Prepared for Carleton River Watershed Area Water Quality ...

Results of the 2018 Water Quality Survey of Fourteen Lakes in Yarmouth and Digby Counties

Prepared for

Carleton River Watershed Area Water Quality Steering Committee

By

John D. Sollows,

Technical Advisory Committee

Hebron, N.S.

March 2020

SUMMARY

Water quality surveys carried out by or for Nova Scotia Environment (NSE) between 2008 and 2015

within the Carleton, Meteghan, and Sissiboo watersheds have shown a number of lakes within these

watersheds to be seriously degraded with respect to nutrient enrichment, leading to harmful algal

bloom events. These studies have also shown this degradation to be primarily due to high phosphorus

inputs. While multiple nutrient sources have been identified including agricultural, aquaculture, and

likely residential sources, previous studies have indicated releases associated with a number of mink

farming operations in the area as likely the largest single source of the nutrients. As a result, the

Nova Scotia Department of Agriculture developed and enacted the Fur Industry Act, and associated

Regulations, which were enacted in 2013. These include a number of measures designed to

minimize the impact of fur farming operations on water quality.

In order to assess water quality trends in the survey lakes, NSE has encouraged and supported efforts

to establish a long-term water quality monitoring program that could be executed with the aid of a

community-based volunteer organization. Such a program could serve to identify changes in water

quality, including potential problem areas. This work can help identify the need for additional studies

and mitigation measures. It can also help evaluate the effectiveness of mitigation measures

implemented to reduce the impact of fur farming operations on water quality. This work, involving

volunteer monitoring, began in 2013, and has continued in subsequent years, with the financial

assistance of the Nova Scotia Department of Environment, Salmon Association’s Adopt-a-Stream

program, Mersey-Tobeatic Research Institute, Municipality of the District of Yarmouth, Municipality

of Argyle, and in-kind support from the Nova Scotia Department of Fisheries and Aquaculture.

Beginning in 2015, the monitoring program has been under the oversight of the Carleton River

Watershed Area Water Quality Monitoring Steering Committee, which consists of representatives of

concerned government departments, concerned municipalities, Nova Scotia Power, the mink farming

industry, concerned NGO’s and affected citizens. The Committee works under the auspices of the

Municipality of the District of Yarmouth.

In 2016, for the first time, local volunteers took the lead in monitoring in all lakes.

In 2017, Stantec was engaged to do a case study on the system in order to develop a complementary

database, clarify environmental stressors in the system, and develop related recommendations related

to management, education, and future research. Their work and subsequent report focused on spring

runoff in headwater lakes and the summer situation in all lakes but Raynards, Salmon River, and

Kegeshook. The Committee conducting additional monitoring in the spring and autumn on the three

lakes not covered by the Stantec study and issued a complementary report.

This report will consider the results of the 2018 monitoring season in spatial and historical context.

The results from 2018 overall are unremarkable: As before, nutrient (phosphorus, nitrogen) levels

typically decreased along the main Carleton, from the headwaters (upstream) to downstream, with

the lowest levels observed in the tributary lakes of Porcupine and Sloans. The year-to-year observed

decrease in total phosphorus levels since the summer of 2015 on the mainstem of the Carleton,

continued in 2018, with notable exceptions in Hourglass and Wentworth. The long-term total

phosphorus concentration statistical trends for the August surface samples since sampling began in

2008 does not indicate a significant decreasing trend in most lakes monitored for this time period

(except Placides). Hourglass Lake was observed to have an increasing trend. Spring total phosphorus

concentration statistical trends, that began as early as 2013, indicate a significant decrease in

Vaughan when lakes are not thermally stratified. Fall total phosphorus concentration statistical

trends, with samples for some lakes starting in 2009, indicate significant decreases in Parr, Fanning

and Vaughan when lakes are not thermally stratified.

Colour was uniformly down from 2017, except in Vaughan. The data indicate a positive relationship

between early summer rainfall and late summer colour. None of the August colour results for lakes

sampled since 2008 have observed a significant increasing or decreasing trend. Recent conditions

support climatologists’ predictions of hotter drier summers. To the extent that this may lead to

reduced colour levels, lakes may become increasingly susceptible to harmful algal/cyanobacteria

blooms.

Nutrient and chlorophyll a levels in Nowlans were down and the microcystin concentration was

below measurable limits for the second consecutive year.

Total phosphorus concentration trends in Hourglass are a concern. To date, no blooms have been

recorded to date.

Kegeshook was observed to maintain a mesotrophic status but is potentially vulnerable to localized

harmful algal blooms. High water transparency (low colour) and cottage development are potential

factors that would contribute to a risk of harmful algal blooms. No significant increasing or

decreasing trends were observed for the summer, spring and fall sample nutrient, chlorophyll a and

colour results. Mitigation measures that could be enacted within the watershed to reduce this risk,

include a landowner education program about the importance of minimum shoreline development

and municipal by-laws limiting shoreline development activities.

Salmon River Lake showed no increasing or decreasing nutrient and colour trends but given likely

future trends in shoreline development and water transparency, continued monitoring is advised.

To the extent that funds permit, harmful algal bloom (cyanobacteria) monitoring is desirable both

shortly after the summer solstice, when blooms tend to peak, and late August, when stratification

tends to be maximal. Monitoring should also occur when blooms are visually observed. Microcystin

concentration monitoring in lakes other than Nowlans should be further evaluated given the

continuous below detection results and potentially be revised to a more targeted program with

academic research partners.

Assessing the contribution of nutrient loads from other sources besides the headwater Carleton lakes

potentially has merit, but costs and other practicalities intrude. Water chemistry monitoring at the

mouths of inlets and outlets of selected lakes is practicable, given sufficient funding, but flow

measurements are considerably more challenging. Further discussion is recommended to the

Committee about the feasibility of this type of program expansion.

Public education and outreach, particularly to acquaint resource-users, including the forestry

industry, and riparian property owners about their responsibilities to help maintain water quality

should continue. Protective municipal by-laws and provincial regulations should be potentially

explored to improve management of lakeshore development activities within the study watersheds

and others within the Province.

Table of Contents

1. Background .......................................................................................................................................... 5

2. Approach and Methods ........................................................................................................................ 6

3. Results .................................................................................................................................................. 7

3.1 Annual and Spatial Variation in Lake Trophic Status ........................................................................ 7

3.2 Seasonal Variation in Trophic Parameters .......................................................................................... 9

3.3 Surface and Bottom Comparisons of Trophic Parameters .............................................................. 180

3.4 Cyanobacterial Abundance, Composition and Presence of Toxins ................................................ 211

4. Discussion .......................................................................................................................................... 11

4.1 Spatial and Temporal Considerations in the Carleton Catchment .................................................... 11

4.2 Seasonal Variation and Surface and Bottom Comparisons of Trophic Parameters ........................ 242

4.3 Cyanobacterial levels, species, and toxins ........................................................................................ 13

4.4 Calculated Carlson Trophic State Indices ......................................................................................... 14

5. Final Considerations .......................................................................................................................... 15

6. Acknowledgements ............................................................................................................................ 16

7. Literature Cited .................................................................................................................................. 16

Appendix 1. Data Base Used in Analyses ............................................................................................. 18

Appendix 2. Water Quality Parameters compared by lake, through Time and Space ........................... 23

Appendix 3. Seasonal Variation in Water Quality Parameters for Selected Lakes ............................... 32

Appendix 4. Comparison of Surface and Bottom Total Phosphorus for Selected Lakes ...................... 44

Appendix 5: Data on Cyanobacterial Abundance, Genus composition, and Microcystin ................... 95

Appendix 5: Calculated Carlson Trophic State Indices, based on August Data ................................ 1034

Results of the 2018 Water Quality Survey of Fourteen Lakes in Yarmouth and Digby Counties

1. Background Since 2008, ten water quality studies have been carried out on a number of lakes located within the

Carleton, Meteghan and Sissiboo River watersheds, with financial and technical support from, or

managed by the Nova Scotia Department of Environment (NSE), with significant supplementary support

from the Nova Scotia Salmon Association’s Adopt-a-Stream program, Mersey-Tobeatic Research

Institute, and the Municipalities of the Districts of Yarmouth (MODY) and Argyle. According to

Brylinsky and Sollows (2014), the studies done annually from 2008 to 2011 indicated many of the lakes

to have degraded water quality as a result of high phosphorus inputs. While nutrients come from many

sources, the predominant spatial pattern of nutrient distribution reported in these studies, particularly

Brylinsky (2012), presented evidence that these increased phosphorus levels resulted primarily from mink

farming operations nutrient loading. In some instances, high algal concentrations associated with these

nutrients contained species of cyanobacteria (blue-green algae), which are known to produce

microcystins, a toxin that under certain conditions can be harmful to humans, livestock and wildlife.

The Nova Scotia Department of Agriculture (NSDA) has various measures in place to mitigate potential

impacts from agricultural activities on water quality, including the Nova Scotia Fur Industry Act and

Regulations, which were enacted in 2013.

NSE has supported efforts to establish a long-term water quality monitoring program that captures the

annual changes in water quality – providing an indication of the efficacy of mitigation programs and

controls implemented to reduce nutrient related impacts. Accordingly, in 2013 a water quality study was

designed and implemented that could form the basis of a routine annual survey to meet this need, and in

the future be carried out primarily by a community, volunteer-based organization. In 2013, the Tusket

River Environmental Protection Association (TREPA) carried out this survey with the assistance of the

Acadia Center for Estuarine Research (ACER) at Acadia University. TREPA took the lead in carrying

out similar studies in subsequent years, with help from the Nova Scotia Department of Fisheries and

Aquaculture (NSDFA).

Beginning in 2015, the monitoring program has been conducted under the oversight of the Carleton River

Watershed Area Water Quality Monitoring Steering Committee, which consists of representatives of

provincial and federal government departments (NSE, NSDFA, NSDA, Agriculture and Agri-Food

Canada [AAFC]) municipalities where the watershed is located (Clare, Argyle, MODY), Nova Scotia

Power Inc., the mink farming industry (NS Mink Breeders Association), Nova Scotia Federation of

Agriculture (NSFA), local non-governmental organizations (TREPA), and citizens within the watershed.

In 2017, Stantec was engaged to do a case study on the system in order to develop a complementary

database, clarify environmental stressors in the system, and develop recommendations related to

management, education, and future research. Their work and subsequent report focused on spring

runoff in headwater lakes and the late August sample event in all lakes but Raynards, Salmon River,

and Kegeshook (Stantec, 2017). A supplementary report focused on data from the spring and autumn

of 2017, as well as the summer data from Raynards, Salmon River, and Kegeshook, and considered

spatial and temporal trends for the entire system (Sollows, 2018).

This report considers results from monitoring activities carried out in 2018, in the context of earlier

reports, spatial relationships and local climate conditions.

2. Approach and Methods The basic approach and water sampling methodologies for the 2018 study followed those of Brylinsky

and Sollows (2014). All lakes are sampled in late August, and seven Yarmouth County lakes (Parr,

Fanning, Sloans, Raynards, Vaughan, Salmon River, and Kegeshook) are also sampled in early May and

late October in order to assess seasonal trends. Sampling is done by NSDFA staff in Provost, Nowlans,

Placides, and Porcupine for the late August event. Otherwise, volunteers living on or near each lake

conduct the sampling of the other lakes for the Spring, late August and Fall events.

Previous to the 2018 monitoring events, nine annual water quality surveys were carried out between 2008

and 2017, but not all were carried out at the same time of year. Seven (2008, 2011 and 2013 to 2017)

were carried out in August, one (2009) predominantly in October, and another (2010) was carried out in

late September. No surveys were carried out in 2012. In 2013 and subsequent years, all lakes of interest

were sampled in August and when possible in May and October. In practice, however, this was possible

for all lakes only in 2013, and spring and fall sampling other years was limited to the above listed seven

Yarmouth County lakes.

In assessing annual variations in water quality, comparisons are made between data for the same season.

The effect of recent past lake environment conditions on observed present conditions (e.g., Summer 2018

effects on Fall 2018) bears consideration. Otherwise, in the spring and autumn, lower air and water

temperatures and stronger winds typically lead to more complete mixing of the lake water column (an

event referred to as lake turnover), which affects surface water quality. The long, warm days of summer

with calmer weather conditions cause some lakes to develop a thermally stratified water column. It is

typically during thermally stratified conditions that harmful algal blooms occur. As a result, more

attention has historically been paid to the situation in late summer, so analyses of annual changes in water

quality in this report were limited to surveys carried out in August and September (i.e., late summer).

