for copper deposits in Elazıg˘, Turkey. J Asian Earth Sci 18:595–601 Paschke SS, Harrison WJ, Walton-Day K (2001) Effects of acidic recharge on groundwater at the St. Kevin Gulch site, Leadville Colorado. Geochem: Explor Environ, Anal 1:3–14 Piper AM (1944) A graphical procedure in the geochemical interpretation of water analysis. Am Geophys Union Trans 25:914–928 Sahinkaya E, Gunes FM, Ucar D, Kaksonen AH (2011) Sulfidogenic fluidized bed treatment of real acid mine drainage water. Bioresour Technol 102:683–689 S¸ as¸ maz A, Yaman M (2008) Maden (Elazıg˘) bakır yatag˘ı c¸evresindeki toprak, bitki ve su o¨rneklerindeki deg˘is¸ ik metal du¨zeylerinin belirlenmesi. TUBITAK (Grant No: 105Y051), p 91 Szczepanska J, Twardowska I (1999) Distribution and environmental impact of coal-mining wastes in Upper Silesia, Poland. Environ Geol 38:249–258
Author's personal copy Effects of AMD on groundwater quality TSE (2005) Water intended for human consumption. TS 266, Ankara, Turkey (in Turkish) TSE (Turkish Standards Institution) (1997) Water quality-samplingpart 2: guidance on sampling techniques, TS 5090 EN 25667-2, Ankara, TURKEY (in Turkish)
493 ¨ stu¨ntas¸ A, Sag˘ırog˘lu A (1993) Two different type of Cu-mineralU izations of Zahuran (Maden–Elazıg˘). Geol Bull Turk 36:179–188 (in Turkish with English abstract) WHO (World Health Organization) (2004) Guidelines for drinkingwater quality. 3rd edn, vol 1. Recommendations. Geneva, 515
123
