Third national assessment
- Executive Summary
- 1.0 Introduction
- 2.0 Methods
- 3.0 Presence or Absence of Effects
- 4.0 Effluent Quality
- 5.0 Biological Monitoring Studies Investigating Observed Effects
- 6.0 Key Findings
- 7.0 Glossary
- 8.0 References
- Appendix A: Metal Mines Subject to the Metal Mining Effluent Regulations in 2013
- Appendix B: Effect Indicators, Critical Effects Sizes and Studies Conducted
- Appendix C: Mine-by-Mine Results of Studies Assessing Potential Effects
- Appendix D: Fish Tissue Mean Total Mercury Concentrations per Mine
- Appendix E: Trends in Sublethal Toxicity
- Appendix F: Trends in Sublethal Toxicity for Ore Types
- Appendix G: Annual Mean Concentrations of Effluent Characterization Data
- Appendix H: Mine-by-Mine Summary of Investigation Studies
4.0 Effluent Quality
4.1 Sublethal Toxicity Testing
Sublethal toxicity (SLT) testing is conducted on metal mining effluent from the final discharge point with potentially the most adverse environmental impact as per the MMER (Schedule 5, subsection 5(2)). Like effluent characterization and water quality monitoring,Footnote 9SLT testing provides supplementary information for the biological monitoring studies, including measures of year-to-year changes in effluent quality and site-specific estimates of the potential effects of effluent on biological components in the receiving environment.
Sublethal toxicity testing involves exposing test organisms to a range of effluent concentrations under laboratory conditions. The effluent concentration that causes 25% inhibition (IC25) in a test organism is determined. The test method that is used dictates the inhibition parameter, such as inhibition of growth or reproduction. A low IC25 (e.g., 10%) indicates a higher level of sublethal toxicity, because the inhibition occurred at a low effluent concentration. A higher IC25 indicates a lower level of sublethal toxicity. When the IC25 is reported as ≥100%,Footnote 10 the effluent is considered to be non-toxic for the sublethal effect being considered for the organism concerned.
Mines are required to conduct SLT testing twice per calendar year for the first three years, and once per year thereafter. Tests are conducted using standardized methods referenced in the MMER (Schedule 5, section 5) and several different tests are required including a fish early-life-stage development test, an invertebrate reproduction test, and plant and algal growth inhibition tests.
SLT testing results from the first 10 years of MMER implementation were compiled to assess the trends in effluent quality presented in this report. Effluent sublethal toxicity was examined for all mines combined and for mines with different ore types: precious metals (gold, silver), base metals (e.g., copper, zinc, and nickel), uranium, iron, and other ore types (e.g., tantalum, titanium, tungsten). Trends were examined over the 10-year period from 2003 to 2012. During this period, a total of 6,761 test results were submitted by 125 mines.
Annual geometric meansFootnote 11 of IC25 values were calculated for all mines combined and for each ore type, for each year. IC25 values from each year were sorted into three SLT categories: higher toxicity (IC25 ≤ 20%), lower toxicity (IC25 > 20% and <100%) and no toxicity (IC25 ≥ 100%). The geometric mean IC25 and percent of IC25 values in each SLT category is shown for each year for each of the five freshwater SLT tests in Appendix E. The annual geometric mean IC25 for each ore type for freshwater SLT test is shown in Appendix F.
4.1.1 Sublethal Toxicity of Mine Effluent
With the exception of the algal growth inhibition test, the overall sublethal toxicity of mine effluent remained stable between 2003 and 2012 (Figure 12). Algal growth inhibition decreased from 2007 to 2011, as shown by increases in IC25 geometric means and decreases in the proportion of “high toxicity” results (IC25 ≤ 20%) (Figure E4). Sublethal toxicity testing results for fish (Pimephales promelas) larval growth, invertebrate (Ceriodaphnia dubia)reproduction, and plant (Lemna minor) growth inhibition tests showed year-to-year variation, but no consistent trends over time (Figure 12).
