Surface Water Quality Report on Current Conditions

Vermilion River Watershed

29 March, 2016

Prepared by: Conservation Sudbury

Table of Contents Table of Contents ...... 2

1.0 Introduction ...... 3

2.0 Watershed Description ...... 4

2.1 Study Area ...... 4

2.2 Sources of Contamination ...... 7

3.0 Material and Methods ...... 8

4.0 Results and Discussions ...... 14

4.1 Exploratory Analysis ...... 14

4.2 Current Water Quality Conditions ...... 14

4.2.1 Field Observations ...... 14

4.2.2 Conventional Contaminants ...... 15

4.2.2.1 Road Salt ...... 15

4.2.2.2 Total Phosphorous (TP) ...... 18

4.2.2.3 Escherichia coli (E. coli) ...... 20

4.2.3 Metal Contaminants ...... 21

5.0 Conclusion ...... 24

6.0 References ...... 26

7.0 Appendix A ...... 27

8.0 Appendix B ...... 40

PWQMN Protocol for Stream Water Quality Monitoring (OMOE, 2006) ...... 40

9.0 Appendix C ...... 41

10.0 Appendix D ...... 42

1.0 Introduction

Canada is the second largest country in the world with very low human population density and is relatively free from industrial activity. As a result, much of the country has escaped the major problems associated with heavy industrial activities (Schindler et al., 2006). But events such as contamination of public water supplies in the Towns of Walkerton, Ontario and North Battleford, Saskatchewan and numerous boil water advisories in various municipalities in Canada have been a constant reminder that a healthy environment cannot be taken for granted. The Walkerton tragedy highlights many key issues such as: lacking an established nationwide water quality program, current monitoring is temporally and spatially fragmented, and the poor use of data and information generated by monitoring activities (Khan et al., 2003).

In Ontario, though limited and fragmented, we are fortunate to have a long running surface water quality monitoring program; where the water quality information from streams at locations across Ontario is collected as part of the Provincial Water Quality Monitoring Network (PWQMN). The network has 390 monitoring stations operated in partnership with 36 conservation authorities across Ontario. This partnership has been operating in the area since 1964, with a short hiatus in the late 1990s. The water quality parameters analyzed for this program include chloride, nutrients, suspended solids, trace metals and other general chemistry parameters. In the City of Greater Sudbury, Conservation Sudbury (CS) monitors ten major rivers and streams under this network, which are located in two main watersheds; the Vermilion River and the Wanapitei River. PWQMN information is one of the main sources of surface water information used by the Ministry of Environment and Climate Change (MOECC) to evaluate applications for certificates of approval and permits to take water and to develop water quality standards.

The Vermilion River Watershed in particular remains one of the important watersheds within the City of Greater Sudbury in spite of just a third of its watershed being located within the municipal jurisdiction. The watershed houses the majority of the city’s population and is also home to many diverse land use activities compared to its neighboring watersheds. For the better part of the 20th century, the City of Greater Sudbury was metaphorically compared to a moonscape due to its damaged landscape, however, decades of hard work and collective efforts from the community have made environmental recovery possible. Though the local environment is still recovering from the historic mining activities, in recent years, some water bodies within the Vermilion River system have been facing challenges from other anthropogenic activities like urban development and nutrient enrichment as well. The impacts of algae blooms (Ella Lake in winter), numerous boil water advisories, new development challenges along with activities mentioned earlier, have been a cause of concern for the residents of the watershed.

Vermilion River Watershed consists of a wide range of land cover categories, which include mining, industrial, urban, suburban, agricultural, wetlands and water bodies. The watershed is approximately

4,429 square kilometers in size, and has an approximate population of 100,0001. Mining and related industries continue to dominate the local economy which is due to the region’s mineral rich conditions. Although most of the urban land use is in the south western area, in and around the Sudbury core (old Sudbury), there are numerous smaller urban centers and settlement areas in other parts of the watershed as well.

Unfortunately, a detailed water quality assessment of the entire Vermilion River and its sub watersheds has never been completed. Therefore, there was a strong need for analyzing water quality data at various sites to better understand different land use issues. Water quality assessment can be a good tool to scan prevailing water quality conditions and establish the areas of concern.

From 2013 to 2015, the Ontario Trillium Foundation (OTF) provided funding to the Vermilion River Stewardship (VRS) to conduct water quality monitoring in the Vermilion River Watershed. In 2012 CS was approached by the VRS group to develop a water quality monitoring program for the Vermilion River Watershed, with the funds approved by the OTF. CS agreed to collect water quality data, analyze and compare the results to the Provincial Water Quality Objectives (PWQO) and or Ontario Drinking Water Standards (ODWS). The principal objective of the monitoring program was to establish baseline information and assess the water quality condition in the watershed.

CS was responsible for the planning and execution of the water quality monitoring program for all three years. This report has been prepared by CS in association with the Vermilion River Stewardship. Water quality data collected from twenty eight stations between 2013 and 2015 have been assimilated and analyzed to prepare this report. The following sections have been developed by compiling available background information for the area including natural characteristics, population distribution and land uses. Several maps are also provided to illustrate much of this information.

2.0 Watershed Description

2.1 Study Area Sudbury is known as “the City of Lakes” encompassing 330 lakes that are larger than 10 hectares and 47 lakes larger than 100 hectares. This section describes this area of lakes, rivers, wetlands, forests, as well as the City of Greater Sudbury, which functions as a service hub for Northeastern Ontario.

The Vermilion River is the main tributary of the Spanish River and its head waters originate in Frechette Township in the rugged northern Precambrian ridges of the watershed. It flows in a southerly direction and follows a meandering path. The watershed area is mostly forested with approximately 302 km2 of lakes.

1 Calculation based on extrapolation of data from the population density maps

The Vermilion River has an approximate length of 248 km with an approximate elevation drop of 251 m and drains an area of 4,429 km2. The flow in the Vermilion River is contributed by a number of tributaries and sub-tributaries as tabulated in Table 2.1.

