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Map of Norway, showing locations of selected Norwegian metal sulphide mines

Figure 4 Map of Norway, showing locations of selected Norwegian metal sulphide mines

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Simplified diagram illustrating reaction pathways for pyrite oxidation (after Stumm and Morgan 1981; Arnesen 1993b) Where mine-water pumping is constant and the mine- water level is stable, little pyrite oxidation occurs below
Simplified diagram illustrating reaction pathways for pyrite oxidation (after Stumm and Morgan 1981; Arnesen 1993b) Where mine-water pumping is constant and the mine- water level is stable, little pyrite oxidation occurs below
omparison of discharge water quality from selected British and Svalbardian pumping and abandoned mines and spoil tips (sources; Younger 1993; Madawee 1994; Fuge anc hers 1991; Lemon 1991; Buchan 1962; Banks 1996; Banks and others 1996b) * The alkaline nature of this water may be partially explained by the use of limestone dust to hinder explosion in the mine, but is probably dominated by the natural hydrochemistry of the deep, cold subpermafrost water entering the mine (Banks 1996) > The saline water derived from this spoil tip probably represents leaching of saline pore water from the spoil derived from this deep mine. Wiggering (1993a) report similar phenomenon from the Ruhr area of Germany © Guide level 4 Maximum allowable concentration C At Ataorharvaa frrnam niuimn ar trontmoant niant
omparison of discharge water quality from selected British and Svalbardian pumping and abandoned mines and spoil tips (sources; Younger 1993; Madawee 1994; Fuge anc hers 1991; Lemon 1991; Buchan 1962; Banks 1996; Banks and others 1996b) * The alkaline nature of this water may be partially explained by the use of limestone dust to hinder explosion in the mine, but is probably dominated by the natural hydrochemistry of the deep, cold subpermafrost water entering the mine (Banks 1996) > The saline water derived from this spoil tip probably represents leaching of saline pore water from the spoil derived from this deep mine. Wiggering (1993a) report similar phenomenon from the Ruhr area of Germany © Guide level 4 Maximum allowable concentration C At Ataorharvaa frrnam niuimn ar trontmoant niant
In very low pH waters (pH <4), dissolution of aluminium may occur from alumino-silicate minerals such as kaolin- ite. When aluminium-rich acidic mine waters are effluent into higher pH surface waters, they typically precipitate white aluminium hydroxide (gibbsite).
In very low pH waters (pH <4), dissolution of aluminium may occur from alumino-silicate minerals such as kaolin- ite. When aluminium-rich acidic mine waters are effluent into higher pH surface waters, they typically precipitate white aluminium hydroxide (gibbsite).
Map of Great Britain, showing locations of coalfields and selected named sites
Map of Great Britain, showing locations of coalfields and selected named sites
* after Rui (1973) > after Arnesen and Iversen (1995) after Arnesen and others (1994) Composition of Norwegian Cu/Zn sulphide ores Table 3
* after Rui (1973) > after Arnesen and Iversen (1995) after Arnesen and others (1994) Composition of Norwegian Cu/Zn sulphide ores Table 3
lingdal shaft was seen to decline with increasing depth in the mine (Banks 1993, 1994), due to either (or both) fur- ther oxidation of ore minerals in the mine or concentra- tion increase due to evaporation (Fig. 6). By June 1994, the Central Station level was submerged and air circula- tion (and hence evaporation) within the mine was cur- tailed (Arnesen and Iversen 1995). Overflow at a rate of some 40 l/min from the Bjgrgan shaft was predicted with- in 40 years. Even if the drainage water were to be div- erted away from the Killingdal shaft, overflow would oc- cur within some 400 years, though this rate of overflow would be unlikely to represent a major problem. The plans for radioactive waste disposal appear to have been dropped (Henriksen and others 1992), but mine water continues to accumulate, and a new solution to the run- off from the spoil tips at the mouth of this shaft may ev- entually have to be found.
lingdal shaft was seen to decline with increasing depth in the mine (Banks 1993, 1994), due to either (or both) fur- ther oxidation of ore minerals in the mine or concentra- tion increase due to evaporation (Fig. 6). By June 1994, the Central Station level was submerged and air circula- tion (and hence evaporation) within the mine was cur- tailed (Arnesen and Iversen 1995). Overflow at a rate of some 40 l/min from the Bjgrgan shaft was predicted with- in 40 years. Even if the drainage water were to be div- erted away from the Killingdal shaft, overflow would oc- cur within some 400 years, though this rate of overflow would be unlikely to represent a major problem. The plans for radioactive waste disposal appear to have been dropped (Henriksen and others 1992), but mine water continues to accumulate, and a new solution to the run- off from the spoil tips at the mouth of this shaft may ev- entually have to be found.
