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Chapter 5b

Sbrionez — Thu, 17 May 2012 18:11:53 GMT

5.4.4 Introduction to Geochemical Characterization -

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	Figure 5-5 (Maest and Kuipers, 2005) schematically presents the components of a typical geochemical characterization program aimed at developing water quality predictions and the general sequence in which these components should be conducted. This flowchart in Figure 5-5 provides more detail on the Phase 1 and Phase 2 testing programs illustrated in Phase 1 consists of a screening-level program, while Phase 2 is more detailed. In some cases, a Phase 1 program may be sufficient for mine water and waste management, whereas in more complex settings, a Phase 2 program is generally required. When a Phase 2 program is required, the results from the Phase 1 program are used to identify samples for kinetic testing or additional static testing, such as those identified in [[Chapter_5#Figure 5-1\|Figure 5-1]] and Figure 5-5.		Figure 5-5 (Maest and Kuipers, 2005) schematically presents the components of a typical geochemical characterization program aimed at developing water quality predictions and the general sequence in which these components should be conducted. This flowchart in Figure 5-5 provides more detail on the Phase 1 and Phase 2 testing programs illustrated in Phase 1 consists of a screening-level program, while Phase 2 is more detailed. In some cases, a Phase 1 program may be sufficient for mine water and waste management, whereas in more complex settings, a Phase 2 program is generally required. When a Phase 2 program is required, the results from the Phase 1 program are used to identify samples for kinetic testing or additional static testing, such as those identified in [[Chapter_5#Figure 5-1\|Figure 5-1]] and Figure 5-5.

-	Therefore, not all components of the geochemical testing program may be necessary depending on site-specific characteristics and prediction needs. Individual test methods are described in more detail in the Sections 5.3.4.2 through 5.3.4.8, and are summarized in [[Table 5-1\|Table 5-1]]. Not all test methods presented in the table are appropriate for evaluation of mine wastes, even though they occasionally are requested by regulatory authorities. Such methods include the Toxicity Characteristic Leaching Procedure (TCLP) and Waste Extraction Test (WET), as explained in more detail in [[Table 5-1\|Table 5-1]].	+	Therefore, not all components of the geochemical testing program may be necessary depending on site-specific characteristics and prediction needs. Individual test methods are described in more detail in the Sections 5.4.7 through 5.4.13, and are summarized in [[Table 5-1\|Table 5-1]]. Not all test methods presented in the table are appropriate for evaluation of mine wastes, even though they occasionally are requested by regulatory authorities. Such methods include the Toxicity Characteristic Leaching Procedure (TCLP) and Waste Extraction Test (WET), as explained in more detail in [[Table 5-1\|Table 5-1]].

	<div id="Figure 5-5" style="text-align:center">'''Figure 5-5: Schematic Illustration of Geochemical Characterization Program <br />(modified from Maest and Kuipers, 2005)'''<br />		<div id="Figure 5-5" style="text-align:center">'''Figure 5-5: Schematic Illustration of Geochemical Characterization Program <br />(modified from Maest and Kuipers, 2005)'''<br />

Chapter 7

Sbrionez — Thu, 17 May 2012 16:26:00 GMT

7.11 References -

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	:Gusek, J.J., 2008. Passive Treatment 101: An Overview of the Technologies. 2008 U.S. EPA/National Groundwater Association Remediation of Abandoned Mine Land Conference, October. Denver, CO.		:Gusek, J.J., 2008. Passive Treatment 101: An Overview of the Technologies. 2008 U.S. EPA/National Groundwater Association Remediation of Abandoned Mine Land Conference, October. Denver, CO.
		+
		+	:Gusek, J.J. and J.S. Waples (2009). A Periodic Table of Passive Treatment for Mining Influenced Water. In: Proceedings of the 8th International Conference on Acid Rock Drainage (ICARD), June 22-26, Skellefteå, Sweden.

	:Gusek, J., Mann, C., Wildeman, T., and D. Murphy, 2000. Operational results of a 1200 gpm passive bioreactor for metal mine drainage, West Fork, Missouri. In: Proceedings of 5th International Conference on Acid Rock Drainage (ICARD), May 21-24, Denver, CO, Society for Mining, Metallurgy, and Exploration, Inc., Littleton, CO, 2:1133-1137.		:Gusek, J., Mann, C., Wildeman, T., and D. Murphy, 2000. Operational results of a 1200 gpm passive bioreactor for metal mine drainage, West Fork, Missouri. In: Proceedings of 5th International Conference on Acid Rock Drainage (ICARD), May 21-24, Denver, CO, Society for Mining, Metallurgy, and Exploration, Inc., Littleton, CO, 2:1133-1137.

Chapter 6

Sbrionez — Thu, 17 May 2012 16:20:31 GMT

6.6.6 Engineered Barriers -

Chapter 4

Sbrionez — Thu, 17 May 2012 16:08:26 GMT

4.3.2 Source Material Geochemical Characterization -

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	ABA analysis typically includes analysis of paste pH, sulphur speciation, neutralizing potential (NP) or acid neutralizing capacity (ANC) and total inorganic carbon (TIC). Paste pH is used as an indicator of the presence of stored acidity. Sulphur speciation data, which includes information on the presence of non-acid generating sulphur minerals, are used to calculate the acid generation potential of the material. NP and ANC provide estimates of the acid neutralizing potential of a material (NP in the units of tCaCO<sub>3</sub>		ABA analysis typically includes analysis of paste pH, sulphur speciation, neutralizing potential (NP) or acid neutralizing capacity (ANC) and total inorganic carbon (TIC). Paste pH is used as an indicator of the presence of stored acidity. Sulphur speciation data, which includes information on the presence of non-acid generating sulphur minerals, are used to calculate the acid generation potential of the material. NP and ANC provide estimates of the acid neutralizing potential of a material (NP in the units of tCaCO<sub>3</sub>
-	/kt and ANC in the units of ~~kgH2SO4~~/t). TIC is used to calculate the carbonate neutralizing value (CNV) or carbonate NP (Ca-NP), and allows assessment of the fraction of NP or ANC attributed to carbonate mineral phases. In some cases the CNV based on TIC (or even total carbon) can be used as a surrogate to estimate the NP or ANC at a particular site. In combination, results from ABA, NAG, and elemental and mineralogical analysis are used to assess the relative proportions of acid generating and acid consuming materials.	+	/kt and ANC in the units of kgH<sub>2</sub>SO<sub>4</sub>/t). TIC is used to calculate the carbonate neutralizing value (CNV) or carbonate NP (Ca-NP), and allows assessment of the fraction of NP or ANC attributed to carbonate mineral phases. In some cases the CNV based on TIC (or even total carbon) can be used as a surrogate to estimate the NP or ANC at a particular site. In combination, results from ABA, NAG, and elemental and mineralogical analysis are used to assess the relative proportions of acid generating and acid consuming materials.

