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Bell, A. V., & Nancarrow, D. R. (1974). Salmon and mining in northeastern New Brunswick (a summary of the northeastern New Brunswick mine water quality program). CIM Bull., 67(751), 44–53.
Abstract: It was aimed toward developing solutions to major water quality problems in the base metal mining regions of northeastern New Brunswick and specifically toward insuring that the extremely valuable fishery resources and aquatic environments of the region could be maintained in the face of existing and future base metal mining developments. The program analyzed in detail the fishery resources of the region, their water quality requirements, the mineral resources of the region and the many aspects of mining waste management at each phase of mine development. This paper describes the reasons for the initial concern and the approach adopted toward finding a solution. It briefly summarizes the important findings and recommendations made to support the conclusion that the fishery resource can be maintained and co-exist with current and future base metal mining developments in the region
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Blowes, D. W., Ptacek, C. J., Benner, S. G., McRae, C. W. T., & Puls, R. W. (1998). Treatment of dissolved metals using permeable reactive barriers. Groundwater Quality: Remediation and Protection, (250), 483–490.
Abstract: Permeable reactive barriers are a promising new approach to the treatment of dissolved contaminants in aquifers. This technology has progressed rapidly from laboratory studies to full-scale implementation over the past decade. Laboratory treatability studies indicate the potential for treatment of a large number of inorganic contaminants, including As, Cd, Cr, Cu, Hg, Fe, Mn, Mo, Ni, Pb, Se, Tc, U, V, NO3, PO4, and SO4. Small scale field studies have indicated the potential for treatment of Cd, Cr, Cu, Fe, Ni, Pb, NO3, PO4, and SO4. Permeable reactive barriers have been used in full-scale installations for the treatment of hexavalent chromium, dissolved constituents associated with acid-mine drainage, including SO4, Fe, Ni, Co and Zn, and dissolved nutrients, including nitrate and phosphate. A full-scale barrier designed to prevent the release of contaminants associated with inactive mine tailings impoundment was installed at the Nickel Rim mine site in Canada in August 1995. This reactive barrier removes Fe, SO,, Ni and other metals. The effluent from the barrier is neutral in pH and contains no acid-generating potential, and dissolved metal concentrations are below regulatory guidelines. A full-scale reactive barrier was installed to treat Cr(VI) and halogenated hydrocarbons at the US Coast Guard site in Elizabeth City, North Carolina, USA in June 1996. This barrier removes Cr(VI) from >8 mg l(-1) to <0.01 mg l(-1).
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Conca, J. L., & Wright, J. (2006). An Apatite II permeable reactive barrier to remediate groundwater containing Zn, Pb and Cd. Appl. Geochem., 21(12), 2188–2200.
Abstract: Phosphate-induced metal stabilization involving the reactive medium Apatite II(TM) [Ca10-xNax(PO4)6-x(CO3)x(OH)2], where x < 1, was used in a subsurface permeable reactive barrier (PRB) to treat acid mine drainage in a shallow alluvial groundwater containing elevated concentrations of Zn, Pb, Cd, Cu, SO4 and NO3. The groundwater is treated in situ before it enters the East Fork of Ninemile Creek, a tributary to the Coeur d'Alene River, Idaho. Microbially mediated SO4 reduction and the subsequent precipitation of sphalerite [ZnS] is the primary mechanism occurring for immobilization of Zn and Cd. Precipitation of pyromorphite [Pb10(PO4)6(OH,Cl)2] is the most likely mechanism for immobilization of Pb. Precipitation is occurring directly on the original Apatite II. The emplaced PRB has been operating successfully since January of 2001, and has reduced the concentrations of Cd and Pb to below detection (2 μg L-1), has reduced Zn to near background in this region (about 100 μg L-1), and has reduced SO4 by between 100 and 200 mg L-1 and NO3 to below detection (50 μg L-1). The PRB, filled with 90 tonnes of Apatite II, has removed about 4550 kg of Zn, 91 kg of Pb and 45 kg of Cd, but 90% of the immobilization is occurring in the first 20% of the barrier, wherein the reactive media now contain up to 25 wt% Zn. Field observations indicate that about 30% of the Apatite II material is spent (consumed).
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Parker, G., Noller, B., & Waite, T. D. (1999). Assessment of the use of fast-weathering silicate minerals to buffer AMD in surface waters in tropical Australia. In D. E. Goldsack, N. Belzile, P. Yearwood, & G. J. Hall (Eds.), Sudbury '99; Mining and the environment II; Conference proceedings.
Abstract: Surface waters in the Pine Creek Geosyncline (located in Australia's “Top End”, defined as the area of Australia north of 15 degrees S) are characterized by their low carbonate buffering capacity. These waters are buffered by silicate weathering and hence are slightly acidic, ranging in pH from 4.0 to 6.0. The Pine Creek Geosyncline contains most of the Top Ends' economic mineral deposits and characteristically shows no correlation between carbonate minerals and sulfidic orebodies hosting gold deposits (unlike uranium deposits). Thus many gold mines do not have ready access to carbonate minerals for buffering acid mine drainage (AMD). It is possible that locally available fast-weathering silicate minerals may be used to buffer AMD seeps. The buffering intensity of silicate minerals exceeds that of carbonate minerals, but their slow dissolution kinetics has ensured that these materials have received little attention in treating AMD. In addition, carbonate mineral dissolution is retarded when contacted with intense AMD solutions due to the formation of surface coatings of iron minerals. The lower pH range of silicate mineral dissolution may prevent the formation of such coatings. The Pine Creek Geosyncline consists of a complex geochemistry, and a number of fast-weathering silicate minerals have been noted in various areas. The difficulty in assessing such minerals for use in buffering AMD is the lack of kinetic data available under conditions prevalent AMD (i.e., low pH solutions saturated with aluminium and silica). This study sets out to evaluate the applicability of using such minerals to treat AMD surface seeps.
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Becker, G., Wade, S., Riggins, J. D., Cullen, T. B., Venn, C., & Hallen, C. P. (2005). Effect of Bast Mine treatment discharge on Big Mine Run AMD and Mahanoy Creek in the Western Middle Anthracite Field of Pennsylvania.
Abstract: The Bast Mine (reopened in 2001) and Big Mine are two anthracite coal mines near Ashland, PA, that were abandoned in the 1930's and that are now causing drastic and opposite effects on the water quality of the streams originating from them. To quantify these effects, multiple samples were taken at 5 different sites: 3 along Big Mine Run and 2 from Mahanoy Creek (1 upstream and 1 downstream of the confluence with Big Mine Run). At each site, one set of the samples was treated with nitric acid for metals survey, one set was acidified with sulfuric acid for nitrate preservation, one set was filtered for sulfate and phosphate tests, and one set was unaltered. Measurements of pH, TDS, dissolved oxygen, and temperature were made in the field. Alkalinity, acidity, hardness, nitrates, orthophosphates and sulfates were analyzed using Hach procedures. Selected metals (Fe, Ni, Mg, Ca, Cu, Zn, Hg, Pb) were analyzed utilizing flame atomic absorption spectroscopy. Drainage from the Bast Mine is actively treated with hydrated lime before the water is piped down to Big Mine Run. pH and alkalinity values were much higher at the outflow compared to those in the water with which it merged. The two waters could be visibly distinguished some distance downstream. pH values decreased, sulfate and dissolved iron increased and alkalinity was reduced to zero until the confluence with Mahanoy Creek. The high alkalinity, turbidity, TDS and calcium values in Mahanoy Creek were somewhat reduced downstream of the confluence with the much lower discharge Big Mine Run.
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