With lake stratification in mind, every surface sample collected by volunteers is a composite, with 50%

collected at the surface (0 m to 0.5 m depth) and 50% at two times the Secchi depth using a discrete

sampling device. In August, an additional sample is collected 1 m above the lake bottom at the same

time. In 2018, NSDFA staff working in Provost, Nowlans, Placides, and Porcupine sample at 0.25 m

depth, two times Secchi depth, at thermocline, and 1 meter off the bottom. However, data from twice

Secchi depth are available only for chlorophyll a. The extent to which this affects comparability with

water chemistry data from previous years depends on each lake.

In previous years, these samples had been collected with a Van Dorn sampler. Beginning in 2016, the

volunteers have used home-made samplers, each consisting of a sturdy, weighted, 500-ml. plastic bottle

with a stopper and a measured line. To collect a sample the stopper is pulled with another line, once the

bottle reached the desired depth. At depths over 7 m bottles tended to deform under pressure; in this case,

samples collected from near bottom need to be collected twice, in order to get a full volume for shipment

to the lab.

Water chemistry parameters are analysed at the Environmental Services Laboratory operated by the Nova

Scotia Health Authority, with chlorophyll a analyses outsourced to ALS in Winnipeg. Up to and

including the spring of 2016, chlorophyll a samples were analysed in New Brunswick. The analytical

method used in New Brunswick was Standard Method 10200 H Spectrophotometric Determination of

Chlorophyll; that used in Winnipeg was based on the Fluorescence Standard Method 10200H, which used

frozen, filtered samples. This change in labs and methodologies may affect year-to-year comparability

for chlorophyll a.

Until 2015, a YSI Professional Series multimeter was used to collect various data at the sampling site,

including dissolved oxygen, temperature, pH, and conductivity. Since 2016, when sampling was done by

volunteers, the meter in question has not been available, so these data, particularly oxygen and

temperature profiles, have not been available since 2015, except for the 2017 Stantec sample events. pH

is assessed as part of the laboratory water chemistry analyses, but this change in method from field to lab

does affect comparability between 2016 and 2018 to some previous years when pH was not assessed in

the lab.

In addition to water quality, shoreline sampling for cyanobacteria speciation and counts, and microcystin

concentration analysis are carried out in targeted lakes in July and August. The sample sites are on the

windward side of lakes and/or at locations where there are visible blooms, when possible. All bottles are

opened about 0.25 m below the surface. Lugol’s solution is added as a fixative for the cyanobacterial

samples at 10 drops per 100 ml. All bottles are capped immediately after collection and kept cold by

application of freezer packs. Samples are kept cold and in the dark to prevent degradation until they are

analysed at the ALS laboratory in Winnipeg.

As part of the 2018 data analysis, Mann-Kendall statistical tests are conducted on select parameters for

the August composite surface water samples (0 to 1 m depth) from 2008 to 2018, and the spring and fall

samples. The Mann-Kendall test assesses whether there is a significant increasing or decreasing trend for

a parameter with respect to time, whether or not the trend is linear (Mann, 1945; Kendall, 1975; Gilbert,

1987). The test is recommended to be used as an exploratory test to identify monitoring locations where

concentration changes are significant or large in magnitude (Hirch, Slack and Smith, 1982). The

following are the parameters Mann-Kendall statistical tests were completed on:

• Chlorophyll a

• Total phosphorus

• Orthophosphate

• Total nitrogen

• Secchi disc depth

• Temperature (summer only)

Several stations began monitoring in later years (e.g., 2013/14), including the spring monitoring events,

and therefore their trend analysis datasets are substantially smaller. The trend analysis results are assessed

with consideration of these smaller datasets.

3. Results The complete database for all NSE-supported surveys carried out to date is available as an Excel

worksheet held by TREPA and the Municipality of the District of Yarmouth. Appendix 1 contains the

results tables used in the analyses for the 2018 monitoring season, and Appendix 2 contains a series of bar

graphs for each lake illustrating the results of all late summer surface water surveys carried out between

2008 and 2018. Appendices 3 and 4 display the results tables used to assess seasonal trends, and

comparison of surface and bottom water quality results, respectively.

Appendix 5 presents nutrient concentrations at various inlets to Parr and Fanning Lakes and their outlets.

Appendix 6 presents the cyanobacterial species composition, abundance, and microcystin level results.

Appendix 7 provides calculated Carlson Trophic Indices, based on the late August water quality data from

all lakes.

Appendix 8 provides Mann-Kendall trend analysis results for select parameters for the annual August

surface composite samples from 2008 to 2018, and the spring (2013/14 to 2018) and fall (2009 to 2018)

surface samples

Appendix 9 displays Environment and Climate Change Canada rainfall data from the Yarmouth Airport

for May to October, from 2008 to 2018 with comparison to the Climate Normal dataset (1981 to 2010).

NS Fisheries and Aquaculture Single Surface Sample Results Interpretation

Review of the temperature and oxygen profiles for the four lakes sampled by NSDFA indicated that

thermoclines lay well below the two times Secchi depth in Provost and Nowlans. This indicates that the

water at twice Secchi depth would have been well-mixed with surface water in both lakes, so water

chemistry data from surface samples is hypothesized to be similar to composite samples collected by the

volunteer-based program. It was assumed for this study that surface sample results could be compared

against historic sample results for trend analysis.

Temperature and oxygen profiles in Porcupine showed a temperature shift of 1.1 Co, between 2 m and 3

m depth below surface with the two times Secchi depth at 3.8 m. Oxygen levels varied marginally

between the 2 m and 4 m below surface. A more noticeable thermocline occurred between 5 m. and 7 m.

Again, surface water chemistry for a single surface sample and that from a composite sample is

hypothesized to be similar, but caution in making year-to-year comparisons is considered.

In Placides, there was a decrease of 1.5 Co between 2 m and 3 m below surface, and a dissolved oxygen

decrease of 1.35 parts per thousand (ppt). The two times Secchi depth was at 2.6 m. The temperature and

percent dissolved oxygen decrease between 3 m and 4 m is higher, but differences of this magnitude for

both parameters make comparisons with composite data from earlier years potentially not as accurate due

to the difference in water quality parameters. The data for surface samples is used for the Mann-Kendall

trend analysis, but potential impacts of differences between 2018 and previous years is considered.

Section 3.1 presents the results and discussion for the above lakes that considers the differences in water

collection methods.

3.1 Annual and Spatial Variation in Algal Blooms and Lake Trophic Status for August

Monitoring Event Levels of chlorophyll a, total phosphorus, orthophosphate, colour, Secchi depth, total nitrogen, and

nitrate, pH, and surface temperature have been considered.

Cyanobacterial blooms were not reported from Raynards and Vaughan in 2018, for the first time since the

author has been involved in reporting (2013). However, blooms in Fanning and Ogden began in June and

lasted till mid-October with only occasional, brief interruptions (Cleveland, pers. comm.). Also reported

were blooms of increased severity in Parr and at the northern end of Wentworth, between the Wentworth

River and Seven Pence Ha’Penny Brook inlets. A cottage-owner reported the Wentworth Lake bloom

event.

The summer of 2018 was characterized by drought conditions, with only two major rainfall events (20.6

mm. on Aug. 18 and 59.6 mm. September 18) between July 6 and late September (Appendix 9). The

Agriculture and Agri-Food Canada Canadian Drought Monitor classified southwest Nova Scotia as being

in moderate drought from August to September 2018 (http://www.agr.gc.ca/atlas/cdm). This was similar

to the dry conditions in the summer of 2016; however, in 2016 southwest Nova Scotia was classified as

having abnormally dry conditions in June and July, severe drought conditions for August and September,

and moderate drought conditions in October.

Spatial considerations in the following sub-sections focus on the connectivity and location of lakes in the

Carleton River catchment (e.g., headwater lakes, tailwater lakes).

Chlorophyll a

August chlorophyll a levels increased in most lakes in 2018 in comparison to 2017 (Appendix 1). Major

decreases from 2017 were noted only in Hourglass and Vaughan (reductions from 49.8 to 24.1 µg/L and

14.7 to 2.61 µg/L, respectively), with minor decreases observed for Provost and Nowlans (reductions of

3.98 to 3.46 µg/L and 48.25 to 46.55 µg/L, respectively). The chlorophyll a level in Wentworth was at

the highest recorded concentration since monitoring started in 2013 for the August monitoring event.

In the Carleton system the highest chlorophyll a concentration was recorded in Hourglass, for the third

consecutive year, with Ogden having the second highest concentration. The tendency for chlorophyll a

concentrations to decrease in mainstream lakes from upstream to downstream was not clearly observed in

2017 and remained weak in 2018.

The Mann-Kendall trend analysis (Appendix 8) for chlorophyll a calculated Hourglass as the only lake

with a significant increasing trend for the August monitoring events since monitoring started in 2008.

Porcupine, Sloans, Nowlans and Provost were observed to have decreasing trends. Monitoring began in

Raynards in 2013 which was an observed peak chlorophyll a concentration year in this lake and for many

others, and therefore the observed trend is potentially biased. Sloans is also observed to have a decreasing

trend, but chlorophyll a concentrations were the lowest observed in all lakes, and this trend is potentially

within the laboratory analysis margin of error. All other lakes did not have an observed significant

increasing or decreasing trend for chlorophyll a. It should be noted that for the trend interpretation for

chlorophyll a there was a change in laboratory methods in 2016 with most previous samples analysed

using spectrophotometric method and those from 2016 onward have been analysed using a fluorometric

method, and year-to-year compatibility may be affected.

Total Phosphorus & Orthophosphate

In the Carleton system, total phosphorus levels were down in 2018 from 2016 and 2017 with a few

exceptions. Increases from 2017 were observed for Hourglass (record high [0.118 mg/L]) and

Wentworth. In Parr there was no change from 2016 as 2017 data were not available for Parr and Ogden

In Vaughan, the level decreased from 2017, but was slightly higher than the 2016 level. Outside the

Carleton system, levels were down in Provost and Nowlans and very slightly up in Kegeshook and

Salmon River.

The tendency for total phosphorus levels along the main Carleton to decrease from upstream to

downstream remained consistent in 2018, except for a slight uptick from Raynards to Vaughan. Levels in

the tributary lakes, Porcupine and Sloans, remained relatively low. Phosphorus levels in Hourglass,

another tributary lake in the upper catchment, while high, remained below those observed in the

downstream Placides and Wentworth Lakes.

Total phosphorus levels reached an historic peak in Placides in 2011, and in downstream lakes on the

mainstream Carleton, peaks were observed in 2013 or 2014. Jim Mullen (personal communication)

identified that the August 23, 2011 sampling date followed a very heavy rainfall, which may have

affected the data. The Yarmouth Airport observed a 9 mm precipitation event on August 22, 2011

(https://climate.weather.gc.ca/).

Orthophosphate levels were down or unchanged in most lakes, with noteworthy increases only in

Hourglass and Salmon River and a more minor increase in Wentworth. Record highs were recorded from

Hourglass and Salmon River in 2018.

Mullen has noted that a former mink farm in the Hourglass catchment closed down about five years prior

to 2018. It is uncertain what, if any, effect this may have had on water quality in Hourglass.

This marks the second consecutive year-to-year decrease in both total phosphorus and orthophosphate in

Nowlans.

Spatially, orthophosphate decreased from Placides to Ogden, where it was barely measurable. The level

in Fanning was slightly higher, then decreased substantially downstream in Raynards and Vaughan.

When Mann-Kendall tests were applied to the entire database for the August sample events, beginning in

2008, Hourglass Lake is the only lake with an observed Mann-Kendall increasing total phosphorus

concentration trends for the surface composite samples. No significant trend was observed for

orthophosphate in Hourglass. Placides and Wentworth were observed to have significantly decreasing

total phosphorus concentration trends. Monitoring began in 2013 in Wentworth and similar but consistent,

statistically non-significant trends were noted in other Carleton mainstream lakes. These decreasing

trends are potentially biased due to the shorter monitoring period that began in a wet year (Appendix 9)

This and other potential factors are considered in the discussion (Section 4.1). Placides, with monitoring

starting in 2008, was the only lake with a corresponding decreasing trend observed for orthophosphate as

well. Sloans also has a decreasing trend, but the total phosphorus concentrations observed within the lake

https://climate.weather.gc.ca/

are typically an order of magnitude lower than other lakes in this study. Ogden was observed to have a

decreasing trend in orthophosphate with no trend observed for total phosphorus. All other lakes had no

statistically significant increasing or decreasing total phosphorus or orthophosphate trend observed for the

August surface composite samples, for the entire research period.