Onaping Lake, which is a head water reservoir for the Onaping River, eventually discharges in three directions: southerly to the Vermilion River, westerly to the Spanish River and northerly to the Mattagami River. The northern flow has been blocked and the water is mainly diverted towards the Spanish River through regulation of the Bannerman Dam. The Onaping River is the main outlet of the lake and a main tributary of the Vermilion River. It drains an area of 1,378 km2 which includes Onaping Lake with a surface area of 66 km2.

Table: 2.1 Vermilion River Watershed Tributaries and Sub-Tributaries

River Length (km) Drainage Area (km2) Drop Average Gradient (m/km) (m) Michaud River 19 145.84 38 2.00 Rapid Creek 34 82.66 146 4.29 Roberts River 28 187.67 108 3.86 Onaping River 71 1377.56 141 1.99 Sancherry Creek 24 139.82 148 6.17 Windy Creek 19 90.64 102 5.37 Junction Creek 49 324.19 55 1.12 Levey Creek 17 148.14 13 0.76 Whitson River 44 312.88 43 0.98 Cameron Creek 34 103 3.03 Fairbank Creek 23 72.47 68 2.96 Nelson River 16 193.35 74 4.63

The Whitson River, another main tributary of the watershed, flows in a south-westerly direction and enters the Vermilion River in Creighton Township in the City of Greater Sudbury. The Whitson River drains an approximate area of 313 km2. This river passes through the urban towns of Val Caron and Chelmsford and has been a source of a number of flooding events in the past.

Junction Creek, another urbanized watershed, has significant mining activity. It drains an area of 324 km2 passing through the City of Greater Sudbury and eventually joins the Vermilion River at McCharles Lake. Nolin Creek and Copper Cliff Creek are the subwatersheds which join Junction Creek in downtown Sudbury.

Table: 2.2 Vermilion River dams and diversion structures

Dam Structure Owner/ Purpose Description of Operational Plan Operator Bannerman Domtar Onaping Lake serves as a The reinforced concrete dam has a single log Dam reservoir. sluiceway, which contains stop logs. The dam also has east and west weir. Onaping Lake Domtar In conjunction with the The reinforced concrete dam has three log Dam Bannerman Dam, sluiceways, which contain many stop logs. regulates the lake level. Strathcona Glencore Is a final effluent polishing A 61 cm diameter pipe is installed in the Creek Dam pond dam. roadway beside the existing 1.83 m diameter The purpose of the control culverts (culverts remain for contingency station is to control water purposes). A separate 31 cm pipe is installed quantity and quality. to provide extra discharge. The 61 cm pipe flow is measured by an ultrasonic flow meter which is controlled by a butterfly valve. Stobie Dam Domtar Water management The reinforced concrete dam has five log sluiceways, four of which have double stop logs. The dam also has an east and west weir. Windy Lake Ministry The dam is used to The dam discharges in to the Windy Creek, Dam of Natural regulate the water level. which finally discharges in to the Onaping Resources River near Dowling. The dam consists of a log sluiceway and an Ogee Spillway. Whitewater Ministry Regulate water level for The reinforced concrete dam has two log Lake Dam of Natural recreational purposes. sluiceways which contain stop logs. Resources Dam controls the level of The sluiceways are 8.5 m in width, the height Whitewater Lake. of the dam is 3.96 m with maximum head of 2.7 m and a total dam length of 24.4 m. Maley Dam CS Flood control Dam discharges through sluiceway and steel gates. Nickeldale CS Flood control Controls a discharge area of 9 km2. Dam The dam is 381 m long and 9 m high with a core of impervious clay covered with earth fill and protected by a layer of rock fill. Lake CS Controls lake level The structure is a concrete box culvert with Laurentian six 4 inch logs installed. Dam Controls a drainage area of approximately 8 km2. Nepahwin CS Water level control The dam has three bays, each approximately Dam 0.9 m wide, with a 10 cm log in each bay. Kelly Lake City of Manage water level in The concrete weir is about 18.3 m wide and Dam Greater Kelly Lake 1.22 m high. Sudbury

Robinson Lake City of Used for recreation and to The concrete weir has one stop log and Dam Greater prevent a back flow from covers a drainage area of 25.4 km2. Sudbury Kelley lake. Ramsey Lake City of Used for flood control, The reinforced concrete dam has two Dam Greater recreation and water level sluiceways and contains up to seven stop logs Sudbury control for the municipal in each sluiceway. The dam covers a drainage water supply intake. area of 12.7 km2. Wabagishik Vale Power generation The run of the river facility consists of a (Lorne Falls) concrete gravity type dam structure. The dam Dam is 221 m in length. The spillway consists of a single motorized gate, which is 12.2 m in length and 7.3 m in height.

The flow in the Vermilion River and tributaries is regulated by a number of dams. The main dams or diversion structures on the system are Bannerman Dam, Onaping Lake Dam, Strathcona Creek Dam, Stobie Dam, Windy Lake Dam, Maley Dam, Nickeldale Dam, Lake Laurentain Dam, Nepahwin Dam, Kelly Lake Dam, Robinson Lake Dam, Ramsey Lake Dam, Frood Dam and Wabagishik Dam.

The water level and flow is measured at various locations by Water Survey of Canada, CS, Domtar and Vale. The river has a mean annul flow of 45.7 m3/s at Lorne Falls and 46.6 m3/s (pro-rated on the basis of recorded flows at Lorne Falls) at the outlet to Spanish River.

2.2 Sources of Contamination2 The Vermilion River consists of a wide range of land use categories, which include mining, industrial, urban, suburban, rural, agricultural, and recreational. Currently there are eight municipal sewage treatment plants (Table 2.3), three sewage lagoons operated by the City of Greater Sudbury and two wastewater treatment plants operated by the mining companies distributed across the Vermilion River Watershed. These treatment plants eventually discharge their effluent into the Lower Vermilion River through different water courses, which has become a growing concern for the residents in the watershed. Some of the major subwatersheds of the Vermilion River, where only a relatively small number of residents are located, are not serviced with sewer hookups and as result rely on septic systems to meet their wastewater disposal needs. Contributions from a small agricultural community and various other non point sources located within the watershed cannot be ignored.