Figure 12. Annual geometric mean IC25 (percent effluent on a volume basis) for all mines, for each freshwater SLT test
Figure 12 is a line chart illustrating the annual geometric mean IC25 for each of five different sublethal toxicity tests conducted between 2003 and 2012. The annual geometric means for fish larval growth inhibition on Pimephales promelas are 77, 76, 87, 89, 85, 90, 88, 90, 92 and 87. The annual geometric means for alga growth inhibition on Pseudokirchneriella subcapitata are 55, 48, 54, 48, 59, 62, 69, 79, 81 and 64. The annual geometric means for plant growth inhibition on Lemna minor dry weight are 44, 33, 40, 50, 43, 49, 45, 45, 41 and 53. The annual geometric means for plant growth inhibition on Lemna minor frond number are 19, 23, 22, 25, 21, 32, 25, 23, 25 and 36. The annual geometric means for invertebrate reproduction inhibition on Ceriodaphnia dubia are 25, 24, 28, 37, 30, 26, 26, 28, 23 and 29.
Note: Ranges in number of tests conducted per year were as follows: Pimephales promelas, n = 111–140; Pseudokirchneriella subcapitata, n = 119–152; Lemna minor dry weight, n = 117–142; Ceriodaphnia dubia, n = 121–155 ; Lemna minor frond number, n = 116–145.
Trends in effluent sublethal toxicity were more variable for different ore types, likely due to the smaller data set size for ore type analyses (Figures F1-F5). The results from base and precious metal mines on algal growth showed decreases in toxicity between 2007 and 2011 and an increase in 2012. Although some trends may be apparent for uranium, iron and “other” ore types, they should be interpreted with caution given the small sample sizes.
In locations where Pimephales promelas (fathead minnow) is not an indigenous species, an analogous fish test is conducted using rainbow trout (Oncorhynchus mykiss). Eight base and two precious metal mines submitted SLT results for tests conducted on rainbow trout between 2003 and 2012. These mines were located predominantly in western Canada. For base metal mines, rainbow trout IC25 values ranged from 54 to 100%, and 62% of tests indicated no sublethal toxicity (IC25 ≥ 100%). For precious metal mines, in all 22 tests conducted, no sublethal toxicity (IC25 ≥100%) to rainbow trout was observed.
Mines that discharge to marine or estuarine environments are required to conduct SLT tests using marine organisms and different test methods than those used for freshwater tests. Two base metal mines conducted marine SLT tests. Sand dollar IC25values ranged from 4 to 18%, white sea urchin IC25 values ranged from 10 to ≥100%, red macroalgae IC25 values ranged from 4 to 56%, topsmelt IC25 values ranged from 67 to 73% and inland silverside IC25 values ranged from 16 to ≥100%. There were no apparent trends in effluent sublethal toxicity over time at either mine.
4.1.2 Responsiveness of Sublethal Toxicity Tests
The effluent concentration at which inhibition occurs is influenced by which standardized test is used. The test that shows inhibition at the lowest effluent concentration is considered the most responsive test. The sublethal toxicity result obtained with one type of test compared to the other tests for the same effluent sample can be used to assess relative responsiveness. It is important to monitor the responsiveness of SLT tests to ensure that the tests being used are still relevant for the effluent being evaluated (for example, species that are consistently non-responsive could be removed from the testing requirements in the future). Changes to effluent quality over time are better captured using responsive tests. The responsiveness of each test compared to other tests can help predict the dominant toxicant. For example, fish are known to be more responsive to ammonia (toxic to fish) than invertebrates, whereas invertebrates are often more responsive to metals than fish. The annual geometric means of IC25 and the proportion of tests indicating no sublethal toxicity for all mines show the relative responsiveness of each test (Figures E1 to E5).