Orthophosphate to total phosphorus ratio

Dissolved inorganic phosphate (orthophosphate) is the form of phosphorus immediately available to

living things, but other forms of phosphorus can be converted into orthophosphate under certain

conditions, such as anoxia. High orthophosphate to total phosphorus ratios, combined with high

phosphorus levels are associated with high biological productivity that could cause a harmful algal bloom.

Arbitrarily, a ratio of greater than 0.5 or higher at a total phosphorus level of 0.02 mg/l or higher

(eutrophic trophic status) has been selected as a threshold for high biological productivity. On this basis,

Placides, and Nowlans would be flagged in 2018, and trends in Hourglass and Wentworth suggest the

need for continued observation.

Compared with 2017, the orthophosphate to total phosphorus ratio increased in Hourglass, Provost,

Nowlans, and Salmon River.

Colour

Most August surface water quality composite samples observed reduced colour in all lakes from which

data are available, compared to 2017. The only exception was the Vaughan surface composite sample,

which observed an increase of 3.5%. Lower colour tends to lead to higher transparency, and penetration

of light to greater depths, which leads to greater susceptibility to blooms.

Dry years (e.g., 2016 and 2018 with drought conditions) have noticeably lower colour than recent wet

years (e.g., 2013 and 2017). Table 3.1.1.1 illustrates this for 10 selected lakes with monitoring programs

with monitoring programs that extend back to 2008 or 2009. Comparing wet and dry year average colour

values wet years for all lakes observed higher colour values for wet years. Average normal year colour

values were also higher than average dry year values and comparable or higher than wet year average

values.

Table 3.1.1: August/Early September Average Surface Colour Results for Dry, Normal and Wet

Year Classifications (2008 to 2018)

Lake Missing Years

Dry Normal Wet Dry vs Wet

Average Colour (TCU) Difference

(TCU)

% difference (compared to

Dry)

Hourglass 2009 64.6 101.6 109.0 44 69%

Placides 2009 67.9 119.8 141.9 74 109%

Porcupine 2009 26.2 56.1 61.0 35 133%

Parr 2009, 2017 71.6 140.0 139.9 68 96%

Ogden 2009, 2017 47.6 92.3 95.9 48 101%

Fanning 2010, 2011 38.8 99.0 101.8 63 162%

Vaughan 2009, 2010 38.9 54.9 63.1 24 62%

Provost 2009, 2010 28.3 82.6 48.6 20 72%

Sloans 2008, 2010 14.6 20.1 21 7 48%

Nowlans

2009, 2011, 2014 64.1 64.5 81 17 26%

Wentworth 2008 to

2011 121.5 304.1 197 75 62%

Raynards 2008 to

2013 32.0 54.0 45.5 14 42%

Salmon River

2008 to 2014 53.2 - 99 46 87%

Kegeshook 2008 to

2013 40.7 60.8 56 15 38%

Notes:

Dry, normal and wet year classification details provided in Appendix 9

Dry - 2008, 2016 and 2018 Normal - 2010 and 2014

Wet - 2009, 2011, 2013, 2015 and 2017

The Mann Kendall trend analysis on the August surface composite samples did not observe a significant

increasing trend for colour in any of the lakes (Appendix 8). Only Wentworth and Raynards were

observed to have a decreasing trend for colour, but both monitoring programs began during the wet years

of 2013 and 2014, respectively, when the highest colour values were observed in many lakes and

therefore the trends are potentially biased (Appendix 8). Sloans also has an observed decreasing trend for

colour, but as with other water quality parameters it is the lowest colour lake within the monitoring

program (maximum 22.3 TCU). The other lakes with monitoring programs starting in 2008 did not

observe significant increasing or decreasing surface sample colour trends.

The spatial pattern in the Carleton system is similar to that in other years. Hourglass, Placides and Parr

show similar, high colour levels with a peak value in Wentworth, colour then decreases consistently

downstream, bottoming out in Raynards. It is worth contrasting the high colour levels in Placides and

Hourglass, where blooms were not noted despite high phosphorus levels, with the much lower colour

levels and not biologically limiting phosphorus concentrations in Nowlans. Like Sloans, low colour

levels in Porcupine make it potentially vulnerable to blooms, should nutrient levels be sufficient.

Secchi Disc Depth

Secchi depth tends to be inversely related to colour, turbidity, and level of suspended particles in the

water.

Given the consistent decrease in colour from 2017 to 2018, which may be related to drier conditions with

reduced surface water runoff, Secchi depth transparency measurements would be expected be uniformly

increased (deeper), which were observed in all lakes except in Vaughan. However, Vaughan, Porcupine,

Ogden, Provost, and Nowlans all had decreased Secchi depths than those observed in 2017, and levels in

Hourglass and Parr were unchanged from 2017.

The Mann-Kendall trend analysis (Appendix 8) for Secchi depths observed significant increasing (lower

depths and greater transparency) trends for Wentworth, Raynards, Sloans, and Provost. Wentworth and

Raynards and Salmon River Secchi disc measurements started in 2013 and 2014, respectively, when peak

colour values were observed in these lakes and many others in the study and are therefore potentially

biased. Sloans has the lowest observed colour and highest Secchi disc depth readings in the study and as

with other parameters the trend may be within the margin of measurement error and therefore not

significant. Provost has observed an increasing trend in Secchi disc depth along with a decreasing

chlorophyll a concentration and no trend associated with colour since monitoring began in 2008.

Total Nitrogen

August surface composite sample total nitrogen levels were slightly down from 2017 in all lakes for

which data were available, except for Hourglass and Wentworth, which observed increases.

The historically decreasing trend in total nitrogen levels from upstream lakes to downstream lakes is still

present but has weakened from earlier years. The level in Wentworth was slightly higher than that in

Placides and the lowest level was observed in Raynards. However, there was a decided decrease between

Wentworth and Parr, with a similar consistent decrease between Fanning and Raynards.

As with total phosphorus levels, total nitrogen reached an historic peak in Placides in 2011, and in

downstream lakes on the mainstream Carleton, peaks were reached in 2013 or 2014.

The Mann-Kendall trend analysis for total nitrogen in the surface composite samples observed significant

decreasing trends in Hourglass and Placides and no significant increasing or decreasing trends in the other

lakes. Nowlans due to sample interference during analysis did not have sufficient total nitrogen samples

(min. 4) for the Mann-Kendall assessment method.

Surface August nitrate levels were below detectable limits in 2018 in all lakes. Since 2013, this has been

more the rule than the exception.

pH

August surface laboratory measured pH levels were up from 2017 in all lakes from which data were

available, except for Vaughan (no change). Provost showed a slight decrease from last year’s composite,

but a rise from last year’s surface laboratory pH. Nowlans showed a very appreciable rise (from 7.3 to

9.1).

Surface Temperature

Surface temperature is more affected by time of day and current weather conditions than many

parameters, but prevailing summer temperatures also play an important role. Surface temperatures were

up over 2017 in all lakes but Wentworth, Fanning, and Raynards.

In the longer term, water temperatures appear to be rising. The summer of 2015 was hot and record high

surface temperatures were recorded from many lakes.

The Mann-Kendall analysis of the full August temporal dataset of the surface temperature readings for all

lakes observes significant increasing temperature trends in Hourglass, Placides, Ogden and Sloans. No

significant increasing or decreasing trends were observed in the other lake datasets.

3.2 Seasonal Variation in Trophic Condition Parameters Water quality data were collected in May, August and October in seven selected lakes in Yarmouth

County, as well as in July for certain lakes in 2013 and 2014. Bar graphs summarizing these seasonal

variations are given in Appendix 3 and are considered briefly here.

Spring sampling only started in 2013 or 2014 and for the Mann-Kendall test spring assessments, Sloans

and Kegeshook were observed to be thermally stratified for many of the sample events and therefore were

potentially not in a completely mixed state when the surface sample was collected and may not represent

average lake water quality. As such, the trend analysis results for Sloans and Kegeshook may not be

applicable and are therefore not included in the results discussion in the following sections. Salmon River

did not have enough samples (less than four) to conduct a Mann-Kendall trend analysis for all parameters

assessed.

Fall sampling for Parr, Fanning, Sloans and Vaughan began in 2009 with Raynards starting in 2014, and

Kegeshook and Salmon River beginning in 2015. Sloans for the fall sample events was also observed to

be thermally stratified for the 2013 to 2017 sample events and therefore Mann-Kendall trend analysis may

not be applicable as sample results would potentially not represent completely mixed lake conditions.

Chlorophyll a

Except for low-colour, oligotrophic Sloans, chlorophyll a levels tend to decrease sharply between August

and October. As spring and fall are typically less biologically productive periods, chlorophyll a

concentrations when compared to the summer season results would be expected to be lower. In 2018,

October levels in Vaughan and Salmon River were only slightly below those in August. Aside from

Sloans, peaks were the norm in the summer. Vaughan was a notable exception, with the April 30 reading

being the highest.

Spring chlorophyll a levels were up from 2017 in all cases, as were summer levels except in Vaughan and

Salmon, where they were lower. Autumn levels were increased from 2017 except in Parr, Kegeshook and

Salmon, where they were slightly lower.

Only Fanning observed a decreasing spring Mann-Kendall test chlorophyll a concentration trend, even

with a mix of wet and dry years over that period (Appendix 8).

No chlorophyll a concentration increasing or decreasing Mann-Kendall test trends were observed for the

fall monitoring events. Sloans was observed to be thermally stratified for the 2013 to 2017 sample events,

and therefore the surface samples collected may not represent average lake water quality conditions.

As with the August results chlorophyll a trend analysis the change in lab analysis methodologies in the

2016 season should be taken into account.

Total Phosphorus

High October levels for total phosphorus have been the norm most years, except in Sloans, and probably

reflect turnover of more nutrient-rich bottom water and less absorption by plants and phytoplankton, in

light of lower temperatures and shorter photoperiods. This year, by contrast, the only lake which did not

show an autumn increase was Vaughan. Summer minima, the most common pattern historically, were

also absent from Parr, which had its annual minimum in the spring, and Kegeshook, and Salmon, which

both had similar spring and summer levels.

Along the mainstem of the Carleton River, seasonal total phosphorus levels were down from

corresponding 2017 levels, except for the October reading from Parr, where there was an increase. Sloans

and Salmon showed similar increases in October over those observed in 2017.

The Mann-Kendall test results for the spring total phosphorus concentrations calculated a decreasing

trend in Vaughan with the program starting in 2014. An increasing spring total phosphorus trend was

observed in Sloans, but the observed concentrations are the lowest for the monitoring program and the

trend may be within the range of measurement error. The fall total phosphorus concentrations had Mann-

Kendall test decreasing trends for Parr, Fanning and Vaughan with all programs starting in 2009.

Orthophosphate

Orthophosphates levels were down from 2017 in most lakes, with a notable exception of the October

readings in Parr and Sloans and the August level in Salmon.

Orthophosphate: total phosphorus ratios were down with some exceptions, which included August

readings in Salmon and October results in Parr and Sloans, all of which had increases.

Lake Vaughan had a Mann-Kendall test decreasing orthophosphate trend for the spring sample events,

which corresponds with the decreasing total phosphorus trend. Parr, Fanning and Vaughan were all

observed to have decreasing orthophosphate trends for the fall sample events, which correspond with the

decreasing total phosphorus trend.

Colour and Secchi Disc Depth

Colour levels in May were up from 2017, and down in August and October, in all cases except in

Vaughan, where the spring level was slightly lower and the August level slightly higher than in 2017.

No spring colour trends were observed in the monitored lakes. Parr, Fanning and Vaughan were observed

to have decreasing colour trends for the fall sample events.

No trends were observed with respect to Secchi disc depths for the spring program. Increasing Secchi disc

depth trends were observed for Parr, Fanning, Raynards and Vaughan for the fall sample events

Total Nitrogen & Nitrate-Nitrite

Total nitrogen levels were down from 2017, except for increases for the October levels in Parr, Fanning,

and Sloans, and for the May level in Kegeshook. Levels were highest in October except in Sloans,

Vaughan, and Kegeshook where spring levels were highest. Kegeshook, Raynards, and Sloans showed

August minima.

