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Water Quality

State of Water Quality Reports for some BC Locations


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Alsek River above Bates River 1992 - 1994

The Alsek River originates in the Yukon Territory and flows through the northwest corner of British Columbia. From here, the Alsek River flows southwest through the Alaskan panhandle into the Pacific Ocean. Activities in the Alsek watershed are minimal as much of the watershed lies within Kluane National Park.

This report assesses the water quality data collected by Environment Canada at the monitoring station just upstream from the Bates River. Water quality samples were collected bi-monthly during 1992 to 1994 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge at the same location. There are several main conclusions to this report:

  1. Not enough data were available to comment on trends in water quality.
  2. Peak non-filterable residue and turbidity values occurred during peak flows and turbidity removal would be necessary before use as drinking water.
  3. High metals levels that exceeded water quality criteria corresponded with high suspended sediments, suggesting that the metals were in a particulate form and probably not biologically available and would be removed by the turbidity removal process needed before drinking.
  4. The river had a low sensitivity to acid inputs.
  5. Hardness levels were within the optimum range for drinking water most of the time, with highest values in the spring and lowest values in the autumn.

Water quality monitoring is continuing for the Alsek River above Bates River at present, and its future will depend on federal obligations under the Heritage Rivers Act and the needs of Kluane National Park. British Columbia has no interest in further monitoring of the Alsek at this time because there were no apparent problems in Alsek River water quality and none are expected in the foreseeable future. The data obtained to date would suffice as baseline information for general planning purposes.


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Bear River at Stewart, 1987 - 1994

This report assesses eight years of water quality data from the Bear River. The Bear River flows in a southerly direction from the north central coastal area of the province, emptying into the top end of the Portland Canal near Stewart, BC. The Portland Canal separates the southern portion of the state of Alaska and the north central BC coast. Environment Canada has monitored the Bear River since 1987 collecting 26 samples per year. One other related monitoring station within this area is the Salmon River near Hyder, Alaska.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest were water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, wildlife, recreation, irrigation and livestock watering. There are several main conclusions of this assessment:

  1. No environmentally significant trends in water quality were detected by visual inspection of the plotted data.
  2. The water quality of the Bear River at Stewart during 1987 to 1994 is believed to be in a state of natural origin. It is influenced by glacial erosion, snow melt and mineralization. The watershed is sparsely populated and relatively unimpacted by resource development.
  3. The water was cool or cold throughout the year and not warm enough during the summer months to permit water-contact recreation such as swimming. This is due, in part, to the fact that a large volume of the water is glacier fed.
  4. The water was high in selenium due to the geology of the watershed and possibly historical mining activities. It often exceeded the selenium criterion for aquatic life.
  5. Because of the impact of glaciers, the water was often very turbid especially during annual freshet when higher flows resulted in increased erosion, suspended sediment, and turbidity. The extent to which human land use activities contribute to this natural phenomenon is unknown.
  6. The increased turbidity makes it necessary to treat drinking water to remove high levels of turbidity prior to use during freshet.
  7. Freshet also brings increased levels of total metals, total phosphorus, total organic carbon and apparent colour. Most of these may not be of concern as they are due to the increased suspended sediment in the water, and thus are probably largely biologically unavailable or would be removed by the treatment needed prior to drinking.
  8. Turbidity and suspended solids have remained stable or decreased slightly over the last 8 years.

The main recommendations are to suspend trend monitoring at this station and identify the sources of the elevated selenium in the watershed for possible remediation.


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Bonaparte River near the mouth, 1980 - 1994

The Bonaparte River, located in British Columbia's southern interior, is a main tributary to the Thompson River. River water quality is important for uses such as drinking water, recreation, irrigation, and livestock watering, as well as for aquatic life and wildlife. Water quality is affected by ranching and agriculture, two sewage treatment plants, two landfill sites, urbanization and forestry. Previous studies on this river have observed high levels of fecal coliforms, suspended solids, turbidity and algae.

In this report, data obtained under the Canada-BC Water Quality Monitoring Agreement, were assessed for trends and concerns in water quality. Monitoring was carried out monthly at the mouth of the river from 1985 to 1995 for 47 variables. These variables were graphed, and then compared to Approved and Working Criteria for Water Quality and to site-specific objectives set by the Ministry of Environment, Lands and Parks (now Water, Land and Air Protection). Related sites within this watershed include the Thompson River at Spences Bridge, the South Thompson River at Kamloops and the North Thompson River at Kamloops. There are several main conclusions of this study:

  1. No environmentally significant trends in water quality were detected through visual assessment of the data.
  2. Fecal coliforms at times exceeded the site-specific objective designed to permit drinking water use after partial treatment and disinfection. It appears that complete water treatment and disinfection are needed and that consumption during spring freshet should be avoided.
  3. Periphyton chlorophyll-a, a measure of attached algal growth, consistently exceeded the site-specific objective to protect recreation and aquatic life. Dissolved phosphorus levels were elevated, indicating an ample supply to support algal growth.
  4. Non-filterable residue (suspended solids) and turbidity were often elevated during spring freshet, and site-specific objectives were not attained on a regularly basis.
  5. Turbidity removal, complete water treatment, and disinfection are needed before drinking water use.
  6. The pH was slightly high for drinking water, possibly affecting chlorination effectiveness and causing encrustation and scaling.
  7. The river was well buffered against acid and metal inputs.
  8. Hardness levels during the winter were poor for drinking water aesthetics, but still tolerable.
  9. The variables that exceeded criteria during spring freshet were: aluminum, chromium, copper, iron, manganese, titanium and zinc. These metals were largely associated with high levels of turbidity and suspended sediments, suggesting that the metals were in particulate form, probably not biologically available, and would be removed by the drinking water treatment needed to remove turbidity.

The following recommendations are made:

  1. Remediation
    1. Efforts to reduce fecal coliforms, non-filterable residue, turbidity, and periphyton chlorophyll-a levels in this river should continue as outlined in the B.C. Water Quality Status report, including rehabilitating streamside vegetation, and preventing direct access to the water by cattle (Ministry of Environment, Lands and Parks, 1996).
  2. Monitoring
    1. Monitoring should continue for the following variables related to agriculture, forestry and urbanization: flow, hardness, periphyton chlorophyll-a, fecal coliforms, true colour, E. coli, ammonia, total dissolved nitrogen, pH, total dissolved phosphorus, non-filterable residue, sulphate, turbidity and specific conductivity.
    2. The following metals have had levels exceeding criteria within the past two years (i.e., 1994-95), and thus should be monitored (total and dissolved): aluminum, chromium, copper, iron, manganese, and titanium.
    3. Minimum detectable limits (MDLs) should be lowered for antimony, arsenic, cadmium, chromium, copper, lead, selenium, silver, thallium and zinc. MDLs should be at least 10 times below the water quality criteria for all variables.
    4. Increased sampling of 5 samples in 30 days should be employed for copper, E. coli and fecal coliforms to compare to criteria and objectives more precisely.


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Boundary Creek at Midway, 1980 - 1994 + February 1996

This report assesses the long-term water quality trends in the Boundary Creek, a trans-boundary stream which flows from south central BC into Washington State. Boundary Creek, a major tributary from the north, joins the Kettle River a short distance downstream from Midway, BC very near the international boundary between Canada and the US. The Boundary Creek at Midway station is located a short distance east of the town of Midway and very near the point where Boundary Creek joins the Kettle river before it crosses the international boundary. Environment Canada has monitored the Boundary Creek at Midway station since 1980 collecting 6 to 8 samples per year.

Three other related monitoring stations within the BC portion of the Kettle River watershed are the Kettle River at Midway, the Kettle River at Carson, and the Kettle River at Gilpin. The Kettle River at Midway station is located near the town of Midway just upstream of the Canada-US border. The Kettle River at Carson station is located south west of Grand forks, BC near the point where the Kettle River crosses back into BC. The Kettle River at Gilpin station is located downstream of the Carson site and just upstream of where the Kettle River returns to the US.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest are water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, fish and wildlife, recreation, irrigation and livestock watering. There were several main conclusions of this assessment.

  1. The water quality of the Boundary Creek at this site was generally excellent during 1980 to 1994.
  2. This water is well buffered against acid input yet soft enough for drinking.
  3. The water is naturally high in fluoride and occasionally exceeds criteria for aquatic life. We are not aware of any effects on the local fish populations and expect that fish may be adapted to the higher levels of fluoride.
  4. Water quality patterns in this watershed are usually closely matched with flow patterns. As a result, increased turbidity (i.e., during freshet) makes it necessary to treat the water for drinking purposes.
  5. The increased levels in total phosphorus and total metals are related to seasonal increased flows due to suspended sediments and thus are largely biologically unavailable.

The main recommendation is that monitoring should be suspended at this station.


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Columbia River at Birchbank, 1983 - 2005

The water quality site on the Columbia River at Birchbank is about 24 km downstream from the community of Castlegar and approximately 25 km north from the international border. The drainage area for the Columbia River at Birchbank is 88,100 km2.

Water quality in this reach of the Columbia River has been influenced by the Hugh Keenleyside Dam, the Kootenay River, and major effluent discharges from the Celgar pulp mill and the City of Castlegar. The designated water uses for Columbia River water at Birchbank are: irrigation, livestock watering, primary-contact recreation (i.e., swimming), drinking water with partial treatment and disinfection, industry, wildlife, and aquatic life.

We conclude that:

  • Total aluminum and total iron had environmentally significant decreasing trends over time, possibly due to the trapping effect of upstream dams and reservoirs.
  • Total phosphorus had a declining trend during 1968-78, possibly due in part to the trapping effect of upstream dams and reservoirs and waste abatement. Phosphorus appeared to have reached a steady state during 1983-97, because the evidence for a declining trend was weak and contradictory for this period.
  • Total chromium and total manganese had decreasing trends over time, but they were not environmentally significant because they were below guidelines or objectives, and the result of improvements in measurement methods.
  • Objectives were met for pH, ammonia, arsenic, cadmium, chromium, colour, copper, lead, thallium and zinc.
  • Total dissolved gas values exceeded the objective (greater than 110% saturation) about 50% of the time between 1994 and 1996 due to air entrainment at the Keenleyside Dam. This can stress fish. BC Hydro has been trying to minimize the water spilled at the dam in recent years to minimize the duration and extent of dissolved gas supersaturation. A power plant is being built at the Keenleyside Dam, which will significantly reduce dissolved gas levels in the Columbia River.
  • Fecal coliform values indicate that objective was probably met, although the values were collected less frequently than required to evaluate the attainment of the objectives rigorously.
  • Water hardness was lower than the optimum range for drinking water, but was still quite acceptable.
  • The river had a low sensitivity to acid inputs.
  • Suspended sediments (non-filterable residue, turbidity) values were lower than those in other rivers in the Kootenay region because of the lakes and reservoirs on the Columbia and Kootenay rivers, which allow suspended sediments to settle out.
  • Columbia River water at Birchbank must be treated to remove turbidity and disinfected prior to drinking.
  • Water temperature of the Columbia River at Birchbank was cool enough to be aesthetically pleasing for drinking, except during the summer when it was warm enough for swimming.

We recommend that monitoring be continued on the Columbia River at Birchbank. Water quality data collected at this site would be used to:

  • determine the effects of the major effluent discharges to this reach of the Columbia River (e.g., Celgar pulp Mill, City of Castlegar);
  • check the attainment of water quality objectives; and
  • provide upstream water quality information, as a control site, for the lower reaches of the Columbia River.


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Columbia River at Revelstoke, 1984 - 1995

The City of Revelstoke and surrounding regions are located in the interior of eastern British Columbia, approximately 220 km north from the Canadian-American international boundary. The drainage area for the Columbia River at Revelstoke is approximately 26,700 km2. The Mica and Revelstoke dams have a substantial effect on the water quantity and quality in this section of the river. The water uses for Columbia River water at Revelstoke are: irrigation, livestock watering, primary-contact recreation (i.e., swimming), drinking water, industry, wildlife, and aquatic life.

We concluded that:

  • There was a declining trend in total phosphorus, probably due to the trapping effect of upstream dams and reservoirs.
  • The river had a low sensitivity to acid inputs.
  • Water hardness was lower than the optimum range for drinking water, but was still quite acceptable.
  • Iron and manganese values that exceeded aquatic life and drinking water guidelines were probably in a particulate form and not biologically available, and would be removed by the drinking water treatment needed to remove turbidity.
  • Turbidity values were lower than other natural rivers in the Kootenay area during freshet because of settling in the Kinbasket Lake and Lake Revelstoke reservoirs.
  • Columbia River water at Revelstoke must be treated to remove turbidity and disinfected prior to drinking.
  • One selenium value exceeded the maximum guideline for aquatic life in 1995. This value was collected in a sample with low suspended sediments (non-filterable residues or turbidity), indicating that the selenium was not in a particulate form, and may have been biologically available. The Bethlehem Resources Corporation's zinc mine in the Goldstream River Valley (now closed) may have been a source of the selenium.
  • Water temperature met the guidelines for aquatic life and drinking water aesthetics, but was too cold for water-contact recreation (e.g., swimming).
  • One zinc value exceeded the maximum guideline for aquatic life (algae) in 1991. This value was collected in a sample with low suspended sediments (non-filterable residues or turbidity), indicating that the zinc was not in a particulate form, and may have been biologically available.

We recommend that routine monitoring be discontinued on the Columbia River at Revelstoke with the exception of total phosphorus to track the trends in phosphorus input to the Arrow Lakes.


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Columbia River at Waneta, 1979 - 2005

The water quality site on the Columbia River at Waneta is 25 km downstream from the Birchbank water quality site, 16 km south from the community of Trail, and approximately 1.5 km upstream from the Pend d'Oreille River, which joins the Columbia River at the international border. The drainage area for the Columbia River at Waneta is approximately 88,800 km2.

Water quality in this reach of the Columbia River was influenced by effluent discharges from the Cominco Metals Smelter and Fertilizer plant, primary-treated sewage from the City of Trail, and secondary-treated sewage from Fruitvale and Montrose. The designated water uses for Columbia River water at Waneta are: irrigation, livestock watering, primary-contact recreation (e.g., swimming), drinking water, industry, wildlife, and aquatic life.

We concluded that:

  • Improving trends in water quality over time at the Columbia River at Waneta due to effluent abatement at the Cominco Smelter and Fertilizer plant were noted for: cadmium, chromium, fluoride, iron, lead, phosphorus, sulphate and zinc. These trends resulted in fewer values exceeding the water quality objectives or guidelines than in the 1980s.
  • Increases in the levels of water quality indicators in the Columbia River between Birchbank and Waneta were found for: arsenic, fecal coliforms, cadmium, chromium, copper, fluoride, iron, lead, ammonia, phosphorus, pH, non-filterable residue, sulphate, thallium and zinc. These increases were mainly due to the effluents from the Cominco Smelter and Fertilizer plant and the Kootenay Boundary sewage treatment plant.
  • The water quality objectives were met in recent years for arsenic, lead, ammonia, pH, fecal coliforms and thallium, but not met in 1995 or 1996 for cadmium, chromium, copper and zinc.
  • Water hardness was lower than the optimum range for drinking water, but was still quite acceptable.
  • The river had a low sensitivity to acid inputs.
  • Suspended sediments (non-filterable residue, turbidity) values were lower than in other rivers in the Kootenay region because of the lakes and reservoirs on the Columbia and Kootenay rivers, which allowed suspended sediments to settle out.
  • Columbia River water at Waneta must be treated to remove turbidity and disinfected prior to drinking.
  • Water temperature of the Columbia River at Waneta was cool enough to be aesthetically pleasing for drinking except during the summer when it was warm enough for swimming. The maximum water temperature guidelines for salmonids were met on all but one of the sampling occasions.

We recommend that waste abatement continue to reduce cadmium, chromium, copper and zinc in the river.

We recommend that monitoring be continued on the Columbia River at Waneta. Water quality data collected at this site would be used to:

  • determine the effects of the Kootenay Boundary Regional District primary sewage treatment plant, agricultural runoff and the Cominco Smelter and Fertilizer plant on water quality in this reach of the Columbia River,
  • check the attainment of the water quality objectives, and
  • determine the state of water quality in the Columbia River entering the United States of America.


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Cusheon Lake, Saltspring Island, 1974 - 1999

Cusheon Lake is located on Salt Spring Island. The watershed for this small lake is 7.24 km2. Domestic consumption, primary (e.g., swimming) and secondary (e.g., canoeing and angling) recreation, irrigation, aquatic life and wildlife are the water uses for Cusheon Lake.

This report assesses water quality data for 1974-95 (1974-99 for total phosphorus). We concluded:

  • There was weak evidence of an increasing trend in spring overturn total phosphorus during 1975 to 1999. Total phosphorus values were above the upper guideline for aquatic life for 6 of 14 years, and above the guideline for drinking water and recreation for 10 of 14 years between 1975 and 1999.
  • Chlorophyll a values were collected in 1980 and exceeded the guidelines for aquatic life, drinking water, and recreation.
  • Phosphorus was the limiting nutrient for algal growth in Cusheon Lake.
  • Increases in sodium, chloride, and specific conductivity indicated possible disturbances within the watershed.
  • Total organic carbon values exceeded the guideline for raw drinking water. Chlorinating the water may produce trihalomethanes that may exceed the drinking water guideline.
  • The Capital Health Region determined that the public beach on Cusheon Lake was suitable for bathing between 1981 and 1995.
  • True colour values exceeded the guideline for drinking water aesthetics in 33% of the samples from Cusheon Lake.
  • Dissolved oxygen did not meet the guideline for protecting adult and juvenile salmonids from production impairment in 29% of the samples during 1974-94. The guideline for protecting adult and juvenile salmonids from moderate production impairment was not met in 2% of the samples during this period.
  • Water temperature exceeded the drinking water aesthetics guideline at the deep station in Cusheon Lake in October 1980. The guideline may also have been exceeded during the summer months.
  • Total calcium values show that the lake had a low sensitivity to acid inputs (the lake was well buffered).
  • Total iron values exceeded the guideline for drinking water aesthetics and aquatic life in two samples collected in 1974. Total manganese exceeded the guideline for drinking water aesthetics in samples collected in 1993 and 1994.
  • One extinction depth value collected in October 1980 did not meet the guideline for swimming and may indicate that the guideline was not met in the summer months when swimming would most likely have occurred.
  • Turbidity exceeded the aesthetics objective for drinking water (with disinfection only) in 20% of the samples collected between 1974 in 1995. The drinking water health guideline was exceeded in 80% of the lake samples. The turbidity levels in the Cusheon Lake were such that treatment processes to remove it are required prior to drinking.

We recommend that a remediation plan be developed and implemented to improve water quality in Cusheon Lake. The focus of the remediation plan would be:

  • to determine the suitability of Cusheon Lake for recreation, drinking water and sustaining aquatic life;
  • to identify the sources of nutrients and contaminants in the watershed and lake;
  • to identify what is required to improve the water quality in Cusheon Lake to make it suitable for recreation, drinking and sustaining aquatic life; and
  • to evaluate remediation options and recommend the most efficient approach to improving water quality in the lake.

The plan should be developed and implemented by a Cusheon Lake stewardship group in conjunction with the Islands Trust.

We recommend monitoring:

  • to establish site-specific water quality objectives to protect water uses;
  • to identify the sources of nutrients and contaminants in the watershed and lake; and
  • to identify changes in water quality due to biological activity in the lakes, activities within the watershed such as urbanization, and changes in non-point discharge.


A Cusheon Lake stewardship group could implement this monitoring program with assistance from the Ministry of Environment, Lands and Parks (now Water, Land and Air Protection).

Other monitoring is also recommended:

  • to determine whether the public beach is suitable for bathing. The Capital Health Region will continue to continue monitor and assess the suitability of the public beach for bathing.
  • to determine trihalomethane levels in chlorinated water from the water works. The water works licensee (Beddis Water Works District) and Capital Health Region are implementing this monitoring.
  • to determine the quality of drinking water at the 35 domestic water licenses on Cusheon Lake. A Cusheon Lake stewardship group could implement this monitoring program with assistance from the Capital Health Region, and/or the Ministry of Environment, Lands and Parks (Water, Land and Air Protection).


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Elk and Beaver Lakes, 1986 - 1995 + April, 1996

Elk and Beaver Lakes are located on southern Vancouver Island near Victoria. A shallow channel connects Elk lake and Beaver Lake. The Elk/Beaver watershed is 11.5 km2. This report assesses 10 years of water quality data and has the following main conclusions.

  1. Two water quality objectives (water temperature, water clarity) for Elk Lake and one water quality objective (water clarity) for Beaver Lake have been met since 1993.
  2. Three water quality objectives (dissolved oxygen, chlorophyll a, and Phytoplankton community) for Elk Lake and two water quality objectives (dissolved oxygen, Phytoplankton community) for Beaver Lake were not met.
  3. Spring overturn sampling indicates that the amount of nutrients (e.g., dissolved ammonia and total phosphorus) in the water column have generally decreased from 1986 to 1995. In 1992, there was a notable increase in nutrient values. These changes in nutrient values may be attributed to a change in the amount of nutrients entering the lake or to a change in lake processes.
  4. Total phosphorus values exceeded the criterion range for protecting aquatic life (0.005 mg/L to 0.015 mg/L) in 1986, 1988, and 1995. The criterion (0.01 mg/L) for recreational use was exceeded by all yearly averages.
  5. Phosphorus is the limiting nutrient for algal growth, and dissolved silica is the limiting nutrient for diatom growth in Elk Lake.
  6. The Capital Regional District's Health Protection and Environmental Division has posted beach advisory notices, warning of the potential for increased risk to bathers' health, at Elk Lake (Hamsterly Beach and Eagle Beach) and Beaver Lake (Beaver Beach) on several occasions between 1980 and 1995. These notices were posted when the geometric mean exceeded 200 fecal coliforms/100 mL over a 30-day period.
  7. Total zinc values exceeded the criterion for protecting phytoplankton populations (0.014 mg/L) in 1992, 1994 and 1995, probably due to uncertainty near the minimum detectable limit (0.01 mg/L).

Monitoring is recommended to determine the following:

  1. whether water quality objectives are being met;
  2. identification of changes in water quality which can be attributed to biological activity in the lakes, to activities within the watershed such as urbanization and to changes in non-point discharge; and
  3. whether public beaches are suitable for bathing.

The first two of these monitoring programs could be implemented by an Elk/Beaver Lake stewardship group with assistance from the Ministry of Environment, Lands and Parks. The second monitoring program is being implemented by the Capital Regional District's Health Protection and Environmental Division.


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Elk River at Highway 93, 1968 - 2005

The Elk River watershed is located in the southeast corner of British Columbia. The water quality sampling site is located near the confluence of the Elk River and Lake Koocanusa on the Kootenay River. This report is based on 11 years of Environment Canada data and a decade of provincial data. One of the main human activities influencing the water quality in the Elk River Valley is open pit coal mining. The amount of coal mining has nearly doubled over the last decade. There are several main conclusions of this assessment.

  1. Selenium levels increased over the decade and the Elk River had among the highest selenium concentrations of any federal-provincial monitoring station in BC. All values in 1993 and 1994 exceeded or equaled the aquatic life criterion. This appears to have been caused by the disturbance of selenium-bearing soils during coal mining. The sources of the selenium and its potential environmental effects are being investigated.
  2. Peak arsenic concentrations increased, but were still below water quality criteria, with most values well below criteria.
  3. Nitrate / nitrite and total dissolved nitrogen concentrations increased over the decade, due to the use of nitrogen-based explosives in mining. Nitrate levels were well below the drinking water guideline, but there was an ample supply of nitrogen for algal growth at all times of the year.
  4. Erosion from mining, logging, roads and land development may have caused increased non-filterable residue, turbidity, and total phosphorus during spring freshet.
  5. Filtration of drinking water is recommended during periods of high turbidity. Most communities in the basin currently use tributaries of the Elk River as drinking water sources.
  6. Water hardness reached a level where water quality was poor for domestic use during the winter and may have been increasing.

There are two main recommendations:

  1. Continue monitoring at this station since there are several indicators that exceeded criteria on a regular basis and/or were showing increasing trends.
  2. Continue investigations to determine the sources of the selenium and arsenic and their potential environmental effects. The results of these investigations will help to show the type of corrective action, if any, that may be needed to reduce selenium or arsenic levels.


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Fraser River at Hansard, 1984 - 2004

The Fraser River at Hansard station is the second from the head waters of five water quality stations on the Fraser River. The others are upstream at Red Pass (near the Moose Lake and the headwaters) and downstream at Stoner, Marguerite and Hope. Hansard is situated on the part of the Fraser River which flows northwest from the Rocky Mountains towards Prince George. Concentrations at Hansard are compared in the report with the levels at Red Pass.

This report is based on data from Environment Canada and the Ministry of Environment, Lands and Parks (Water, Land and Air Protection). Environment Canada began collecting data in 1984 and the Ministry of Environment, Lands and Parks in 1987. There are several main conclusions.

  1. No increasing trends jeopardizing water uses such as aquatic life, wildlife, drinking water, livestock, irrigation, and recreation were found.
  2. Specific water quality objectives are being met.
  3. Total metals were high due to preservative vial contamination between 1986 and 1991.
  4. Water hardness was within the optimum range for drinking water between November and April.
  5. The river has a low sensitivity to acid inputs.
  6. Increased turbidity and non-filterable residue values may be attributed to natural erosion in the upper Fraser basin during periods of high flow.
  7. Seven water quality indicators increased in the winter months of last two years, but were still below all criteria.
  8. Total metal values in this reach of the river are naturally occurring as there are no man-made source upstream of Hansard.
  9. High metals and suspended sediments, reported in samples collected between 1992 and 1994, indicate that the metals are in a particulate form and not biologically available.
  10. Dissolved phosphorus values decreased between 1993 and 1994.
  11. A decrease in selenium values may be attributed to an increase of control over contamination during the measuring process.
  12. Water temperature exceeded the criterion for drinking water in the summer months in 1986 and between 1992 and 1994.
  13. The Fraser River at Hansard was below the desirable range for water-contact recreation for most of the year.
  14. Fraser River water at Hansard must be treated to remove turbidity prior to drinking.
  15. The increase in suspended sediments and flow in the Fraser River caused water quality indicator values to increase between Red Pass and Hansard.

It is recommended that monitoring be continued for the Fraser River at Hansard. It is the control station upstream from the first major population centre, Prince George, and industrial waste discharges, pulp mills, on the Fraser River. Several water quality indicators are important for future monitoring.

  1. flow
  2. water temperature
  3. specific conductivity
  4. pH
  5. total dissolved phosphorus
  6. total dissolved nitrogen
  7. periphyton chlorophyll-a
  8. dissolved oxygen
  9. fecal coliforms
  10. chlorine residuals
  11. colour (true or TAC)
  12. turbidity
  13. non-filterable residue
  14. hardness
  15. dissolved aluminum
  16. total and dissolved copper, lead, nickel and zinc.


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Fraser River at Hope, 1979 - 2004

The water quality sampling station on the Fraser River at Hope is one of five long-term water quality stations on the Fraser River. The others are upstream at Marguerite, Stoner, Hansard, and Red Pass. Hope is used as a control station for the Upper Fraser Valley and Fraser River Estuary. It represents the effects on water quality from discharges to the upper and middle reaches of the river and its major tributary, the Thompson River.

This report is based on data from Environment Canada since 1979 and the Ministry of Environment, Lands and Parks (now Water, Land and Air Protection) since 1987.

We concluded that:

  • Water quality objectives for ammonia-N, nitrate/nitrite, and pH were met. These objectives are meant to protect aquatic life, irrigation, drinking water, secondary-contact recreation, and industrial use.
  • Fecal coliforms probably did not meet the objective to protect drinking water. More frequent monitoring (i.e., five to 10 samples in 30 days) is required to improve the comparison to the objective.
  • It could not be determined whether the colour objectives were met. Most values that exceeded these objectives were from samples with high turbidity that caused apparent colour to increase. True colour should be measured to evaluate the actual attainment of the objectives for colour.
  • Decreasing trends were found for chloride and AOX. AOX continued to exceed the objective, but this is considered to be of low environmental significance because chlorinated phenolics, dioxins, and furans met the objectives. AOX is merely a surrogate indicator for these chlorinated compounds. The decline in AOX and chloride was most likely due to pulp mill AOX effluent reduction. Four mills using chlorine bleaching incorporated process changes in 1990-92, which included oxygen delignification and chlorine dioxide substitution.
  • Water temperature exceeded the aesthetics guideline for drinking water (15°C) in 16% of the samples collected between 1979 and 1994. One value exceeded the maximum guideline for salmonids (22-24°C) in 1991. During the summer months (June to September) the water was warm enough for primary-contact recreation (e.g., swimming).
  • Water hardness was lower than the optimum range for drinking water, but was still quite acceptable.
  • The river had a low sensitivity to acid inputs (well buffered).
  • Fraser River water at Hope must be treated to remove turbidity and disinfected prior to drinking.
  • Several total metals exceeded the guidelines for aquatic life and drinking water. Usually, these values occurred with high suspended sediment values, indicating that these metals were in a particulate form, probably not biologically available, and would be removed by drinking water treatment needed to remove turbidity.

We recommend that it be determined whether the water quality objective for fecal coliforms is being attained. Remediation measures may be required after this initial assessment.

We recommend monitoring for:

  • flow, air and water temperature, specific conductivity, hardness, dissolved oxygen, pH;
  • total phosphorus, total dissolved phosphorus, ammonia, nitrate/nitrite, total dissolved nitrogen, dissolved organic carbon, AOX, fecal coliforms;
  • dissolved chloride, true colour, turbidity, total and dissolved metals (aluminum, cadmium, chromium, cobalt, copper, iron, lead, and zinc), using minimum detectable limits at least 10 times below objectives or guidelines.


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Fraser River at Marguerite, 1984 - 2004

The Fraser River flows through a vast portion of the southern half of British Columbia, from the Rocky Mountains to the Pacific Ocean. Marguerite is located in central BC, north of Williams Lake and south of Prince George and Quesnel. It is the third of four major water quality stations on the Fraser River. The others are upstream at Red Pass (near the Moose Lake and the headwaters of the river) and Hansard (mid-way between Red Pass and Prince George), and downstream at Hope. Hansard is the closest of the three and the report compares concentrations between the two sites.

This report is based on data from Environment Canada and Ministry of Environment, Lands and Parks (now Water, Land and Air Protection). The federal data are from 1984 onwards and the provincial data commence in 1987. There are several major conclusions.

  1. Water quality objectives for ammonia, nitrate/nitrite, and pH, were met. These objectives are meant to protect aquatic life, irrigation, domestic consumption, secondary-contact recreation, and industrial use.
  2. No increasing trends jeopardizing water uses such as aquatic life, wildlife, drinking water, livestock, irrigation, and recreation were found.
  3. Decreasing trends were noted for AOX, chloride, fecal coliforms, nickel, and aluminum. The decline in AOX and chloride is due to pulp mill AOX effluent reduction. Despite the decrease in fecal coliforms, criteria were still possibly being exceeded.
  4. Total dissolved and ortho-phosphorus levels increased. Their effects on algal growth in the river are unknown, but are likely minimal due to the turbidity of the river.
  5. Fourteen water quality indicators had higher values at Marguerite than the upstream station at Hansard.
  6. Colour values were due to pulp mills and this is an aesthetics concern.
  7. Higher non-filterable residues and turbidity values may occur as a result of natural processes such as erosion. Filtration and disinfection of drinking water would be needed most of the year but the river is not expected to be used for drinking in the near future.
  8. Total metals were high due to preservative vial contamination between 1986 and 1991.
  9. High metals and suspended sediments indicate that the metals were in a particulate form and not biologically available.
  10. The river is well-buffered against acidic inputs and the water is fairly soft.

It is recommended that monitoring be continued for the Fraser River at Marguerite. It is the first major Fraser River station downstream from significant population and industry. Several water quality indicators are important for future monitoring.

  1. flow
  2. dissolved phosphorus
  3. water temperature
  4. dissolved oxygen
  5. ammonia, nitrate-N
  6. nitrite-N
  7. residual chlorine
  8. turbidity
  9. AOX
  10. non-filterable residue
  11. colour (true or TAC)
  12. periphyton chlorophyll-a
  13. total and dissolved copper, cadmium, lead and zinc
  14. fecal coliforms


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Fraser River at Red Pass, 1984 - 2004 May, 2007

The Fraser River at Red Pass, near Moose Lake and the headwaters, station is the first of five water quality stations on the Fraser River. The others are downstream at Hansard, Stoner, Marguerite, and Hope. Red Pass is situated on the part of the Fraser River which flows northwest from the Rocky Mountains towards Prince George. Concentrations at Red Pass are compared in the report with the levels at Hansard. This report is based on data from Environment Canada. They began collecting data at the station in 1984. There are several major conclusions.

  1. No increasing trends jeopardizing water uses such as aquatic life, wildlife, drinking water, livestock, irrigation, and recreation were found.
  2. Specific conductivity and dissolved sulphate showed minor increasing patterns.
  3. Water hardness was lower than the optimum range for drinking water, but was still quite acceptable.
  4. The river has a low sensitivity to acid inputs.
  5. Increased turbidity values may be attributed to natural erosion in the upper Fraser basin during periods of high flow.
  6. Fraser River water at Red Pass must be treated to remove turbidity prior to drinking.
  7. Total metals were high due to preservative vial contamination between 1986 and 1991.
  8. Total metal values in this reach of the river are naturally occurring as there are no man made sources upstream of Red Pass.
  9. The site-specific colour objectives were met, but true colour should be measured to evaluate the objectives for colour effectively.

Monitoring should be continued for the Fraser River at Red Pass. It is the headwaters station upstream from all population centres and industrial waste discharges on the Fraser River. We recommend that there be several control stations in the province located in key and relatively pristine watersheds. These stations would be used as quality assurance stations for impacted areas, and to detect trends in water quality due to global changes (e.g., climate changes, changes in ultra violet radiation, atmospheric deposition) There are several water quality indicators that are important for future monitoring.

  1. flow
  2. air and water temperature
  3. specific conductivity
  4. alkalinity
  5. hardness
  6. dissolved oxygen
  7. pH
  8. total phosphorus
  9. total dissolved phosphorus
  10. dissolved ammonia
  11. nitrate/nitrite
  12. kjeldahl nitrogen
  13. total and dissolved organic carbon
  14. dissolved magnesium, sodium, potassium, fluoride, chloride and sulphate
  15. magnesium
  16. silica
  17. colour (true or TAC)
  18. turbidity (non-filterable residue)
  19. total and dissolved metals
  20. periphyton chlorophyll-a


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Glen Lake, 1981 - 1995 + April, 1996

Glen Lake is located on southern Vancouver Island near Victoria, BC. The watershed for this small lake is 11.9 km2. This report assesses 12 years of water quality data and has several conclusions.

  1. Glen Lake is classified as a mildly dystrophic lake. Dystrophic lakes receive a large quantity of organic material, are acidic (low pH), and have low productivity.
  2. Spring overturn sampling indicates that in recent years there was less total phosphorus in the water column. However, nitrogen values (e.g., nitrate/nitrite nitrogen) are increasing in the water column.
  3. Phosphorus is the limiting nutrient for algal growth in Glen Lake.
  4. The Capital Regional District's Health Protection and Environmental Division has posted advisory notices at Glen View Beach on several occasions between 1980 and 1995, warning of the potential for increased risk to bathers' health. These notices were posted when the geometric mean exceeds 200 fecal coliforms/100 mL over a 30-day period.
  5. Three water quality indicators, total manganese, total iron and total zinc, exceeded the criterion for protecting aquatic life.
  6. True colour exceeded the desirable criterion for recreational use.

The following water quality objectives are recommended for Glen Lake.

  1. Total phosphorus
  2. True color
  3. Total manganese
  4. Total iron
  5. Total zinc
  6. Dissolved oxygen

These objectives would set the goals for a remediation plan, which we recommend be developed for Glen Lake. Monitoring should occur to determine the following:

  1. whether water quality objectives are being met;
  2. whether changes in water quality can be attributed to activities within the watershed such as urbanization, changes in nonpoint discharge, biological activity and lake aeration;
  3. whether the public beach is suitable for bathing.

The first two monitoring programs could be implemented by a Glen Lake stewardship group with assistance from the Ministry of Environment, Lands and Parks. The third monitoring program is continuing to be implemented by the Capital Regional District's Health Protection and Environmental Program.


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Iskut River below the Johnson River, 1969 - 2002

The Iskut River is located in northwest British Columbia, flowing from Kinaskan Lake to the Stikine River. From here, the Stikine River flows through Alaska into the Pacific Ocean. Activities in the Iskut watershed include mining and, to a lesser extent, forestry. This report assesses water quality data from Environment Canada at the monitoring station below Johnson River, 8 km upstream from the confluence with the Stikine River. Water quality samples were collected between 1980 and 1994 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge at the same location. There are several major conclusions.

  1. There were no obvious environmentally significant trends in water quality that could be identified through visual examination of the data.
  2. Peak non-filterable residue and turbidity values occurred during peak flows and were probably a natural occurrence.
  3. Turbidity removal and disinfection would be needed prior to drinking.
  4. Total aluminum, arsenic, cadmium, chromium, copper, iron, lead, manganese and zinc, organic carbon, apparent colour, non-filterable residue and turbidity values did not meet various water quality criteria due to the high levels of suspended sediment in the water during freshet.
  5. High metals and suspended sediments occurred together in samples collected during periods of high flow. This indicates that the metals were in a particulate form, probably not biologically available and would be removed by the treatment needed to remove turbidity prior to drinking.
  6. Total barium, beryllium, cobalt, nickel, selenium and vanadium, dissolved chloride and sulphate, total alkalinity, calcium, magnesium, nitrate/nitrite, pH, potassium, filterable residue, sodium and specific conductivity met all criteria.
  7. The river had a low sensitivity to acid inputs.
  8. The river was cool enough for drinking, but too cold for water-contact recreation.
  9. Hardness levels were generally below the optimum range for drinking water in the summer months and at or above the optimum range in the winter months, but were still quite acceptable.

It is recommended that monitoring be continued for the Iskut River below Johnson River for several reasons.

  1. It is being used to determine transboundary effects between British Columbia and Alaska.
  2. It is being used to assess the environmental impacts of upstream activities such as mining and forestry.
  3. It is being used to determine Iskut River water quality before its confluence with the Stikine River.


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Kettle River at Carson, 1980 - 2002

This report assesses the long-term water quality trends in the Kettle River, a trans-boundary river which flows from south central BC into Washington State crossing the international border at the town of Midway, BC and then re-entering BC at Carson. Environment Canada has monitored the Kettle River at Carson station since 1980 collecting 26 samples per year. Three other related monitoring stations within the BC portion of this watershed are the Kettle River at Midway, Boundary Creek at Midway, and the Kettle River at Gilpin sites. The Kettle River at Midway station is located at the international boundary near the town of Midway, BC where the Kettle River first enters the US. The Boundary Creek at Midway station is located on Boundary Creek very near the town of Midway where this major tributary from the north joins the Kettle River adjacent to the international boundary. The Kettle River at Gilpin station is located downstream of the Carson site but just upstream of where the Kettle River returns to the US.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest are water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, fish and wildlife, recreation, irrigation and livestock watering. There are several main conclusions of this assessment.

  1. The water quality of the Kettle River at this site was generally excellent during 1980 - 1994.
  2. This water is well buffered against acid input yet soft enough for drinking.
  3. The water is naturally high in fluoride and exceeds criteria for aquatic life. We are not aware of any effects on the local fish populations and expect that fish may be adapted to the higher levels of fluoride.
  4. Water quality patterns in this watershed are usually closely matched with flow patterns. As a result, increased turbidity (i.e, during freshet) makes it necessary to treat the water for drinking purposes.
  5. The increased levels in total phosphorus and total metals are related to seasonal increased flows due to suspended sediments and thus are largely biologically unavailable.

The main recommendation is to continue monitoring at this station because there are regional concerns related to resource development within the Kettle River watershed (US and Canada). The potential for the proposed Washington State mine should be considered as mining development will impact the watershed. Design and implement a specific monitoring program to study this impact. The Kettle river at Carson serves as an excellent background site for the collection and assessment of water quality data before the Kettle River re-enters Canada near Grand Forks, BC.


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Kettle River at Gilpin, 1980 - 1994 + February, 1996

This report assesses the long-term water quality trends in the Kettle River, a trans-boundary river which flows from south central BC into Washington State first crossing the international border at the town of Midway, BC and then re-enters BC at Carson upstream from Gilpin. Environment Canada has monitored the Kettle River at Gilpin station since 1980 collecting 26 samples per year. Three other related monitoring stations within the BC portion of this watershed are the Kettle River at Midway, Boundary Creek at Midway, and the Kettle River at Carson sites. The Kettle River at Midway station is located near the town of Midway, BC and the international boundary. Boundary Creek, a major tributary from the north, joins the Kettle River a short distance downstream from Midway, BC and is also very near the boundary between Canada and the US. The Kettle River at Carson station is located downstream of Midway at the point where the Kettle River crosses back into BC. The Kettle River at Gilpin station, the most easterly of the four stations, is located downstream of the Carson site but just upstream of where the Kettle River returns to the US.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest are water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, fish and wildlife, recreation, irrigation and livestock watering. There were several main conclusions of this assessment.

  1. The water quality of the Kettle River at Gilpin site was generally excellent during 1980 to 1994.
  2. This water is well buffered against acid input and yet soft enough for drinking.
  3. The water is naturally high in fluoride and exceeds criteria for aquatic life. We are not aware of any effects on the local fish populations and expect that fish may be adapted to the higher levels of fluoride.
  4. Water quality patterns in this watershed are usually closely matched with flow patterns. As a result, increased turbidity (i.e., during freshet) makes it necessary to treat the water for drinking purposes.
  5. The increased levels in total phosphorus and total metals are related to seasonal increased flows due to suspended sediments and thus are largely biologically unavailable.

The main recommendation is that monitoring should be suspended at this station.


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Kettle River at Midway, 1972 - 2000

This report assesses the long-term water quality trends in the Kettle River, a trans-boundary river which flows from south central BC into Washington State crossing the international border at the town of Midway, BC and then re-entering BC at Carson. Environment Canada has monitored the Kettle River at Midway station since 1980 collecting 26 samples per year. Three other related monitoring stations within the BC portion of this watershed are the Boundary Creek at Midway, the Kettle River at Carson, and the Kettle River at Gilpin sites. Boundary Creek, a major tributary from the north, joins the Kettle River a short distance downstream from Midway, BC very near the international boundary between Canada and the US. The Kettle River at Carson station is located downstream of Midway at the point where the Kettle River crosses back into BC. The Kettle River at Gilpin station is located downstream of the Carson site but just upstream of where the Kettle River returns to the US.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest are water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, fish and wildlife, recreation, irrigation and livestock watering. There are several main conclusions of this assessment.

  1. The water quality of the Kettle River at this site was generally excellent during 1980 to 1994.
  2. This water is well buffered against acid input yet soft enough for drinking.
  3. The water is naturally high in fluoride and exceeds criteria for aquatic life. We are not aware of any effects on the local fish populations and expect that fish may be adapted to the higher levels of fluoride.
  4. Water quality patterns in this watershed are usually closely matched with flow patterns. As a result, increased turbidity (i.e., during freshet) makes it necessary to treat the water for drinking purposes.
  5. The increased levels in total phosphorus and total metals are related to seasonal increased flows due to suspended sediments and thus are largely biologically unavailable.
  6. There is an apparent declining trend in non-filterable residue and turbidity. This may be due to declining peak flows and better land management, or both.

The main recommendation is to continue monitoring at this station because there are regional concerns related to resource development within the Kettle River watershed (US and Canada). The potential for the proposed Washington State mine should be considered as mining development will impact the watershed. Design and implement a specific monitoring program to study this impact. The Kettle river at Midway serves as an excellent background site for the collection of water quality data before the Kettle River crosses into the US.


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Kootenay River at Creston, 1965 - 2000

This report assesses the long-term water quality trends in the Kootenay River at Creston just before it enters Kootenay Lake. The Kootenay River is a trans-boundary river that flows south from Kootenay National Park in BC. into Koocanusa Lake (Libby Dam Reservoir), then swings north from Koocanusa Lake through Montana and Idaho before flowing back into BC at Creston. Environment Canada began monitoring at this station in 1979 whereas the Province has monitored the Kootenay River at Creston since 1987 collecting approximately 26 samples per year. Five other related water quality monitoring stations within the BC portion of the Kootenay River watershed are, proceeding upstream, the Moyie River at Kingsgate, Elk River at Highway 93 bridge, Kootenay River at Fenwick (also known as Picture Valley), Kootenay River at Canal Flats, and nearest to the source of the Kootenay River, the Kootenay River at Kootenay Crossing in Kootenay National Park.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest are water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, wildlife, recreation, irrigation and livestock watering. There are several main conclusions of this assessment.

  1. No environmentally significant trends were noted during the visual assessment of the plotted data except for the apparent decline in total phosphorus. Declining fisheries production in Kootenay Lake has been attributed to a lack of phosphorus. Fertilization of the lake began in 1992 to boost production.
  2. This water is well buffered throughout the year against acid input, yet soft enough for drinking.
  3. Water quality patterns in this watershed are fairly closely matched with flow patterns. As a result, increased turbidity (e.g., during freshet) makes it necessary to treat the water to remove turbidity for drinking purposes.
  4. The increased levels of total metals were usually related to seasonal increased flows and suspended sediment. The metals were probably largely biologically unavailable and would be removed by treatment needed to remove turbidity prior to drinking.
  5. Fecal coliform levels met the criteria for irrigation, recreation, and drinking water receiving partial treatment.
  6. A few high lead values occurred during 1991-94. Further monitoring is warranted.

Our main recommendation is to continue monitoring at this trans-boundary station for the following list of variables related to the nutrient loading from the USA (Koocanusa Lake) into Kootenay Lake.

  1. flow
  2. fecal coliforms
  3. conductivity
  4. hardness (for metals toxicity)
  5. dissolved organic carbon
  6. total dissolved nitrogen
  7. pH
  8. dissolved ortho-phosphorus (low level)
  9. total phosphorus
  10. air and water temperature
  11. turbidity
  12. total and dissolved Cd, Cr, Cu, Pb, Se and Zn


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Kootenay River at Fenwick Station, 1984 - 2005

This report assesses the long-term water quality trends in the Kootenay River at Fenwick, a water quality monitoring station downstream from the St. Mary River confluence and upstream from Koocanusa Lake. The Kootenay is a trans-boundary river that flows south from Kootenay National Park in BC into Koocanusa Lake (Libby Dam Reservoir), then swings north from Koocanusa Lake through Montana and Idaho before flowing back into BC at Creston. Environment Canada began monitoring at this station in 1984 whereas the Province has monitored the Kootenay River at Fenwick since 1985 collecting approximately 26 samples per year. Five other related water quality monitoring stations within the BC portion of the Kootenay River watershed are the Moyie River at Kingsgate, Elk River at Highway 93 bridge, Kootenay River at Creston, Kootenay River at Canal Flats, and nearest to the source of the Kootenay River, the Kootenay River at Kootenay Crossing in Kootenay National Park.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest are water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, wildlife, recreation, irrigation and livestock watering. There are several main conclusions of this assessment.

  1. The water was well buffered throughout the year against acid input yet reasonably soft for drinking.
  2. Water quality patterns in this watershed were very closely matched with flow patterns. As a result, increased turbidity and particulate material (i.e., during freshet) makes it necessary to treat the water for drinking purposes.
  3. Zinc levels occasionally exceeded criteria for aquatic life due to continuing acid rock drainage at the Cominco Ltd. Kimberley operations. Zinc levels appear to be declining due to on-going remediation.
  4. The increased levels of total metals were related to seasonal increased flows and suspended sediment. The metals were probably largely biologically unavailable with the possible exception of zinc.
  5. Manganese showed a decline in peak levels, especially after 1991 due to declining peak flows.
  6. The Kootenay River at Fenwick contributed minor amounts of dissolved, bio-available phosphorus to Koocanusa Lake, but major amounts of particulate phosphorus with suspended sediments during freshets.

There are two main recommendations:

  1. Continue the reclamation and acid rock drainage abatement program at Cominco Ltd.'s Kimberley operation.
  2. Continue monitoring at this trans-boundary station for the following variables related to major waste discharges upstream from the US border.

    a. flow
    b. hardness (for metals toxicity)
    c. colour (SW and true)
    d. conductivity
    e. turbidity
    f. total dissolved nitrogen
    g. pH
    h. dissolved ortho-phosphorus
    i. total phosphorus
    j. sodium
    k. water temperature
    l. total and dissolved Cd (low level), Cr, Cu, Pb and Zn


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Liard River at Fort Liard, 1984 - 1995

The Liard River is a major tributary of the Mackenzie River, flowing southeast from the Yukon into British Columbia, looping through northern BC, and then flowing northeast into the Northwest Territories to the Mackenzie. Water quality is affected by various activities including oil and gas development, mining, forestry and agriculture.

There are three water quality stations on the Liard River: Upper Crossing near the Yukon-BC border, Lower Crossing at Liard River, BC, and at Fort Liard in the Northwest Territories. This report assesses water quality data collected at the Fort Liard monitoring station, located at the Hudson's Bay Company Post near Fort Liard. Water quality samples were collected between 1984 and 1995 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge at the water quality monitoring station. Several main conclusions resulted from this study.

  1. There were no environmentally significant trends in water quality that could be identified through visual examination of the data.
  2. Total aluminum, arsenic, cadmium, organic carbon, chromium, copper, iron, lead, manganese, selenium and zinc at times exceeded water quality criteria for aquatic life or drinking water due to high levels of suspended sediment during high river flow. These substances were probably not biologically available and would be removed by drinking water treatment needed to remove turbidity.
  3. Turbidity removal and disinfection are needed prior to drinking water use.
  4. The river was often too turbid for recreation during the summer.
  5. The river had a low sensitivity to acid inputs.
  6. Hardness levels were mostly above the optimum range for drinking water, reaching the poor range during winter.
  7. The water was cool enough for drinking except during the summer, when it was warm enough for water-contact recreation.

We recommend that monitoring be terminated for the Liard River at Lower Crossing because there are no apparent water quality trends or concerns at this time.


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Liard River at Lower Crossing, 1984 - 1994

The Liard River is a major tributary of the Mackenzie River, flowing southeast from the Yukon into British Columbia, looping through northern BC and then flowing northeast into the Northwest Territories to the Mackenzie. Water quality is affected by mining and forestry. There are three water quality stations on the Liard River: Upper Crossing near the Yukon-BC border, Lower Crossing at Liard River, BC, and at Fort Liard in the Northwest Territories.

This report assesses water quality data collected at the Lower Crossing monitoring station, located at Mile 496 on the Alaska Highway at Liard River, BC. Water quality samples were collected between 1984 and 1994 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge at the water quality monitoring station. Several major conclusions arose from this monitoring assessment.

  1. There were no environmentally significant trends in water quality that could be identified through visual examination of the data.
  2. Total aluminum, cadmium, chromium, copper, iron, lead, manganese and zinc at times exceeded water quality criteria for aquatic life or drinking water due to high levels of suspended sediment during high river flow. These metals were probably not bio-available and would be removed by drinking water treatment needed to remove turbidity.
  3. Turbidity removal and disinfection are needed prior to drinking water use.
  4. The river had a low sensitivity to acid inputs.
  5. Hardness levels were generally within the optimum range for drinking water in the summer and above the optimum range in the winter.
  6. The water was cool enough to be aesthetically pleasing for drinking, but too cold for water-contact recreation.

We recommend that monitoring be terminated for the Liard River at Lower Crossing because there are no apparent water quality trends or concerns at this time.


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Liard river at Upper Crossing, 1983 - 1994

The Liard River is a major tributary of the Mackenzie River, flowing southeast from the Yukon into British Columbia, looping through northern BC, and then flowing northeast into the Northwest Territories to the Mackenzie. Water quality is affected by mining and forestry.

There are three water quality stations on the Liard River: Upper Crossing near the Yukon-BC border, Lower Crossing at Liard River, BC, and at Fort Liard in the Northwest Territories. This report assesses water quality data collected at the Upper Crossing monitoring station located at the Alaska Highway bridge near the Yukon-BC border. Water quality samples were collected between 1983 and 1994 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge at the water quality monitoring station.

We concluded that:

  • There were no environmentally significant trends in water quality that could be identified through visual examination of the data.
  • Total aluminum, cadmium, iron, manganese and zinc at times exceeded water quality criteria for drinking water or aquatic life due to high levels of suspended sediment during high river flow. These metals were probably not bio-available and would be removed by drinking water treatment needed to remove turbidity.
  • Turbidity and disinfection are needed prior to drinking water use.
  • The river had a low sensitivity to acid inputs.
  • Hardness levels were at or below the optimum range for drinking water in the summer, but above the optimum range in the winter months, reaching the poor range for short periods.
  • The water was cool enough to be aesthetically pleasing for drinking, but too cold for water-contact recreation.

We recommend that monitoring be terminated for the Liard River at Upper Crossing because there are no apparent water quality trends or concerns at this time.


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Langford Lake, 1973 - 1995 + April, 1996

Langford Lake is located on southern Vancouver Island near Victoria, BC. The watershed for this small lake is 3.3 km2. This report assesses 16 years of water quality data and made the following conclusions.

  1. Spring overturn sampling indicates that there are less nutrients (e.g., total phosphorus, total dissolved phosphorus, Kjeldahl nitrogen, and dissolved ammonia) in the water column in recent years. These changes in nutrient values may be attributed to a change in the amount of nutrients entering the lake, to a change in hydrological and limnological processes of the lake or to the cumulative effect of operating the aerator in the lake.
  2. Phosphorus is the limiting nutrient for algal growth in Langford Lake.
  3. The public bathing beach on the north side of Langford Lake was suitable for recreational bathing between 1980 and 1995.
  4. Total manganese values exceeded the lower criterion (0.10 mg/L) for the protection aquatic life in 1984 and 1985. These values have declined and met this criterion since 1985.
  5. Specific conductivity values increased over time but were below all criteria.

We recommend monitoring to identify the following:

  1. changes in water quality attributed to activities within the watershed such as urbanization, changes in nonpoint discharge, biological activity and lake aeration.
  2. whether the public beach is suitable for bathing.

The monitoring program for the first recommendation could be implemented by a Langford Lake stewardship group with assistance from the Ministry of Environment, Lands and Parks (Water, Land and Air Protection). The monitoring program for the second recommendation is being implemented by the Capital Regional District's Health Protection and Environmental Program Division. In future, local interest groups (e.g., Langford Lake stewardship group, Municipality of Langford) could assist with this ongoing monitoring.


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Moyie River at Kingsgate, 1980 - 2004

This report assesses the long-term water quality trends in the Moyie River, a trans-boundary river which flows from south central BC into Idaho, crossing the international boundary at Kingsgate. The federal government has operated a water quality monitoring station there since 1979. There is also a flow station just downstream at the border at Eastport. The Moyie River flows toward Cranbrook from its source east of Kootenay Lake, then south through Moyie Lake and southwest to the border. After crossing the border, it heads south for an additional 30 km before joining the Kootenay River in Idaho.

Water quality indicator concentration were generally very low at this station. Most criteria were easily met and no trends were found. In fact, many indicators could not often be detected at he current minimum detectable limits. Most indicators which exceeded criteria did so more frequently closer to the beginning of the data collection period. Only turbidity exceeded criteria in the last four years. The only other water quality issue was a moderate to high sensitivity to acidic inputs as indicated by calcium and total alkalinity. The main recommendation is to discontinue trend monitoring at this site.


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Nechako River at Prince George, 1985 - 2004

The Nechako River is one of the major tributaries that affect flow and water quality in the Fraser River. Its headwaters are located in the Nechako Reservoir drainage basin. The drainage area of the river at Prince George is 46,000 km2. The Nechako River water quality is influenced by the water quality from the Stuart, Nautley, and Chilako rivers. Nechako River water is used for irrigation, livestock watering, primary and secondary-contact recreation (i.e., swimming and boating), drinking water with partial treatment, by wildlife, and to sustain aquatic life.

Based on regular water quality monitoring of the Nechako River at Prince George, we concluded that:

  • There were no environmentally significant trends in water quality.
  • Site-specific water quality objectives for ammonia, nitrite-N, and pH were met.
  • Fecal coliforms probably met the objective to protect drinking water with partial treatment at Prince George. More frequent monitoring (i.e., five to 10 samples in 30 days) is required to improve the comparison to the objective.
  • All phenol values exceeded the guideline to prevent fish tainting. However, the phenol was naturally occurring and fish tainting is not known to be a concern in the Nechako River.
  • The drinking water (aesthetics) guideline for water temperature (15 °C) was exceeded in 86% of the samples collected between June and September during 1985-95. However, the water was warm enough for primary-contact recreation (e.g., swimming) at these times. The maximum guideline (22-24 °C) for adult and juvenile salmonids was exceeded once.
  • Water hardness was lower than the optimum range for drinking water, but was still quite acceptable.
  • The river had a low sensitivity to acid inputs.
  • Elevated non-filterable residue and turbidity may have been due to natural erosion within the Nechako River basin during spring freshet, augmented to an unknown extent by non-point sources such as forestry and agriculture.
  • Nechako River water at Prince George must be treated to remove turbidity prior to drinking.
  • Several metals had levels above aquatic life or drinking water guidelines when suspended sediments (non-filterable residues or turbidity) were elevated. This indicates that the metals were in a particulate form, probably not biologically available, and would be reduced by drinking water treatment to remove turbidity.

We recommend that monitoring be continued on the Nechako River at Prince George. Water quality data collected at this site would be used to:

  • represent the water quality from the upper portion of the interior plain ecosystem,
  • check attainment of site-specific water quality objectives, and
  • determine changes in the water quality of the Fraser river basin downstream from the Nechako River confluence.


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North Thompson River at North Kamloops, 1985 - 1995

The North Thompson River originates in British Columbia's Rocky Mountain interior southwest from Valemount, flows south to Clearwater and McLure and joins the South Thompson River at Kamloops to become the Thompson River. Approximately 300 km in length, the river is important for uses such as drinking water, recreation, aquatic life, wildlife, irrigation and livestock watering. Water quality is affected by agriculture, urbanization, and forestry, particularly in the southern section of the river downstream from McLure. There are no significant industrial or municipal discharges into the river. Other long-term monitoring stations on the Thompson River are South Thompson River at Kamloops and Thompson River at Spences Bridge.

In this report, nine years of data (1987-1995) obtained under the Canada-BC Water Quality Monitoring Agreement were assessed for trends and concerns in water quality. The 47 variables were graphed, and compared to water quality guidelines and to site-specific water quality objectives set by BC Environment.

The main conclusions of this study are:

  • No environmentally significant trends were found.
  • The site-specific fecal coliform objective to protect drinking water receiving only disinfection appeared to have been exceeded at times. Partial treatment and disinfection of drinking water are needed due to frequent high fecal coliform, E. coli and turbidity levels.
  • Occasionally, levels of aluminum, copper, iron and zinc exceeding guidelines for aquatic life or drinking water have been observed in winter and fall, in association with low levels of non-filterable residue. Levels appeared to be naturally high in the river, since higher values during low flows have occasionally occurred since monitoring began in 1987, and since there were no significant industrial discharges into the river.
  • Variables exceeding guidelines at times during spring freshet were aluminum, chromium, copper, iron, manganese and titanium. High levels occurred in conjunction with high levels of non-filterable residue and turbidity, suggesting that the metals were in particulate form, not biologically available, and would be removed by drinking water treatment needed to remove turbidity.
  • Guidelines were consistently met for most of the sampled variables, including: barium, beryllium, boron, dissolved chloride, magnesium, nickel, molybdenum, ammonia, nitrate/nitrite, pH, specific conductivity, dissolved sulphate and vanadium.
  • The water was well buffered against acid inputs.


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Okanagan River at Oliver, 1979 - 2002

The Okanagan River at Oliver is located in the southern interior region of BC, just upstream from Osoyoos Lake. The river originates at the south end of Okanagan Lake near Penticton and flows south through Skaha, Vaseux, and Osoyoos lakes. Osoyoos Lake straddles the border with the United States. Urbanization, agriculture and logging are the major human impacts in the south Okanagan. The sampling site is between Oliver and Osoyoos Lake. This report reviews water quality data collected by Environment Canada for 15 years and by the province for ten years. The report reached several conclusions about water quality in the Okanagan River.

  1. No environmentally significant trends in water quality were detected by visual assessment of the data.
  2. Fecal coliforms may have exceeded the criterion for raw drinking water receiving disinfection only.
  3. Turbidity removal and disinfection are recommended prior to drinking.
  4. Water temperatures were quite high, good in the spring and summer for recreation, but not for fisheries or drinking water supplies.

The recommendation is to continue monitoring of water quality and flow for the Okanagan River at Oliver because of its proximity to Osoyoos Lake, a transboundary water body. A minimum of five fecal coliform samples should be collected every 30 days to make a better statistical assessment of the fecal contamination situation.


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Peace River above Alces River, 1984 - 2002

The Peace River is a major river located in northeastern British Columbia, flowing from the W.A.C. Bennett Dam and Williston Reservoir eastward to the Alberta border. River water quality is important to aquatic life, recreation, livestock watering, industry, wildlife, and irrigation. Also, the Peace River is a drinking water supply for the Village of Taylor and the District of Hudson's Hope. Waste discharges from the McMahon gas plant, the Fibreco pulp mill and the City of Fort St. John affect river water quality, as do agriculture and forestry.

This report assesses water quality data collected at the monitoring station above Alces River, near the Alberta border. Water quality samples were collected bi-weekly between 1984 and 1995. Flow was measured at a Water Survey of Canada flow gauge near Taylor. There are several main conclusions.

  1. Individual chromium, copper, lead, and zinc values did not always meet the site-specific water quality objectives due to the high levels of suspended sediment in the water during freshet.
  2. Total aluminum, arsenic, cadmium, iron, manganese and selenium, fecal coliform, apparent colour and turbidity values did not always meet water quality criteria due to the high levels of suspended sediment in the water during freshet.
  3. No obvious environmentally significant trends in water quality were identified through visual examination of the data.
  4. The Peace River above the Alces River had very high levels of suspended solids and turbidity during spring freshet due to the inflow from tributaries downstream from the W.A.C. Bennett Dam. These tributaries drain areas of highly erodible soils that support agricultural and forestry land uses. The high suspended solids had a major influence on the levels of many other water quality variables as outlined above.
  5. High metals and turbidity values occurred together in samples collected during 1984-94. This indicates that the metals were probably in a particulate form and not biologically available and would be removed by the drinking water treatment needed to remove turbidity. Turbidity removal and disinfection are required prior to drinking.
  6. The river has a low sensitivity to acid inputs.
  7. Hardness levels were at or above the optimum range for drinking water, but still quite acceptable.
  8. No remedial activities appear to be necessary at this time.

It is recommended that monitoring be continued for the Peace River above Alces River for the following reasons:

  1. It is the only long-term station on the Peace River.
  2. It is being used to determine transboundary effects and Alberta maintains a high interest in the quality of water crossing its border.
  3. It is necessary to confirm that the upstream point source discharges, Fibreco Pulp Inc., McMahon Gas Plant, Fort St. John sewage treatment facilities, continue to have no influence at the border.
  4. It is being used to determine the impact of non-point sources such as agriculture and forestry.


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Pend d'Oreille River at the U.S. Border, 1997 - 2003

The Canadian portion of the Pend d'Oreille River is about 15 km long, and is located in southern British Columbia near the United States border, southeast of Trail, BC. The total drainage area of the Pend d'Oreille River is about 66600 km2, with 65300 km2 in the United States. There were several main conclusions.

  1. There were no environmentally significant trends in water quality that could be detected through visual examination of the data.
  2. The water quality of the Pend d'Oreille River was very good, with most of the water quality indicators meeting their criteria.
  3. Aluminum and iron exceeded criteria for drinking water and aquatic life at times, but they appeared to be in a particulate form and were probably not bio-available and would be removed by drinking water treatment needed to remove turbidity.
  4. Turbidity and non-filterable residue were low, probably due to the settling in upstream reservoirs.
  5. Turbidity and disinfection are needed before use for drinking.
  6. The river was well buffered to withstand acid inputs.
  7. Water temperatures were warm enough for water-contact recreation in the summer, but these higher temperatures are not desirable for salmonids or drinking water aesthetics. The upstream reservoirs may have increased summer water temperatures.


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Prospect Lake, 1980 - 1995 + April, 1996

Prospect Lake s located on southern Vancouver Island near Victoria, BC. The watershed for this small lake is 23 km2. The surface area of Prospect Lake is 7.2 ha. This report assesses 16 years of water quality data and comes to the following conclusions.

  1. Spring overturn sampling indicates that in recent years there were less nutrients (e.g., total phosphorus, dissolved ammonia) in the water column. These changes in nutrient values may be attributed to a change in the amount of nutrients entering the lake or to a change in lake processes.
  2. Total phosphorus values exceeded the criterion range for protecting aquatic life (0.005 mg/L to 0.015 mg/L) in 1984. The criterion (0.01 mg/L) for recreational use and drinking water was exceeded in eight of eleven years between 1980 and 1995.
  3. Phosphorus is the limiting nutrient for algal growth in Prospect Lake.
  4. The Capital Regional District's Health Protection and Environmental Division has posted advisory notices at Prospect Lake (North Lakeside Park Beach) on several occasions between 1980 and 1995, warning of the potential for increased risk to bathers' health. These notices were posted when the geometric mean exceeded 200 fecal coliforms/100 mL over a 30-day period.
  5. There were insufficient fecal coliform data to assess the suitability of the lake water as a drinking source.
  6. True colour values exceeded the criteria for drinking water (aesthetics) and for recreation (15 colour units) in 1992 and 1995.
  7. Total organic carbon values exceeded the drinking water criteria (4 mg/L) in 1980. Prospect Lake water has the potential to form trihalomethanes in excess of the 0.1 mg/L criterion when chlorinated.
  8. Total aluminum values exceeded the 30-day average criterion for protecting aquatic life (0.05 mg/L) in 1992.
  9. Total copper values exceeded the criterion for protecting aquatic life (0.002 mg/L) in 1992.

The recommended monitoring includes the following:

  1. to determine whether water quality objectives need to be established for aluminum, true colour, or copper in Prospect Lake
  2. to identify changes in water quality attributed to biological activity in the lakes, to activities within the watershed such as urbanization, and to changes in nonpoint discharge
  3. to determine whether public beaches are suitable for bathing
  4. to determine whether drinking water from the lake meets the fecal coliform criterion

The first two monitoring programs could be implemented by a Prospect Lake stewardship group with assistance from the Ministry of Environment, Lands and Parks (Water, Land and Air Protection), the third monitoring program is currently being conducted by the Capital Regional District's Health Protection and Environmental Division and the fourth monitoring program should be implemented by the Capital Regional District's Health Protection and Environmental Division or by a Prospect Lake stewardship group.