The tests that were the most responsive to effluent were the invertebrate reproduction and plant growth (frond number) inhibition tests, for which the annual geometric means of IC25 were in the range from ~20 to 40%. The plant growth (frond dry weight) inhibition test was slightly less responsive, with IC25 annual geometric means ranging from ~40 to 50%, followed by the algal growth inhibition test, with a wider range of annual geometric means of IC25, specifically ~50 to 80%. The fish early-life-stage development inhibition test was the least responsive test, with IC25 annual geometric means in the ~80 to 90% range. The relative responsiveness of these different tests was found to be the same when the proportion of tests that indicated no sublethal toxicity was compared. These results corroborate the findings of the Second National Assessment (Environment Canada 2012b), thus indicating that the relative responsiveness of SLT tests to metal mine effluent has remained constant through the first 10 years of testing.
The most responsive SLT tests among ore types with large data sets (precious and base metals) were the invertebrate reproduction and plant growth (frond number) inhibition tests (Figures E1, E2). Although the data for uranium and “other” ore types are more variable, the invertebrate reproduction and plant growth (frond number and dry weight) inhibition tests appeared to be the most responsive tests, and the fish early-life-stage development inhibition test, the least responsive (Figures E3, E4). For iron ore mines, there were no consistent differences in test responsiveness (Figure E5).
4.1.3 Stimulation in Algal and Plant Growth Inhibition Tests
The algal and plant growth inhibition test methods require that the occurrence of growth stimulation be reported. Stimulation refers to an increase in growth of test organisms relative to controls after effluent exposure. If stimulation at low concentrations is followed by an inhibitory response at higher concentrations, this low-dose stimulation may be related to an organism’s response to low levels of a toxic substance. This effect is referred to as hormesis. If the stimulatory effect is observed across all effluent concentrations, or increases with increasing effluent concentration, the results may be indicative of an enrichment effect related to increased nutrient availability rather than hormesis.
From 2010 to 2012, stimulation was reported in 55% of algal growth tests and 19% of plant growth inhibition tests. Stimulation appears to be more frequent for base and precious metal mines than for other ore types, particularly in the case of the plant growth inhibition test (Table 1).
|Test||Ore Type||Percent of tests with stimulation||Total number of tests conducted|
|Plant Growth Inhibition Lemna minor frond number||base metal||26||135|
|Plant Growth Inhibition Lemna minor frond number||precious metal||19||177|
|Plant Growth Inhibition Lemna minor frond number||iron ore||6||31|
|Plant Growth Inhibition Lemna minor frond number||other||5||19|
|Plant Growth Inhibition Lemna minor frond number||uranium||0||23|
|Plant Growth Inhibition Lemna minor frond number||Total||19||385|
|Algal Growth Inhibition Pseudokirchneriella subcapitata||base metal||67||144|
|Algal Growth Inhibition Pseudokirchneriella subcapitata||precious metal||53||180|
|Algal Growth Inhibition Pseudokirchneriella subcapitata||other||42||19|
|Algal Growth Inhibition Pseudokirchneriella subcapitata||uranium||42||26|
|Algal Growth Inhibition Pseudokirchneriella subcapitata||iron ore||29||34|
|Algal Growth Inhibition Pseudokirchneriella subcapitata||Total||55||403|
The overall stimulation results presented here include both types of stimulation observed--hormesis or enrichment effect--and thus likely overestimate the enrichment effect. Additional test information is needed to differentiate between these types of stimulation.
4.2 Effluent Characterization
Effluent characterization is conducted by analyzing a sample of effluent from each final discharge point (FDP) to determine the concentrations of substances in mine effluent that are potential contaminants. The annual mean concentration of each of the nine specified substances (MMER, Schedule 5, section 4) was calculated for two different groups of FDPs. The first group contained the FDPs associated with the biological monitoring studies and the second group contained all other FDPs. These annual means are presented in Appendix G to give a general overview of effluent chemistry.
- Date modified: