1. Christie Lake and Watershed Description
1.1. How Christie Lake Got Its Name
Prior to 1816, Christie Lake was called Myers Lake, and the Tay River was known as Pike River (Perth Municipal
Museum Notes, 1857). The two prominent families living on the lake around that time were the Allan‟s and the
Christy‟s. Word has it, they drew straws to decide which family name would be used to identify the lake, and in
1816, the lake was so named after John Christy. The original spelling of the lake was “Christy‟s Lake”, which was
th
changed by the Geographic Board of Canada to “Christie” on April 10 , 1908.
rd
John Christy, his wife Isabella (nee Wright), and daughter sailed on the ship Eliza from Scotland on the 3 of
nd
August, 1815 and arrived in Quebec City on September 22 , that same year. It has been assumed they wintered
somewhere between Quebec City and Kingston, which was the norm in those days due to distances and harsh
winters. In 1816, the Christy‟s occupied Concession 2, Lot 2 in Bathurst District. Little else is known about the
Christy family except that they had ten children.
1.2. Location and General Description
Christie Lake is located in Lanark County, Tay Valley Township (formerly Township of Bathurst Burgess
Sherbrooke). The lake is approximately 15 km (9 mi) southwest of Perth refer to Map 1. The physical
characteristics of the lake and its immediate watershed are outlined in Table 1 below.
Table 1: Physical Characteristics of Christie Lake and its Watershed
Latitude 44o 48‟ north
Longitude 76o 26‟ east
Immediate Drainage Area 67 km2 (26 mi2)
Lake Surface Area 646.4 ha (1597 ac)
Lake Elevation Above Sea Level 155 m (509 ft)
Height of Land in the Watershed (north end of lake) 206 m (676 ft)
Shoreline Perimeter 27.4 km (17 mi)
Length 6.2 km (3.9 mi)
Maximum Width 2.2 km (1.4 mi)
Average Depth 8.5 m (28 ft)
Maximum Depth 18.3 m (60 ft)
18 Crown Land
Number of Islands
10 Privately Owned
Flushing Rate of Lake (times per year) 2.7
The Christie Lake watershed is the area of land that drains into the lake and includes part of the Tay River, eight
intermittent streams, and several small wetlands (Esseltine, 2003) (refer to Map 1). It is one of 14 smaller
subwatersheds, which together form the larger Tay River watershed. Water from Bobs Lake, and the smaller Long
and Eagle Lakes, flows into the Tay River and enters the southwest end of the Christie Lake. From the lake‟s
outflow at the northeast end of the lake, water flows downstream through the Tay River, where it eventually enters
into Lower Rideau Lake, east of Perth (Kerr, 1998, MNR, 1983).
Typical of the Canadian Shield, the watershed is characterized by thin soils and areas of exposed bedrock. The
topography of the backshore area (200 m back from the high water mark) ranges from flat to gentle slopes in the
eastern end of the lake, to very steep hills and cliffs in the southwestern end of the lake, with a range of 38 m in
relief. Elevations within the watershed range from 190 m above sea level, to the height of land at 206 m above sea
level. This varied topography results in the drainage of precipitation into small, localized wetlands found in areas of
low-lying bedrock (MNR, 1983) (refer to Map 1).
The lake has a long, irregular shoreline, with rocky outcrops and steep cliffs dominating most of the northern and
southern shoreline. The lake has 28 islands, ranging in size from a very small outcrop of 0.04 ha (0.1 ac) to 6 ha
(15 ac) in size (refer to Map 1 for island names). For listed information about the islands on the lake, refer to
Appendix 1.
The lake basin (the shape of the lake bottom) is non-uniform and trough-like, showing evidence of repeated glacial
advances and retreats. Basin slope is a determining factor on how sediments and organic material will settle in a
lake. Sediments tend not to settle on steep slopes along lake bottoms. For example, in the deep areas of the lake,
along the north and southwest shore along McManus Bay, there is little decomposition of organic material.
Shallower areas, such as the area found at the lake‟s inlet and outlet, and along the southeast shore, have more
settling of organic materials, resulting in a greater variety in lake bottom cover, higher nutrient availability, and
higher light levels. These areas are more biologically productive, and provide good habitat for aquatic vegetation
and fish.
The littoral zone or the area along the shoreline makes up about 35% of the lake area (MOE 1975). This zone is
an area of high biological activity and provides critical habitat that many species depend upon for feeding, breeding,
and the rearing of young including warm water fish, amphibians, waterfowl, and mammals such as muskrat.
The flushing rate of a lake is the time it takes the lake to undergo an exchange in volume of its water and is an
important parameter of water quality. Flushing rates vary from lake to lake. The flushing rate of Christie Lake is 2.7
times/year. This high turnover of water volume means that sediments, nutrients, and pollutants may not
accumulate as quickly in the lake. This may enable the lake to withstand a higher density of shoreline
development, as the water exchange helps to provide a buffer against the negative water quality impacts that can
be experienced from increased shoreline development (MNR 1984).
Water levels and flow rates on the lake are influenced by the uncontrolled outlet of the lake and the water control
operation at the Bolingbroke Dam (at the Bobs Lake outlet) by Parks Canada – Rideau Canal. For more
information about water levels, refer to the Water Levels Section.
The term floodplain is given to lands adjacent to a waterway that are susceptible to flooding. If these areas are
developed, it may result in significant property damage during flooding events . The Tay River floodplain begins at
the inlet to Bobs Lake and continues from the outlet of lake, past the Town of Perth. For more information about
floodplains, refer to the Development Pressures Section.
1.3. Bedrock Geology
The bedrock underlying the majority of the watershed is made up of igneous and metamorphic Precambrian rocks.
These rocks underwent extreme metamorphism 1.5 billion years ago. Much of the lake is surrounded by gneiss
(primarily igneous in origin) and syenite rock types, with the exception of a large area of diorite adjacent to the
northwest shore. Exposed bedrock outcrops are visible throughout the lake‟s watershed (MNR 1984).
Paleozoic rocks, sedimentary in origin, are found along the northeast portion of the watershed, north of the Tay
River outflow. Originating 500 million years ago, these rocks, such as limestone and sandstone, were formed when
sand, clay, and calcium carbonate were deposited by seas during the Cambrian and Ordovician eras, and overlay
the igneous and metamorphic rocks of the Precambrian Shield.
Faulting is common in the Canadian Shield. A fault-line extends northwest to southeast across the midpoint of the
lake. The alignment of the lake‟s two inflow streams outlines this fault. The Frontenac Axis (the contact zone
between the Precambrian and Paleozoic rock types), extends past the eastern end of the lake‟s watershed (MNR
1984).
1.4. Soils
The makeup and distribution of soil types found around the lake are the result of glacial activity, topography and
drainage. The predominant soil type in the lake area is made up of Monteagle sandy loam. Since the parent rock
for this soil is granite, the soil is acidic. This sandy loam is shallow, well drained, and extensively stony soil. As a
result, it holds little agricultural potential. Trees such as white pine, sugar maple, red oak, and basswood can be
productive on this soil (MNR 1984). Soil cover to the west, in the watershed‟s Precambrian Shield area, is
characterized by thin, erosion prone and drought-prone soils. The limestone plain area in the eastern portion of the
lake‟s watershed is characterized by clay and thin drought-prone soils, which offers marginal agricultural potential.