2 Exact locations of mining effluent treatment plants or treatment lagoons are not available at the time of writing this report

Table 2.3 List of Municipal Wastewater Treatment Plants and Lagoons Plant Location Easting Northing Treatment Type Capreol 505307 5171852 Lagoon Azilda 487400 5155100 WWTP Chelmsford 483700 5156800 WWTP Chelmsford 484306 5159927 Lagoon Dowling 474927 5160384 WWTP Garson 508341 5155858 Lagoon Levack 469807 5165175 WWTP Valley East 498425 5163250 WWTP Waldon 486379 5139004 WWTP Lively 488979 5142083 WWTP Sudbury 497336 5145746 WWTP

3.0 Material and Methods

A two-year water quality monitoring program began with a site reconnaissance which was conducted in early April 2013 to ensure the access to the sampling sites and other logistics (like boat access) were worked out. The sampling sites were finalized after consultation with the VRS Strategic Planning Committee. At the end of 2014, a considerable amount of money was still available and OTF granted permission to extend the monitoring program for another year. With an additional contribution of $15,000 from KGHM the 2015 monitoring program was modified to fit the funds available. This resulted in reduced sampling stations and changes in the water quality parameters analyzed. The details of the sampling stations and locations are available in Table 3.1.

The surface water quality data for this study has been collected through two different monitoring programs; the VRS program and the PWQMN program. Ontario’s PWQMN3 collects surface water quality information from rivers and streams across Ontario in partnership with Conservation Authorities of Ontario. The conservation authorities obtain water samples and readings of water quality at the monitoring locations using portable hand-held equipment. Selected sites are sampled from eight to twelve times a year for selected water quality parameters (Table 3.2), for which the MOECC lab in Toronto performs the laboratory analysis. CS monitors ten stations within its jurisdiction; seven of the ten PWQMN stations are located in the Vermilion River Watershed. All the VRS samples were analyzed by the Maxxam Lab located in Mississauga.

3 PWQMN sampling protocol provided in the appendix.

Vermilion River Watershed sampling began in May 2013 by amalgamating seven PWQMN stations to the VRS program in order to optimize the monitoring area. Monthly samples were taken from twenty eight stations during 2013-2014 season and 22 stations in 2015. All the twenty eight stations are shown in the map below (Figure 3.1 and 3.2). The sampling stations are spread across five different sub watersheds, and these stations are located on eight different lakes and sixteen different watercourses. The six stations eliminated for the 2015 sampling season include station # 2, 4, 5, 15, 17 and 22. The rationales behind eliminating those six stations were based on proximity to other sampling stations, duplication of a water course monitored and minimal impact from the loss of data.

The water quality indicators were selected based on various local land use impacts and other pressing water quality issues in the Vermilion River Watershed. Indicator parameters analyzed are listed in Table 3.2. All PWQMN water chemistry samples were analyzed by the OMOE&CC laboratories using standard analytical techniques (OMOE, 1983). The indicator parameters included in both the sampling programs mentioned above and the methods adopted to analyse them were consistent throughout the study period. For 2013 and 2014, lake sampling included phytoplankton, chlorophyll a (chl a), nutrients, metals (full suite), lake temperature profiles and Secchi depth measurements. The monthly samples in 2015 included all of the above excluding phytoplankton and chl a.

Table 3.2 List of water quality indicators analyzed

Category Quality Parameters

Routine Chemistry pH, alkalinity, conductivity, dissolved oxygen

Nutrients total nitrate, nitrite, phosphate, total phosphorous, total kjeldahl nitrogen

Metals all total metals (See Appendix) analyzed under ICPMS and mercury

Routine Physical temperature

Major Ions Sodium, chloride, Calcium

Microbial E- coli, Chlorophyll a

Nutrients, chl a and phytoplankton4 samples on lakes were collected as non-volume-weighted tube composite samples through the euphotic zone. The euphotic zone was defined as either twice the Secchi depth, or 1 m off the bottom, whichever was shallower. Phytoplankton samples were preserved using Lugol‘s iodine (5% w/v iodine) in the field.

4 Phytoplankton samples were only collected and preserved by the Conservation Sudbury staff. The samples were collected as a part of academic project and as a result the results are not discussed in this report.

The remaining water chemistry samples were taken as non-volume weighted tube composite samples from surface through to the bottom of the metalimnion (defined as either a change in temperature of less than 0.5 0C/m, or 1 m off bottom, whichever was shallower). In the event that anoxia (defined herein as <2mg/L of DO) occurred in the sampling zone, water was only taken until 1 m above where anoxia began. Temperature and dissolved oxygen profiles were taken using a YSI multi-probe every meter through the entire depth of the water column. The composite sampling technique used in the field was consistent with the MOECC guidelines and the grab samples adhered to the PWQMN sampling protocols5.

5 PWQMN sampling protocol provided in the Appendix B

Table 3.1 Sampling station locations and description Site No. Water Body Location Program UTM 1 Vermilion River North of Milnet, upstream of Roberts River VRS Stream 17N5028335186783 2 Vermilion River Downstream of Desmarais Rd Bridge VRS Stream 17N4992815170220 3 Onaping River Upstream of Bridge, Levack PWQMN 17N4693715165655 4 Onaping River Morgan Road Bridge VRS Stream 17N4763535161254 5 Vermilion Lake Near Vermilion River Intlet VRS Lake 17N4687595152260 6 Vermilion River Gordon Lake Road Bridge VRS Stream 17N4763095153836 7 Whitson River Main Street, Val Caron PWQMN 17N4974815161801 8 Whitson River Upstream of Vermilion Confluence PWQMN 17N4796145153856 9 Levy Creek Hwy 144 PWQMN 17N4849465152232 10 Vermilion River Vale Public Water Intake PWQMN 17N4783685142278 11 Lily Creek Downstream of Ramsey Lake PWQMN 17N5002635146582 12 Copper Cliff Creek Ceasar Road VRS Stream 17N4971585146056 13 Junction Creek Fielding Road PWQMN 17N4924465141518 14 Meatbird Creek Alexander St, Walden VRS Stream 17N4880225139383 15 Mud Lake Deepest spot VRS Lake 17N4879795138971 16 Simon Lake 2 Center/ deepest spot VRS Lake 17N4849805138048 17 Mc Charles Lake 1 East end VRS Lake 17N4830195137204 18 Mc Charles Lake 2 Centre VRS Lake 17N4811885136339 19 Mc Charles Lake 3 West end VRS Lake 17N4789375136941 20 Fairbank Creek Upstream of Confluence, MR 55 VRS Stream 17N4773815136735 21 Kusk Lake Deepest spot VRS Lake 17N4741555129791 22 Grassy Lake East end VRS Lake 17N4702225132584 23 Grassy Lake West end VRS Lake 17N4698885132275 24 Ella Lake East end VRS Lake 17N4617615128483 25 Ella Lake Upstream of rapids VRS Lake 17N4603745129152 26 Wabagishik Lake East end VRS Lake 17N4554835128164 27 Wabagishik Lake West end VRS Lake 17N4549405126651 28 Vermilion River Downstream of Wabagishik Lake VRS stream 17N4488765123771

VRS station locations with respect to population density population to respect with locations station VRS Figure 3.1 PWQMN and and PWQMN 3.1 Figure

Figure 3.2 Vermilion River Watershed and Sampling Stations

4.0 Results and Discussions

4.1 Exploratory Analysis The water quality data collected through the VRS and the PWQMN programs were found to be consistent in terms of intermittent missing values, unequal sampling intervals, etc. Initially, the raw water quality data were explored by plotting concentrations of each variable against the time period on the time series plots using Sigma Plot 11.2 (Systat Software Inc.) and MS Excel. On these plots the concentration of a particular water quality variable is shown on the y-axis while the x-axis represents time. In this report all the data are represented in bar charts of mean (three-year) or median values for better representations. Bar graphs and statistical summaries of the water quality parameters are used to describe the variability in water quality properties and constituents at each site.

4.2 Current Water Quality Conditions The primary focus of this study is to characterize the lower Vermilion River to better understand the source of negative inputs and outputs that are impacting on existing water quality conditions and to better understand predominant and emerging issues within the Vermilion River Watershed. In order to determine the health of the watershed, indicator parameters from 2013 to 2015 have been compared to the PWQO or ODWS. The drinking water standards were compared only when PWQO for a particular indicator parameter was not available. The following sections summarize the water quality data in the groups divided based on the relevance to the source of contamination. Finally, water quality parameters with significant health or environmental effects are discussed in the subsequent sections of this chapter as well. The percent of water quality samples complying with PWQO are tabulated for all the 28 stations in two different tables.

4.2.1 Field Observations Dissolved Oxygen (DO) in all watercourses within the Vermilion River Watershed never dipped below the 4 mg/L and 5mg/L criteria6 during the study period. The DO levels ranged from 7.3 mg/L to 11.6 mg/L at stations 16 (Simon Lake) and 4 (Onaping River) respectively. Median and maximum DO levels were much higher for the 2015 monitoring period, relative to the 2013-2014 data for the all the stations, this indication of increasing DO levels over the study period might be a sign of improving water quality. The highest dissolved oxygen concentrations observed in the field was 15.5 mg/L at station 19 (McCharles Lake) during the 2015 season, which when converted to percent saturation was found to be supersaturated (>190%). Super-saturation of gases within the water can lead to gas exchange problems in aquatic life such as blood gas trauma in fish (Fidler & Miller, 1994). However, there has yet to be a criteria set for the upper limit of DO for the protection of aquatic life. Also, sampling generally occurred

6 Dissolved oxygen limit for cold water biota at 25 0 C is 5 mg/L (e.g. salmonid fish communities) and 4 mg/L for warm water biota at 25 0C (e.g. centrarchid fish communities).

between 9a.m. and 5p.m. and as a result, the data presented here does not characterize the diurnal fluctuations in DO levels. Thus, determining if the range in dissolved oxygen concentration within the Vermilion River Watershed was limiting to aquatic organisms could not be accurately assessed with the 2013-2015 sampling regime.

Dissolved oxygen data for the PWQMN stations were not available at the time of data analysis for the comparison. The graph in the Appendix-A presents dissolved oxygen distribution throughout the watershed for the study period (VRS stations only).

4.2.2 Conventional Contaminants Conventional pollutants discussed in this section were grouped based on their relevance to the common land use concerns within the urban and suburban watersheds. Their effects and sources are summarized in Table 4.1. More detailed summary statistics and graphs for each contaminant are included in the Appendix.

Table 4.1 The environmental effects and sources for key water quality variables.

Variable Effect Source

Phosphorus Phosphorus is essential to the growth and survival of Sources include lawn organisms. However, oversupply of this nutrient and garden fertilizers, promotes eutrophication of surface waters by stimulating eroded soil particles, nuisance algal and aquatic plant growth, which deplete sanitary sewage, animal oxygen levels as they decompose resulting in adverse waste and decaying impacts to aquatic fauna and restrictions on recreational plant material. use of waterways. Chloride Chloride levels influence the aesthetic quality and The largest source of and taste of drinking water. Elevated levels may also chloride is from road salt harm aquatic life. Background concentrations in natural applications during the surface waters are typically below 10 mg/L. winter months. E. coli The presence of Escherichia coli in surface water is Bacterial sources include indicative of loadings of faecal matter of either animal or leaking septic systems, human origin. Elevated levels can result in restrictions on sewage disposals and inputs the recreational use of water bodies. from wildlife and domestic animals.

4.2.2.1 Road Salt The predominant chloride salt used as a de-icer in North America is sodium chloride, which is composed of about 40% sodium and 60% chloride by weight (MDOT, 1993). Road salts have come under increased scrutiny since they were deemed to be a toxic substance as defined in Section 64 of the Canadian Environmental Protection Act (CEPA, 1999). The five year risk assessment leading to the designation of

road salts as ‘toxic’ suggested a limit for chloride of approximately 250 mg/L7,8 for the protection of sensitive aquatic organisms (Health Canada, 2001). Chloride is highly soluble and does not readily absorb to mineral surfaces, as a result it is not effectively treated by stormwater technologies such as ponds that rely on settling for pollutant removal (SWAMP, 2005).

Chloride concentrations in the Vermilion River Watershed varied considerably among stations. All samples collected during the study period from various water bodies excluding Copper Cliff Creek were well within the prescribed guidelines. The highest median value was recorded at the Junction Creek station (116.5 mg/L), but Copper Cliff Creek had the highest number of samples (25%) above the 250 mg/L limit. Road salt discharging from the densely urbanized drainage area upstream of the Kelley Lake road and the community of Copper Cliff likely explains much of this result. However, understanding Vale’s salt application practices will help better understand the elevated sodium and chloride levels in Copper Cliff creek.

For sodium the only available guideline is the aesthetic objective i.e., 200 mg/L9, however if the water is used for drinking purposes, sodium levels above 20 mg/L should be reported to the local health unit. Elevated levels for sodium were found in all four stations on the Junction Creek system below Kelly Lake; however, results from all the samples were well within the aesthetic objective of 200 mg/L. Copper Cliff Creek is the only station which contains sodium concentrations higher than 200 mg/L with 24% of its samples exceeding the aesthetic objective.

The graphs indicating three-year moving average sodium and chloride concentrations for all 28 stations can be accessed from the appendix. The map below displays spatial distribution of sodium in different parts of the watershed.

7 Ontario Drinking Water Standards for Chloride is 250 mg/L and Guidelines for Canadian Drinking Water Quality for Chloride is ≤ 250 mg/L 8 Sodium and Chloride is not listed in the PWQO as a result ODWS are used for the comparisons 9 Ontario Drinking Water Standards and Guidelines for Canadian Drinking Water Quality for Sodium is 200 mg/L

Table 4.2: Percentage of samples that met guidelines for selected contaminants

Station ID Sodium Chloride Total Phosphorus10 E.Coli Guidelines 200 mg/L 250 mg/L 20 µg/L and 30 µg/L CFU/100 ml 1 100 100 100 100 2 100 100 100 100 3 100 100 100 87 4 100 100 92 100 5 100 100 100 100 6 100 100 100 100 7 100 100 94 67 8 100 100 93 87 9 100 100 100 100 10 100 100 100 100 11 100 100 75 80 12 76 75 100 71 13 100 100 13 100 14 100 100 79 33 15 100 100 19 100 16 100 100 13 88 17 100 100 19 100 18 100 100 32 100 19 100 100 85 100 20 100 100 100 81 21 100 100 82 100 22 100 100 100 100 23 100 100 68 100 24 100 100 100 90 25 100 100 95 0 26 100 100 95 83 27 100 100 90 50 28 100 100 100 100

10 PWQO for TP in Lakes is 20 µg/L and Streams is 30 µg/L 17

Figure: 4.1 Spatial distribution of Sodium in the Vermilion River Watershed

4.2.2.2 Total Phosphorous (TP) In most lakes and rivers, phosphorus is the primary nutrient that limits the growth of algae and plants. In some systems, the nutrient form of phosphorus is taken up very quickly and so is difficult to measure accurately. Because of this difficulty, it is best to measure the total of all forms of phosphorus. To avoid nuisance concentrations of algae in lakes, average total phosphorus concentrations for the ice-free period should not exceed 20µg/L and excessive plant growth in rivers and streams should be eliminated at a total phosphorus concentration below 30µg/L (Interim PWQO)11.

A high level of protection against aesthetic deterioration will be provided by a total phosphorus concentration for the ice-free period of 10µg/L or less. This should apply to all lakes naturally below this value.

11 Interim PWQO: Current scientific evidence is insufficient to develop a firm Objective at this time. Accordingly, the following phosphorus concentrations should be considered as general guidelines which should be supplemented by site-specific studies

atershed

patial distribution of total phosphorus in the Vermilion River River Vermilion the in phosphorus total of distribution patial Figure: 4.2 S 4.2 Figure:

Median concentrations of total phosphorus in samples collected from 2013 to 2015 were between 6.0 and 19.0 µg/L at all stations except stations on the Junction Creek system located downstream of Kelly Lake, for which the median concentrations ranged from 26 to 40.5 µg/L. At sixteen stations the provincial objective for total phosphorous were exceeded at least once12. TP concentrations in Junction Creek station are observed to have significantly higher values compared to other stations. Junction Creek station downstream of Kelly Lake reported the highest value (103µg/L) which is at least three times higher than the PWQO of 30µg/L. Considerably higher values were also found in Meatbird Creek, Mud Lake, Simon Lake, and Mc Charles Lake stations; more than 80% of the samples exceeded the provincial objective. Discharge from the Sudbury Wastewater Treatment Plant, a short distance upstream of Kelly Lake, is probably an important source of elevated phosphorus concentrations in Junction Creek stations. However, contributions directly from the Kelly Lake and Simon Lake sediments can also be a significant contributor. The watershed map, Figure 4.2 illustrates the spatial distribution of TP across the watershed.

4.2.2.3 Escherichia coli (E. coli) The Escherichia coli (E. coli) and fecal coliform groups of bacteria indicate the presence of fecal matter of human or animal origin, and can indicate the potential presence of other harmful pathogens or viruses that could infect humans, pets, and other warm blooded animals. Fecal matter can originate from human sewage, via cross contamination between storm and sanitary sewers, or wet weather overflows of combined sewers, as well as from pet, livestock, and wildlife feces washed off fields, lawns and paved surfaces during rain events. Levels of E. coli bacteria in excess of the provincial guideline of 100 colony forming units (CFU) per 100 mL can result in beach postings and create health risks associated with other forms of body contact recreation such as wading (PWQO, 1994). The indicator bacteria group selected for the provincial guideline changed from fecal coliforms to E. coli in 1994 because studies reported that, among the coliform group of bacteria, E. coli is the most suitable and specific indicator of fecal contamination (PWQO, 1994).

E. coli concentrations in monthly grab samples collected between 2013 and 2015 exceeded the provincial guideline13 of 100 CFU/100 mL 31 times, at water quality monitoring stations throughout the watershed. The Meatbird Creek station had the highest number of samples of E. coli concentrations

12 The Maxxam laboratory had set 20ug/L as detection limit for 2013 sampling year which is considerably higher than normal detection limit available for the TP analysis. All samples analyzed in 2014 and 2015 sampling year laboratory adopted 0.02ug/L as a standard detection limt for TP. Therefore values below the detection limit were assumed to meet the guideline (20ug/L), the actual number of samples that met the guideline may be significantly less than stated.

13 PWQO for E. coli is based upon a geometric mean of levels of E. coli determined from a minimum of 5 samples per site taken within a given swimming area and collected within a one month period. If the geometric mean E. coli level for the sample series at a given site exceeds 100 per 100 mL, the site should be considered unsuitable for swimming and bathing (Ontario Ministry of Health, 1992).

above the 100 CFU/100mL limit. Though thirty one samples from various watercourses reported higher than the guideline value, results from the preceding and subsequent monthly samples were below detection limits14, and any result below the detections limit is deemed to meet the water quality objectives. The geometric mean E. coli level for the sample series at any given station never exceeded the PWQO.

4.2.3 Metal Contaminants Metals are found naturally in the environment, but many are toxic to aquatic life at elevated levels. Sudbury is a city well known for its deposits of nickel and copper, but is arguably more famous for the severe environmental damage that resulted from metal smelting activities. Copper, lead and zinc can also originate from various urban land use activities, as a result these metals are commonly found metals in stormwater runoff.

The PWQO for Nickel in water is 25 µg/L. About 63 percent of the samples have reported in excess of 25 µg/L. Station 1 (baseline station) located on the northern reaches of the Vermilion River reported the lowest value (1.4 µg/L) and the highest nickel concentration being 440 µg/L was found in Mud Lake.

14 Detection limits for the E.coli was set at 10 CFU/100mL

Mean Nickel concentrations from stations along Junction Creek were very high compared to mean concentrations from the rest of the watershed. Three stations on the lower Vermilion just below the Junction Creek and Vermilion River confluence (West end of Mc Charles Lake) had zero compliance along with Junction Creek and Copper Cliff creek. A spatial distribution of Nickel throughout the watershed is illustrated in the map provided in the Appendix D.

Table 4.3 Percent of samples that met guidelines for selected metals Station ID Nickel Copper Lead Cadmium Cobalt Arsenic Aluminum Zinc PWQO 25 µg/L 5 µg/L 1 µg/L 0.2 µg/L 0.9 µg/L 5 µg/L 75 µg/L 20 µg/L 1 100 100 100 100 100 100 80 100 2 100 100 0 100 100 100 83 100 3 100 100 67 100 100 100 71 100 4 50 92 100 100 82 100 67 100 5 100 100 100 100 100 100 75 100 6 100 100 100 100 100 100 65 80 7 56 63 100 13 87 100 93 100 8 80 60 100 7 100 100 87 80 9 0 0 100 8 80 100 93 100 10 100 93 100 38 100 100 87 100 11 6 0 100 20 88 100 94 100 12 0 0 75 40 0 100 65 0 13 0 0 0 0 0 100 94 0 14 0 0 100 100 18 100 0 100 15 0 0 100 25 0 100 75 17 16 0 6 0 88 6 100 88 69 17 0 0 100 100 8 100 92 83 18 0 19 100 100 44 100 94 86 19 0 50 100 0 100 100 88 100 20 100 59 100 100 100 100 24 100 21 0 41 77 100 83 100 65 65 22 0 42 100 100 100 100 75 100 23 0 29 64 100 75 100 41 63 24 22 44 90 50 88 100 67 78 25 100 100 100 100 100 100 94 93 26 13 50 100 100 100 100 81 93 27 13 50 50 100 100 100 81 93 28 19 27 100 100 100 100 88 67

Copper occurs naturally in the environment but is rarely present in raw water. The PWQO for copper is 5 µg/L and it is tolerated up to 1000 µg/L15 in drinking water. At levels above 1000 µg/L, copper may impart an objectionable taste to the water. About 53 percent of the samples exceeded the PWQO. Copper is the only other metal after Nickel with more than 50 percent of its samples exceeding the provincial guidelines. All the samples tested positive for copper are well within the drinking water standard.

The interim objectivites for lead in water is 1 µg/L. Majority of the samples tested were well with in the deduction limit of 0.50 µg/L, which are deemed to meet the interim PWQO. Fifteen samples out of 468 collected reported above the 1 µg/L limit during the study period. The spatial distribution of lead does not give clear indications of a potential source from which lead could be entering the waterbody, however it is fair to assume the past practices of using Lead in gasoline products as additives might have contributed to the few elevated levels reported from the samples collected.

Cadmium is a relatively rare element that is extremely unlikely to be present as a significant natural contaminant in any given environment. However, Cadmium can make its way into water bodies through the application of chloride salts or as a by-product of metal ores (CCME, 2014). Cadmium compounds are widely used in electroplated materials and electroplating wastes may be a significant source of water contamination. Other than occupational exposure and inhalation from cigarette smoke, food is the main source of cadmium intake. The provincial objective for Cadmium is 0.2 µg/L and its interim objective ranges from 0.1 to 0.5 µg/L, however the interim objective depends on the level of hardness in water. For this analysis 0.2 µg/L limit is used to compare the results, as the hardness levels in the watershed ranged from 0 to 1000 mg/L of CaCo3. Junction Creek below Kelly Lake and Mc Charles Lake stations are the only stations with zero compliance. Whitson River and Levey Creek are the other two water courses with very low compliance which need further inviestigation to understand the likely source of contimination.

The Interim PWQO for Arsenic in water is set at 5 µg/L. 122 samples reported Arsenic values above the detection limit (1 µg/L). Only the results from Maxxam Lab are discussed here, as Arsenic levels for PWQMN stations were not available at the time of analysis. All 21 stations have 100 percent compliance.

Cobalt is a relatively rare element of the earth’s crust; its main sources include weathering of cobalt-rich ores and from anthropogenic sources such as emission from coal burning industries. The essentiality of cobalt has also been demonstrated in the environment as a micronutrient for some blue-green algae species, including diatoms, chrysophytes and dinoflagellates (BC-EMA, 1981). Some of these species are already known to be present in the Junction Creek watershed. The Provincial guideline limit for cobalt is 0.9 µg/L. Though 50 percent of the monitoring stations have reported cobalt levels in excess of the provincial limit at least once, all the water bodies outside the city limits were all well below the detection limits (0.5 µg/L).

15 ODWS: The aesthetic objective for copper in drinking water

Zinc is an abundant and essential element, constitutes approximately 0.004 percent of the Earth's substance, and is generally considered to be non-toxic (Health Canada, 1987). The most common zinc mineral is often associated with the sulphides of other metallic elements, e.g., lead, copper, cadmium, and iron. The median zinc concentration for all the stations, barring Copper Cliff Creek, Junction Creek (Downstream of Kelly Lake) and Mud Lake were below the PWQO which is 20 µg/L. The zinc levels in the entire watershed ranged from 1.3 to 100 µg/L for the study period. Both Copper Cliff Creek and Junction Creek (Downstream of Kelly Lake) had zero compliance against the PWQO.

There is no consistent, convincing evidence that aluminum in drinking water causes adverse health effects in humans. Aluminum is used in a variety of products and processes, so daily exposure of the general population to aluminum is inevitable. Aluminium is one of the few metals which has wider spatial distribution compared to the other metals analyzed during the study (see bar graph in Appendix A). The PWQO for Aluminum is 75 µg/L with median values ranging from 14 to 160 µg/L. The highest value for aluminum was reported in Grassy Lake (890 µg/L) in the fall of 2015.

5.0 Conclusion

Surface water quality in all the major sub watersheds of the Vermilion River clearly reflect a watershed that is heavily impacted by the archaic mining practices and the enduring effects of urban development. Water quality in many parts of the Vermilion River Watershed has improved significantly since the 1970s and early 1980s, and signs of recovery can be noticed at some of the long term monitoring stations (GSSPA Assessment Report, 2014).

Elevated levels of phosphorus at the Junction Creek station suggest that effluent discharges from the Sudbury Wastewater Treatment Plant, a short distance upstream of Kelly Lake may be the reason for elevated nutrients in the lower reaches of the watershed, however contributions from potential faulty septic systems cannot be ignored. Although progress has been made in the last few years on implementing better wastewater treatment facilities, they are not yet extensive enough to change pre- existing water quality conditions which can be attributed to archaic sewage disposal practices. In addition, untreated sewage is still occasionally bypassed into the Vermilion River through its tributaries during heavy rainfall events. The provincial objective for total phosphorus in these receiving waters downstream of Kelly Lake was exceeded more than 60% of the time in the Junction Creek system. While the lower Junction Creek watershed exhibits the poorest overall water quality, areas north and west of old Sudbury fared significantly better. When there are several sewage treatment plants and wastewater lagoons discharging to the river, large spikes in phosphorus can be expected, however contributions from the lake sediments such as Kelly Lake and Simon Lake, cannot be overlooked. Detailed sediment analysis will give better understanding of the nutrient loading.

While mean E.coli concentrations on Whitson River were lower than the guideline, they were significantly higher than on the Junction Creek stations. Even during dry weather flows, E. coli concentrations at both stations on Whitson River never met the provincial guideline for body contact recreation. Though this was an unexpected finding as the Whiston River receives significant clean water discharges from the tributaries, stormwater in the drainage area upstream of the monitoring station with significant agricultural land use might be the source. The cause of this potential problem requires further investigation. Generally, E.coli has been reported sparsely for the entire watershed during the study period.

Elevated sodium and chloride levels in the urban streams are attributed to intense road salt applications. Chloride and sodium concentrations are generally expected to increase in proportion to the rising number and density of roads to which road de-icing salts are applied. This is apparent to a smaller extent in the Junction Creek compared to other watersheds because much of the upstream watershed has been completely developed. Nevertheless, there is an apparent increase in chloride and sodium levels at the Copper Cliff station which needs further investigation. On the other hand, the stations 1, 2 and 3 on Upper Vermilion and Onaping Rivers, had the lowest median concentrations of sodium, chloride, and metals. Alternatives to road salts will need to be considered on local roads and drive-ways if significant reductions in chloride levels are to occur.

Nickel, copper, zinc and cobalt were identified earlier as some of the most important metals of concern in the watershed. All are common contaminants contributing primarily from the mining activities; for known reasons it is evident that all higher concentrations of metals recorded are mostly located downstream of the Copper Cliff smelter complex. Median concentrations of nickel declined at all stations as you move downstream from Kelly Lake to McCharles Lake. The majority of lead levels have been reported below the detection limit and these lower levels in lead might reflect the phase out of lead in fuels initiated in the 1970s.

6.0 References

Fidler, L.E., and S.B. Miller. 1997. British Columbia water qualitycriteria for dissolved gas supersaturation. Contract report to the B.C. Ministry of Environment, Canada Department of Fisheries and Oceans, and Environment Canada. Aspen Applied Sciences Ltd., Cranbrook, BC.

Great Lakes Science Advisory Board (GLSAB), 1998. Non-point Sources of Pollution to the Great Lakes Basin, Toledo, Ohio.

Environment Canada and Health Canada, 2001. Road Salts: Priority Substances List Assessment Report. Prepared for the Canadian Environmental Protection Act, 1999 Priority Substances List. Internet Publication.