No increasing or decreasing total nitrogen trends were observed for the spring sample event lakes.

Vaughan was the only lake monitored with a significant decreasing fall total nitrogen trend.

There were insufficient data to detect any seasonal patterns with regard to nitrate-nitrite because most

levels were below the minimum reportable limit.

pH

pH was seasonally low in May in all lakes, and peaked in the summer, except in Raynards and Sloans

(where August and October levels were similar) and Vaughan (October peak) Spatially, pH again tended

to climb downstream from Parr to Raynards, which receives inflow from Sloans.

3.3 Surface and Bottom Comparisons of Trophic Parameters Surface and bottom sampling was done only in August when stratification is normally observed.

Appendix 4 provides graphical comparisons. Total phosphorus is given the most attention since it is

typically the chemical parameter most strongly linked to trophic status. The sample collected from

Kegeshook at depth was contaminated by bottom sediments and is not included in the assessment.

Bottom total phosphorus concentration increases and increased values compared to surface due to thermal

stratification were noted in Hourglass, Placides, Porcupine, Fanning, and Nowlans compared to 2017.

Nowlans was observed for the first time to have well oxygenated waters near the bottom (>8 mg/L).

Wentworth and Sloans showed minor increases from 2017 in bottom total phosphorus and weak thermal

stratification. Stratification for Vaughan and Provost were clear, but both lakes showed decreases in

bottom total phosphorus concentrations from 2017. Provost had well oxygenated waters at depth (>8

mg/L), which could have contributed to the reduced total phosphorus concentration. Raynards showed a

similar decrease but no thermal stratification. Salmon and Parr also showed no thermal stratification.

Orthophosphate patterns were similar, except in Sloans, unchanged from 2017 but with larger increase

with depth than for total phosphorus, and Salmon, which showed marked increases in both surface and

bottom orthophosphate concentrations in 2018 over 2017.

Orthophosphate: total phosphorus ratios in bottom waters were higher than the ratios in surface waters for

Hourglass, Porcupine, Ogden, Fanning, Vaughan, and Provost compared to 2017. The ratio was lower in

Nowlans in 2018 compared to 2017. The reduced ratio in Nowlans could be due to the presence of well

oxygenated waters at depth.

Increases in bottom total nitrogen levels combined with increased concentrations for bottom samples

compared to surface were noted in Hourglass, Placides, Porcupine and Fanning. Nowlans also showed a

very marked increase in bottom total nitrogen concentration compared to all other lakes, and surface total

nitrogen was not measurable due to sample interference. It is important to note that Nowlans was

observed to have well oxygenated waters at depth in 2018, which could have contributed to the higher

value. There was similar concentration increases with depth but decreases in bottom total nitrogen

concentrations from 2017 in Sloans, Vaughan and Provost. Bottom total nitrogen concentrations in 2018

were the highest observed for Hourglass, Porcupine, and Nowlans for the monitoring program.

Colour levels tended to be considerably different potentially due to thermal stratification than in 2017,

with higher bottom levels the norm compared to surface composite results. In contrast to surface trends,

bottom levels were increased compared to 2017 in Hourglass, Placides, Porcupine, Fanning and Nowlans,

with the highest observed values for the monitoring program in Hourglass and Nowlans in 2018.

Increased colour levels with depth were observed in Vaughan and Provost, but bottom colour levels were

down from 2017.

Major contrasts between surface and bottom lab pH were noted in Vaughan and Provost (where bottom

pH levels were higher) and Nowlans (where bottom pH was considerably lower) in 2018.

3.4 Spring Investigation of Inlet, Mid-Lake, and Outlet Parameters on Parr and

Fanning Earlier reports (Taylor, 2010 and Brylinsky, 2011) indicated some anomalous readings from inlets and

outlets in Parr and Fanning. The total phosphorus anomalies were particularly striking. Taylor’s 2010

paper noted that phosphorus levels at the outlet from Parr were higher than levels at any inlet, and that

mid-lake levels were highest of all on October 22, 2009. The level in Fanning outlet was also reported as

slightly higher than at the mid-lake stations on October 14, 2009. Brylinsky’s 2011 report noted a very

high total phosphorus level on September 30, 2010 at Station IN1, the Carleton River inlet into the Lake

Fanning. Both reports also consistently indicated phosphorus levels at Parr station INC similar to, but

slightly lower than those at INA, the Carleton River inlet into Parr (See Figure 3.4.1.). This is at the

mouth of a highly intermittent waterway on the northeast shore of the lake. On July 12, 2016, Nguyen

Quang (2016) also noted relatively high levels of phosphorus at or near the inlet into Fanning from Lower

Crawley Lake (Station IN2 in Taylor, 2010). The results of these studies led to continued monitoring at

these sites to assess changes in water quality.

Consequently, Sollows (2017) investigated late August parameters at selected inlets and other locations

on Parr and Fanning. Levels of phosphorus and orthophosphate were slightly higher at Parr inlet INC

than in INA; there was no appreciable flow at INC, so nutrient loading would be expected to be

substantial only during runoff events. In Fanning. phosphorus was higher at IN-1, the main Carleton

inlet.

Stantec (2017) noted a higher phosphorus concentration for Parr at INA in comparison to the other two

inlets, but the concentration at the outlet was the highest, indicating potential internal loading, whereas

total nitrogen levels were highest at the secondary inlets. In Fanning, the pattern was unremarkable, with

both phosphorus and nitrogen highest at IN1.

Figure 3.4.1: Map of Parr showing three inlet stations, mid-lake station (DS1), and Outlet station (OL1) From Brylinsky (2011)

Figure 14.2: Map of Parr showing three inlet stations, mid-lake station (DS1), and Outlet station (OL1) From Brylinsky (2011)

In 2018, on the advice of colleagues from the Committee and Stantec, investigations were continued, but

in the spring, when higher post-winter flows would better indicate levels of nutrient contribution from

various sources. While highly desirable, it was not practicable to measure stream cross-sectional areas

and velocities. Data were collected from four inlets on Parr (A point in the channel linking Petes Lake

and Parr was added.), three inlets on Fanning, both deep stations, and both outlets.

Results since 2009 are summarized in Appendix 5, and those from 2018 follow.

Table 3.4.1: Nutrient and Colour levels from Inlets, Deep Stations, and Outlets of Parr and

Fanning

Station Date Total P (mg/l) OrthoP (mg/l) Total N (mg/l) Colour (TCU)

Parr INA Apr. 29/18 .027 .012 .26 104

Parr INB Apr. 29/18 .022 .008 .37 104

Parr INC Apr. 29/18 .039 .012 .30 90.1

Parr Pete’s Apr. 29/18 .007 .003 .17 32.9

Parr Deep Apr. 29/18 .026 .010 .25 97.7

Parr Outlet Apr. 29/18 .023 .010 .24 86.9

Fanning IN1 Apr. 29/18 .021 .008 .22 76.8

Fanning IN2 Apr. 29/18 .009 .004 .19 55.8

Fanning IN3 Apr. 29/18 .006 .003 .18 34.4

Fanning Deep Apr. 29/18 .020 .007 .22 68.0

Fanning Outlet Apr. 29/18 .018 .006 .21 65.9

In Parr, the highest levels of total phosphorus and orthophosphate were again recorded at INC, followed

by INA, mid-lake, and the outlet. Levels at INB were slightly lower and those at the channel from Petes

were much lower (less than one-third the level at INB). Total nitrogen levels were highest at INB,

followed by INC. INA, mid-lake, and the outlet. The level in the channel from Pete’s was, once again,

the lowest, at just under three-quarters the outlet level.

Colour levels were highest at INA and INB, followed by mid-lake, INC, and the outlet. The colour in the

channel from Petes was only three-eighths that at the outlet

In Fanning, the patterns of total phosphorus and orthophosphate were as expected: highest at IN1,

followed by mid-lake, the outlet, IN2 and IN3 with levels at IN2 and IN3 roughly one-half and one-third

those at the outlet, respectively. Total nitrogen levels at IN1 and mid-lake were the same and slightly

lower at the outlet. Levels at IN2 and IN3 were 80%-90% those at the outlet.

Spatial patterns in colour in Fanning followed those for phosphorus, with levels at IN2 and IN3 roughly

85% and 50% those at the outlet, respectively.

3.5 Cyanobacterial Abundance, Composition and Presence of Toxins Appendix 6 provides cyanobacterial counts, percent species composition, and microcystin concentrations

by lake and year. This year, for the second time, sampling was also done in late June-early July, when

blooms tended to be maximal.

Given the method of sample collection, the raw cell counts cannot be compared with much rigour. In

2018, high levels (over 2,000 cells/ml) were recorded from Provost, Nowlans, Hourglass, Placides Parr,

Fanning, and Sloans in July, and from Nowlans and Ogden in August.

Compared with 2017, July counts were up in six of 12 lakes for which data are available, and there was

no change in Salmon (zero count each year). August counts were up in seven out of 12. Only Placides

and Sloans showed year-to-year increases for both months. There were no comparable 2017 data for

Provost and Nowlans, and no comparable August data for Kegeshook and Salmon. There were major

decreases for July in Raynards, Vaughan, and Kegeshook and major increases in Hourglass, Parr and

Fanning. The August decreases in Provost, Hourglass, and Fanning were over an order of magnitude, as

was the increase in Nowlans. The August count from Ogden set a record high. Given only two years of

data from July, looking for July records is premature.

In 2017, July counts were higher than those for August in seven out of 10 lakes for which data were

available; in 2018, July counts were higher than in August for eleven out of 14. In Wentworth, August

counts were higher for both years. Both Ogden and Salmon showed increases from July to August in

2018.

For the first time in recent years, the writer received no reports of blooms from Vaughan and Raynards.

On the other hand, severe blooms were observed in Fanning and Ogden from June till mid-October, and

the blooms in Parr and the upper end of Wentworth were observed as well.

Microcystin concentrations, if present, were below detectable levels in all lakes, including Nowlans, for

the second consecutive year.

4. Discussion Chlorophyll a levels in the water column are a conveniently quantifiable indicator of phytoplankton

levels. High levels of chlorophyll a reflect levels of all phytoplankton species, not just

cyanobacteria. Cell counts are also helpful, but given sampling methods used, only provide order-of-

magnitude level comparisons.

This section will assess and provide potential hypotheses for changes between years and locations in

surface water quality.

4.1 Spatial and Temporal Considerations in the Carleton Catchment This section assesses the temporal and spatial variation in August surface chlorophyll a readings, as a

reflection of various environmental parameters, most notably nutrients and colour (which affects the

depth to which light can penetrate). Spatial comments focus on trends along the mainstem of the Carleton

River.

Spatial trends in chlorophyll a along the Carleton remained weak for the third consecutive year in a row.

The highest reading in the Carleton catchment came from Hourglass, a headwater tributary lake, and the

second highest was observed in Ogden, for the first time since 2011. Levels were up from 2017 to

varying degrees for all lakes in the Carleton catchment, except for Hourglass and Vaughan. Hourglass is

the only lake that has observed an increasing August sample event chlorophyll a concentration trend

(90% confidence interval; Mann-Kendall), which coincides with an increasing total phosphorus

concentration trend. Of lakes with monitoring programs beginning in 2008/09 Porcupine is the only lake

with a statistically significant decreasing trend with no trends observed for other nutrient parameters.

Spatial and temporal trends for both total phosphorus and orthophosphate were similar to previous years,

with the lowest concentrations in Raynards, as was the case in 2017. However, it is worth discussing a

few lake-specific anomalies.

Besides Raynards, there was a surface composite sample orthophosphate minimum concentration

observed in Ogden, which coincided with a severe algal bloom. The bloom activity potentially absorbed

the dissolved orthophosphate, reducing the concentration within the water column.

Both total phosphorus and total nitrogen concentrations were higher in Hourglass and Wentworth than in

2017. There are a variety of potential sources in the small catchment around Hourglass, including a

former mink farm, a fish hatchery, and cleared land (Stantec, 2017), as well as a potential groundwater

spring. In Wentworth, besides upstream sources, there is a substantial silviculture operation (Stantec,

2017). Furthermore, Google Earth scrutiny shows extensive clearcutting immediately west of Highway

340, to the west of Wentworth, and a number of new cottage developments. This would potentially

account for some of the increase in nutrients in Wentworth, but the extent of this contribution is difficult

to quantify. However, the August 2018 total phosphorus is not the maximum surface concentration

observed in this lake since monitoring began in 2013.

The increase in chlorophyll a levels in all lakes but Hourglass and Vaughan contrasts with the widespread

decrease in nutrients between 2017 and 2018. However, the decrease in colour from 2017 in all lakes,

except Vaughan, would cause enhanced light penetration. This environment would be potentially more

conducive to increased biological activity and chlorophyll a production in all lakes where nutrients were

not limiting. The record high chlorophyll a reading from Wentworth potentially reflects a rise in nutrients

combined with a decrease in colour. Water temperatures, as indicated by surface temperatures, were also

up in a number of lakes (Hourglass, Wentworth, Fanning, and Raynards excepted) from 2017 and

potentially played a role in the increased chlorophyll a concentrations.

The decreases in chlorophyll a in Hourglass and Vaughan from 2017 were substantial (down by 52% and

80%, respectively) and are difficult to explain. The slight increase in colour in Vaughan would not be

expected to lead to the observed large decrease in chlorophyll a. The nutrient parameters in Hourglass

were at concentrations that would be not considered limiting to biological activity in 2018. The

Hourglass August Mann-Kendall trend results for chlorophyll a and total phosphorus both were

calculated as significantly increasing and was the only lake in this study with increasing trends for these

parameters.

Both total phosphorus and total nitrogen August concentrations peaked in Placides in 2011, and in the

lower lakes along the Carleton in either 2013 or 2014. As presented in Appendix 9, 2011 and 2013 were

wet years with above climate normal total precipitation amounts for May to July. The year 2014 was

within -3% of the climate normal total precipitation amount for the May to July period. The trend for

orthophosphates is less consistent. These years would be expected to have high surface water runoff

volumes entering the lake system. The heavy spring flood of 2015 would potentially have transported

nutrients from upstream parts of the catchment and is also classified as a wet year (Appendix 9). The

Mann-Kendall trend analysis indicates for many of the lakes that there are no significant increasing or

decreasing trends in nutrient concentrations in the August surface composite samples since monitoring

began in 2008. Placides is the only lake with a decreasing Mann-Kendall test trend for the August results

for these three parameters with monitoring starting before 2013/14. Hourglass has an observed increasing

trend in total phosphorus concentrations.

The following are a number of land use activity changes and general climate observations that have

occurred within the watershed that potentially contributed to observed nutrient concentration trends:

• In January 2013, Fur Industry Regulations went into effect, which included discharge criteria for

surface water runoff from fur farms. Many fur farms employed mitigation measures to manage

surface water runoff quality, including nutrient concentrations.

• In recent years (2014 to present), fur pelt prices have been relatively low, and a number of fur

farms have closed within the watershed. Closed farms would not be generating new animal

wastes.

• 2016 and 2018 were relatively dry spring and summer periods (Appendix 9) that would have had

lower surface water runoff amounts, potentially causing reduced nutrient and colour loading.

The four lakes outside the Carleton River basin show a variety of conditions.

The level of chlorophyll a in Nowlans has historically been the highest of any lake, which has coincided

with low colour and high phosphorus levels. In 2018, chlorophyll a was down slightly from 2017,

continuing a declining trend that began in 2015. The Mann-Kendall trend analysis observed a significant

decreasing trend since August surface water composite samples were first collected in 2008 (Appendix 8)

with no significant trends for nutrient parameters. The increase in temperature and decrease in colour

from 2017 may help explain why the decrease in chlorophyll a was so slight.

The chlorophyll a level in Provost was slightly down from 2017, as were nutrient levels. The decrease in

colour was considerable, but neither that nor the increase in temperature seemed to have much effect.

Phosphorus levels had decreased to 0.009 mg/l, similar to those observed in Raynards and Vaughan,

which is in the oligotrophic (low nutrient concentration) range. A decreasing chlorophyll a concentration

trend and increasing Secchi disc depth trend were observed for the August sample events.

The increase from 2017 in chlorophyll a in Kegeshook probably reflects lower colour and higher water

temperatures. Nutrient levels were all slightly down.

Chlorophyll a in Salmon was up by 132% over 2017; phosphorus was slightly up and total nitrogen down

by about 25%. The decrease in colour (from 108 TCUs to 53 TCUs) is a potential reason for the

increased biological activity, and supports the hypothesis that colour limited production in 2017. There

was also an increased surface temperature from 2017 of over 4o, which would potentially enhance

chlorophyll a production.

4.2 Seasonal Variation and Surface and Bottom Comparisons of Trophic Parameters

These issues are interrelated and therefore are considered jointly.

Spring chlorophyll a levels were consistently up from 2017 in the lakes studied. Lower phosphorus and

orthophosphate levels and increases in spring colour, except in Raynards (essentially unchanged) and

Vaughan (slightly down) were also observed. Total spring nitrogen was also down in the study lakes,

except in Kegeshook (increase) and Salmon (essentially unchanged). Slight surface temperature increases

from 2017 were noted from Raynards, Kegeshook, and Salmon; elsewhere, temperatures were down. The

increase in spring chlorophyll a may reflect the relatively high levels of nitrogen and phosphorus noted

the previous autumn more than the relevant parameters at the time of measurement, but other factors may

also be behind the increases. Vaughan has an observed decreasing trend for total phosphorus and

orthophosphate for the spring events.

Summer chlorophyll a concentration maxima were observed in all lakes except Sloans (October

maximum) and Vaughan (spring maximum). The Sloans and Vaughan maximum concentration seasons

have been observed in previous years with Vaughan having a similar spring maximum in 2016, when

there was a severe summer drought season.

The low winds and high temperatures of summer tend to lead to thermal stratification in most lakes, with

warm upper and colder lower layers. This separation into layers leads to chemical differences, including

lower oxygen levels in deep water. As oxygen is depleted, phosphorus deposited on the bottom can

become mobilized.

The summer of 2018 was hot and dry; in spite of these, differences between surface and bottom

temperatures were down from 2017 in most lakes. Only in Placides, Porcupine, and Nowlans were the

differences between surface and bottom temperatures greater than in 2017.

Temperatures at surface and bottom were the same in Wentworth, Parr, Raynards, and Salmon, and

differences in Fanning, Kegeshook, and Vaughan were below 5Co, so little or no stratification would be

expected in these lakes.

Uniform temperature indicates well-mixed water. As expected, there were negligible differences in

nutrient levels and colour at surface and bottom in the four lakes with uniform temperature distribution.

Contamination by bottom sediment in the bottom water sample in Kegeshook made comparison to

surface problematic and the sample was removed from the assessment. In Fanning and Vaughan bottom

nutrient and colour levels were several times those of surface levels; the contrast was particularly high for

orthophosphate concentrations (25 times surface levels in Vaughan and 15 times in Fanning).

In the lakes with stronger differences in temperature between surface and bottom, bottom nutrient

concentrations were commonly multiple times higher than surface levels. There were exceptions for total

phosphorus in Provost, and for total nitrogen and colour in Ogden and Sloans, where differences between

surface and bottom were minor. As in Fanning and Vaughan, the greatest contrasts tended to be for

orthophosphate, which may reflect mobilization of phosphorus from bottom sediments. There were

exceptions only in Nowlans, where the difference was still seven-fold, and Ogden, where surface

orthophosphate was not measurable, possibly because of uptake present an observed algal bloom.

Nowlans for the first monitoring season since 2008 was observed to have well oxygenated waters at

depth.

October chlorophyll a levels from the seven Yarmouth County lakes were up from 2017 except in Parr,

Kegeshook, and Salmon, and differences in Kegeshook and Salmon were minor. As expected, they were

down from summer levels, except in Sloans. Lower water temperatures and much shorter photoperiods

would potentially account for this.

Given the stratification encountered during the summer, the autumn turnover would bring nutrient-rich

water to the surface from the lower layers. This conveniently explains the high October levels of

nutrients in all lakes. Vaughan was the exception: August and October levels of all nutrients were

similar. Also, in Salmon, orthophosphate levels remained unchanged. While colour should show an

October increase for similar reasons, there was a substantial decrease in Vaughan and smaller decreases in

Raynards and Kegeshook. Increased autumn runoff from low-nutrient, low-colour, well-mixed Raynards

may help explain the pattern in Vaughan. Parr, Fanning and Vaughan have observed significant

decreasing trends for total phosphorus, orthophosphate and colour for the fall sample events with a

corresponding increased Secchi disc depth trend with these monitoring programs beginning in 2009.

4.3 Spring Investigation of Inlet, Mid-Lake, and Outlet Parameters on Parr and

Fanning The nutrient and colour dynamics acting in Parr and Fanning will be considered in light of historical

data, and the data most recently collected on April 29, 2018. The 2018 data are the first collected in

the spring, when flows are high and most likely to carry nutrients accumulated through the winter

from the watershed.

A number of anomalies were noted from earlier studies in both lakes and following these up was

deemed prudent.

Parr

In Parr in October 2009, the reported total phosphorus level in mid lake was extremely high. The

orthophosphate and nitrogen levels were less extreme, but still higher than at any of the inlets.

Nutrient levels at INA, the mainstem of the Carleton River, were higher than at the other inlets, but

the data indicated potential additional sources of nutrients to the lake other than INA.

The pattern in September 2010 suggested that INA transported the highest level of phosphorus and

orthophosphate. The total nitrogen at INC was somewhat higher, but this is a very low-volume,

intermittent stream. The August 2011 pattern was similar, except that inlet INB had the highest total

nitrogen concentrations, and orthophosphate levels were highest at mid-lake.

Nutrient levels at the outlet were lower than at mid-lake, except for the August 2011 total nitrogen,

which was high at the outlet. The overall picture suggested that there were potential substantial

additional nutrient sources in Parr, in addition to the upstream Carleton River.

The August 2016 survey observed higher levels of phosphorus and orthophosphate in INC and higher

levels of nitrogen in INA. Mid-lake levels were slightly lower to unchanged, in the case of nitrogen,

and had further decreased at the outlet. In August 2017, total phosphorus and orthophosphate levels

were higher in INA, but total nitrogen was higher in INB and INC. Total nitrogen levels were lower

at the outlet, but both phosphorus and orthophosphate were recorded at higher concentrations than at

any inlet.

The 2018 survey showed phosphorus and orthophosphate patterns similar to those in 2016 and once

again, INB had the highest total nitrogen levels. Levels of all nutrients in the channel connecting

Petes Lake to Parr were much lower than the other sites.

The streams whose mouths are inlets INB and INC have a considerable area of silviculture in their

catchment areas. This may explain in part the relatively high nutrient levels reported from them.

They are also considerably lower in volume than INA, so their specific contributions to nutrient

loading are potentially minor. Additional point sources of nutrient loading may also exist around the

lake perimeter, but they have not been observed to date.

Cleveland has pointed out that a popular bass-fishing tournament may lead to stirring of sediments

and bottom waters via motorboat propeller agitation, which would add to internal phosphorus

loading.

Colour in the three Parr inlets was high, but the mid-lake level tended to be lower than that at INA.

The only time when mid-lake colour was higher was October 2009. As with nutrients, colour levels

in the channel from Petes Lake were considerably lower than those in Parr at the mid-lake site. The

outlet colour was typically lower than at mid-lake

Fanning

In Fanning, the main Carleton River inlet, had consistently higher levels of total phosphorus,

orthophosphate, and total nitrogen than the two secondary inlets. Mid-lake levels tended to be lower

than those at IN1 except for the August 2011 total phosphorus and the August 2016 total nitrogen,

which were slightly higher. Again, in most cases, levels at the outlet were similar to or lower than

those at mid-lake, except in October 2009, when both nitrogen and phosphorus were somewhat up at

the outlet, and August 2017 when there was a slight uptick in orthophosphate.

While additional nutrient loading may occasionally have occurred in Fanning, it appears to be less

frequent than in Parr.

In Fanning, colour tended to be highest at IN1 (mainstem Carleton River inlet); levels in the

secondary inlets tended to be lower than at mid-lake and only in September 2010 was colour higher

at the mid-lake site in comparison to IN1. As with Parr, levels at the outlet were consistently lower

than at mid-lake.

4.4 Cyanobacterial levels, species, and toxins As earlier noted, comparisons of algal cell counts must be interpreted with caution because of the

collection method. Given the decrease in colour levels, counts would be expected to be up from 2017.

This was the case in a bare majority of lakes each month and only in Placides and Sloans were there

consistent increases over 2017. Lower phosphorus levels may help explain the August decreases in

Porcupine and Fanning, but not in Provost and Hourglass, and there are insufficient data for Parr.