	Short-term extraction tests (such as 24-hour batch extraction tests using deionised water) provide information on the short term metal leaching potential. The nature of the sample (e.g., unoxidized vs. oxidized; oxidation products absent vs. oxidation products present), test solution to solid ratio, lixiviant, reaction time, and sample particle size should all be considered in the evaluation and comparison of leach test results.		Short-term extraction tests (such as 24-hour batch extraction tests using deionised water) provide information on the short term metal leaching potential. The nature of the sample (e.g., unoxidized vs. oxidized; oxidation products absent vs. oxidation products present), test solution to solid ratio, lixiviant, reaction time, and sample particle size should all be considered in the evaluation and comparison of leach test results.

Chapter 7

Sbrionez — Thu, 17 May 2012 15:25:26 GMT

7.5 Mine Drainage Treatment Technologies -

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	A wide spectrum of drainage treatment technologies has been developed, proven, and applied to many different applications. The generic range of mine drainage treatment technologies is reflected in Figure 7-2. The description of the different drainage treatment technologies in this section will be framed in the context of current best practice of proven technologies.		A wide spectrum of drainage treatment technologies has been developed, proven, and applied to many different applications. The generic range of mine drainage treatment technologies is reflected in Figure 7-2. The description of the different drainage treatment technologies in this section will be framed in the context of current best practice of proven technologies.

-	Mine drainage treatment technologies can be broadly classified into active treatment, passive treatment, and in situ treatment as described in Table 7-1. The selection of the appropriate category of mine drainage for a specific application is influenced by the aspects summarized in Table 7-1	+	Mine drainage treatment technologies can be broadly classified into active treatment, passive treatment, and in situ treatment as described in Table 7-1. The selection of the appropriate category of mine drainage for a specific application is influenced by the aspects summarized in Table 7-1

	<div id="Figure 7-2" style="text-align:center">'''Figure 7-2: Generic Range of Drainage Treatment Technologies'''<br />		<div id="Figure 7-2" style="text-align:center">'''Figure 7-2: Generic Range of Drainage Treatment Technologies'''<br />

Chapter 4

Sbrionez — Thu, 17 May 2012 06:02:24 GMT

4.3.2 Source Material Geochemical Characterization -

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	An essential component of static testing is mineralogical analysis that, at a minimum, includes identification of all sulphur and carbonate minerals. If possible, mineralogical analysis should be quantitative. A description of how minerals with acid generation and acid neutralization potential occur (e.g., grain size, grain morphology, disseminated, fracture coatings, as inclusions) is also relevant in the assessment of reactivity (i.e., rate of oxidation or dissolution).		An essential component of static testing is mineralogical analysis that, at a minimum, includes identification of all sulphur and carbonate minerals. If possible, mineralogical analysis should be quantitative. A description of how minerals with acid generation and acid neutralization potential occur (e.g., grain size, grain morphology, disseminated, fracture coatings, as inclusions) is also relevant in the assessment of reactivity (i.e., rate of oxidation or dissolution).

-	ABA analysis typically includes analysis of paste pH, sulphur speciation, neutralizing potential (NP) or acid neutralizing capacity (ANC) and total inorganic carbon (TIC). Paste pH is used as an indicator of the presence of stored acidity. Sulphur speciation data, which includes information on the presence of non-acid generating sulphur minerals, are used to calculate the acid generation potential of the material. NP and ANC provide estimates of the acid neutralizing potential of a material (NP in the units of ~~tCaCO3~~/kt and ANC in the units of kgH2SO4/t). TIC is used to calculate the carbonate neutralizing value (CNV) or carbonate NP (Ca-NP), and allows assessment of the fraction of NP or ANC attributed to carbonate mineral phases. In some cases the CNV based on TIC (or even total carbon) can be used as a surrogate to estimate the NP or ANC at a particular site. In combination, results from ABA, NAG, and elemental and mineralogical analysis are used to assess the relative proportions of acid generating and acid consuming materials.	+	ABA analysis typically includes analysis of paste pH, sulphur speciation, neutralizing potential (NP) or acid neutralizing capacity (ANC) and total inorganic carbon (TIC). Paste pH is used as an indicator of the presence of stored acidity. Sulphur speciation data, which includes information on the presence of non-acid generating sulphur minerals, are used to calculate the acid generation potential of the material. NP and ANC provide estimates of the acid neutralizing potential of a material (NP in the units of tCaCO<sub>3</sub>
		+	/kt and ANC in the units of kgH2SO4/t). TIC is used to calculate the carbonate neutralizing value (CNV) or carbonate NP (Ca-NP), and allows assessment of the fraction of NP or ANC attributed to carbonate mineral phases. In some cases the CNV based on TIC (or even total carbon) can be used as a surrogate to estimate the NP or ANC at a particular site. In combination, results from ABA, NAG, and elemental and mineralogical analysis are used to assess the relative proportions of acid generating and acid consuming materials.

	Short-term extraction tests (such as 24-hour batch extraction tests using deionised water) provide information on the short term metal leaching potential. The nature of the sample (e.g., unoxidized vs. oxidized; oxidation products absent vs. oxidation products present), test solution to solid ratio, lixiviant, reaction time, and sample particle size should all be considered in the evaluation and comparison of leach test results.		Short-term extraction tests (such as 24-hour batch extraction tests using deionised water) provide information on the short term metal leaching potential. The nature of the sample (e.g., unoxidized vs. oxidized; oxidation products absent vs. oxidation products present), test solution to solid ratio, lixiviant, reaction time, and sample particle size should all be considered in the evaluation and comparison of leach test results.

Chapter 7

Sbrionez — Thu, 17 May 2012 05:57:52 GMT

7.5.2.7 Alkaline Leach Beds -

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	Thus, longevity of treatment is a major concern for ALDs, especially in terms of water flow through the limestone. Unless there is no Fe3+, dissolved oxygen, or Al present, eventual clogging of the limestone pore spaces with precipitated Al and Fe and/or gypsum is predicted at many sites (Nairn et al., 1991). Selection of the appropriate water and environmental conditions is critical for long-term alkalinity generation in an ALD. Like wetlands, ALDs may be a solution for ARD treatment for specific water conditions or for a finite period, after which the system must be replenished or replaced.		Thus, longevity of treatment is a major concern for ALDs, especially in terms of water flow through the limestone. Unless there is no Fe3+, dissolved oxygen, or Al present, eventual clogging of the limestone pore spaces with precipitated Al and Fe and/or gypsum is predicted at many sites (Nairn et al., 1991). Selection of the appropriate water and environmental conditions is critical for long-term alkalinity generation in an ALD. Like wetlands, ALDs may be a solution for ARD treatment for specific water conditions or for a finite period, after which the system must be replenished or replaced.