Schindler, D. W., P. J. Dillon, and H. Schreier, 2006. A review of anthropogenic sources of nitrogen and their effects on Canadian aquatic ecosystems. Biogeochemistry, Vol. 79: 25-44

Greater Sudbury. (2015). 2014 Annual Wastewater Report.

Stormwater Assessment Monitoring and Performance (SWAMP) Program, 2005. Synthesis of Monitoring Studies conducted under the SWAMP Program. Toronto, Ontario. TRCA.

Ontario Ministry of the Environment (OMOE), 1999b. Water Management, Policies, Guidelines: Provincial Water Quality Objectives, Ontario. Queen’s Printer, Toronto. https://www.ontario.ca/document/water-management-policies-guidelines-provincial-water-quality- objectives

Ontario Ministry of the Environment (OMOE), 1999a. Surface Water Monitoring and Assessment: 1997 Lake Ontario Report, Queen’s Printer for Ontario, Toronto.

Ontario Ministry of the Environment (OMOE), 1991. Waste Disposal Site Inventory. Queen’s Printer for Ontario

Ontario Ministry of the Environment (OMOE), 2006. Technical Support Document for Ontario Drinking Water Standards, Objectives and Guidelines: Queen’s Printer, Toronto. https://www.ontario.ca/document/technical-support-document-ontario-drinking-water-standards- objectives-and-guidelines

Greater Sudbury Source Protection Area: “The Assessment Report” http://sourcewatersudbury.ca/en/assessment-report.html

Scientific Criteria Document for the Development of the Canadian Water Quality Guidelines for the Protection of Human Health – (2015)

7.0 Appendix A

8.0 Appendix B

PWQMN Protocol for Stream Water Quality Monitoring (OMOE, 2006) Sample collection by wading

If conditions permit sampling within the stream, enter the stream downstream of the sampling location. Carefully wade upstream taking care to disturb as little sediment as possible. Allow sufficient time for disturbed sediments to be carried downstream by the current. Sample away from the stream bank in the main current. Do not sample stagnant water. Face upstream into the current and collect the samples by reaching into the flow in an upstream direction.

Remove the lid of the sample bottle just before collecting the sample. Touch only the outer surface of the sample bottle when removing the lid. Invert and submerse the sample bottle under the surface of the water to a depth of approximately 0.3 m. If the stream is less than 0.3 m deep, the sample should be collected halfway between the surface and the bottom of the stream. Do not collect samples if the bottle cannot be submerged. Take care to avoid collecting debris that may be floating on the surface of the water when submerging the bottle. While under the surface, turn the bottle upright by rotating the mouth of the bottle to face upstream into the current. Rinse twice the inside of the bottle and the underside of the lid. Dispose of the rinse water downstream and refill the bottle in the same manner for the actual sample. Secure the lid on the bottle without touching the inside of the bottle or the underside of the lid. Sample collection using a reaching pole

If conditions (e.g. high flows, steep bank) inhibit sampling within the stream, collect the samples by attaching the sample bottle to the end of a reaching pole using an adjustable clamp. Extendable poles, such as those used for window washing, can be modified to serve this purpose or a specially designed sampling pole can be purchased. Similar to the in-stream (wading) sampling procedures, try to sample away from the bank and into the main current. Invert the sample bottle and submerge it to a depth of approximately 0.3 m by reaching into the stream with the pole. Turn the bottle upright into the current by twisting the pole. Ensure that the bottles (including lids) are rinsed twice with sample water before collecting the samples that are submitted to the laboratory. Sampling from a bridge or culvert

Where wading or sampling with a reaching pole is not possible, sampling can be conducted from a bridge or culvert that crosses over the stream. Samples are collected by lowering a sampling container to the stream using a rope. Try to eliminate all of the potential sources of contamination. Do not disturb the sediment at the stream bottom with the sampling container. The most effective method of sampling from bridge or culvert uses a weighted container that securely holds one or more sampling bottles. The container is lowered into the stream and water is collected directly in the sample bottles. A second, less- preferred method uses a stainless steel sampling bucket to collect water that is subsequently transferred to the sample bottles. Thoroughly rinse the sampling container and the sample bottles, disposing of the rinse water downstream, before collecting the samples that are submitted to the laboratory.

9.0 Appendix C Total Metals analysis by ICPMS Parameters Symbol RDL Units Aluminum (Al) 5 µg/L Antimony (Sb) 54 µg/L Arsenic (As) 1 µg/L Barium (Ba) 2 µg/L Beryllium (Be) 0.5 µg/L Bismuth (Bi) 1 µg/L Boron (B) 1 µg/L Cadmium (Cd) 0.1 µg/L Calcium (Ca) 200 µg/L Chromium (Cr) 5 µg/L Cobalt (Co) 0.5 µg/L Copper (Cu) 1 µg/L Iron (Fe) 100 µg/L Lead (Pb) 0.5 µg/L Lithium (Li) 5 µg/L Magnesium (Mg) 50 µg/L Manganese (Mn) 2 µg/L Molybdenum (Mo) 0.5 µg/L Nickel (Ni) 1 µg/L Potassium (K) 200 µg/L Silicon (Si) 50 µg/L Selenium (Se) 2 µg/L Silver (Ag) 0.1 µg/L Sodium (Na) 100 µg/L Strontium (Sr) 1 µg/L Tellurium (Te) 1 µg/L Thallium (Tl) 0.05 µg/L Thorium (Th) 2 µg/L Tin (Sn) 1 µg/L Titanium (Ti) 5 µg/L Tungsten (W) 1 µg/L Uranium (U) 0.1 µg/L Vanadium (V) 0.5 µg/L Zinc (Zn) 5 µg/L Zirconium (Zr) 1 µg/L

10.0 Appendix D Figure: AD1 Spatial distribution of Nickel in the Vermilion River Watershed

Figure: AD2 Spatial distribution of E.coli in the Vermilion River Watershed