In the north portion of the lake (Station Bay area), soils called White Lake and Tweed sandy loams are dominant.
Tweed sandy loams are associated with Precambrian limestone and are stony. Both soils are of little agricultural
value because they have low soil fertility and are drought-prone. Bedrock outcrops make up 40-50% of this area.
At the east end of the lake, soils in the low lying area around the Tay River are made up of sandy and clay loams
as well as poorly drained organic soils (muck) found in the area‟s wetlands. The sandy loam (Tennyson and
Wemyss series) found in this area is deeper and well drained, offering better agricultural potential compared to the
rest of the lake.
The area around the lake may be susceptible to the effects of acid rain. Acid rain is the wet deposition of rain,
snow, sleet, or hail, mixed with particulate by-products found in industrial emissions such as sulphur dioxide and
nitrogen oxides. When mixed with precipitation, they become moist secondary pollutants of sulphuric acid (H 2SO4),
ammonium nitrate (NH4NO3) and nitric acid (HNO3). When acid rain falls, terrestrial and aquatic systems such as
lakes can become acidified over time, affecting the health of plants, animals and microorganisms within these
systems.
As mentioned earlier, the parent bedrock for soils around the lake is Precambrian rock, which can contribute to the
soil acidity level (lower calcium content and lower pH). The sandy soils around the lake that are acidic naturally
have a lower ability to neutralize or buffer the acid in precipitation, which can result in higher levels of acidity in
soils. The bedrock north and west of the lake includes crystalline limestone (marble), which offers a buffering
capacity to the soils around the lake. More research is needed to better identify the buffering capacity of the soils
around the lake and the effects acid rain may have on the lake‟s ecosystem. For more information about the lake‟s
pH and water quality, refer to the Surface Water Quality Section.
In 1976, the Ministry of the Environment (MOE) tested the soils around the lake to analyze its capacity to take up
phosphorus, a nutrient found in septic system effluent. The tests found the soil had a good phosphate retention
capability, but because of the thin soils found around the watershed, additional aggregates were required during
septic system construction and installation, to assist in the take-up of nutrients in septic effluent (MNR 1984).
Retention of phosphorus is an important factor in the maintenance of the lake‟s water quality. Soil limitations
should be considered for current and future septic system installation around the lake.
1.5. Land Cover
1.5.1. Forest
Forested areas around the lake provide critical habitat for wildlife and are part of the overall balance of the
lake‟s ecology. Forests play an important role in our water cycle by pumping water from the soil back into
the atmosphere through transpiration. Forested areas also stabilize soils, reducing the potential for erosion
and sedimentation into the lake. Protection and enhancement of the watershed‟s forested areas will help to
maintain the important ecological values they provide to the lake ecosystem.
The 1984 MNR Christie Lake Management Plan reported a forest cover of 85% at that time around the
lake. Currently, wooded areas make up approximately 71% (66.9% Shield forest, 4.5% mixed hardwood
forest) of the watershed (Esseltine, 2003). Forested areas are comprised of a mixture of coniferous and
deciduous trees including white pine, cedar, birch, aspen and hard maple. Smaller stands of white elm,
white spruce, red oak, red pine, willow and hemlock, also occur. In general, the shallow, stony soils and
steep slopes found around the lake limit its potential for valuable forestry efforts. Currently, much of the
treed areas along the shoreline are being altered as cottages and permanent homes are built. For more
information about the trees found in the area, refer to the „Tree World‟ website
http://www.domtar.com/arbre/english/album_photo.asp#.
Refer to Map 2 for an outline of forest landcover in the lake watershed. Please note the data presented in
Map 2 shows provincial landcover data from 2000. Updated landcover data for the lake‟s watershed is
expected to be available in 2009/2010. Please also note, the landcover data is given in „patches‟ or
polygons that are a certain size, scale, and cover a certain area of land. Therefore, at the scale the data is
available, some low lying areas, or small islands may not appear due to the data‟s polygon size.
1.5.2. Agriculture
The watershed has limited areas that provide viable agriculture land due to poor soil depth and fertility.
Land suitable for pasture or cropland, found primarily in the eastern part of the watershed, makes up only
3% of the land cover around the lake (refer to Map 2 for agricultural land cover).
1.5.3. Wetlands and Other Natural Areas
Two significant natural areas in our watershed include the locally significant Christie Lake Wetland and the
Christie Lake Area of Natural and Scientific Interest (A.N.S.I.). Refer to Map 3 for locations of these
ecologically significant areas. For a detailed description of both of these natural areas, see Appendices 2
and 3 for the Natural Heritage Information Centre‟s Natural Areas Reports.
The Christie Lake Wetland is 80% privately owned and provides valuable nesting and feeding habitat for
water birds and other wildlife. More information about the significance of this wetland is found in the
Surface Water Quality Section. Wetlands are natural filters that improve water quality. They help
neutralize a number of different contaminants that can be carried into water bodies from overland runoff.
Wetlands help remove nutrients like phosphorus and nitrogen from water that flows into lakes, streams,
rivers and groundwater. Wetlands also recharge our groundwater and help attenuate water levels during
flooding events by storing large amounts of water. When wetlands are destroyed, groundwater recharge
capability is reduced, and the probability of a rainfall event causing flooding can increase significantly
(Ducks Unlimited, 2006).
The regionally significant Christie Lake A.N.S.I. occupies an area of 600 ha (1483 ac). The area is
characterized by escarpment and rock barrens, riverine swamp, and marsh wetlands, and contains
significant plant and species. The rock barren meadows support the regionally significant Northern Downy
Violet. The provincially rare Stiff Gentian has been recorded from a swamp edge of Christie Lake,
however, it is not known whether the location is from the present candidate (NHIC, 2009). The wetland
portion of the A.N.S.I. is primarily an organic landform. Dr. Paul Keddy in his book Earth, Water, Fire: An
Ecological Profile of Lanark County, describes the area as the „Christie Lake Fire Barrens‟ containing the
few trees that are resistant to fire such as red oak, bur oak, and large-toothed poplar. There are open
grassy areas with shrubs such as blueberry, juniper and sumac. The explanation for this prairie-like habitat
is open to speculation, but the area‟s characteristics may have been formed as a result of wild fire after
settlement and logging. Dr. Keddy also reports „unusual reptiles, including rare species such as the Five-
Lined Skink (Ontario‟s only lizard) and the Spotted Turtle‟.
1.6. Land Use
Prior to settlement in the early 1800‟s, First Nations people likely used the area‟s lakes and rivers for seasonal
places to fish and hunt, but their impact on the area was minimal. There are no known archaeological sites in the
lake‟s watershed.
In 1805, to encourage settlers to the area, the Crown offered land grants of 100-200 acre lots. The list of original
property owners, mainly Scottish and Irish settlers and soldiers, is available through the Ontario Land Association
(OLA). Land settlement around the lake would have involved small mixed farming operations due to the poor
farming lands and low soil fertility. Land in the eastern area of the lake, in Bathurst Township, was settled early on
because of the availability of better agricultural land and easy access to Perth via the Tay River (Kerr, 1998, MNR
1984).
Following the pioneering period, the next period of settlement came early in the 1950‟s, much of it in the form of
recreational use. Many properties on the south shore were owned by descendants of families who farmed land
between the lake and Perth (P. Higgins 2008). Cottage development also came from American citizens. Rapid
shoreline development occurred between 1970 and 1985. Between 1970 and 1978, the number of total cottages
increased by 78%, with much of the increase (51%) occurring in the early 1970s (MNR 1984). For more
information about development trends on the lake, refer to the Development Pressures Section.
Currently, the majority of land around Christie Lake is privately owned. Public lands within the lake watershed
include the Christie Lake Camp for Boys and Girls, and Scouts Canada‟s Camp Opemikon. Visitor accommodation
is available at Christie Lake Cottages and Marina, Jordan‟s Cottages, as well as the Tay River Tent and Trailer
Park.
1.6.1. Forestry
In the early 1900‟s forestry was an important part of the area‟s economy. Lumber shanties on the lake
were commonplace around 1915, with logging activity taking place until 1938. Logging reports show 8000
logs were harvested off the lake, using the Tay River to move them to markets in Quebec.
On the north shore of the lake, a 7 ha (17 ac) parcel of land was sold in 1868 to construct the Canadian
Bark Works. The factory was involved in the extraction of tannin from the bark of hemlock (MNR, 1983).
The tannin extract from the factory was shipped to tanners as far away as Boston and the United Kingdom.
The factory closed operations in 1874, owing to the low supply of hemlock bark in the area.
In 1983, there were ten forestry agreements administered under the Woodland Improvement Act between
property owners and the Ministry of Natural Resources (MNR) in areas of poor agricultural land. There are
currently no commercial forestry operations in the watershed.
1.6.2. Mining and Aggregates
Minor occurrences of iron, feldspar, mica and gold are sporadically located around the lake (refer to
Appendix 4 for location of these minerals). Four different mining operations (feldspar, mica, iron and gold)
occurred in the area. Feldspar mines were active in Bathurst and South Sherbrooke townships from 1916
to 1923. The mica mine in Bathurst Township was active in 1907.
In 1956, uranium prospecting started on lots 15-20, Concession 3 of South Sherbrooke. Extensive staking
by the Christie Lakes Mines Ltd. took place ¾ of a mile west of the Canadian Pacific Railway (CPR)
Christie Lake Station. The last report accessed on this mine indicated that drilling had started in 1958, but
has not been continued. Map 5 shows the location of some abandoned mines sites around the lake.
Currently, there is a small licensed sand and gravel pit operation south of the lake, off Althorpe Road.
There are several small sand and gravel deposits within the lake‟s watershed. Three identifiable sand and
gravel reserves could have potential impacts (such as sediment loading) on adjacent tributaries and
wetlands, if put into operation. One reserve is found in the western portion of the lake (McManus Bay
backshore), a second pit is found close to the CPR line and the Christie Lake wetland, and the third is
found on the east bay backshore of the lake (Ottawa point) (Tay Valley Township, 2008 Schedule A3
Sherbrooke Ward). The MNR is responsible for the sustainable extraction of sand, gravel and crushed
stone resources in Ontario. If these reserves were licensed to operate, sediment and erosion control
measures will be required throughout their operation to protect against any potential erosion and
sedimentation into nearby tributaries and wetlands that could potentially harm water quality and fish habitat.
For more information about how aggregates mining operations are managed in Ontario, refer to
http://www.mnr.gov.on.ca/en/Business/Aggregates/index.html.
1.6.3. Current Mining Issues
The Mining Act R.S.O. 1990, originating in the 1860‟s, is little known in eastern and southern Ontario, yet
has significant impacts on private properties, municipalities and the environment. If you own the mineral
rights to your property, you own everything in, on or under your land, including the minerals. If you hold
only the surface rights to your property, the minerals in, on or under the land you own belong to the
province of Ontario.
Exploration and mining activity around the lake could have a significant impact on noise levels, ground and
surface water quality, wetland health, and property values. The lack of regulations in the current Mining Act
to govern the restoration of property following both exploration and mineral extraction is a large concern for
the communities in eastern Ontario. The Mining Act clauses of specific concern to clean water, source
protection and lake health are as follows:
Section 78(1) provides the holder of a mining claim permission to enter a property for the purpose of
carrying out assessment work of their claim, after providing 24 hours notice to the surface rights
landowner of the property. The following assessment activity can be carried out on the property, and is
not subject to the regulations listed under Part VII Advanced Exploration of the Act, or to an
Environmental Bill of Rights posting:
Excavation of up to 1,000 tonnes of material;
2 2
Surface stripping of overburden over an area up to 10,000 m (11,960 yd ) or a volume up to
3 3
10,000 m (13,080 yd )
2 2
Surface stripping of overburden over an area up to 2,500 m (2990 yd ) or a volume up to
3 3
2,500 m (3270 yd ) within 100 m (328 ft) of a body of water
Section 175(1) provides rights to the holder of a mining claim over other lands. These include the right to:
Discharge water;
Drain, divert or lower the water of any lake, pond, river stream or watercourse;
Collect or dam back water although it may overflow other land;
Deposit tailings, slimes, or other waste products, etc.
Much attention has been brought to the provincial government by several concerned groups and individuals
to modernize the Act. In August 2008, MNDM launched a review of the Mining Act. The discussion paper
Modernizing Ontario's Mining Act: Finding a Balance notes that the Mining Act, originally passed in 1868
and revised in 1906, had few amendments until the early 1990's when requirements for mine closure and
reclamation were introduced.
Public consultations held between August 11 and September 8, 2008 in Timmins, Sudbury, Thunder Bay,
Kingston, and Toronto discussed the modernization of the Act. Additional consultations were held with
First Nations and Métis leaders and organizations. Focused meetings for mineral sector and other
stakeholders were also held.
The Citizens' Mining Advisory Group (CMAG) joined with a number of like-minded organizations under the
umbrella name of the Coalition for Balanced Mining Act Reform. The Coalition called for adoption of the
following Three Modest Proposals:
1. Single ownership/ Re-unification of Minerals with the land;
2. Strengthen Municipal Planning power regarding mining activity; and
3. Require a review and impact assessment/analysis for mining activity.
The Mining Amendment Act
The Minister of Northern Development and Mines (MNDM) introduced the Mining Amendment Act, Bill 173,
on April 30, 2009. The Minister expects that the Bill, which has passed first and second reading, will
receive royal assent by the end of the year. Under the new legislation, and effective April 30, 2009, all
surface rights only land that is not presently staked is withdrawn from mining in southern Ontario (south of
Lake Nipissing and the French and Mattawa Rivers). Further, when claims lapse on surface rights only
land in southern Ontario, the mineral rights will be withdrawn. The new legislation does not address the
role of municipalities in land use planning, including mineral land use designation. The section on the
purpose of the Mining Act references minimal environmental impact; however, it is silent on how this
purpose would be achieved. For more information on Bill 173 go to www.ontario.ca/mines-news.
The following Tay Valley Township document explains the numerous initiatives undertaken by the
municipality from 2001 to 2008 (posted on their website):
www.tayvalleytwp.ca/INDEX/Mining%20Concerns%20Committee/mining_act_of_ontario.htm. Additionally,
a detailed review of mining history in the Tay Watershed has been compiled by Donald F. Sherwin,
Geologist, and Orion Clark in the “Geology, Mineral Deposits and History of Mining in the Tay River
Watershed” and may be found on the Friends of the Tay Valley Watershed Association website:
http://www.tayriver.org/documents/geology_report/geology_report.htm. The Christie Lake Association
(CLA) will maintain support for the efforts being carried out by the Tay Valley Township, the CMAG and
other groups working towards updating the Mining Act.
1.6.4. Elliot Road Drain
A farmer‟s ability to produce good quality foods depends on the natural environment, good weather, and
workable soil. However, farmers sometimes need to modify the environment in order to grow crops. One
of these changes may require the drainage of surface and subsurface water from their land. This is usually
done by constructing open ditches, also known as open drains. Drains effectively remove excess water
from the surrounding land, improving drainage, and keeping crops dry throughout the growing season.
There are different types of drains – municipal, private, and mutual agreement drains (Ontario Federation
of Agriculture, 2006).
Within the Christie Lake watershed, there is a mutual agreement drain. These are private drains that have
been constructed through an agreement between two or more property owners. In this case, the Elliot
Road Drain agreement is between Tay Valley Township and nine landowners. The drain is registered on
the property titles through the Land Registry Office to ensure it continues to serve its original purpose,
regardless of who owns the land. The 2.8 km (1.7 mile) ditch drains parts of Lots 4 - 7, Concession 3,
Bathurst, and eventually empties into the lake at the north shore (See Map 5). Refer to the Surface Water
Quality Section for more information about this drain.
1.7. Climate
Our lake area experiences a temperate climate with warm summers and cold winters. Over 11 years, average
monthly temperatures have remained relatively constant with a minimum mean temperature during
January/February of -1.2°C (29.8°F) and a maximum mean temperature in July/August of 13.8°C (56.4°F). The
most extreme temperatures recorded over the 11 year time frame occurred in January 1994 at -36°C (-32.8°F) and
in July 2001 at 37°C (98.6°F). Average temperature data from the nearest weather station (Drummond Centre, 45
01‟N, 76 15‟W) between 1997 and 2007 is outlined in Appendix 5.
The average annual precipitation that fell over this same period was 705 mm (27.8 in), with 237.6 mm (9.4 in) or
33.7% falling during the summer months of June, July and August. The average snowfall for the area was
approximately 178.9 cm (7.0 in). The wettest year (rain) was 2006, with 991 mm (39.0 in). The driest year was
2001, with only 527.1 mm (20.8 in). Refer to Appendix 6 for the average monthly precipitation (rain and snow) for
the lake area from 1997 to 2007.
Dates when the lake was ice-free and when the ice returned, has been recorded since 1981 (see Appendix 7). Ice-
th th
out time on the lake has been as early as March 27 in 2000, and as late as April 28 in 1992. Ice-in dates have
th th
been as early as December 4 in 1997 and as late as January 14 in 2002.
Twenty-seven years of ice-on and off data offers a good range of information, but it is still too short of a time span
to observe if there are trends or effects of climate change on our watershed. Temperature measurements taken at
various points on the same day, each year, may yield more interesting data regarding climate change in our lake
environment. Temperature data is currently being collected by the MNR during times of walleye spawning.
We continue to learn about how our changing climate poses risks to the health and safety of people, wildlife,
forests, farms and water quality and quantity. Continued monitoring will help us track temperature changes, rainfall
patterns, as well as how extreme hazardous weather events like heavy spring rains and heat waves can affect our
lake‟s water quality, fish communities, and other resources we enjoy. Working in partnership with various agencies
in research and sharing of information will help us better understand and project the impacts of climate change in
our region.
The MNR has developed the „Climate Change Mapping Browser‟ which projects temperature and precipitation
patterns based on human activities and greenhouse gas emissions by regions. For more information, refer to
http://www.web2.mnr.gov.on.ca/mnr/ccmapbrowser/climate.html.
2. Surface Water Quality
According to the Christie Lake Survey, circulated in July 2007, 45% of survey respondents identified water quality
as the most important priority on the lake. Everyone that uses, lives, cottages or runs a business on the lake
depends on clean, safe water. In a watershed, we all live downstream. This means the activities carried around
the lake determine the quality and health of the lake ecosystem available to all of us. The cumulative impact of
human activity around the lake can cause deterioration in water quality, and an overall decline in the quality of life in
the watershed.
The lake provides important habitat for numerous species of plants and animals, including species at risk. Poor
water quality can negatively affect wildlife and human health, and can affect recreational activities such as
swimming and fishing. The thin soils and exposed fractured bedrock around the lake can provide a direct route for
chemicals and nutrients from land use activities, and bacteria (e.g. E.coli) from faulty septic systems, to be carried
through surface runoff to the lake, which can be harmful to the overall health of the ecosystem.
The real estate value of lakefront property can also be affected by poor water quality. Continued excessive aquatic
vegetation growth and algal blooms due to high levels of nutrients in the lake system can impact the aesthetics of
the area and result in reduced desirability of properties around the lake. Sustainable land use practices and
reducing the amount of nutrients reaching the lake can help protect water quality.
2.1. How is the Lake Affected?
The levels of phytoplankton (algae), measures of the water clarity, dissolved oxygen levels and nutrient
concentrations can be used to estimate the biological productivity of a lake (also known as the trophic status).
The depth to which light can penetrate into the water column is called the euphotic zone of the lake. As the
amount of phytoplankton (algae), suspended organic materials and sediments in the lake increases, the depth to
which light can penetrate into the lake decreases, reducing the clarity of the lake. Dissolved oxygen levels
determine the lake‟s ability to support all forms of aquatic life. For example, different types of fish require specific
levels of dissolved oxygen in the water in order to successfully carry out their life stages. Total phosphorus is
generally considered the limiting nutrient in lakes and is a measure of the amount of phosphorus available for
aquatic plant growth.
The biological productivity of a lake can be classified as:
Oligotrophic: low productivity - light and oxygen levels are high, nutrient levels are low; a young lake
Mesotrophic: moderate productivity - medium levels of nutrients available in the lake system
Eutrophic: high productivity – high levels of nutrients, that promote the growth of excessive aquatic vegetation,
reduced dissolved oxygen content in the lake
Christie Lake is considered a mesotrophic water body, and is capable of supporting a good population of living
organisms. The lake has experienced a gradual change in water quality over the past decade, reflecting a slow
transition towards a eutrophic state. The process of a lake aging, also known as eutrophication, occurs naturally
(i.e., an oligotrophic lake that becomes increasingly enriched with nutrients eventually moves into mesotrophic and
eventually to eutrophic status). However, the introduction of excessive nutrients from human activity (e.g. shoreline
erosion, removal of shoreline vegetation, development, faulty septic systems, fertilizer runoff) can increase the rate
in which a lake ages. This increase in nutrients can increase the lake‟s productivity; potentially resulting in
excessive aquatic vegetation growth and algal blooms. For more information on algal blooms and aquatic
vegetation, refer to the Aquatic Vegetation Section.
2.2. History
In the early 1970s, an increasing awareness and concern for the changes in water quality and pollution levels in
recreational lakes began as cottage development around Christie and neighbouring lakes accelerated. By 1970,
the townships of South Sherbrooke and Bathurst had developed Official Plans and implemented Zoning By-laws to
allow better control on shoreline development in order to protect water quality.
The collection of water quality data on the lake was initiated as early as 1970 when the Ottawa Chapter of Pollution
Probe carried out a bacterial study of lakefront properties. In 1971, with help from the Ministry of Environment‟s
(MOE) Self Help Program, more water sampling was carried out on the lake.
A lake survey conducted in 1975 by the MOE and the MNR estimated the phosphorus nutrient supply entering the
lake from different sources including overland runoff (349 kg), upstream lakes (1199 kg), atmospheric loading (484
kg), and shoreline development (173 kg). The survey used the 1974 development levels on the lake, which
included 265 cottages, 5 resorts, no permanent residences, and 57 vacant lots.
In 1982, the MNR prepared the Christie Lake Management Plan outlining the water quality sampling results taken
throughout the early 1970‟s and early 1980‟s. The report indicated at that time, the lake was considered to be in a
mesotrophic state, and was gradually moving toward a eutrophic state due to the increase in development around
the shoreline.
In 1983, a selective study of septic systems on the lake was conducted in collaboration with the Leeds, Grenville
and Lanark District Health Unit. Many septic systems surveyed at that time were classified as substandard, or did
not meet minimum setback requirements.
In 1995, a M.A.P.L.E (Mutual Association for the Protection of Lake Environments) Shoreline Classification Survey
was carried out by the Christie Lake Association (CLA). The purpose of the survey was to identify the state of
vegetation along the lake‟s shoreline, gather septic system information, and outline the restoration action that could
be carried out to enhance or rehabilitate individual shoreline properties around the lake. A second shoreline
vegetation survey update was carried out in the summer of 2008. Results of the 1995 survey are summarized in
the Building a Sense of Community through Stewardship Section.
2.3. Trends
Lake volunteers first started collecting water quality data in 1971. Sampling techniques, evaluation procedures,
and measured water quality parameters have changed over the decades, making it difficult to compare water
quality data from year to year. However, the data collected to date does provide an overall picture of the lake‟s
water quality.
In 1998, Dr. Ley assisted the CLA in more vigorous testing of Escherichia coli (E.coli) and chemical parameters in
the lake. From 1999 to 2007, Dr. Paul Hamilton from the Canadian Museum of Nature provided detailed assistance
in sampling and analysis of many physical and chemical parameters, as well as algae on the lake. Beginning In
2003, RVCA‟s Watershed Watch Program added to our knowledge of phosphorus and nitrogen concentrations,
dissolved oxygen levels, as well as bacterial counts at selected areas around the lake. Sampling through this
program continues. Refer to Map 6 for all monitoring sites around the lake and throughout the watershed.
Water quality information presented in the State of the Lake Report includes data from the MOE‟s Lake Partner
Program and Self Help Program, Canadian Museum of Nature, MNR, RVCA‟s Watershed Watch Program as well
as information collected by the CLA, and analyzed by Accutest Laboratories in Ottawa. The following parameters
have been monitored on the lake:
Water Clarity: measured by lowering a black and white disc (Secchi disk) into the water;
Chlorophyll a: green pigment suspended in phytoplankton which can be used as an indicator of algae quantity in
the water;
Total Phosphorus (TP): a measure of all forms of phosphorus in a sample (Note: Total Phosphorus replaced
chlorophyll a as a measure of nutrient loading in 1994 (MOE);
Total Kjeldahl Nitrogen (TKN): the amount of organic nitrogen and ammonia; occurring from natural
decomposition and discharges into the lake (such as wastewater and manure);
Dissolved Oxygen (DO), Temperature and pH: a profile for both dissolved oxygen and temperature is
measured through the water column. pH is the measure of the acidity or alkalinity of a solution;
Alkalinity: the alkalinity of water refers to its capacity to neutralize acids;
Dissolved Organic Carbon (DOC): dissolved compounds found in water that are derived from organic materials
such as plant material;
Bacteria: Escherichia coli (E.coli) is used as an indicator of the possible presence of other harmful bacteria and
pathogens in the water. Main sources include decaying dead animals, defecation near water and human waste
(grey water and septic system runoff).
2.3.1. Water Clarity
As part of the MOE Self-Help Program, water clarity has been measured at the Blueberry Island sample
site using Secchi disk measurements since 1971 (Refer to Map 6 for sample site DP1 and DP2). The
measurements have ranged from 7.6 m (24.9 ft) in 1971, to 3.3 m (10.8 ft) in 2001. The average water
clarity reading on the lake is 4.8 m (15.7 ft). This measurement supports the mesotrophic designation for
the trophic status of the lake (refer to Appendix 8 for the interpretation of Secchi disk measurement).
As mentioned earlier, water clarity measurements indicate the amount of light penetrating into a lake, and
provide an indirect measure of the amount of suspended material in the water. The amount of
phytoplankton (algae), suspended soil or sediment, levels of dissolved organic carbon (DOC) from natural
decomposition, and weather events, can influence the Secchi disk readings. Figure 1 shows the Secchi
disk measurements from 1987 to 2007 and chlorophyll a readings from 1987 – 1995 and 1999 – 2002.
Chlorophyll a is a pigment that makes plants and algae green. Plants and algae use this pigment to trap
the energy from the sun so they can grow. Measured in micrograms/L (µg/L) chlorophyll a can be used as
an estimate of potential plant growth and of the abundance of algae in the water (more information about
this parameter is discussed below). Comparison of Secchi disk readings and chlorophyll a data can
provide an indication of the relationship of chlorophyll a amounts in the water, and water clarity
measurements. Appendix 9 shows the data for both these, and other water quality parameters.
6
Secchi Disk (m)
Chlorophyll a concentrations (µg/L) and Secchi Depth (m)
Chlorophyll a (µg/L)
5
4
3
2
1
0
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
Year
Figure 1: Average annual water clarity and chlorophyll a measurements on Christie Lake
(1987 - 2007)
2.3.2. Chlorophyll a
As part of the Self-Help Program, twenty samples of chlorophyll a were collected between 1971 and 1994
to estimate the potential for plant growth in the lake. Between 1999 and 2002, samples were collected and
analyzed by the Canadian Museum of Nature. The Provincial Water Quality Objective (PWQO) for
chlorophyll a was 5 µg/L. Chlorophyll a measurements exceeded the PWQO in 1977, 1979, 1985, and
2001. The average of chlorophyll a readings collected on the lake is 3.93 µg/L. This parameter
measurement indicates the lake is in the upper mesotrophic range (refer to Appendix 10 for the
interpretation of this measurement). Figure 1 shows the chlorophyll a readings from 1987 to 2002.
2.3.3. Total Phosphorus
Between 1975 and 1995, sampling for total phosphorus (TP) was sporadic (3 samples). Since 1996,
sampling for TP has been continuous; these samples have been collected by the CLA, Canadian Museum
of Nature, and RVCA‟s Watershed Watch Program. Phosphorus concentrations (24 data sets) have also
been calculated using chlorophyll a concentration data. The average for all total phosphorus samples
taken from surface water is 11.4 µg/L; which falls below the PWQO of 20µg/L (the guideline used to avoid
persistent/large-scale concentrations of algae growth in a lake), and at the lower end of the mesotrophic
category.
Water flowing through the Tay River from Bobs and Crow Lakes contributes total phosphorus to Christie
Lake. It appears this input is attenuated by the Christie Lake Wetland.
Phosphorus inputs from the Elliot Road Drain is being assessed. The 2.8 km (1.8 mile) long ditch drains
parts of Lots 4 - 7, Concession 3, Bathurst, and eventually empties into the lake at the eastern end of the
north shore (See Map 5). This drain has a wide drainage area that can carry overland contaminants
including phosphorus, nitrate, ammonia, E. coli and chloride. The possibility for contamination of surface
water from sources such as fertilizer and manure runoff, and sedimentation from soil erosion, specifically
during rainfall events, is high. Continuing to maintain the natural vegetation along the drain‟s shoreline can
help stabilize the drain‟s banks, reducing the effects of erosion, and help filter out nutrients and other
contaminants from overland sources before it enters the lake. Currently, sedimentation plumes are still
observed entering the lake after heavy rainfall events.
Phosphorus inputs from the intermittent and permanent tributaries (Watershed Watch Program‟s sites E
and H) (refer to Map 5 for sample locations) also require further assessment in order to gain a better
understanding of the amount of phosphorus being contributed to the lake from these tributaries. TP
sampling of inlets or tributaries around the lake has been conducted by the CLA in April 2008 and 2009.
Higher TP concentrations are typically found in deep parts of a lake and within lake sediments. Dr. Smol,
of Queen‟s University sampled a lake sediment layer from 200 years ago that inferred the TP amount was
19.3µg/L. Sampling microfossils of diatoms (siliceous algae) in the sediments inferred that the lake has a
modern day average TP concentration of 17.1 µg/L. In the summer months, lakes commonly undergo
periods of low dissolved oxygen due to temperature increases, lake stratification, and decomposition of
aquatic vegetation at the lake bottom or hypolimnion. Lake sediments can have as much as 1000 times
the amount of phosphorus found in water, and therefore can have a large storage potential of phosphorus
that can be released into lake waters in anoxic conditions (low oxygen - less than 1 µg/L of dissolved
oxygen at the lake‟s sediments). Phosphorus from the lake‟s sediments is released into the water when
dissolved oxygen levels become low and pH levels become more acidic in the hypolimnion. Phosphorus is
commonly associated with elemental iron, aluminum, and to a lesser degree, calcium. The ability of this
area of the lake to buffer the effects of a pH change will influence the solubility of phosphorus aggregates
involving iron, aluminum and calcium. The extent and nature of the laminated sediments in the lake
remains an unknown. In a lake with very little glacial or postglacial sedimentary deposits, like Christie
Lake, the sensitivity to acidification is closely related to the capability of surrounding bedrock to react with
and buffer acidic groundwater and surface water.
Water samples taken from the lake‟s deep point (1 m from the bottom of the lake) in 2002, 2006, and 2007
found an average TP concentration of 145.7 µg/L. Recent water quality measurements, taken earlier in
the summer at the deep point of the lake, showed anoxic conditions. As the pH in this area of the lake
becomes more acidic, phosphorus is released from its association with sediment-bound iron, enters the
water column and becomes available for aquatic vegetation and algae uptake and growth. More data is
needed to better understand the rate of phosphorus release from the sediments in the lake.
In the fall and spring, changes in lake temperatures, and wave and wind action, creates the water in a lake
to turnover. Water is most dense (heaviest) at 4 ºC (39 ºF). As temperatures increase or decrease from
4 ºC, water becomes increasingly less dense (lighter). In the summer, lakes are maintained in a stratified
condition. Less dense water is at the surface (epilimnion) and more dense water is near the bottom
(hypolimnion).
During late summer and autumn, air temperatures cool the surface water, causing its density to increase.
The heavier water sinks, forcing lighter, less dense water to the surface. This continues until the water
temperature at all depths reaches approximately 4ºC (39º F). Because there is very little difference in
density at this stage, the waters are easily mixed by the wind. The sinking action and mixing of the water
by the wind results in the exchange of surface and bottom lake water, which is called "turnover." In the
spring, when ice melts, wind mixes the water, causing spring turnover. This turnover can also introduce
phosphorus found in solution above the lake sediments into the water column and surface water. Wind and
continued warming of the upper waters eventually create the stratification of the lake. The high TP
concentrations measured in 1998, 1999, and 2002 at ice-out (average 22 µg/L) may be reflecting the
effects of spring turnover on surface waters. Only five measurements are in this dataset. More sampling of
phosphorus throughout the water column during spring turnover is needed to help assess the impact of
bottom waters on the lake‟s general water quality.
2.3.4. Dissolved Oxygen and Temperature
Concentrations of dissolved oxygen (DO) in water are dependant on water temperature. As water
temperatures increase; the ability of water to hold oxygen declines and dissolved oxygen levels decrease.
Other factors that influence DO concentrations include the amount of aquatic vegetation (oxygen is
produced through photosynthesis), the rate of aquatic vegetation decomposition, and wave action (mixing
of water with surface air). As mentioned earlier, after spring turnover, a lake will stratify into the epilimnion
(warm water zone where light penetrates and photosynthesis occurs at optimum rate), the hypolimnion
(water closer to the bottom of the lake where cooler temperatures maintain a more favorable level of
dissolved oxygen for longer periods of time) and the thermocline (the transition layer between the mixed
warmer layer of water near the surface, and the deep water layer). Fish and wildlife require certain levels
of dissolved oxygen to survive; these species‟ habitats are limited to the areas of the lake where DO levels
meet their habitat needs.
Appendix 11 shows measured DO and temperature profiles for the lake for seven different years between
1975 and 2007. As discussed earlier, anoxic conditions typically occur near a lake‟s bottom during the
summer months. This loss of oxygen is mainly due to the action of aerobic bacteria breaking down
decomposing aquatic vegetation and other organic material. The identification of midges (larval insects
that can live in low oxygen habitats) in the lake sediment by Dr. Smol shows that the bottom waters of the
lake are anoxic before the end of the summer. Anoxic conditions were measured at the deepest point in
the lake on August 27, 1975; a similar condition was measured on August 22, 1999. Temperature and DO
profiles measured between 2000 and 2007 were measured earlier in the season than in the past. Anoxic
conditions were measured in the hypolimnion on August 20, 2000, August 5, 2001, and August 2, 2007.
The August 2, 2007 reading was recorded at a depth of 12 m (39.4 ft). This lack of oxygen in the
hypolimnion could be negatively affecting the fish communities on the lake.
2.3.5. Total Kjeldahl Nitrogen
Organic nitrogen or Total Kjeldahl Nitrogen (TKN) concentrations measured on the lake are generally found
between 235 to 401 µg/L, with an average of 358 µg/L. Refer to Figure 2 for an outline of TKN
measurements on the lake. Since there are no provincial guidelines for TKN, the RVCA has adopted an
upper accepted limit of 500 µg /L as a reference point to indicate the presence of excessive nitrogen in the
lake. Water samples were taken from the lake‟s deep point and analyzed in 2000, 2003, 2006, and 2007 to
determine TKN concentrations. Concentrations were found to increase as the summer season progressed.
The average concentration of TKN during that period is 490 µg/L. The difference between surface and
bottom TKN concentrations do not reflect as much of a change in concentrations when compared to the TP
measurements taken at the surface and bottom of the lake.
In warm water lakes, it is normal for the total nitrogen: total phosphorus ratio (TKN:TP) to be 30:1 or
greater. However, if this ratio is less than 20:1, and the TP concentration is high (greater than 20 µg/L),
surface algal blooms form. Using the TKN and TP averages (490 µg/L and 145.7 µg/L respectively)
measured at the lake‟s deep point, a ratio of 3.4:1 is achieved which supports the presence of algal bloom
data discussed in the Aquatic Vegetation Section. It is recommended that TKN and TP measurements be
made in water adjacent to the bloom areas to better understand the link of nutrient levels and bloom
occurrences (Hamilton, 2008). For more information about algal blooms on the lake, refer to the Aquatic
Vegetation Section.
0.45
0.40
0.35
0.30
TKN (mg/L)
0.25
0.20
0.15
0.10
0.05
0.00
1975 1994 1995 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 2006 2007
Years
Figure 2: Average TKN µg/L across sample sites on Christie Lake (1975/1994-2007)
2.3.6. Alkalinity
The alkalinity of water refers to its capacity to neutralize acids. Alkalinity of natural waters is due primarily
to the presence of hydroxides, bicarbonates, and carbonates. Alkalinity is usually expressed in parts per
million of calcium carbonate (CaCO3). Calcium is the building block for shell and bone development of
aquatic animals (i.e. mussels and fish). A lake in the Canadian Shield will typically have low alkalinity
values, due to their geology. They are more susceptible to acid rain, but less susceptible to colonization of
zebra mussel populations.
Research on North American lakes, which included lakes in Ontario, has been carried out in order to
estimate the threshold calcium levels in lakes below which zebra mussel populations cannot succeed.
Based on various research findings, the estimated thresholds are as low as 8 mg/L and as high as 28
mg/L. Cohen and Weinstein‟s 2001 literature review found that zebra mussel populations are unlikely to be
established in lakes with a calcium concentration below 20 mg/L. Their review found that lakes with zebra
mussel populations where calcium concentrations were below 20 mg/L might be the result of recruitment of
larvae or juveniles drifting from upstream populations established in higher calcium waters. Experimental
data suggest that populations cannot be sustained where calcium levels are below 15 mg/l, although there
are few reports of zebra mussel veligers from inland lakes with calcium measurements in this range.
Based on eight samples taken from 1971 to 2003 (refer to Appendix 9), the alkalinity values for the lake
have been very static with an average of 62 mg/L of CaCO3. For more information about zebra mussels
refer to the Wildlife Section.
2.3.7. Dissolved Organic Carbon
Dissolved organic carbon (DOC) is composed of acidic products derived from the decomposition of organic
sources, such as plant material. DOC can enter a lake system through precipitation, leaching and
decomposition. The DOC released to the water by phytoplankton (colorless, primarily amino acids,
carbohydrates) makes up only a small proportion of DOC contributed to lake systems. The acids of DOC
can affect the acid-base chemistry of lake water and can influence the amount of trace metals found in
aquatic organisms. DOC can also slow down the primary production in lakes.
An increase in DOC levels can decrease lake transparency, causing shallower euphotic zones and
thermoclines. DOC samples have been collected on the lake from 1998 to 2007 and have an average of
4.3 mg/L. Secchi disk readings reflect that a decrease in water clarity is not occurring at present.
DOC can provide UV-B protection to aquatic organisms and plants. Recent literature reports that direct
effects of UV exposure are a concern in freshwater lakes when the DOC is less than 3 mg/L.
Highly productive wetlands (for example the Christie Lake Wetland) can generate large amounts of organic
matter that can enter the lake in a dissolved form. This source may be an often overlooked variable when
measuring lake productivity. The DOC input from the Christie Lake Wetland may be another important
consideration (in addition to phosphorus) when addressing nutrient contributions to the lake.
2.3.8. Bacteria
E. coli counts were sampled at Badours Creek, Minnow Creek and the Tay River inlet in 1998, 2001 and
2002. While E. coli counts may provide an indication of agricultural runoff, no phosphorus measurements
were conducted on these samples. Samples from these sites could be used in the future to measure the
amount of phosphorus being contributed to the lake from these tributaries.
Concern around the impacts of faulty septic systems on the lake‟s water quality was identified in the July
2007 survey responses. The importance of septic maintenance and water quality were both rated at the
same level by respondents to the survey. While 31% of respondents indicated their septic system was
between 15 and 30 years old, the value of monitoring and maintaining septic systems appears to be
understood by survey respondents.
Bacterial testing of waters in front of lakefront properties was first conducted in 1971. As mentioned earlier,
in 1983, a selective study of waste disposal systems on the lake was conducted in collaboration with the
Leeds, Grenville and Lanark District Health Unit. Many septic systems surveyed at that time were
classified as substandard, or did not meet minimum setback requirements, potentially impacting water
quality on the lake.
Retesting of specific properties was initiated in 1998 by the CLA. This action was in response to the lack of
septic information from 115 properties out of 266 surveyed in the 1995 Shoreline Survey. Specific areas of
the lake were targeted to try and locate failing septic systems by measuring bacteria (E.coli) counts in
surface lake water. This testing was continued by the CLA from 1998-2003.
Based on E. coli results, residents were notified if they resided in an E. coli „hot zone‟. The CLA had
McIntosh Hill Engineering conduct a visual inspection of the „hot zones‟ in September 2000. The CLA
presented a formal request to Tay Valley Township Council for a septic re-inspection policy on October
th
26 , 2000. In October 2000, the volunteer Tay Valley Township Sewage System Re-inspection Program
pilot was initiated, and carried out on the lake. In 2006, 31 properties were re-inspected. A tank inspection
component was added to the program, with permission of the owner.
The results of the volunteer re-inspection program carried out on the lake are outlined in Table 2 below.
For more information about the program, contact the Mississippi-Rideau Septic System Office (1-800-267-
3504). Christie Lake is scheduled for re-inspections again in 2009. This successful re-inspection program
continues to educate lake residents and cottagers about the importance of proper maintenance of septic
systems.
Table 2: Results of the Tay Valley Re-inspection Program on Christie Lake
(2000- 2006)
Criteria Number of Properties
No visual concerns 55
Too Close to Water 4
Pump out required 3
Tank in Poor condition 9
Surface Discharge 6
Erosion of bed 3
Roots in tank 1
Response required 4
Other 6
Total number inspected 91
The collection of E. coli samples from surface water can help identify potential input of pathogen sources
around the lake. Since 2003, E. coli data has been collected at four sites around the lake as part of the
Watershed Watch Program. On average, the E. coli count from these sites is 2 E. coli colonies/ 100 mL in
the lake‟s surface water. Table 3 below outlines the sample exceedances of E. coli. “Exceeds 1” is a
reference used by RVCA to reflect bacterial counts greater than 10 E. coli colonies/100 mL in a sample.
When counts are consistently greater than 10/100 mL, it could possibly mean there is a source of bacterial
pollution nearby. While 13% of the 215 samples were in the “Exceeds 1” category, none were consistently
so. In the five years of testing, the PWQO (100 colonies / 100 mL) was not exceeded by any of the
samples. The results indicate the surface water in the lake should not pose a health concern for people
swimming or carrying out other water contact recreational use.
Table 3: E. coli Sample Exceedances (2003 to 2007)
Number of Exceeds 1 Exceeds 2
Year % %
Samples (10 colonies/100 mL) (100 colonies / 100 mL)
2003 64 6 9 0 0
2004 40 9 23 0 0
2005 36 11 31 0 0
2006 35 0 0 0 0
2007 76 2 2.6 0 0
Total 215 28 13 0 0
2.4. Christie Lake Wetland
The Christie Lake Wetland is found at the inlet of the lake (refer to Map 3 for location). Wetlands play an important
role in protecting water quality. The quality of water in receiving waterbodies can be strongly influenced by the
quality of water coming in from the streams and wetlands that feed into them. Wetlands act as natural filters,
taking up nutrients such as nitrogen and phosphorus, processing them by transforming them into biologically useful
forms, and preventing them from traveling into other waterbodies. Wetlands can also neutralize contaminants
carried into surface water from overland runoff. They also recharge groundwater aquifers and help regulate water
levels during flooding events.
The Natural Areas Report- Christie Lake Wetland (Appendix 2), provides detail of this locally significant wetland.
This rich ecosystem is composed of two wetland types (63% swamp and 36.5% marsh) and 0.5% upland areas.
This wetland supports many diverse plant and animal species. The operation of the Bolingbroke Dam at the outlet
of Bobs Lake causes water level fluctuations on Christie Lake. The Christie Lake Wetland moderates water level
fluctuations and flow at the lake‟s inlet at the Tay River. Table 4 below outlines the chemical and physical
th
characteristics of the wetland, collected in 1996 by the MNR. Sampling on June 24 , 1996, showed the water was
fully saturated with oxygen, representing a very productive, photosynthetic ecosystem. Continued monitoring
should carried out for this important wetland in order to better understand its contribution the lake‟s water quality.
Table 4: MNR Data: Characteristics of Christie Lake Wetland (1996)
Parameter June 24 August 26
Temperature (ºC) 21.4 19.5
Dissolved Oxygen (mg/L) 8.9 4.0
Total Phosphorus (µg/L) 30.9 Not measured
Total Kjeldahl Nitrogen (µg/L) 900 1800
Chlorophyll a (µg/L) 6.25 3.41
Secchi depth (m) 2 4
2.5. Benthic Invertebrates
Benthic invertebrates are organisms that inhabit the lake bottom in sediment, tree snags, and aquatic plants for at
least part of their life cycle. Typically, this fauna includes aquatic insects (e.g. stoneflies, mayflies, caddisflies,
beetles); crustaceans (e.g. isopods, amphipods, crayfishes); mollusks (e.g. snails, clams, mussels); annelids (e.g.
leeches, oligochaetes); and a few other groups (e.g. Proboscis worms, flatworms). These are a link in the aquatic
food chain. Algae and plant leaves are eaten by invertebrates, which in turn are a source of energy for animals
such as fish.
Benthic invertebrates all differ in their sensitivity to water pollution. In a healthy lake, the benthic community will
include a variety of pollution-sensitive invertebrates. In an unhealthy lake, there may be only a few types of non-
sensitive, pollution-tolerant, invertebrates. Considering both the water chemistry data and the sampled invertebrate
community can offer a long-term look at what creatures the lake can support.
In 2003, as part of the Watershed Watch program, three sites were sampled for benthic invertebrates. Three
replicates of species were collected at each of the three sites around the lake and identified (Refer to Map 6 for
Ontario Benthos Biomonitoring Network sample sites). As mentioned earlier, with good habitat diversity and
suitable water quality, typically, more groups of invertebrates (or Taxa Richness) will be found. Taxa richness
counts above 10 are considered to have excellent diversity and invertebrate communities are very stable. Anything
below 5, indicate low diversity and the communities are unstable. Results for the replicates at the three sites are
found in the Table 5 below (data collected in the spring and fall of 2004 are included in the brackets).
Table 5: Taxa Richness - Christie Lake Sampling 2003 (Fall), 2004 (Spring & Fall)
Site Replicate #1 Replicate #2 Replicate #3
CL-1 10 (20,12) 10 (17,17) 11 (19,14)
CL-2* 8 (26,10) 11 (19,10) 11 (22,16)
CL-3 9 (17,18) 10 (20,16) 10(17,19)
*Note: Site CL-2 was sampled in an area minimally impacted by development.
Comparisons have been made between the first and third values outlined in Table 5 above (data collected in the
fall). Table 6 categorizes the benthics sampled into various pollution tolerances: sensitive, somewhat sensitive,
and tolerant. The tolerance index of benthics sampled in 2003-2004, showed sensitive organisms dominating the
sample - indicating good water quality. Further sampling of benthic invertebrates was scheduled for 2008. In order
to track changes over the coming years, sampling should be continued.
Table 6: Tolerance Index for Benthic Invertebrates Sampled on Christie Lake Fall
(2003 - 2004)
Sensitive Somewhat Sensitive Tolerant
Caddisfly Beetle larvae Aquatic worms
Hellgrammite Clams Blackfly larvae
Mayfly nymphs Crane fly larvae Leeches
Gilled snails Crayfish Midge larvae
Riffle beetle adults Damselfly/dragonfly nymphs Pouch snails
Stonefly nymphs Scuds
Water penny larvae Sowbugs
Fishfly/alderfly larvae
Table 7: Hilsenhoff Index
The Hilsenhoff Family Biotic Index (FBI) takes into
consideration the habitat requirements of each taxa,
indicates organic and nutrient pollution, and provides an
estimate of water quality for each site using established
pollution tolerance values for each taxa. Table 8 compares
the average index values for the three sites over three time
periods (refer to Table 7 to interpret the values). In 2004,
Site 2 showed potential for organic pollution compared to
Site 1 or Site 3. It should be noted this „very poor to
excellent‟ scale system was developed based on empirical data for stream environments. Lake data compared to
this index should consider that factors other than water quality could be affecting the presence or absence of
certain intolerant species.
Table 8: Hilsenhoff Family Biotic Index Data for Christie Lake (2003 – 2004)
Site Sample # Fall 2003 Spring 2004 Fall 2004
1 6.955 5.362 6.574
2 6.356 5.927 6.305
1
3 6.53 5.27 6.383
Average 6.65 5.52 6.42
1 7.108 6.148 7.074
2 6.543 6.833 7.263
2
3 6.312 6.233 6.954
Average 6.62 6.40 7.10
1 6.437 6.407 6.375
2 7.588 6.521 5.491
3
3 7.426 7.267 6.122
Average 7.15 6.73 6.00
2.6. Who Regulates Surface Water Quality?
The MOE has the responsibility for enforcing the following: Environmental Protection Act, Nutrient Management
Act; Ontario Water Resources Act and the Environmental Assessment Act. The MNR is responsible for enforcing
the Lakes and Rivers Improvement Act.
The Building Code Act (BCA) (1992), and Part 8 of the Ontario Building Code (OBC) regulates the design,
construction, operation and maintenance of sewage systems. The OBC regulation extends to systems with a
design flow of less than 10,000 Litres/day, serving no more than one lot. Systems, that do not fall within these
parameters, are regulated by the MOE, under the Ontario Water Resources Act (Saunders, 2006)
The authority for the Mississippi-Rideau Septic System Office, and other enforcement agencies, to conduct
inspections of potentially unsafe sewage systems is provided by BCA s.15(1). This Act provides inspectors with the
right of entry onto land “to determine whether a building is unsafe”, and BCA s.15(2.1) deems a sewage system to
be “unsafe” if it is not maintained or operated in accordance with the BCA and the OBC (Saunders, 2006).
Further authority will be given with amendments proposed to the BCA under the Clean Water Act, 2005. The
amendments to this Act define a „maintenance inspection‟, and allow for: „an inspector (to) enter upon land and into
buildings at any reasonable time without a warrant for the purpose of conducting a maintenance inspection‟
(Saunders, 2006).