-	Tracer studies indicated that while ALDs approximate plug-flow systems, some short-circuiting occurs, and dead areas do exist. Calculated retention times, using 49% porosity, were in fairly good agreement with the median retention times of the tracer tests (Watzlaf et al., 2004). Water quality data determine the applicability of an ALD and flow data provide the basis for sizing an effective ALD for the desired design life. Approximately 15 hours of contact time between mine water and limestone in an ALD is necessary to achieve a maximum concentration of alkalinity. In order to achieve 15 hours of contact time within an ALD, 2,800 kg of limestone is required for each L/min of mine water flow. For example, an ALD that discharges water with 300 mg/L of alkalinity (the maximum sustained concentration thus far observed in an ALD effluent), dissolves 1,750 kg of limestone (90% calcium carbonate) in ten years, per each L/min of mine water flow. Therefore, a limestone bed should contain 6,200 kg of limestone for each L/min of flow (equivalent to 26 tons of limestone for each gallon per minute of flow). This assumes that the ALD is constructed with 90% ~~CaCO3~~ limestone rock and has a porosity of 49%. The calculation also assumes that the original CMD does not contain Fe3+ or Al. The presence of these ions could result in faster rates of limestone dissolution due to the generation of acidity during hydrolysis. More importantly, they have the potential to limit limestone dissolution and cause a significant reduction in permeability that could very well lead to failure (as previously discussed). For a more detailed discussion of limestone dissolution rates, see Cravotta and Watzlaf (2002).	+	Tracer studies indicated that while ALDs approximate plug-flow systems, some short-circuiting occurs, and dead areas do exist. Calculated retention times, using 49% porosity, were in fairly good agreement with the median retention times of the tracer tests (Watzlaf et al., 2004). Water quality data determine the applicability of an ALD and flow data provide the basis for sizing an effective ALD for the desired design life. Approximately 15 hours of contact time between mine water and limestone in an ALD is necessary to achieve a maximum concentration of alkalinity. In order to achieve 15 hours of contact time within an ALD, 2,800 kg of limestone is required for each L/min of mine water flow. For example, an ALD that discharges water with 300 mg/L of alkalinity (the maximum sustained concentration thus far observed in an ALD effluent), dissolves 1,750 kg of limestone (90% calcium carbonate) in ten years, per each L/min of mine water flow. Therefore, a limestone bed should contain 6,200 kg of limestone for each L/min of flow (equivalent to 26 tons of limestone for each gallon per minute of flow). This assumes that the ALD is constructed with 90% CaCO<sub>3</sub> limestone rock and has a porosity of 49%. The calculation also assumes that the original CMD does not contain Fe3+ or Al. The presence of these ions could result in faster rates of limestone dissolution due to the generation of acidity during hydrolysis. More importantly, they have the potential to limit limestone dissolution and cause a significant reduction in permeability that could very well lead to failure (as previously discussed). For a more detailed discussion of limestone dissolution rates, see Cravotta and Watzlaf (2002).

	To summarize, the success of ALDs depends on the following:		To summarize, the success of ALDs depends on the following:
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	====7.5.2.7 Alkaline Leach Beds====		====7.5.2.7 Alkaline Leach Beds====
-	Alkaline leach beds are ponds or cells filled with limestone or steel slag. Like OLDs, they have occasionally been used to improve water quality at abandoned mine sites. The alkalinity is added up-gradient of significant concentrations of dissolved metals. Ideally, slightly acidic water with no metals is introduced into limestone-filled ponds. The limestone dissolution adds 50 to 75 mg/L of alkalinity as ~~CaCO3~~ to the water. The alkalinity buffers the stream and mitigates the effects of ARD entering downstream. At several sites where limestone-filled alkaline leach beds have been installed, fisheries have been re-established.	+	Alkaline leach beds are ponds or cells filled with limestone or steel slag. Like OLDs, they have occasionally been used to improve water quality at abandoned mine sites. The alkalinity is added up-gradient of significant concentrations of dissolved metals. Ideally, slightly acidic water with no metals is introduced into limestone-filled ponds. The limestone dissolution adds 50 to 75 mg/L of alkalinity as CaCO<sub>3</sub> to the water. The alkalinity buffers the stream and mitigates the effects of ARD entering downstream. At several sites where limestone-filled alkaline leach beds have been installed, fisheries have been re-established.

-	In situations where large metal and acid loads enter downstream, the upstream water must be charged with greater levels of alkalinity. Steel slag, a by-product and waste from the making of steel, contains high levels of alkalinity that are released into water. Alkaline leach beds can be filled with steel slag, which can generate much higher alkalinities in water (as much as 2,000 mg/L as ~~CaCO3~~). Sites where these high alkalinities are generated must be carefully selected, because water that is too alkaline can be toxic to aquatic life.	+	In situations where large metal and acid loads enter downstream, the upstream water must be charged with greater levels of alkalinity. Steel slag, a by-product and waste from the making of steel, contains high levels of alkalinity that are released into water. Alkaline leach beds can be filled with steel slag, which can generate much higher alkalinities in water (as much as 2,000 mg/L as CaCO<sub>3</sub>). Sites where these high alkalinities are generated must be carefully selected, because water that is too alkaline can be toxic to aquatic life.

	[[#top\|Top of this page]]		[[#top\|Top of this page]]

Chapter 10

Sbrionez — Thu, 17 May 2012 05:48:47 GMT

10.9 References -

Chapter 8

Sbrionez — Thu, 17 May 2012 05:46:37 GMT

8.6 References and Further Reading -

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Chapter 3

Sbrionez — Thu, 17 May 2012 05:43:42 GMT

3.7 References -

Acknowledgments

Sbrionez — Thu, 17 May 2012 05:33:05 GMT

Version 1 Chapter Champions -

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	===Version 1 Chapter Champions===		===Version 1 Chapter Champions===

-	Spanish translation Executive Summary – Mr. Patrick Williamson	+	Spanish translation Executive Summary – Mr. Patrick Williamson – Schlumberger Water Services

-	French translation Executive Summary – Mr. Gilles ~~Tremblay – Natural~~ Resources Canada (Canada)	+	French translation Executive Summary – Mr. Gilles TremblayNatural Resources Canada (Canada)

	<table border="0" cellspacing="0" cellpadding="0" width="62%">		<table border="0" cellspacing="0" cellpadding="0" width="62%">