The more consistent tendency for counts in July to be higher than those in August may be explained by

several possibilities: Shortly after the summer solstice when photoperiods are maximal; early in the

season when nutrient concentrations may be less depleted. Blooms also sometimes crash as the season

progresses, leading to more inconsistent counts later in the summer.

August cell counts were higher than for July for Wentworth, Ogden, and Salmon. Both Wentworth and

Salmon are relatively high in colour and decreases in colour through the season and corresponding dry

conditions (Appendix 9) may have been a cause.

The high cyanobacterial cell count reported from the June 27, 2017 sample from Kegeshook was not

repeated in 2018. This was a localized phenomenon but does speak to the potential vulnerability of

Kegeshook to cyanobacterial blooms.

Zero cell counts were reported from July in Salmon (as in 2017) and Wentworth, and for August in

Provost, Porcupine, and Parr.

Continued sampling both in early July (when blooms normally peak) and late August (when summer

conditions of stratification tend to peak) remains advisable, if budget permits. Targeted sampling of

occurring algal bloom events would also be of interest.

As in 2017, no measurable level of microcystin was detected in Nowlans Lake in 2017. In previous

years, measurable microcystin was the norm. It is potentially worth testing for microcystin again in 2019

in Nowlans, but given the cost involved, the consistent unmeasurably low levels in other lakes, and

overall trends, continued testing in the other lakes is not recommended.

Identified cyanobacteria consisted of sixteen genera, of which Anabaena, Pseudanabaena, and

Gomphosphaeria predominated, in that order. Anabaena is a microcystin producing genus. Chi-squared

tests showed significant variations among years (p<0.002) and lakes (p<0.001). Since sampling was

conducted in different months, from July to November, a chi-square test was also conducted to tests

species composition among months, but the probability of independence (p<0.1) is too high to be

conclusive.

For the comparison among years, the genera accounting for most of the deviation from expectation were

Planktolyngbya, Apahnizomenon, Pseudanabaena, and Eucapsis, which account for half of the total

variation. The first two genera appear to be decreasing in relative abundance, and Eucapsis seems to be

increasing. There is no overall observable trend with Pseudanabaena. Also, the change for Eucapsis is

due to a large extent to the recent inclusion of Salmon River Lake in the sampling, so there may or may

not be a trend with this genus. In terms of years, 2008, 2009, and August 2018 accounted for just over

half the deviations from other years. Part of the atypical pattern from 2009 may be because sampling was

done almost entirely in October instead of July and August, which was later than usual and would be

problematic for year-to-year comparisons due to seasonal differences.

Among lakes, only three genera, Eucapsis, Gomphosphaeria, and Microcystis accounted for just of half

the deviations from previous years. Three lakes, Nowlans, Salmon, and Sloans accounted for over half

the deviations. Salmon is a more recent addition, though, and this would help explain part of its

difference from expectation. Otherwise, species composition in Sloans and Nowlans consistently tend to

show similarities which are not shared with other lakes. These lakes also have some of the lowest colour

values within the monitoring program. In particular, Anabaena, which commonly predominates in other

lakes, is rarely abundant in Nowlans and has not been recorded in Sloans; Gomphosphaeria, on the other

hand, tends to be abundant in both lakes but not in others, and Microcystis is consistently abundant only

in Nowlans and is a producer of cyanotoxins.

4.5 Calculated Carlson Trophic State Indices

Relevant data and histograms are given in Appendix 7.

The Carlson Trophic State Index (TSI) is an imperfect, but convenient, way of estimating the trophic

health/status of a lake. The index is based on levels of chlorophyll a, total phosphorus, and Secchi depth;

as chlorophyll a and total phosphorus increase, so does the TSI value, and as Secchi depth increases, the

TSI value decreases, since it is based on the assumption that transparency is based primarily on plankton

density. Hence, a high TSI implies a higher level of eutrophication and a system not biologically limited.

No single number can adequately reflect the trophic health of a lake. The utility of the Carlson TSI in

some of the lakes under study is further compromised by high colour levels. Colour reduces both Secchi

depth and productivity. Here, this has been addressed historically by dropping Secchi depth from the

calculation in any lake where the colour was higher than 125 TCU, because above this level, colour seems

to have a negative effect on cyanobacteria abundance and chlorophyll a levels. In 2018, only the summer

level in Wentworth was over this threshold, so Secchi depths were ignored in this case.

Carlson TSI values below 40 are considered to reflect oligotrophic situations (low nutrient); mesotrophic

lakes have indices between 40 and 50; eutrophic lakes between 50 and 70, and hypereutrophic lakes have

indices over 70.

On this basis, Sloans was as in previous years classified as oligotrophic. Porcupine rose from oligotrophic

in 2017 to mesotrophic in 2018. Other lakes rating as mesotrophic in August 2018 include Kegeshook,

Salmon, Raynards, Provost, Fanning, and Vaughan. Vaughan’s status was down from eutrophic in 2017,

and Fanning’s status was close to eutrophic in 2018. Five other lakes, Hourglass, Placides, Wentworth,

Parr, and Ogden were all classified as eutrophic, with the values for Parr and Ogden considerably lower

than those of the other three. Placides’ status was close to the hypereutrophic range limit, and Nowlans

remained in the hypereutrophic category.

In most lakes changes in August TSI values were minor. The consistent lower colour levels potentially

led to an increase in TSI values with increased biological activity (chlorophyll a). Kegeshook, Salmon,

Fanning, Porcupine, Wentworth and Placides conformed to this hypothesis. The increase in phosphorus

concentration observed in Wentworth in 2018 is particularly noteworthy but does not yet have an

observed cause and falls within the results from past years. Slight decreases were noted in Provost,

Nowlans, Hourglass, Sloans, and Raynards with a larger decrease in Vaughan mainly because of

decreases in chlorophyll a concentrations. The decline in August TSI indices since 2013 remained

consistent in Provost. The decline since 2015 in Nowlans has also remained consistent.

Given recent year-to-year trends, the change in Wentworth marks a potential reversal of a trend in TSI

values which had been declining since 2014 and warrants additional assessment in 2019.

4.6 Relationship between Rainfall and Colour Appendix 9 provides historical precipitation data for Yarmouth from 2008 to 2018, by month, from May

to October each year and summed for various combinations of months, in order to assess precipitation

patterns that were most closely associated with August colour results.

The correlation between May rainfall and late August colour was extremely tenuous for all lakes and the

relationship between August rainfall and late August colour was also uniformly weak. However, the

relationship between all of June rainfall, July rainfall, and combined June-July rainfall as the independent

variable and late August colour as the dependent variable were consistently positive. Table 4.6

summarizes the relevant regression equations.

Of these three rainfall estimators, coefficient of determination (r2) values were highest for combined June

and July rainfall versus colour for Nowlans, Hourglass, Placides, Porcupine, Parr, Ogden, Fanning,

Sloans, Raynards, Vaughan, and Kegeshook. Linear regressions tested late August colour against

combined June and July rainfall for each lake. Significant positive relations were indicated for ten of the

eleven lakes; only in Sloans was the relationship observed to be non-significant; it also had the lowest

recorded colour values.

The r2 values were highest for June rainfalls versus colour for Provost, and for July rainfalls versus colour

for Wentworth and Salmon. The regressions of June-July rainfall to late August colour were non-

significant for all three lakes, but only barely so for Provost (p=.069) and Wentworth (p=.074). The

regressions for June rainfall to late August colour in Provost and for July rainfall against late August

colour for Wentworth and Salmon proved significant.

Table 4.6: Regressions of August Colour against June, July, and June plus July Rainfall for

Monitored Lakes

Lake Regressions Equations for August Colour versus Rainfall for

June June and July July

Provost C=.537x+4.4041, p≈.01 C=.2725x+9.903 C=.1961x+44.504

Nowlans C=.2947x+1.3508 C=.1977x+.1836, p≈.01 C=.3199x+13.41

Hourglass C=.481x+49.547, C=.3625x+33.912, p≈.007 C-.4664x+61.752

Placides C=.7512x+41.266 C=.5658x+16.894, p≈.001 C=.7277x+60.377

Porcupine C=.36x+14.489 C=.276x+1.9656, p≈.003 C=.3617x+22.673

Wentworth C=.6346x+118.61 C=.604x+82.01 C=1.2478x+196.93 p≈.029

Parr C=.7223x+50.298 C=.4828x+34.661, p≈.025 C=.5933x+71.407

Ogden C=.5339x+29.28 C=.345x+19.778, p≈.027 C=.4057x+47.477

Fanning C=.4789x+23.593 C=.332x+13.044, p≈.003 C=.3875x+41.532

Sloans C=.81x+13.432 C=.0289x+12.123, p≈.149, ns C=.0341x+14.807

Raynards C=.1178x+30.019 C=.1255x+22.838, p≈.012 C=2134x+30.841

Vaughan C=.2221x+31.137 C=.1569x+25.731, p≈.01 C=.1876x+38.863

Salmon C=.3774x+68.115 C=.6776x+3.54 C=1.6725x+20.165, p≈.024

Kegeshook C=.1387x+37.106 C=.1257x+31.886, p≈.011 C=.174x+41.938

Note: C=colour; x = rainfall over period.

Probabilities are reported only for the regression with the highest associated r2 value.

Climate change predictions call for hotter, drier summers. These analyses indicate that lower colour

levels for lakes can potentially be anticipated due to decreased runoff and input of dissolved organics, that

would cause an increased vulnerability to cyanobacteria blooms, if nutrient levels are high enough to

allow production.

5. Conclusions In general, water quality patterns observed in 2018 were similar to those observed in previous years,

particularly 2016 as both had late summer dry/drought conditions. The tendency for high total

phosphorus levels along the mainstem of the Carleton River to decrease from the headwaters to

downstream remained consistent in 2018, as was the contrast with the low levels in the tributary lakes

Porcupine and Sloans. Phosphorus levels were down in most lakes from 2017. Increases in phosphorus

concentrations were noted in Hourglass, Wentworth, Kegeshook, and Salmon from 2017. Hourglass is the

only lake with an increasing trend of chlorophyll a and total phosphorus concentrations. Hourglass is

recommended for further monitoring and assessment in 2019.

Colour was consistently down from 2017 in all lakes but Vaughan. This would have made conditions

more conducive to light penetration and hence, given sufficient nutrients, to algae growth.

In recent years, blooms have been weakening in extent and duration in Raynards and Vaughan and in

2018, for the first time, we received no reports of blooms. Further, no blooms were present when

cyanobacterial samples were collected near the Carleton River inlets of both lakes, locations where

historically, blooms tended to be the heaviest.

The decrease in chlorophyll a in Provost seems to reflect similar conditions in Raynards and Vaughan of

low colour as well as decreases in total phosphorus to a level at or below 0.01 mg/l. to the lower total

phosphorus concentration would potentially limit biological production in the presence of other

conditions conducive to blooms.

While Nowlans remained hypereutrophic, nutrient levels and chlorophyll a concentrations continued to

decrease from the previous year, and for the second consecutive year, microcystin concentrations were

below measurable levels. Also for the first time waters at depth were observed to be well oxygenated

instead of anoxic (no oxygen). Given the low colour level and extremely high nutrient levels in this lake,

visible algal blooms are likely to continue.

Phosphorus levels have become higher in Hourglass Lake, and with lower colour levels during a dry year,

blooms could potentially occur. There is a former mink farm and a fish hatchery in the watershed, as well

as cleared lands, that all should be investigated further with respect to nutrient loading.

The upper Carleton is a major nutrient source into Parr, but there are other sources from silviculture

operations to the east of the lake and possibly other activities.

Nutrient levels remained low in Kegeshook, but low colour levels and a growing number of lakeshore

cottages make this lake potentially vulnerable to blooms. The bloom noted in late June 2017, at the boat

launch site was not observed in 2018. Mitigation measures such as educational outreach focusing on

landowners around Kegeshook and upstream lakes, and by-laws limiting shoreline development could be

potentially explored.

Salmon tends to be a well-mixed lake with phosphorus and colour levels comparable to those in Raynards

and the Vaughan sampling site, with slightly higher nitrogen levels. To date, no cyanobacteria cells have

been counted in early July samples. As with Hourglass, cyanobacterial cell counts tend to be lower than

would be predicted, based on observed total phosphorus and colour concentrations.