© Mine water, average for 1990/1991, Arnesen and Iversen (1995) * Mine water from Grabergstollen, average for 1990, Arnesen and Iversen (1995) & Mine water from Gruvebekken, Arnesen and Iversen (1995) » Mine water from base of Killingdal mine, after Noteby (1992) and Banks (1994) * Mine water after sedimentation basin, average 1993, Arnesen and Iversen (1995) > Collected run-off from Kjgli mine, average for 1984, Arnesen and Iversen (1995) © Mine water, average for period 1961-1975, Arnesen and Iver- sen (1995) “ Average for water samples from the Astrup shaft, March 1988-October 1989, Arnesen and others (1994); Arnesen and Iversen (1995) Composition of a variety of mine waters from Norwegian sulphide mines Table 4
© Mine water, average for 1990/1991, Arnesen and Iversen (1995) * Mine water from Grabergstollen, average for 1990, Arnesen and Iversen (1995) & Mine water from Gruvebekken, Arnesen and Iversen (1995) » Mine water from base of Killingdal mine, after Noteby (1992) and Banks (1994) * Mine water after sedimentation basin, average 1993, Arnesen and Iversen (1995) > Collected run-off from Kjgli mine, average for 1984, Arnesen and Iversen (1995) © Mine water, average for period 1961-1975, Arnesen and Iver- sen (1995) “ Average for water samples from the Astrup shaft, March 1988-October 1989, Arnesen and others (1994); Arnesen and Iversen (1995) Composition of a variety of mine waters from Norwegian sulphide mines Table 4
from this part of the mine was pumped into the Wallen- berg complex but comprised only some 5-10% of the to- tal quantity pumped from the latter (Arnesen and Iversen 1995). Up until 1983, the water pumped from the mine complex was the largest single emission of Cu and Zn in Norway. The water contained 0.5-1 g/l Cu and a similar quantity of Zn, and was discharged to Orklafjord at some 500,000-600,000 m?°/year. In 1983, the old part of the mine around Wallenberg was closed and sealed off from the deeper Astrup complex with concrete plugs. The Wal- lenberg complex was allowed to fill up and water from the Astrup complex was also pumped at some 55,000 m*/ year into the Wallenberg mine until 1987, when the As- trup mine was closed and also started to fill up. In 1989, when the Wallenberg mine was still filling, the major source of mining-related pollution was assessed by the Norwegian Institute for Water Research (NIVA) as
from this part of the mine was pumped into the Wallen- berg complex but comprised only some 5-10% of the to- tal quantity pumped from the latter (Arnesen and Iversen 1995). Up until 1983, the water pumped from the mine complex was the largest single emission of Cu and Zn in Norway. The water contained 0.5-1 g/l Cu and a similar quantity of Zn, and was discharged to Orklafjord at some 500,000-600,000 m?°/year. In 1983, the old part of the mine around Wallenberg was closed and sealed off from the deeper Astrup complex with concrete plugs. The Wal- lenberg complex was allowed to fill up and water from the Astrup complex was also pumped at some 55,000 m*/ year into the Wallenberg mine until 1987, when the As- trup mine was closed and also started to fill up. In 1989, when the Wallenberg mine was still filling, the major source of mining-related pollution was assessed by the Norwegian Institute for Water Research (NIVA) as
Water quality in Wheal Jane Mine, Cornwall, following refilling of mine (after Bowen and others 1994) Table 5
Water quality in Wheal Jane Mine, Cornwall, following refilling of mine (after Bowen and others 1994) Table 5
Killas shales intruded by quartz porphyry dykes which carry veins bearing cassiterite, chalcopyrite, pyrite, wol- framite, arsenopyrite, galena and silver. While the tin mi- nerals were always the most important ores, some of the more extensive old workings at Wheal Jane were among the most prolific producers of pyrite (as a by-product) in Cornwall. Additionally, arsenopyrite was worked for ars- enic from the Nangiles mine (also connected to Jane). The modern workings reach depths of 450 m and were exceptionally wet by UK standards, with routine dewater- ing around 107 I/day, and peak pumping rates up to six times this amount. Recent data strongly suggest that these high flow rates arise from the huge extent of the associated old workings, rather than from any unusual permeability in the Killas host rocks (Bowen and others 1994). During mining, pumped water was discharged to the River Carnon after partial treatment. In March 1991, a UK government grant to support dewatering was with- drawn, resulting in an immediate cessation of pumping and consequent closure of the mine (Hamilton and oth- ers 1994a). Tha eitheaniont mina «urator rico utmaamanitaroadn hath in