Chapter 7

Sbrionez — Thu, 17 May 2012 05:23:37 GMT

7.11 References -

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Case Studies Chapter 4

WikiSysop — Sat, 12 May 2012 19:25:43 GMT

Geochemical Characterisation in Australia -

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	Samples generally contained relatively low concentrations of Total C and essentially no TOC, and hence Total C values were effectively equivalent to Carbonate C and therefore consistent with the generally low ANC values. Likewise, there was generally a good correlation between measured NAPP values (Table 1) and NAPP values calculated from existing Total Sulfur and Total Carbon values for the same samples. Based on this correlation, NAPP values could be calculated for each 1m interval within the pit shell using the S and C assay data. This calculation was incorporated into the mine block model to create an environmental geochemistry layer. The ARD risk classification system (above) was then applied to the mine block model, based on the calculated NAPP layer, permitting estimation of the annual production of waste rock within each ARD risk category (Figure 2).		Samples generally contained relatively low concentrations of Total C and essentially no TOC, and hence Total C values were effectively equivalent to Carbonate C and therefore consistent with the generally low ANC values. Likewise, there was generally a good correlation between measured NAPP values (Table 1) and NAPP values calculated from existing Total Sulfur and Total Carbon values for the same samples. Based on this correlation, NAPP values could be calculated for each 1m interval within the pit shell using the S and C assay data. This calculation was incorporated into the mine block model to create an environmental geochemistry layer. The ARD risk classification system (above) was then applied to the mine block model, based on the calculated NAPP layer, permitting estimation of the annual production of waste rock within each ARD risk category (Figure 2).
-
-	Table 1: Average static geochemical results for the major waste rock lithologies.

	<div id="Table 1" style="text-align:center">'''Table 1: Average static geochemical results for the major waste rock lithologies.'''<br />		<div id="Table 1" style="text-align:center">'''Table 1: Average static geochemical results for the major waste rock lithologies.'''<br />

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Case Studies Chapter 4

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Geochemical Characterisation in Australia -

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	Despite the broad range in sulfur contents of the bulk samples, the sulfide-normalised PORs for all lithologies were similar and averaged 0.2 wt% FeS<sub>2</sub> / year. These POR units (wt% FeS<sub>2</sub> / year) mean that 0.2 wt% of all pyrite exposed to atmospheric oxygen will be oxidised to form sulfuric acid (H<sub>2</sub>SO<sub>4</sub>) per year. In this form, PORs can be used to produce annual (or monthly) acidity generation rates for any unsaturated sulfidic material, as long as the total mass of the material and its sulfide content are known (see box below).		Despite the broad range in sulfur contents of the bulk samples, the sulfide-normalised PORs for all lithologies were similar and averaged 0.2 wt% FeS<sub>2</sub> / year. These POR units (wt% FeS<sub>2</sub> / year) mean that 0.2 wt% of all pyrite exposed to atmospheric oxygen will be oxidised to form sulfuric acid (H<sub>2</sub>SO<sub>4</sub>) per year. In this form, PORs can be used to produce annual (or monthly) acidity generation rates for any unsaturated sulfidic material, as long as the total mass of the material and its sulfide content are known (see box below).

-		+	<div id="Table 2" style="text-align:center">[[Image:aciditygenerationratesforanyunsaturated.gif]]</div>

	For example, in Year 1 of operations, it was estimated that 3,668 kt of unsaturated waste rock (category AG4) would be produced, with an average 0.9 wt% FeS<sub>2</sub>. For a POR of 0.2 wt% FeS<sub>2</sub> per year, this material can be expected to generate approximately 108 tonnes H2SO4 per year without any ARD management intervention (Table 2). This is equivalent to 29 kg H<sub>2</sub>SO<sub>4</sub> per tonne of waste rock per year. Using this approach, the annual acidity generation loads produced during Years 1 to 5 of mining operations were quantified for all lithologies (see Table 2).		For example, in Year 1 of operations, it was estimated that 3,668 kt of unsaturated waste rock (category AG4) would be produced, with an average 0.9 wt% FeS<sub>2</sub>. For a POR of 0.2 wt% FeS<sub>2</sub> per year, this material can be expected to generate approximately 108 tonnes H2SO4 per year without any ARD management intervention (Table 2). This is equivalent to 29 kg H<sub>2</sub>SO<sub>4</sub> per tonne of waste rock per year. Using this approach, the annual acidity generation loads produced during Years 1 to 5 of mining operations were quantified for all lithologies (see Table 2).

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Case Studies Chapter 4

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Geochemical Characterisation in Australia -

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	Table 2: Estimated annual acidity generation loads from unsaturated waste rock for Years 1 to 5 in the absence of ARD management strategies. The LAC (likely to be acid consuming) category was disregarded to provide a conservative assessment.		Table 2: Estimated annual acidity generation loads from unsaturated waste rock for Years 1 to 5 in the absence of ARD management strategies. The LAC (likely to be acid consuming) category was disregarded to provide a conservative assessment.

-		+	<div id="Table 2" style="text-align:center">[[Image:Estimatedannualaciditygeneration.gif]]</div>

	'''Development of waste rock designs'''		'''Development of waste rock designs'''

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Case Studies Chapter 4

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Geochemical Characterisation in Australia -

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-	Figure 1: NAGpH vs. NAPP for seven waste rock lithologies.	+	<div id="Figure 1" style="text-align:center">'''Figure 1: NAGpH vs. NAPP for seven waste rock lithologies.'''<br />
-		+	[[Image:NAGpHvsNAPPforsevenwasterocklithologies.gif]]</div>
-	NAGpHvsNAPPforsevenwasterocklithologies.gif	+


-	Figure 2: Annual production of waste rock according to ARD risk classification.	+	<div id="Figure 2" style="text-align:center">'''Figure 2: Annual production of waste rock according to ARD risk classification.'''<br />
-		+	[[Image:AnnualproductionofwasterockaccordingtoARDrisk.gif]]</div>
-	AnnualproductionofwasterockaccordingtoARDrisk.gif	+


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-	For example, in Year 1 of operations, it was estimated that 3,668 kt of unsaturated waste rock (category AG4) would be produced, with an average 0.9 wt% ~~FeS2~~. For a POR of 0.2 wt% ~~FeS2~~ per year, this material can be expected to generate approximately 108 tonnes H2SO4 per year without any ARD management intervention (Table 2). This is equivalent to 29 kg ~~H2SO4~~ per tonne of waste rock per year. Using this approach, the annual acidity generation loads produced during Years 1 to 5 of mining operations were quantified for all lithologies (see Table 2).	+	For example, in Year 1 of operations, it was estimated that 3,668 kt of unsaturated waste rock (category AG4) would be produced, with an average 0.9 wt% FeS<sub>2</sub>. For a POR of 0.2 wt% FeS<sub>2</sub> per year, this material can be expected to generate approximately 108 tonnes H2SO4 per year without any ARD management intervention (Table 2). This is equivalent to 29 kg H<sub>2</sub>SO<sub>4</sub> per tonne of waste rock per year. Using this approach, the annual acidity generation loads produced during Years 1 to 5 of mining operations were quantified for all lithologies (see Table 2).

