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Entrena, A. L., Serrano, J. R., & Villoria, A. (1988). Descontaminacion de aguas de mina con recuperacion de los metales contenidos en ellas. Decontamination of mine waters by recovering the metals contained within them VIII congreso internacional de Mineria y metalurgia; tomo 8. VIII international conference on Mining and metallurgy; Volume 8. In Congreso Internacional de Mineria y Metalurgia, vol.8 (pp. 156–173).
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Arnekleiv, J. V., & Storset, L. (1995). Downstream effects of mine drainage on benthos and fish in a Norwegian river; a comparison of the situation before and after river rehabilitation. Heavy metal aspects of mining pollution and its remediation, 52, 35–43.
Abstract: Parts of the Norwegian river Gaula are strongly polluted from former mining activity in the area. In the most polluted parts of the river the concentration levels of Cu and Zn in 1986-1987 were up to 155 mu g l (super -1) and 186 mu g l (super -1) , respectively. In 1989 the spoil heaps in the mining area were covered with protective layers of moss-covered plastic. In 1991-1992 the concentration levels of Cu and Zn had decreased by 75% and 65%, respectively. Animal life in the polluted area seemed to be strongly affected by the trace metals in 1986-1987. The 1991-1992 results showed a marked increase in the number of species and in the number of individuals of each species of Ephemeroptera and Plecoptera, compared with the results from 1986-87. Good correlations were found between the concentrations of Cu in the water and both the number of species and the number of individuals of Ephemeroptera and Plecoptera. Analysis of the species Baetis rhodani, Diura nanseni and Rhyacophila nubila showed an average total dry weight content of Cu up to 264 mu g g (super -1) , of Zn up to 1930 mu g g (super -1) and of Cd up to 16 mu g g (super -1) . The contents of the three trace metals were significantly different from one species to another and in part between the stations for each species. In 1987 trout died after an exposure of one to two days on three test sites in the river, whereas in 1991-1992 40-75% of the trout survived an exposure period of several weeks at two of the sites. Electrofishing in 1991-1992 indicated recolonization of trout in the lower parts of the former affected and uninhabitable area.
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Bolzicco, J., Carrera, J., & Ayora, C. (2004). Eficiencia de la barrera permeable reactiva de Aznalcollar (Sevilla, Espana) como remedio de aguas acidas de mina. Reactive permeable disposal barrier at Aznalcollar Mine, Seville, Spain; as remediation for acid mine drainage. Revista Latino-Americana de Hidrogeologia, 4, 27–34.
Abstract: As a result of the collapse of a mine tailing dam in april 1998 about 40 km of the Agrio and Guadiamar valleys were covered with a layer of pyrite sludge. Although most of the sludge was removed, a small amount remains in the soil of the Agrio valley and the aquifer remains polluted with acid water (ph<4) and metals (10 mg/L Zn, 5 mg/L Cu and Al). A permeable reactive barrier was build across the aquifer to increase the alcalinity and retain the metals. The barrier is made up of three sections of 30 m longX1.4 m thickX5 m deep (average) containing different proportions of limestone gravel, organic compost and zero-valent iron. The residence time of the water in the barrier is about two days. Within the barrier, the pH values increase to near neutral mainly due to calcite dissolution. Metals co-precipitate as oxyhydroxides, and they are also adsorbed on the organic matter surface. Down-stream the barrier, the total pollution removal is around 60-90% for Zn and Cu, and from 50 to 90% for Al and acidity.
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Younger, P. L. (2000). Holistic remedial strategies for short- and long-term water pollution from abandoned mines. Transactions of the Institution of Mining and Metallurgy Section a-Mining Technology, 109, A210–A218.
Abstract: Where mining proceeds below the water-table-as it has extensively in Britain and elsewhere-water ingress is not only a hindrance during mineral extraction but also a potential liability after abandonment. This is because the cessation of dewatering that commonly follows mine closure leads to a rise in the water-table and associated, often rapid, changes in the chemical regime of the subsurface. Studies over the past two decades have provided insights into the nature and time-scales of these changes and provide a basis for rational planning of mine-water management during and after mine abandonment. The same insights into mine-water chemistry provide hints for the efficient remediation of pollution (typically due to Fe, Mn and Al and, in some cases, Zn, Cd, Pb and other metals). Intensive treatment (by chemical dosing with enhanced sedimentation or alternative processes, such as sulphidization or reverse osmosis) is often necessary only during the first few years following complete flooding of mine voids. Passive treatment (by the use of gravity-flow geochemical reactors and wetlands) may be both more cost-effective and ecologically more responsible in the long term. By the end of 1999 a total of 28 passive systems had been installed at United Kingdom mine sites, including examples of system types currently unique to the United Kingdom. Early performance data for all the systems are summarized and shown to demonstrate the efficacy of passive treatment when appropriately applied.
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Fyson, A., Nixdorf, B., & Steinberg, C. E. W. (1998). Manipulation of the sediment-water interface of extremely acidic mining lakes with potatoes; laboratory studies with intact sediment cores Geochemical and microbial processes in sediments and at the sediment-water interface of acidic mining lakes. In S. Peiffer (Ed.), Water, Air and Soil Pollution (pp. 353–363). 108.
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