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Quamichan Lake, 1988 - 1995 + April, 1996

Quamichan Lake is located on southern Vancouver Island 3 km east of Duncan, BC. The watershed for this large, shallow lake is 16.3 km2. This report assesses 5 years of water quality data, 21 years (1973-1995) of fecal coliform data, and comes to the following conclusions.

  1. Spring overturn sampling indicates that in recent years there were less nutrients (e.g., total phosphorus, total dissolved phosphorus, dissolved ammonia) in the water column. These changes in nutrient values may be attributed to a change in the amount of nutrients entering the lake or to a change in lake processes.
  2. Total phosphorus values from Quamichan Lake were outside the limits (0.005-0.015 mg/L) for aquatic life in 1992 and 1993, but within them in 1994 and 1995 and exceeded the criteria for drinking water and protecting recreational use (0.010 mg/L) in 1992, 1993, and 1995.
  3. Total phosphorus is the limiting nutrient for algal growth in Quamichan Lake.
  4. The Central Vancouver Island Health Unit has posted Art Mann Park Beach as being unfit for recreational bathing since 1986, warning of the potential for increased risk to bathers' health. Fecal coliform values increased between 1973 and 1995. This increase may be due to an increasing resident waterfowl population.
  5. True colour values were constant (5 colour units) since 1993. One value exceeded the criteria for drinking water and for recreation.
  6. Three water quality indicators, total aluminum, total copper and total zinc, exceeded the criterion for protecting aquatic life. This increase may be due to the level of uncertainty near their minimum detectable limits.
  7. It is recommended that a remediation plan be developed and implemented to improve water quality in Quamichan Lake.

The following monitoring is recommended:

  1. to determine if aluminum, copper, manganese and zinc exceed the criteria for protecting aquatic life in Quamichan Lake
  2. to identify changes in water quality attributed to activities within the watershed such as urbanization, changes in nonpoint discharge and biological activity
  3. to determine whether public beaches are suitable for bathing
  4. to determine whether drinking water from the lake meets the fecal coliform criterion

The first two monitoring programs could be implemented by the Ministry of Environment, Lands and Parks (Water, Land and Air Protection) with assistance from a Quamichan Lake stewardship group, the third monitoring program will continue to be implemented at Art Mann Beach by the Central Vancouver Island Health Unit and the fourth monitoring program should be implemented by the Central Vancouver Island Health Unit, or by a Quamichan Lake stewardship group.


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Quinsam River, 1986 - 2004

The Quinsam River is located on eastern Vancouver Island, west of the town of Campbell River, BC. The total drainage area of the Quinsam River is 280 km2. The main economic activities pertaining to the Quinsam River are fishing, coal mining, and hydroelectric power. This report assesses water quality and flow data collected by Environment Canada at stations near the mouth of the Quinsam River between 1986 and 1995. There were several main conclusions.

  1. Increasing trends were observed for calcium, hardness, specific conductivity, magnesium, sodium, sulphate, and strontium. These increases were probably due to weathering of exposed rock at the coal mining operation within the drainage basin.
  2. Selenium values appeared to decrease towards being consistently at or below the minimum detectable limit. We have no explanation for this apparent decline.
  3. Turbidity, apparent colour and total metal values followed an annual cycle similar to that of river flow, peaking in the winter and subsiding in the summer. Turbidity removal and disinfection are needed prior to use for drinking water.
  4. Aluminum, cadmium, iron, lead, manganese and zinc exceeded water quality criteria or objectives for aquatic life or drinking water at times, but this was due to elevated turbidity. The metals were probably not bio-available, and would have been removed by the treatment needed to remove turbidity prior to drinking.
  5. Chromium and copper exceeded aquatic life criteria or objectives at times. At least half of these instances were due to elevated turbidity, but some of them occurred when turbidity was low, indicating that the metal may have been bio-available. Elevated chromium may have been due to either natural causes or artificial contamination.
  6. The water was soft with a low to moderate sensitivity to acid inputs.
  7. The water was usually cool enough to be aesthetically pleasing for drinking, but was rarely warm enough for swimming.

The Quinsam River sustains an important fishery and is a potential drinking water supply. We recommend that monitoring be continued at this site on the Quinsam River near the mouth due to increasing trends in a number of water quality indicators. These increases, while not a direct threat to aquatic life at present, will also be addressed through additional monitoring near the mine.


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Salmon river near Hyder, Alaska, 1981 - 2002

This report assesses twelve years of water quality data from the Salmon River. The Salmon River is a transboundary river which flows in a southerly direction from the north central coast of the province, emptying into the north end of the Portland Canal near Hyder, Alaska (USA). The Portland Canal separates the southern portion of the state of Alaska and the north central BC coast. Environment Canada has monitored the Salmon River since 1982, collecting approximately 52 samples per year. One other related water quality monitoring station within this area is the Bear River at Stewart, BC.

Known errors were removed and the plotted data were compared to BC Environment's Approved and Working Criteria for Water Quality. Of special interest were water quality levels and trends that are deemed deleterious to sensitive water uses including drinking water, aquatic life, fish and wildlife, recreation, irrigation and livestock watering. There were several main conclusions of this assessment.

  1. The water quality of the Salmon River near Hyder over the 1982 to 1995 sampling period is believed to be largely influenced by natural phenomena such as glacial erosion and mineralization. The watershed is sparsely populated and relatively unimpacted by humans except for some mining.
  2. The only environmentally significant trend in water quality detected by visual appraisal of the plotted data was the dramatic increase in cyanide between 1989 and 1992, and the subsequent decline to low levels by 1993.
  3. Zinc exceeded aquatic life criteria on a few occasions during the winter. This may have been due to contamination during sampling or zinc-rich drainage from old mines. An investigation of the impact of the zinc from the old mine workings is underway.
  4. The water was high in selenium, probably due to the geology of the watershed, and often exceeded the criterion for aquatic life. It is not clear what effect historical and active mining played in contributing to the selenium levels.
  5. Because this is a glacier-fed river, the water was often turbid, especially during annual freshet when higher flows resulted in increased erosion, suspended sediment and turbidity.
  6. The increased turbidity during freshet would make it necessary to treat the water to remove turbidity prior to use as drinking water.
  7. Freshet also brought increased levels of total metals, total phosphorus, total organic carbon and apparent colour. Most of these may not be of concern because they were due to the increased suspended sediment in the water, and thus were probably largely biologically unavailable or would be removed by the treatment needed prior to drinking.

There are two main recommendations:

  1. Continue monitoring at this station because it is a transboundary river with mining activity.
  2. Investigate the sources of the high levels of selenium and zinc for potential abatement.


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Shawnigan Lake, 1976 - 1995 + April, 1996

Shawnigan Lake is located on southern Vancouver Island near Victoria, BC. The watershed for this medium-sized lake is 69.4 km2. This report assesses 20 years of water quality data and comes to the following conclusions.

  1. The turbidity objectives for Shawnigan Lake have been met at the deepest point (50 m) of the lake. Turbidity decreased between 1977 and 1995.
  2. Total phosphorus values exceeded the objective to limit algal growth only in 1980. These values have decreased since 1985. This may be attributed to a decrease in nutrients entering the lake or to an increase in biological production.
  3. Phosphorus is the limiting nutrient for algal growth in Shawnigan Lake.
  4. Total organic carbon values exceeded the criterion for drinking water in 1980. Chlorinated drinking water may produce trihalomethanes which exceed the drinking water criterion (0.1 mg/L) when total organic carbon values are greater than 4 mg/L.
  5. Central Vancouver Island Health Unit determined that all public beaches were fit for bathing between 1988 and 1995.
  6. There were insufficient data to assess the suitability of the lake water as a drinking source.

The following monitoring is recommended:

  1. to determine whether water quality objectives are being met
  2. to identify changes in water quality attributed to biological activity in the lake, to activities within the watershed such as urbanization and to changes in nonpoint discharge
  3. to determine whether public beaches were suitable for bathing
  4. to determine whether trihalomethanes values in chlorinated drinking water from Shawnigan Lake meet the drinking water criterion

The first two monitoring programs could be implemented by the Ministry of Environment, Lands, and Parks (Water, Land and Air Protection) with assistance from a Shawnigan Lake stewardship group, the third monitoring program will continue to be implemented at the four bathing beaches by the Central Vancouver Island Health Unit and the fourth monitoring program should be implemented by the two water works licencees, Sherwood Water Works and Lidtech Holdings Ltd. The results of this monitoring should be reported, on a quarterly basis to the Central Vancouver Island Health Unit.


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Similkameen River, 1966 - 2000

There have been three long-term water quality monitoring stations on the Similkameen River. This report focuses on the water quality at the site on the Similkameen River near the US Border, and incorporates water quality conditions at the two upstream sites on the Similkameen River at Princeton and Hedley. Similkameen River water is used for irrigation, livestock watering, drinking, primary and secondary-contact recreation, and industrial use, and sustains aquatic life and wildlife. We conclude that:

  • No environmentally significant trends were detected through visual assessment of the data.
  • A trend of increasing average yearly dissolved chloride concentration exists since 1980, but guidelines will not be exceeded in the foreseeable future.
  • Water quality objectives for ammonia and pH were met.
  • Arsenic was above the guidelines levels during spring freshet near the US Border but not upstream, indicating that the source of arsenic is between Hedley and the US Border, possibly abandoned mines. It was probably in particulate form as it was high during periods of high turbidity, and was probably not bio-available.
  • Copper objectives were met except during spring freshet. As copper was high at all three Similkameen River sites during freshet, it appears to be a basin-wide phenomenon. It is probably in particulate form and thus not bio-available.
  • Cyanide objectives were met except on one or two occasions at each of the three sites. These exeedances were not due to the mines downstream from Hedley, and may have been due to unknown sources or artificial contamination.
  • Fecal coliform levels probably did not meet the water quality objective to protect drinking water that receives only disinfection. More frequent monitoring (i.e., 5 to 10 samples in 30 days) is required to improve the comparison to the objective. Consideration should be given to changing the objective to 100 fecal coliforms/100 mL since the water needs to receive partial treatment (e.g. filtration) and disinfection before drinking; this change would reflect the fact that fecal coliforms tend to attach to suspended particles and would be removed by filtration.
  • Water temperature exceeded the aesthetics guideline for drinking water (15°C) in 18% of the samples collected between 1979 and 1997. During the summer months (June to September) the water was warm enough for primary-contact recreation (e.g., swimming).
  • Water hardness was acceptable.
  • The river had a low sensitivity to acid inputs (well buffered).
  • Similkameen River water at all sites must be treated to remove turbidity and disinfected prior to drinking during times of high turbidity.
  • Total cadmium, chromium, cobalt, copper, iron, lead, manganese and zinc exceeded the guidelines for aquatic life. Usually, these values coincided with high suspended sediment values, indicating that these metals were likely in a particulate form, probably not biologically available, and would be removed by drinking water treatment needed to remove turbidity.

Recommendations:

  • This cursory examination of the water quality objective for fecal coliforms has led us to believe that the current level may not be appropriate. It is recommended that this be the subject of a more thorough review than possible here, taking into account background levels of turbidity and microbiological contaminants throughout the basin, numbers of domestic withdrawals, current levels of water treatment, and other similar factors.
  • We recommend that consideration be given to reducing the arsenic objective to 0.005 mg/L to reflect the proposed new guidelines for drinking water and aquatic life.