Monitoring of cyanobacterial blooms potentially deserves less priority than water chemistry monitoring

with respect to observing changes in lake water quality and health. It remains desirable to monitor twice

during the summer: a week or two after the summer solstice, when blooms have been observed to peak,

and late in /august, when summer stratification tends to be maximal or develop a targeted program

sampling observed blooms only. The need to continue monitoring for microcystin concentrations at past

levels of effort is more questionable given the analysis costs and the number of samples that have been

observed to have non-detection results. Measurable levels historically have been observed only in

Nowlans. The Steering Committee should consider suspending microcystin concentration monitoring as

part of the overall program.

Monitoring of secondary inlets in Parr and Fanning suggest that there are nutrient sources besides the

upstream Carleton River, particularly in Parr. However, comparison of flows between the inlets did not

occur in 2018 beyond anecdotal. Silviculture operations on the eastern shore of the lake potentially are

contributing via surface water runoff, and other sources may also be present, including lake sediments.

Inputs from overland flow, seepage, and point sources deserve consideration, but quantifying them is not

practicable.

Since monitoring began in many of the lakes in 2008, there are no significant increasing or decreasing

trends via Mann-Kendall analysis in total phosphorus, orthophosphate, chlorophyll a and total nitrogen in

many of the lakes in the study. Total phosphorus and chlorophyll a concentrations were observed to be

increasing only in Hourglass Lake. Placides observed a decreasing total phosphorus concentration for the

August sample events. Parr, Fanning and Vaughan have observed decreasing total phosphorus,

orthophosphate and colour concentrations and increasing Secchi disc depths for the fall events. Vaughan

is the only lake with decreasing trends for total phosphorus and orthophosphate for the spring sampling

events. Changes in Fur Industry Regulations, a recent reduction in the number of operating fur farms

within the watershed and hot, dry summers with increased light penetration in the water column are

potential reasons for some of the observed trends within the study lakes.

Public education and outreach, particularly to acquaint resource-users, including the forestry industry, and

riparian property owners about their responsibilities to help maintain water quality should continue.

Protective municipal by-laws and provincial regulations should be potentially explored to improve

management of lakeshore development activities within the study watersheds and others within the

Province.

6. Acknowledgements This study was funded primarily by Nova Scotia Environment, with supplementary funding from the

Nova Scotia Salmon Association’s Adopt-a-Stream program, Municipality of the District of Yarmouth,

Municipality of Argyle, and Tusket River Environmental Protection Association. Valuable technical

advice was provided by Andrew Sinclair of Nova Scotia Environment and Jim Mullen of Nova Scotia

Mink Breeders’ Association, and Jean Cleveland provided valuable on-the-ground perspective. Corey

Bowen and Colin Buhariwalla from NSDFA did additional field work on Provost, Nowlans, Placides, and

Porcupine Lakes. The volunteers who made monitoring most of the lakes possible include Raymond

/Gaudet (Hourglass and Wentworth), Wayne Brittain (Parr), Howard Heyward (Ogden), Jean Cleveland,

(Fanning), Adele Richard (Sloans) Will Poole (Vaughan), Mike Raynard (Raynards), Virginia Smith

(Kegeshook) and Cory Cook (Salmon). Their efforts were coordinated by Jean Cleveland, who has

helped assure lake-specific ownership of the program.

7. Literature Cited Brylinsky, M. 2012. An Assessment of Sources and Magnitudes of Nutrient Inputs Responsible for

Degradation of Water Quality in Seven Lakes Located Within the Carleton River Watershed Areas of

Digby and Yarmouth Counties, Nova Scotia. Report prepared for Nova Scotia Department of

Environment. 31 pp.

Brylinsky, M., and J. Sollows. 2014. Results of the 2013Water Quality Survey of Eleven Lakes Located

in the Carleton River Watershed Area of Digby and Yarmouth Counties, Nova Scotia. Report prepared

for Nova Scotia Department of Environment. 39 pp.

Cleveland, J. 2018. Pers. comm.

Gilbert, R.O. 1987. Statistical Methods for Environmental Pollution Monitoring. Wiley, NY.

Hirsch, R.M., J.R. Slack, and R.A. Smith. 1982. Techniques of trend analysis for monthly water quality

data. Water Resources Research 18(1):107-121.

Kendall, M.G. 1975. Rank Correlation Methods, 4th edition. Charles Griffin, London.

Mann, H.B. 1945. Non-parametric tests against trend. Econometrica 13:163-171.

Mullen, J. 2019 Pers. comm.

Nguyen-Quang, T., K. Hishchyna, McLellan, K., and Warren. A. 2016. Preliminary Report for Five

Lakes in the Yarmouth & Digby Areas. Dalhousie University Faculty of Agriculture. 18 pp.

Sollows. J. D. 2017. Results of the 2016 Water Quality Survey of Fourteen Lakes in Yarmouth and

Digby Counties. Report prepared for Carleton River Watershed Water Quality Monitoring Steering

Committee, Municipality of the District of Yarmouth. 81 pp.

Sollows, J. D. 2018. Supplemental Results of the 2017 Water Quality Survey of Fourteen Lakes in

Yarmouth and Digby Counties. Report prepared for Carleton River Watershed Water Quality Monitoring

Steering Committee, Municipality of the District of Yarmouth. 79 pp.

Stantec Consulting Ltd. 2017. Results of the 2017 Water Quality Survey of Eleven Lakes in Yarmouth

and Digby Counties. Report prepared for Carleton River Watershed Area Water Quality Monitoring

Steering Committee. 159 pp.

Taylor, D. 2010. A Water Quality Survey of Ten Lakes in the Carleton River Watershed Area, Yarmouth

and Digby Counties, Nova Scotia. Report prepared for Nova Scotia Department of Environment. 64 pp.

Appendix 1. Analysis Results Table: Summer Surface Data

Lake_ID Date Secchi Depth

(m) Chlorophyll a

(µg/l) Total Phosphorus

(mg/l) Orthophosphate

(mg/l) OrthoP/ Total

P ratio Total nitrate

(mg/l) Total Nitrogen

(mg/l) Colour (TCU)

pH

Hourglass Aug. 13/2008 1.30 15 0.069 0.034 0.493 0.03 0.57 60 6.2

Hourglass Sept. 25/2010 1.25 13 0.050 0.022 0.440 0.01 0.35 58 6.80

Hourglass Aug. 13/2011 1.40 2.1 0.045 0.018 0.400 0.04 0.64 89 6.80

Hourglass Aug. 12/2013 0.63 7 0.056 0.029 0.518 <.01 0.56 161.7 6.07

Hourglass Aug. 18/2014 0.80 44 0.067 0.037 0.552 <.01 0.45 145.2 6.31

Hourglass Aug. 17/2015 0.93 19 0.065 0.038 0.585 <.01 0.4 105 6.35

Hourglass Aug. 21/2016 0.925 44.9 0.08 0.026 0.325 <.01 0.39 66.5 6.5

Hourglass Aug. 24/2017 1 49.8 0.073 0.028 0.383562 <.02 0.41 80.4 6.7

Hourglass Aug. 28/18 1 24.1 0.118 0.056 0.474576 <.01 0.49 67.2 6.9

Placides Aug. 13/2008 1.30 20 0.740 0.58 0.784 0.35 1.69 68 6.50

Placides Sept. 26/2010 0.70 15.5 0.820 0.705 0.860 0.47 1.23 90 6.90

Placides Aug. 22/2011 ND 2.8 0.960 0.786 0.819 0.58 1.83 117 6.80

Placides Aug. 6/2013 0.40 52 0.792 0.764 0.965 0.52 1.34 227.8 6.80

Placides Aug. 25/2014 0.63 32 0.806 0.611 0.758 <.01 0.57 149.5 ND

Placides Aug. 26/2015 0.95 22 0.698 0.592 0.848 <.01 0.5 126 ND

Placides Aug. 30/2016 1.40 15.1 0.624 0.5725 0.917 <.01 0.38 66 6.90

Placides Aug. 22/17 3.375 8.28 0.618 0.506 0.81877 <.01 0.46 98.6 6.2

Placides Aug. 29/17 1 4.01 0.609 0.512 0.840722 <.01 0.48 96.8 6.8

Placides Aug. 29/18 1.3 14.1 0.583 0.481 0.825043 <.01 0.45 69.4 6.9

Porcupine Aug. 12/2008 2.50 7.8 0.012 0.005 0.417 0.01 0.22 25 6.60

Porcupine Sept. 26/2010 1.95 2.8 0.021 0.005 0.238 0.01 0.25 39 6.80

Porcupine Aug. 14/2011 0.90 3.4 0.014 0.005 0.357 0.01 0.3 46.6 6.90


(m)

Chlorophyll a

(µg/l)

Total Phosphorus

(mg/l)

Orthophosphate

(mg/l)

OrthoP/ Total

P ratio

Total nitrate

(mg/l)

Total Nitrogen

(mg/l)

Colour

(TCU) pH

Porcupine Aug. 6/2013 0.59 7.0 0.032 0.014 0.438 0.02 0.42 105.3 6.90

Porcupine Aug. 25/2014 1.63 6.9 0.016 0.005 0.313 <.01 0.28 73.2 ND

Porcupine Aug. 26/2015 1.90 7.3 0.016 0.003 0.188 <.01 0.24 53.2 ND

Porcupine Aug. 30/2016 2.30 3.2 0.018 0.0055 0.306 <.01 0.255 30.55 6.80

Porcupine Aug. 22/17 0.875 2.41 0.017 0.013 0.764706 <.01 0.29 44.7 6.9

Porcupine Aug. 29/17 2.5 1.13 0.013 0.004 0.307692 <.01 0.3 38.3 6.8

Porcupine Aug. 29/18 1.9 5.53 0.01 0.003 0.3 <.01 0.26 23.9 7.0

Wentworth Aug. 12/2013 0.46 14 0.160 0.138 0.863 0.01 0.58 250.6 5.58

Wentworth Aug. 18/2014 0.33 13 0.187 0.140 0.749 <0.01 0.54 304.1 5.64

Wentworth Aug. 17/2015 0.6 11 0.130 0.111 0.854 <0.01 0.37 182 6.00

Wentworth Aug. 21/2016 1.57 3.9 0.154 0.146 0.948 0.06 0.51 115 6.10

Wentworth Aug. 21/17 0.625 4.63 0.084 0.082 0.97619 <.01 0.46 158 6.3

Wentworth Aug. 28/18 1 14.7 0.128 0.089 0.695313 <.01 0.48 128 6.5

Parr Aug. 14/2008 1.5 11 0.033 0.012 0.364 0.01 0.27 64 6.20

Parr Aug. 24/2010 1 6.7 0.075 0.075 1.000 0.01 0.03 97.2 6.20

Parr Sept. 26/2010 0.75 13 0.061 0.031 0.508 0.01 0.33 86 6.20

Parr Aug. 12/2013 0.51 6.1 0.105 0.080 0.762 0.04 0.53 199.6 5.71

Parr Aug. 25/2014 0.57 11 0.111 0.084 0.757 <0.01 0.49 193.9 5.86

Parr Aug. 20/2015 1.8 7.8 0.075 0.047 0.627 <0.01 0.41 123 6.26

Parr Aug. 21/2016 1.35 13.7 0.055 0.022 0.400 <0.01 0.38 67.7 6.30

Parr Aug. 23/18 0.9 11.9 0.056 0.022 0.392857 <.01 0.32 83 6.4

Ogden Aug. 14/2008 1.8 10 0.014 0.005 0.357 0.01 0.25 39 6.10

Ogden Sept. 27/2010 0.95 18.8 0.029 0.008 0.276 0.05 0.35 58 6.30

Ogden Aug. 24/2011 1.2 12.5 0.022 0.005 0.227 0.01 0.28 59.2 6.10

Ogden Aug. 6/2013 0.6 9.4 0.052 0.035 0.673 0.02 0.41 145.3 6.40

Ogden Aug. 25/2014 0.66 26 0.046 0.021 0.457 <0.01 0.44 126.5 6.20


(m)

Chlorophyll a

(µg/l)

Total Phosphorus

(mg/l)

Orthophosphate

(mg/l)

OrthoP/ Total

P ratio

Total nitrate

(mg/l)

Total Nitrogen

(mg/l)