	Table 2: Estimated annual acidity generation loads from unsaturated waste rock for Years 1 to 5 in the absence of ARD management strategies. The LAC (likely to be acid consuming) category was disregarded to provide a conservative assessment.		Table 2: Estimated annual acidity generation loads from unsaturated waste rock for Years 1 to 5 in the absence of ARD management strategies. The LAC (likely to be acid consuming) category was disregarded to provide a conservative assessment.

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Case Studies Chapter 4

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Geochemical Characterisation in Australia -

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	Table 1: Average static geochemical results for the major waste rock lithologies.		Table 1: Average static geochemical results for the major waste rock lithologies.

		+	<div id="Table 1" style="text-align:center">'''Table 1: Average static geochemical results for the major waste rock lithologies.'''<br />
		+	[[Image:AveragestaticgeochemicalresultsforLithologies.gif]]</div>

-	* n = number of samples


-	Figure 1: NAGpH vs. NAPP for seven waste rock lithologies.	+	Figure 1: NAGpH vs. NAPP for seven waste rock lithologies.
		+
		+	NAGpHvsNAPPforsevenwasterocklithologies.gif
		+

-	Figure 2: Annual production of waste rock according to ARD risk classification.	+	Figure 2: Annual production of waste rock according to ARD risk classification.
		+
		+	AnnualproductionofwasterockaccordingtoARDrisk.gif
		+
		+

	'''Kinetic geochemical testwork and estimation of annual acidity generation rates'''		'''Kinetic geochemical testwork and estimation of annual acidity generation rates'''
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	The measured oxygen consumption rate for each bulk sample was assumed to be proportional to the mass of pyrite in the sample and was converted into a POR using the stoichiometric relationship in the complete reaction for pyrite oxidation by oxygen (ie. 3.75 moles of oxygen are consumed to fully oxidise 1 mole of pyrite). This assumes that all sulfur present is in the form of reactive pyrite and that the pyrite oxidation reaction is driven to completion. Oxygen dilution associated with carbon dioxide generation from carbonate dissolution (independently measured) was also taken into account in oxygen consumption calculations.		The measured oxygen consumption rate for each bulk sample was assumed to be proportional to the mass of pyrite in the sample and was converted into a POR using the stoichiometric relationship in the complete reaction for pyrite oxidation by oxygen (ie. 3.75 moles of oxygen are consumed to fully oxidise 1 mole of pyrite). This assumes that all sulfur present is in the form of reactive pyrite and that the pyrite oxidation reaction is driven to completion. Oxygen dilution associated with carbon dioxide generation from carbonate dissolution (independently measured) was also taken into account in oxygen consumption calculations.

-	Despite the broad range in sulfur contents of the bulk samples, the sulfide-normalised PORs for all lithologies were similar and averaged 0.2 wt% ~~FeS2~~ / year. These POR units (wt% ~~FeS2~~ / year) mean that 0.2 wt% of all pyrite exposed to atmospheric oxygen will be oxidised to form sulfuric acid (~~H2SO4~~) per year. In this form, PORs can be used to produce annual (or monthly) acidity generation rates for any unsaturated sulfidic material, as long as the total mass of the material and its sulfide content are known (see box below).	+	Despite the broad range in sulfur contents of the bulk samples, the sulfide-normalised PORs for all lithologies were similar and averaged 0.2 wt% FeS<sub>2</sub> / year. These POR units (wt% FeS<sub>2</sub> / year) mean that 0.2 wt% of all pyrite exposed to atmospheric oxygen will be oxidised to form sulfuric acid (H<sub>2</sub>SO<sub>4</sub>) per year. In this form, PORs can be used to produce annual (or monthly) acidity generation rates for any unsaturated sulfidic material, as long as the total mass of the material and its sulfide content are known (see box below).

Chapter 5

WikiSysop — Sat, 12 May 2012 18:45:40 GMT

5.3.1 Acid Rock Drainage/Metal Leaching Characterization -

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	The concept of desulphurization of tailings to prevent ARD has been considered since the early 1990s (Bois et al., 2004). The concept is based on the separation of non-economic sulphide minerals into a low-volume stream, leaving the majority of the tailings with a low sulphur content that will be less reactive and preferably non-acid generating. The two tailings streams can then be managed differently. The high-sulphur material can be selectively deposited in the tailings pond to remain submerged in water during operations and post closure. Alternatively, the high-sulphur tailings can be managed to ensure that they will be covered by the low-sulphur material after closure if assessment shows that this approach is considered protective of water quality during operations and in the long term. In any case, there will be a need to manage the high-sulphur tailings that presumably will represent only a small fraction of the total tailings volume produced during the operation.		The concept of desulphurization of tailings to prevent ARD has been considered since the early 1990s (Bois et al., 2004). The concept is based on the separation of non-economic sulphide minerals into a low-volume stream, leaving the majority of the tailings with a low sulphur content that will be less reactive and preferably non-acid generating. The two tailings streams can then be managed differently. The high-sulphur material can be selectively deposited in the tailings pond to remain submerged in water during operations and post closure. Alternatively, the high-sulphur tailings can be managed to ensure that they will be covered by the low-sulphur material after closure if assessment shows that this approach is considered protective of water quality during operations and in the long term. In any case, there will be a need to manage the high-sulphur tailings that presumably will represent only a small fraction of the total tailings volume produced during the operation.

-	Desulphurization can be achieved in different ways, depending on the ore type and metallurgical process used to extract economic minerals from the ore. A separate flotation circuit or additional flotation cells to increase sulphide removal in the mill can be constructed. Bois et al. (2004) showed that metal mine tailings containing about 20% S could be separated by flotation, into materials containing 0.5% S and 43% S. Hesketh et al. (2010) also demonstrated sulphur removal by flotation technology and achieved a low sulphur tailings with 0.22% S that was non-acid generating with a net neutralization potential (NNP) of 25 kg-~~CaCO3~~/t.	+	Desulphurization can be achieved in different ways, depending on the ore type and metallurgical process used to extract economic minerals from the ore. A separate flotation circuit or additional flotation cells to increase sulphide removal in the mill can be constructed. Bois et al. (2004) showed that metal mine tailings containing about 20% S could be separated by flotation, into materials containing 0.5% S and 43% S. Hesketh et al. (2010) also demonstrated sulphur removal by flotation technology and achieved a low sulphur tailings with 0.22% S that was non-acid generating with a net neutralization potential (NNP) of 25 kg-CaCO<sub>3</sub>/t.