Monitoring Recommendations:

  • Monitoring should continue at the Similkameen River near the US Border, and at the upstream control station, Princeton. The site near the US Border is both a trans-border station and is downstream of the largest number of industrial waste discharges to the Similkameen River.


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South Thompson River at Kamloops, 1973 - 1997

This report assesses the long-term water quality trends of the South Thompson River at Kamloops. The South Thompson River, in the Southern Interior of British Columbia, begins at the outlet of Little Shuswap Lake, and flows southwest and west for 60 km before it converges with the North Thompson River at the City of Kamloops. Water quality has been monitored on the South Thompson River at Kamloops, with a flow station near Chase. BC Environment began water quality monitoring at Kamloops in 1973. Five other related water quality monitoring stations within the Thompson River watershed are: the North Thompson River at North Kamloops, the Bonaparte River near mouth, the Thompson River at Spences Bridge, the Salmon River at Highway #1, and the Nicola River at Spences Bridge.

The plotted data were compared to the water quality objectives for the South Thompson River and to British Columbia's approved and working guidelines for water quality to see if any of the measurements had exceeded objectives or guidelines. Of special interest were water quality levels and trends that were deemed deleterious to sensitive water uses, including drinking water, aquatic life, wildlife, recreation, irrigation, and livestock watering.

The main conclusions of this assessment are:

  • No environmentally significant trends in water quality were detected by visual appraisal of the data with the exception of suspended solids which is thought to be largely non-point source related such as from agriculture, forestry and residential development.
  • The water was well buffered against acid inputs throughout the year, but yet quite soft for drinking water.
  • The water was cool or cold enough throughout most of the year to be aesthetically pleasing for drinking, and usually warm enough during the summer months to permit water-contact recreation such as swimming.
  • Turbidity and non-filterable residue levels were elevated during freshet when higher flows resulted in increased runoff and erosion, particularly from tributary streams. Remediation of non-filterable residue and turbidity sources and levels is needed.
  • Fecal coliforms probably did not meet the water quality objective for the South Thompson River designed to protect raw drinking water for use after only disinfection, and the remediation of the sources of fecal contamination is probably needed.
  • During freshet, elevated levels of aluminum and iron occurred. These levels may not have been of concern however, since they were due to the increased suspended sediment in the water, and thus were probably mostly biologically unavailable.
  • During freshet, elevated levels of phosphorus occurred, but the phosphorus was largely in particulate form, and not readily available for algal growth.

Our main recommendation:

  • Reduce sources and levels of fecal coliforms, non-filterable residue, and turbidity in the watershed. Continue monitoring at this site as the South Thompson River is important both as a water resource and as an aquatic habitat.


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Stikine River above Choquette River, 1981 - 1994

The Stikine River is located in northwest British Columbia, flowing westward to Alaska and the Pacific Ocean. Activities occurring in the Stikine watershed include mining and forestry. This report assesses water quality data collected at the monitoring station upstream from the confluence with the Iskut River. Water quality samples were collected between 1981 and 1994 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge located 58 km southwest of Telegraph Creek and about 70 km upstream from the water quality station. There are several main conclusions.

  1. There were no environmentally significant trends in water quality.
  2. Peak non-filterable residue and turbidity values occurred during peak flow periods.
  3. High metals and non-filterable residue occurred together in samples collected over the period of record. This would indicate that the metals were in a particulate form, probably not biologically available and would be removed by drinking water treatment needed to remove turbidity.
  4. Total aluminum, cadmium, chromium, copper, iron, lead, manganese, nickel and zinc, organic carbon, apparent colour, non-filterable residue and turbidity values did not meet various water quality criteria at times due to high levels of suspended sediment carried by high river flow.
  5. Copper levels exceeded the aquatic life criteria most of the time, suggesting a naturally high copper mineralization in the watershed.
  6. Turbidity removal and disinfection would be needed prior to drinking.
  7. The river had a low sensitivity to acid inputs.
  8. The river was cool enough for drinking, but too cold for water-contact recreation.
  9. Hardness levels were generally below the optimum range for drinking water in the summer and at or above the optimum range in the winter, but were still quite acceptable for drinking.

It is recommended that monitoring be discontinued for the Stikine River above Choquette River.

  1. There were no obvious or deleterious trends observed in the plotted data over the 1981 to 1994 sampling period.
  2. There are no water quality concerns at the present time.
  3. We now have an adequate baseline of data for comparison to future data.


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St. Mary Lake, 1975 - 1995 + April, 1996

St. Mary Lake is located on Saltspring Island. The watershed for this small lake is 7.07 km2. This report assesses 20 years of water quality data and comes to the following conclusions.

  1. Total phosphorus values in the water column have decreased since 1980. However, phosphorus values exceeded the criteria for recreation and aquatic life.
  2. Phosphorus has been the limiting nutrient for algal growth in St. Mary Lake since 1986.
  3. Total organic carbon values exceeded the criterion for drinking water. Chlorinated drinking water may produce trihalomethanes which exceed the drinking water criterion (0.10 mg/L) when total organic carbon values are greater than 4 mg/L.
  4. The Capital Regional District's Health Protection and Environmental Division determined that the public beach on St. Mary Lake was suitable for bathing between 1988 and 1995.
  5. All mean summer chlorophyll a values collected between 1979 and 1989 exceeded the upper limits for protecting drinking water (2.5 µg/L) and aquatic life (3.5 µg/L).
  6. Extinction depth values from St. Mary met the criterion (greater than 1.2 m) for recreational use in 65% of the measurements.
  7. Turbidity values from St. Mary were outside the limits (5 NTU and 1 NTU) for drinking water. North Saltspring Water Works uses a sand filter to reduce the turbidity of the water to meet the drinking water criterion (1 NTU).
  8. It is recommended that a remediation plan be developed and implemented to improve water quality in St. Mary Lake.

The following monitoring is recommended:

  1. to identify changes in water quality attributed to biological activity in the lakes, to activities within the watershed such as urbanization, and to changes in nonpoint discharge.
  2. to determine whether the public beach is suitable for bathing.
  3. to determine whether drinking water from the lake meets the fecal coliform criterion.
  4. to determine whether trihalomethanes values in chlorinated drinking water from St. Mary Lake met the drinking water criterion.

The first monitoring program could be implemented by an St. Mary Lake stewardship group with assistance from the Ministry of Environment, Lands and Parks (Water, Land and Air Protection), the second monitoring program will continue to be implemented at the bathing beach by the Capital Regional District's Health Protection and Environmental Division. In future, local interest groups (e.g., St. Mary Lake stewardship group, Island Trust) could assist with this ongoing monitoring, the third monitoring program could be implemented by the Capital Regional District's Health Protection and Environmental Division, or by a St. Mary Lake stewardship group and the fourth monitoring program should be implemented by the two water works licencees (North Saltspring Waterworks District and Capital Regional District). The results of this monitoring should be reported, on a quarterly basis, to the Capital Regional District's Health Protection and Environmental Division.


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Thompson River at Spences Bridge, 1984 - 2004

This report assesses the long-term water quality trends of the Thompson River at Spences Bridge. The Thompson River watershed, which has a drainage area in excess of 55,000 km2, occupies a significant portion of southern British Columbia. It encompasses the North Thompson, the South Thompson and the lower Thompson rivers, and is a major tributary of the Fraser River. The lower Thompson originates at Kamloops, at the confluence of the North and South Thompson rivers, and flows for approximately 160 km before emptying into the Fraser River at Lytton. Water quality has been monitored on the Thompson River at Spences Bridge since 1985. Five other long-term water quality monitoring stations within the Thompson River watershed are: the North Thompson at North Kamloops, the South Thompson at Kamloops, the Bonaparte River near mouth, Salmon River at Highway #1 Bridge, and the Nicola River at Spences Bridge.

The plotted data were compared to water quality objectives for the Thompson River and to British Columbia's approved and working guidelines for water quality. Of special interest were water quality levels and trends that may have been deleterious to sensitive water uses including drinking water, aquatic life, wildlife, recreation, irrigation, and livestock watering.

The main conclusions of this assessment are:

  • Levels of adsorbable organic halides (AOX), chloride, dioxins and furans and sodium have shown a decrease since the early 1990's, a result of changes made by the upstream pulp mill.
  • The water was cool or cold enough throughout most of the year to be aesthetically pleasing for drinking, and usually warm enough during the summer months to permit water-contact recreation such as swimming, while remaining cool enough for salmonids.
  • The water turbidity often exceeded drinking water guidelines, especially during annual freshet when higher flows resulted in increased erosion, increased runoff, and suspended sediment. Treatment to remove the turbidity prior to use as drinking water is needed.
  • During freshet, fairly high levels of phosphorus and many metals occurred, but since these were likely due to raised particulate levels, they were not necessarily bio-available, and would be reduced by the treatment needed to remove turbidity prior to drinking.


Our main recommendation:
Continue monitoring at this site, especially for variables related to the major waste discharges of the upstream pulp mill near Kamloops. Key variables to monitor in the future are: flow, total and dissolved aluminum, cadmium, chromium, iron and zinc, dissolved organic carbon, AOX, true colour, hardness, pH, total dissolved and dissolved ortho-phosphorus, turbidity, and air and water temperature. Minimum detectable limits should be at least one-tenth of the water quality guidelines for all variables.


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Unuk River near US border, 1991 - 1993

The Unuk River is located in northwest British Columbia, flowing southwest to Alaska and the Pacific Ocean. Proposed and active mining projects are located within the Unuk River watershed. Also, the Unuk is important to sport and commercial fishing, mainly in the Alaskan portion of the river. This report assesses water quality data collected at the monitoring station 3 km upstream from the Alaska border and 65 km northwest of Stewart, BC. Water quality samples were collected between 1991 and 1993 by Environment Canada. Flow was measured at a Water Survey of Canada flow gauge at the water quality monitoring station. There were several main conclusions:

  1. Not enough data were available to comment on trends in water quality, although a slight downward trend in pH was apparent.
  2. High metals and non-filterable residue occurred together. This suggests that metals were in a particulate form, probably not biologically available, and would be removed by the turbidity removal needed before drinking.
  3. Total aluminum, cadmium, chromium, copper, iron, lead, manganese and zinc, apparent colour, non-filterable residue and turbidity values did not meet various water quality criteria at times due to high levels of suspended sediment in the water during freshet.
  4. Copper levels exceeded the aquatic life criteria at all times, suggesting a naturally high copper mineralization in the watershed.
  5. The river had a low sensitivity to acid inputs.
  6. Hardness levels were generally below the optimum range for drinking water in the summer and within the optimum range in the winter.
  7. Treatment to remove turbidity, plus disinfection, would be necessary before the water was used for drinking.
  8. The water was cool enough to be aesthetically pleasing for drinking, but too cold for water-contact recreation such as swimming.

It is recommended that reactivation of water quality monitoring be considered for the Unuk River near the US border for the following reasons:

  1. It is a trans-boundary river that supports an important fishery.
  2. There are active and potential mine sites within the watershed.
  3. The watershed is relatively small, 1480 km2, and thus potentially sensitive to change.
  4. The existing baseline water quality record is short and sparse.
  5. The forthcoming road construction will improve access for the purpose of monitoring.


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Last Updated: February 2009
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