Killas shales intruded by quartz porphyry dykes which carry veins bearing cassiterite, chalcopyrite, pyrite, wol- framite, arsenopyrite, galena and silver. While the tin mi- nerals were always the most important ores, some of the more extensive old workings at Wheal Jane were among the most prolific producers of pyrite (as a by-product) in Cornwall. Additionally, arsenopyrite was worked for ars- enic from the Nangiles mine (also connected to Jane). The modern workings reach depths of 450 m and were exceptionally wet by UK standards, with routine dewater- ing around 107 I/day, and peak pumping rates up to six times this amount. Recent data strongly suggest that these high flow rates arise from the huge extent of the associated old workings, rather than from any unusual permeability in the Killas host rocks (Bowen and others 1994). During mining, pumped water was discharged to the River Carnon after partial treatment. In March 1991, a UK government grant to support dewatering was with- drawn, resulting in an immediate cessation of pumping and consequent closure of the mine (Hamilton and oth- ers 1994a). Tha eitheaniont mina «urator rico utmaamanitaroadn hath in
oe Rate of rise of water levels (mOD =above sea level) in Wheal Jane tin mine, shaft No. 2, following pump shutdown in March 1991 (reproduced with permission from J. Wright, Environment Agency, UK) Schematic section through Lokken mine, Norway
oe Rate of rise of water levels (mOD =above sea level) in Wheal Jane tin mine, shaft No. 2, following pump shutdown in March 1991 (reproduced with permission from J. Wright, Environment Agency, UK) Schematic section through Lokken mine, Norway
Time weighted annual transport of sulphate, copper, zinc and iron (t/a=tonnes/year) from the Kjoli mine area (after data from Arnesen and Iversen 1995) TOSVIGUUTT ~ WT TEIN, INUIWay Kjgli mine is another Cu and Zn mine in the vicinity of Killingdal which contributed heavily to pollution in the River Gaula. One million tonnes of ore were mined be- tween its opening in 1766 and its abandonment in 1941. Some 200,000 tonnes (or 80,000 m’*) of spoil have been dumped in tips around the mine area and these have been responsible for a yearly run-off of 4.2 tonnes Cu, 0.24 tonnes Zn, 38.3 tonnes Fe and 198 tonnes sulphate (@stmoe 1991; Iversen 1992). In 1981, the tips were col- lected in one area and were limed with 100 tonnes of cal- cium hydroxide (the quantity being that calculated to neutralize the run-off for 1 year). This failed to provide any long-term improvement in run-off. Indeed, following liming the situation appeared to deteriorate (Fig. 9). This is likely to have been due to the physical disturbance and hence oxygenation of the spoil tips. After a careful as- sessment, isolation of the spoil heaps (to hinder access by oxygen and water) was found to be the most promising course of remedial action. The isolation, which took place in 1989, employed spoil tip capping using synthetic geomembranes overlain by a natural till cover. The op- tion of using till alone was not considered to be suffi- ciently impermeable to hinder access of water. Also in 1989, the mine adit was plugged by concrete. The water level within the mine rose some 17 m but, by 1990, a new overflow had occurred at a higher level (Arnesen and Iv- ersen 1995). Nevertheless, the remedial action appears to have been largely successful. Although the yearly trans- port of Cu and Zn from the mine area is still around 600 kg/year Cu and 90 kg/year Zn (1992 values; Arnesen and Iversen 1995), these still represent a significant de- cline in Cu and Zn compared with 1985.