	Sulphur separation was used at a mill that processed nickel sulphide ore in Canada. The sulphur was initially removed to lower the sulphur content in coarse-grained tailings that were used for mine backfill. The fine fraction or cyclone overflow was utilized as a low-sulphur cover material on existing high-sulphur tailings (Martin and Fyfe, 2011).		Sulphur separation was used at a mill that processed nickel sulphide ore in Canada. The sulphur was initially removed to lower the sulphur content in coarse-grained tailings that were used for mine backfill. The fine fraction or cyclone overflow was utilized as a low-sulphur cover material on existing high-sulphur tailings (Martin and Fyfe, 2011).
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	Blending is the mixing of waste rock types of varying acid generation and neutralization potential to create a deposit that generates a discharge of acceptable quality. The effectiveness of blending as an option depends on the availability of materials and the mine plan, the general stoichiometric balance between acid producing and acid neutralizing materials, geochemical properties, reactivity of waste rock types, flow pathways created within the deposit, and the extent of mixing and method of blending. Homogeneous and thorough mixing is generally required to achieve maximum benefit (MEND, 1998a and 2001). Evidence from field trials indicates limited success with mixing of waste rock types using haul trucks, but better mixing of waste rock with limestone was achieved using a conveyor system and stacker (Miller et al., 2006).		Blending is the mixing of waste rock types of varying acid generation and neutralization potential to create a deposit that generates a discharge of acceptable quality. The effectiveness of blending as an option depends on the availability of materials and the mine plan, the general stoichiometric balance between acid producing and acid neutralizing materials, geochemical properties, reactivity of waste rock types, flow pathways created within the deposit, and the extent of mixing and method of blending. Homogeneous and thorough mixing is generally required to achieve maximum benefit (MEND, 1998a and 2001). Evidence from field trials indicates limited success with mixing of waste rock types using haul trucks, but better mixing of waste rock with limestone was achieved using a conveyor system and stacker (Miller et al., 2006).

-	Operational experience indicates that, for effective blending of PAG rock with limestone, it is essential that all size fractions within the blend be at least acid-base neutral (i.e., NPR (ANC/MPA) of at least 1). Since the run of mine particle size of limestone is generally coarser than PAG rock, the acid base balance or NPR of the bulk waste rock needs to be greater than one. Experience with rock types at Freeport (Indonesia) and Ok Tedi (Papua New Guinea) indicates that well-mixed PAG and limestone rock needs to have a bulk NNP of more than 150 kg ~~CaCO3~~/t (or net acid production potential (NAPP) of less than 150 kg H2SO4/t). The actual blend will depend on site factors and particle size distribution for each rock type.	+	Operational experience indicates that, for effective blending of PAG rock with limestone, it is essential that all size fractions within the blend be at least acid-base neutral (i.e., NPR (ANC/MPA) of at least 1). Since the run of mine particle size of limestone is generally coarser than PAG rock, the acid base balance or NPR of the bulk waste rock needs to be greater than one. Experience with rock types at Freeport (Indonesia) and Ok Tedi (Papua New Guinea) indicates that well-mixed PAG and limestone rock needs to have a bulk NNP of more than 150 kg CaCO<sub>3</sub>/t (or net acid production potential (NAPP) of less than 150 kg H2SO4/t). The actual blend will depend on site factors and particle size distribution for each rock type.

	'''6.6.3.7 Co-disposal'''		'''6.6.3.7 Co-disposal'''
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	A relatively common approach to mitigation of ARD is the control of solution pH by the addition of alkaline materials. Methods for use of alkaline materials include blending with waste rock, amendment of tailings, placement of alkaline material above or below wastes as liner or cover materials, and treatment of drainage (BC AMD, 1989; PaDEP, 1998, Chapter 13; Miller et al., 2003 and 2006; and Taylor et al., 2006).		A relatively common approach to mitigation of ARD is the control of solution pH by the addition of alkaline materials. Methods for use of alkaline materials include blending with waste rock, amendment of tailings, placement of alkaline material above or below wastes as liner or cover materials, and treatment of drainage (BC AMD, 1989; PaDEP, 1998, Chapter 13; Miller et al., 2003 and 2006; and Taylor et al., 2006).

-	Addition of alkaline materials can control ARD, provided intimate blending can be achieved; this is often a difficult task. The effectiveness of the method is dependent on the pathways of movement of water through the system, degree of mixing, and the nature of the contact between acidic rock and the alkaline materials. If the mixture is not homogeneous and there is not good contact between the materials, then localized “hot spots” of acid generation may occur. The type, purity, reactivity, availability, and proportion of the alkaline material are also important. Common additives at metal mines include limestone (~~CaCO3~~) and lime (CaO or Ca(OH)2). Liquid forms are considerably diluted relative to solid forms and have limited longevity, but may provide better penetration of the acid generating mine waste.	+	Addition of alkaline materials can control ARD, provided intimate blending can be achieved; this is often a difficult task. The effectiveness of the method is dependent on the pathways of movement of water through the system, degree of mixing, and the nature of the contact between acidic rock and the alkaline materials. If the mixture is not homogeneous and there is not good contact between the materials, then localized “hot spots” of acid generation may occur. The type, purity, reactivity, availability, and proportion of the alkaline material are also important. Common additives at metal mines include limestone (CaCO<sub>3</sub>) and lime (CaO or Ca(OH)2). Liquid forms are considerably diluted relative to solid forms and have limited longevity, but may provide better penetration of the acid generating mine waste.

-	At coal mines, limestone is often the least expensive and most readily available source of alkalinity. It has a neutralization potential (NP) between 75 and 100% of ~~CaCO3~~ equivalent, and is safe and easy to handle. On the other hand, it has no cementing properties and cannot be used as a barrier or low-permeability material. Fluidized Bed Combustion (FBC) ash generally has NP values between 20 and 40% of ~~CaCO3~~ equivalent, and tends to harden into a cement after wetting (Skousen et al., 1997a). Other power-generation ashes, like flue gas desulfurization (FGD) products, may also have significant NP, which can represent suitable alkaline amendment materials (Stehouwer et al., 1995). Kiln dust, produced by lime and cement kilns, contains similar NP levels as FBC ash, but also contains 50 to 70% un-reacted limestone. Kiln dust absorbs moisture and hardens upon wetting (Rich and Hutchison, 1994), and is widely used as a stabilization and barrier material at coal mines in the US.	+	At coal mines, limestone is often the least expensive and most readily available source of alkalinity. It has a neutralization potential (NP) between 75 and 100% of CaCO<sub>3</sub> equivalent, and is safe and easy to handle. On the other hand, it has no cementing properties and cannot be used as a barrier or low-permeability material. Fluidized Bed Combustion (FBC) ash generally has NP values between 20 and 40% of CaCO<sub>3</sub> equivalent, and tends to harden into a cement after wetting (Skousen et al., 1997a). Other power-generation ashes, like flue gas desulfurization (FGD) products, may also have significant NP, which can represent suitable alkaline amendment materials (Stehouwer et al., 1995). Kiln dust, produced by lime and cement kilns, contains similar NP levels as FBC ash, but also contains 50 to 70% un-reacted limestone. Kiln dust absorbs moisture and hardens upon wetting (Rich and Hutchison, 1994), and is widely used as a stabilization and barrier material at coal mines in the US.

-	Steel slags, when fresh, have NP values from 45 to 90% of ~~CaCO3~~ equivalent. Steel slag can be used as an alkaline amendment as well as a medium for alkaline recharge trenches. Slags are produced by a number of processes, so care is needed to ensure that candidate slags are not prone to leaching metal ions like Cr, Mn, and Ni. Potential sources of alkaline material should be checked by a complete analysis (see Chapter 5) to evaluate the possibility of adverse effects on leachate water quality.	+	Steel slags, when fresh, have NP values from 45 to 90% of CaCO<sub>3</sub> equivalent. Steel slag can be used as an alkaline amendment as well as a medium for alkaline recharge trenches. Slags are produced by a number of processes, so care is needed to ensure that candidate slags are not prone to leaching metal ions like Cr, Mn, and Ni. Potential sources of alkaline material should be checked by a complete analysis (see Chapter 5) to evaluate the possibility of adverse effects on leachate water quality.

	Use of alkaline materials overlying acid generating mine waste can provide a long-term source of alkalinity, may lead to formation of a “chemical cap” (i.e., a hardpan) at the interface between alkaline and acid generating material, and may produce a passivating coating on the surface of acid generating particles. However, the effectiveness of this approach depends on the solubility of the neutralizing agent and the flux of infiltrating water available to carry the alkalinity down to the underlying sulphidic waste. Use of alkaline materials underneath acid generating mine waste may result in formation of a passivating coating on the surface of alkaline particles, thus reducing considerably the effectiveness of this strategy. Benefits and limitations of alkaline amendments are summarized in Table 6-3.		Use of alkaline materials overlying acid generating mine waste can provide a long-term source of alkalinity, may lead to formation of a “chemical cap” (i.e., a hardpan) at the interface between alkaline and acid generating material, and may produce a passivating coating on the surface of acid generating particles. However, the effectiveness of this approach depends on the solubility of the neutralizing agent and the flux of infiltrating water available to carry the alkalinity down to the underlying sulphidic waste. Use of alkaline materials underneath acid generating mine waste may result in formation of a passivating coating on the surface of alkaline particles, thus reducing considerably the effectiveness of this strategy. Benefits and limitations of alkaline amendments are summarized in Table 6-3.
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	'''6.6.4.3 Examples of Alkaline Materials Applications'''		'''6.6.4.3 Examples of Alkaline Materials Applications'''

-	'''''Limestone, ~~CaCO3~~'''''	+	'''''Limestone, CaCO<sub>3</sub>'''''

	Rotary drum stations have been used in West Virginia to grind limestone into a powder form before application into acidic streams (Zurbuch, 1984; 1996).		Rotary drum stations have been used in West Virginia to grind limestone into a powder form before application into acidic streams (Zurbuch, 1984; 1996).
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	'''''Dry Covers Nomenclature'''''		'''''Dry Covers Nomenclature'''''

-	*Alkaline Covers – Cover systems designed to release alkalinity to infiltrating waters. Alkalinity generally consists of dissolved carbonate species that are derived from the dissolution of limestone (~~CaCo3~~).	+	*Alkaline Covers – Cover systems designed to release alkalinity to infiltrating waters. Alkalinity generally consists of dissolved carbonate species that are derived from the dissolution of limestone (CaCo<sub>3</sub>).
	*Dry Covers – Cover layer(s) consisting of earthen or synthetic materials in contrast to “wet” covers that involve water.		*Dry Covers – Cover layer(s) consisting of earthen or synthetic materials in contrast to “wet” covers that involve water.
	*Organic Covers – Covers consisting of organic material that may act as a reductant (electron donor) that can scavenge or remove oxygen and possibly drive other reducing reactions such as sulphate reduction.		*Organic Covers – Covers consisting of organic material that may act as a reductant (electron donor) that can scavenge or remove oxygen and possibly drive other reducing reactions such as sulphate reduction.

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	:International Cyanide Management Institute (ICMI), 2006. International Cyanide Management Code For The Manufacture, Transport and Use of Cyanide In The Production of Gold (Cyanide Code). http://www.cyanidecode.org/		:International Cyanide Management Institute (ICMI), 2006. International Cyanide Management Code For The Manufacture, Transport and Use of Cyanide In The Production of Gold (Cyanide Code). http://www.cyanidecode.org/
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	:Kimberley Process Certification Scheme (KPCS), 2008. http://www.kimberleyprocess.com/home/index_en.html		:Kimberley Process Certification Scheme (KPCS), 2008. http://www.kimberleyprocess.com/home/index_en.html
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	:Lee, M., 1999. Risk Assessment Framework for the Management of Sulphidic Mine Wastes. Australian Centre for Mining Environmental Research (ACMER), September.		:Lee, M., 1999. Risk Assessment Framework for the Management of Sulphidic Mine Wastes. Australian Centre for Mining Environmental Research (ACMER), September.
-

	:Mine Environment Neutral Drainage (MEND), 2005. List of Potential Information Requirements in Metal Leaching/Acid Rock Drainage (ML/ARD) Assessment and Mitigation Work. MEND Report 5.10E.		:Mine Environment Neutral Drainage (MEND), 2005. List of Potential Information Requirements in Metal Leaching/Acid Rock Drainage (ML/ARD) Assessment and Mitigation Work. MEND Report 5.10E.
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	:Minerals Council of Australia (MCA), 2006. Enduring Value - the Australian Minerals Industry Framework for Sustainable Development. http://www.minerals.org.au/enduringvalue		:Minerals Council of Australia (MCA), 2006. Enduring Value - the Australian Minerals Industry Framework for Sustainable Development. http://www.minerals.org.au/enduringvalue
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	:Mining Association of Canada (MAC), 2007. Towards Sustainable Mining. http://www.mining.ca/www/Towards_Sustaining_Mining/index.php		:Mining Association of Canada (MAC), 2007. Towards Sustainable Mining. http://www.mining.ca/www/Towards_Sustaining_Mining/index.php
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	:Mining, Minerals & Sustainable Development Project (MMSD), 2002. http://www.iied.org/sustainable-markets/key-issues/business-and-sustainable-development/mining-minerals-and-sustainable-development		:Mining, Minerals & Sustainable Development Project (MMSD), 2002. http://www.iied.org/sustainable-markets/key-issues/business-and-sustainable-development/mining-minerals-and-sustainable-development
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	:Newmont Metallurgical Services, 2003. Newmont, Standard ARD Waste Rock Evaluation Methods. February 20, Englewood, CO.		:Newmont Metallurgical Services, 2003. Newmont, Standard ARD Waste Rock Evaluation Methods. February 20, Englewood, CO.
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	:New Zealand Government, 1991. Resource Management Act (RMA). Ministry for the Environment.		:New Zealand Government, 1991. Resource Management Act (RMA). Ministry for the Environment.
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	:Price, W.A., 1997. Draft Guidelines and Recommended Methods for the Prediction of Metal Leaching and Acid rock Drainage at Mine sites in British Columbia. British Columbia Ministry of Employment and Investment, April.		:Price, W.A., 1997. Draft Guidelines and Recommended Methods for the Prediction of Metal Leaching and Acid rock Drainage at Mine sites in British Columbia. British Columbia Ministry of Employment and Investment, April.
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	:Price, W.A., and J.C. Errington, 1998. Guidelines for Metal Leaching and Acid Rock Drainage at Mine sites in British Columbia. Ministry of Energy and Mines, August.		:Price, W.A., and J.C. Errington, 1998. Guidelines for Metal Leaching and Acid Rock Drainage at Mine sites in British Columbia. Ministry of Energy and Mines, August.
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	:Richards, D.G., Borden, R.K., David, J.W., Blowes, D.W., Logsdon, M.J., Miller, S.D., Slater, S., Smith, L., and G.W. Wilson, 2006. Design and Implementation of a Strategic Review of ARD Risk at Rio Tinto. In: R.I. Barnhisel (Ed.), Proceedings 7<sup>th</sup> International Conference on Acid Rock Drainage (ICARD), March 26-30, St. Louis, MO, American Society of Mining and Reclamation (ASMR), Lexington, KY.		:Richards, D.G., Borden, R.K., David, J.W., Blowes, D.W., Logsdon, M.J., Miller, S.D., Slater, S., Smith, L., and G.W. Wilson, 2006. Design and Implementation of a Strategic Review of ARD Risk at Rio Tinto. In: R.I. Barnhisel (Ed.), Proceedings 7<sup>th</sup> International Conference on Acid Rock Drainage (ICARD), March 26-30, St. Louis, MO, American Society of Mining and Reclamation (ASMR), Lexington, KY.
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	:Rio Tinto, 2003. Standard E3 - Acid rock drainage prediction and control. December. http://www.riotinto.com/documents/AcidRockDrainageControl.pdf		:Rio Tinto, 2003. Standard E3 - Acid rock drainage prediction and control. December. http://www.riotinto.com/documents/AcidRockDrainageControl.pdf
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	:World Bank Group, 2007. Environmental, Health and Safety Guidelines for Mining. International Finance Corporation (IFC), December.		:World Bank Group, 2007. Environmental, Health and Safety Guidelines for Mining. International Finance Corporation (IFC), December.
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←Older revision		Revision as of 18:45, 12 May 2012
Line 98:		Line 98:
	====5.3.1 Acid Rock Drainage/Metal Leaching Characterization====		====5.3.1 Acid Rock Drainage/Metal Leaching Characterization====

-	Figure 5-1 represents an idealized generic overview of a comprehensive ARD/ML prediction program. Application of this approach needs to be customized to account for site-specific aspects. The program, as presented, applies to a project that advances from exploration through to mine closure.	+	Figure 5-1 represents an idealized generic overview of a comprehensive ARD/ML prediction program. Application of this approach needs to be customized to account for site-specific aspects. The program, as presented, applies to a project that advances from exploration through to mine closure.
		+
	The flowchart in Figure 5-1 assumes that ARD/ML prediction activities are performed at every stage of a project. These activities are coupled with other project planning activities and the level of detail of ARD/ML characterization activities is determined by the stage of the project. Data are accumulated as the project proceeds so that the appropriate information needed to support engineering design is available in a timely manner.		The flowchart in Figure 5-1 assumes that ARD/ML prediction activities are performed at every stage of a project. These activities are coupled with other project planning activities and the level of detail of ARD/ML characterization activities is determined by the stage of the project. Data are accumulated as the project proceeds so that the appropriate information needed to support engineering design is available in a timely manner.
		+
	The following six mine phases are identified in the GARD Guide:		The following six mine phases are identified in the GARD Guide:
	*Exploration		*Exploration
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	The flowchart focuses on the earlier stages of mine development, a critical period for proactive mine development, when the initial geochemical characterization is usually conducted. The description of mine phases in Figure 5-1 therefore differs slightly from the convention used in the GARD Guide. Both sets of nomenclature are presented.		The flowchart focuses on the earlier stages of mine development, a critical period for proactive mine development, when the initial geochemical characterization is usually conducted. The description of mine phases in Figure 5-1 therefore differs slightly from the convention used in the GARD Guide. Both sets of nomenclature are presented.
		+
	The major “pillars” of the flowchart are as follows:		The major “pillars” of the flowchart are as follows:
	*'''Typical Project Phase.''' Five typical major project phases of the mining cycle are included in Figure 5-1 (initial exploration, advanced exploration, prefeasibility, feasibility/permitting, and project implementation).		*'''Typical Project Phase.''' Five typical major project phases of the mining cycle are included in Figure 5-1 (initial exploration, advanced exploration, prefeasibility, feasibility/permitting, and project implementation).
Line 115:		Line 118:
	*'''ML/ARD Program Activities.''' This element indicates the main types of prediction and characterization activities. All activities are considered cumulative. Activities occurring in earlier phases are continued here as needed to meet future objectives.		*'''ML/ARD Program Activities.''' This element indicates the main types of prediction and characterization activities. All activities are considered cumulative. Activities occurring in earlier phases are continued here as needed to meet future objectives.

-	If new information becomes available during any one of the stages of the ARD/ML program (e.g., a change in mine plan, or unexpected monitoring results), re-evaluation of earlier stages may be required. These types of iterations are omitted from the flowchart in Figure 5-1 for clarity.	+	If new information becomes available during any one of the stages of the ARD/ML program (e.g., a change in mine plan, or unexpected monitoring results), re-evaluation of earlier stages may be required. These types of iterations are omitted from the flowchart in Figure 5-1 for clarity. An approach for characterization, classification and prediction adopted by Earth Systems is documented in the [[Case_Studies_Chapter_4#Geochemical Characterisation in Australia\|'''Characterization Case Study''']].
-		+

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