Time weighted annual transport of sulphate, copper, zinc and iron (t/a=tonnes/year) from the Kjoli mine area (after data from Arnesen and Iversen 1995) TOSVIGUUTT ~ WT TEIN, INUIWay Kjgli mine is another Cu and Zn mine in the vicinity of Killingdal which contributed heavily to pollution in the River Gaula. One million tonnes of ore were mined be- tween its opening in 1766 and its abandonment in 1941. Some 200,000 tonnes (or 80,000 m’*) of spoil have been dumped in tips around the mine area and these have been responsible for a yearly run-off of 4.2 tonnes Cu, 0.24 tonnes Zn, 38.3 tonnes Fe and 198 tonnes sulphate (@stmoe 1991; Iversen 1992). In 1981, the tips were col- lected in one area and were limed with 100 tonnes of cal- cium hydroxide (the quantity being that calculated to neutralize the run-off for 1 year). This failed to provide any long-term improvement in run-off. Indeed, following liming the situation appeared to deteriorate (Fig. 9). This is likely to have been due to the physical disturbance and hence oxygenation of the spoil tips. After a careful as- sessment, isolation of the spoil heaps (to hinder access by oxygen and water) was found to be the most promising course of remedial action. The isolation, which took place in 1989, employed spoil tip capping using synthetic geomembranes overlain by a natural till cover. The op- tion of using till alone was not considered to be suffi- ciently impermeable to hinder access of water. Also in 1989, the mine adit was plugged by concrete. The water level within the mine rose some 17 m but, by 1990, a new overflow had occurred at a higher level (Arnesen and Iv- ersen 1995). Nevertheless, the remedial action appears to have been largely successful. Although the yearly trans- port of Cu and Zn from the mine area is still around 600 kg/year Cu and 90 kg/year Zn (1992 values; Arnesen and Iversen 1995), these still represent a significant de- cline in Cu and Zn compared with 1985.
Sr ie ae The treatment system commenced between April and Au- gust 1992. Spoil tip drainage is introduced at a rate of 600,000 m*/year to the mine complex at the tourist mine Gamlegruva (Old Mine) and, after a journey of approxi- mately 1.2 km, taking several years, is pumped up from the newer Wallenberg shaft (Kommunal Teknikk 1994). The workings contain a considerable quantity of basic li- thologies, such as greenstone and calcite, which contri- bute towards raising the water’s pH. The other parameter most radically affected is Cu. Whereas the original water contains 75-200 mg/l Cu, the pumped effluent water con- tains a mere 0.5-10 mg/l Cu and around 20 mg/l Zn (Ar-
Sr ie ae The treatment system commenced between April and Au- gust 1992. Spoil tip drainage is introduced at a rate of 600,000 m*/year to the mine complex at the tourist mine Gamlegruva (Old Mine) and, after a journey of approxi- mately 1.2 km, taking several years, is pumped up from the newer Wallenberg shaft (Kommunal Teknikk 1994). The workings contain a considerable quantity of basic li- thologies, such as greenstone and calcite, which contri- bute towards raising the water’s pH. The other parameter most radically affected is Cu. Whereas the original water contains 75-200 mg/l Cu, the pumped effluent water con- tains a mere 0.5-10 mg/l Cu and around 20 mg/l Zn (Ar-
Water quality at the exit from Dausjo Lake, Skorovas mine (after data from Arnesen 1993b) These remedial works were only partially successful. To control contamination in the watercourse, 400 tonnes of lime per year were required, while the metal hydroxides precipitating out downstream of the liming station were causing a significant problem in themselves. In 1987- 1988, it was therefore decided to negate the need for lim- ing by removing the major source of the acid drainage contamination to the Skorovas catchment, namely the spoil tips. The favoured location for their removal was the bed of the 20 m deep Dausjo Lake. The lake was par- tially emptied and the spoil emplaced and covered with
Water quality at the exit from Dausjo Lake, Skorovas mine (after data from Arnesen 1993b) These remedial works were only partially successful. To control contamination in the watercourse, 400 tonnes of lime per year were required, while the metal hydroxides precipitating out downstream of the liming station were causing a significant problem in themselves. In 1987- 1988, it was therefore decided to negate the need for lim- ing by removing the major source of the acid drainage contamination to the Skorovas catchment, namely the spoil tips. The favoured location for their removal was the bed of the 20 m deep Dausjo Lake. The lake was par- tially emptied and the spoil emplaced and covered with
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Civil EngineeringEnvironmental GeologyAcid Mine DrainageMine WaterEarth and Environmental SciencesInterdisciplinary Engineering
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