Colour

(TCU) pH

Ogden Aug. 20/2015 1.17 11 0.022 0.004 0.182 <0.01 0.32 83.2 6.53

Ogden Aug. 21/2016 1.25 4.46 0.024 0.004 0.167 0.02 0.33 48.6 6.30

Ogden Aug. 23/18 1.375 16.8 0.018 0.001 0.055556 <.01 0.31 55.2 6.6

Fanning Aug. 16/2008 2.3 5.8 0.011 0.005 0.455 0.01 0.21 31 6.40

Fanning Sept. 12/2009 0.75 1.3 0.056 0.037 0.661 0.06 0.4 120 5.90

Fanning Sept. 29/2010 1.15 21.9 0.021 0.005 0.238 0.06 0.35 55 6.40

Fanning Aug. 17/2011 1.3 19.2 0.023 0.005 0.217 0.01 0.05 63.1 6.20

Fanning Aug. 11/2013 1.01 3.8 0.045 0.023 0.511 0.01 0.4 131.4 5.93

Fanning Aug. 24/2014 0.98 8.7 0.027 0.012 0.444 0.02 0.34 99 6.07

Fanning Aug. 16/2015 1.4 14 0.019 0.006 0.316 <0.01 0.34 73.6 6.19

Fanning Aug. 21/2016 1.55 10.4 0.023 0.003 0.130 0.03 0.32 43.8 6.40

Fanning Aug. 23/2017 1.5 3.39 0.022 0.01 0.454545 <.01 0.33 82.2 6.4

Fanning Aug. 27/18 1.8 10.8 0.014 0.004 0.285714 <.01 0.26 41.6 6.6

Sloans Sept. 12/2009 3.8 1.9 0.005 0.005 1.000 0.01 0.18 20 6.90

Sloans Sept. 30/2010 4.3 4.3 0.009 0.005 0.556 0.01 0.12 12 7.00

Sloans Aug. 15/2011 4.6 4.6 0.005 0.005 1.000 0.01 0.13 15.3 7.00

Sloans Aug. 1/2013 3.11 2.4 0.004 0.003 0.625 <0.01 0.14 22.3 6.77

Sloans Aug. 4/2014 4.65 1.8 0.004 0.001 0.25 <0.01 0.13 20.1 6.85

Sloans Aug. 6/2015 5.375 2.2 0.004 0.004 1.000 0.02 0.16 21.2 6.50

Sloans Aug. 8/2016 6.25 1.78 0.004 0.004 1.000 0.01 0.14 18.6 6.90

Sloans Aug. 21/2017 4.35 1.35 0.004 0.004 1 <.01 0.15 14.6 7.0

Sloans Aug. 27/18 4.75 1.37 0.003 0.003 1 <.01 0.15 10.5 7.1

Raynards Aug. 1/2013 1.2 26.66 0.021 ND ND ND ND ND 6.20

Raynards Aug. 4/2014 1.23 16 0.013 0.002 0.154 <0.01 0.27 54 6.19

Raynards Aug. 9/2015 1.85 12 0.011 0.004 0.364 <0.01 0.27 47 6.44

Raynards Aug. 4/2016 1.5 4.27 0.009 0.004 0.444 <0.01 0.2 32.3 6.50


(m)

Chlorophyll a

(µg/l)

Total Phosphorus

(mg/l)

Orthophosphate

(mg/l)

OrthoP/ Total

P ratio

Total nitrate

(mg/l)

Total Nitrogen

(mg/l)

Colour

(TCU) pH

Raynards Aug. 17/2017 2.25 5.3 0.012 0.004 0.333333 <.01 0.25 43.9 6.5

Raynards Aug. 26/18 2.5 5.79 0.008 0.001 0.125 <.01 0.2 31.6 6.6

Vaughan Sept. 4/2008 3 3.9 0.012 0.005 0.417 0.01 0.17 22 7.20

Vaughan Sept. 0/2010 1.2 2.8 0.019 0.005 0.263 0.04 0.34 69 6.20

Vaughan Aug. 6/2011 1.9 2.6 0.01 0.005 0.500 0.01 0.22 63 6.20

Vaughan Aug. 3/2013 1.17 14 0.02 0.0025 0.125 <0.01 0.29 81 6.24

Vaughan Aug. 8/2014 1.43 14 0.012 0.003 0.250 <0.01 0.35 54.9 6.32

Vaughan Aug. 8/2015 1.8 10 0.01 0.003 0.300 <0.01 0.24 57 6.52

Vaughan Aug. 4/2016 1.3 7.87 0.008 0.003 0.375 <0.01 0.21 41.8 6.40

Vaughan Aug. 24/2017 1.625 14.7 0.015 0.01 0.666667 <.01 0.28 51.2 6.5

Vaughan Aug. 21/18 1.4 2.96 0.01 0.002 0.2 <.01 0.22 53 6.5

Provost Aug. 4/2008 1.7 18 0.011 0.005 0.455 0.01 0.45 32 6.10

Provost Sept. 30/2010 1.7 20.3 0.016 0.005 0.313 0.04 0.29 36 6.00

Provost Aug. 14/2011 0.6 19.6 0.011 0.005 0.455 0.01 0.03 43.8 6.00

Provost Aug. 13/2013 0.99 32 0.016 0.0025 0.156 0.05 0.48 74.3 5.96

Provost Aug. 24/2014 1.05 31 0.016 0.006 0.375 0.02 0.52 82.6 ND

Provost Aug. 25/2015 2.65 8.4 0.029 0.007 0.241 <0.01 0.56 127.55 ND

Provost Aug. 30/2016 2.4 5.68 0.017 0.005 0.2647 <0.01 0.27 19.7 6.30

Provost Aug. 22/2017 2.2 4.15 0.008 0.004 0.5 <.01 0.29 34.3 6.4

Provost Aug. 30/2017 3 4.7 0.012 <.002 0.083333 <.01 0.33 74 6.6

Provost Aug. 30/18 2.35 3.79 0.009 0.002 0.111111 <.01 0.24 23.8 6.5

Nowlans Aug. 14/2008 0.85 67 0.4 0.3 0.75 0.01 1.01 16 6.50

Nowlans Sept. 26/2010 0.55 64.5 0.42 0.287 0.683 0.01 1.06 15 8.50

Nowlans Aug. 6/2013 ND 100 0.446 0.39 0.874 0.005 0.73 57.4 ND

Nowlans Aug. 26/2015 0.625 90 0.497 0.43 0.865 <0.01 0.77 58.9 ND

Nowlans Aug. 31/2016 0.85 73.9 0.556 0.525 0.944 <0.01 n/a 15.3 7.40

Nowlans Aug. 20/2017 1 48.6 0.553 0.437 0.790235 0.01 n/a 25.4 7.3

Nowlans Aug. 30/18 0.85 47.1 0.464 0.409 0.881466 <.01 n/a 14 9.1


(m)

Chlorophyll a

(µg/l)

Total Phosphorus

(mg/l)

Orthophosphate

(mg/l)

OrthoP/ Total

P ratio

Total nitrate

(mg/l)

Total Nitrogen

(mg/l)

Colour

(TCU) pH

Kegeshook Aug. 15/2013 0.98 7.55 0.010 ND ND ND ND ND 5.51

Kegeshook Aug. 21/2014 1.97 3.4 0.005 <.002 0.200 <0.01 0.18 60.8 6.00

Kegeshook Aug. 25/2015 2.125 5.1 0.006 0.004 0.167 <0.01 0.19 55.6 6.04

Kegeshook Aug. 21/2016 1.87 14.9 0.007 0.003 0.143 <0.01 0.18 38.2 6.40

Kegeshook Aug. 28/2017 1.25 2.75 0.005 0.003 0.6 <.01 0.21 56.5 6.3

Kegeshook Aug. 23/18 1.65 4.42 0.006 0.001 0.166667 <.01 0.19 43.1 6.6

Salmon Aug. 20/2013 0.78 3.38 0.011 ND ND ND ND ND 5.84

Salmon Aug. 19/2014 1.03 7.99 0.011 ND ND ND ND 223.95 6.04

Salmon Aug. 18/2015 1.55 4.9 0.014 0.004 0.071 <0.01 0.76 90.4 6.12

Salmon Aug. 21/2016 2.25 9.99 0.016 0.003 0.063 <.0.01 0.28 53.3 6.40

Salmon Aug. 17/2017 1.375 2.28 0.009 0.004 0.444444 <.01 0.48 108 6.2

Salmon Aug. 27/18 1.625 5.3 0.01 0.006 0.6 <.01 0.35 53 6.4

ND=No Data

Appendix 2. Water Quality Parameters compared by lake for August/ September sample events (2008 to 2018)

0

20

40

60

80

100

120

Ho

urg

lass

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

e

Po

rcu

pin

e

Po

rcu

pin

e

We

ntw

ort

h

We

ntw

ort

h

Par

r

Par

r

Par

r

Ogd

en

Ogd

en

Ogd

en

Fan

nin

g

Fan

nin

g

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

k

Ke

gesh

oo

k

Salm

on

Salm

on

Ch

loro

ph

yll a

(µg/

l)

Lake

August-September Chlorophyll a levels by lake and year

2008200920102011

201320142015201620172018

0

0.2

0.4

0.6

0.8

1

1.2

Ho

urg

lass

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

eP

orc

up

ine

Po

rcu

pin

e

We

ntw

ort

hW

en

two

rth

Par

rP

arr

Par

rO

gde

nO

gde

nO

gde

n

Fan

nin

gFa

nn

ing

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

kK

ege

sho

ok

Salm

on

Salm

on

Ph

osp

ho

rus

(m

g/l)

Lake

August-September Total phosphorus levels by lake and year

200820092010201120132014

201520162017 2018

0

0.1

0.2

0.3

0.4

0.5

0.6

0.7

0.8

0.9

Ho

urg

lass

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

eP

orc

up

ine

Po

rcu

pin

e

We

ntw

ort

hW

en

two

rth

Par

rP

arr

Par

rO

gde

nO

gde

nO

gde

n

Fan

nin

gFa

nn

ing

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

kK

ege

sho

ok

Salm

on

Salm

on

Ort

ho

ph

osp

hat

e (

mg/

l)

Lake

August-September Orthophosphate levels by lake and year200820092010201120132014

2015201620172018

0

0.2

0.4

0.6

0.8

1

1.2

Ho

urg

lass

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

eP

orc

up

ine

Po

rcu

pin

e

We

ntw

ort

hW

en

two

rth

Par

rP

arr

Par

rO

gde

nO

gde

nO

gde

n

Fan

nin

gFa

nn

ing

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

kK

ege

sho

ok

Salm

on

Salm

on

Ort

ho

P:T

ota

lP

Lake

August-September Orthophosphate:Phosphate ratios by lake and year 2008

200920102011201320142015201620172018

0

50

100

150

200

250

300

350

Ho

urg

lass

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

e

Po

rcu

pin

e

Po

rcu

pin

e

We

ntw

ort

h

We

ntw

ort

h

Par

r

Par

r

Par

r

Ogd

en

Ogd

en

Ogd

en

Fan

nin

g

Fan

nin

g

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

k

Ke

gesh

oo

k

Salm

on

Salm

on

Co

lou

r (T

CU

)

Lake

August-September Colour levels by lake and year 2008200920102011201320142015

201620172018

0

1

2

3

4

5

6

7H

ou

rgla

ss

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

e

Po

rcu

pin

e

Po

rcu

pin

e

We

ntw

ort

h

We

ntw

ort

h

Par

r

Par

r

Par

r

Ogd

en

Ogd

en

Ogd

en

Fan

nin

g

Fan

nin

g

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

k

Ke

gesh

oo

k

Salm

on

Salm

on

Secc

hi D

ep

th (

m)

Lake

August-September Secchi Depths by lake and year 2008200920102011201320142015201620172018

0

0.2

0.4

0.6

0.8

1

1.2

1.4

1.6

1.8

2H

ou

rgla

ssH

ou

rgla

ssH

ou

rgla

ss

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

eP

orc

up

ine

Po

rcu

pin

e

We

ntw

ort

hW

en

two

rth

Par

rP

arr

Par

rO

gde

nO

gde

nO

gde

n

Fan

nin

gFa

nn

ing

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

kK

ege

sho

ok

Salm

on

Salm

on

Tota

l N (

mg/

l)

Lake

August-September Total Nitrogen levels by lake and year2008200920102011201320142015201620172018

0

0.1

0.2

0.3

0.4

0.5

0.6

0.7H

ou

rgla

ss

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

e

Po

rcu

pin

e

Po

rcu

pin

e

We

ntw

ort

h

We

ntw

ort

h

Par

r

Par

r

Par

r

Ogd

en

Ogd

en

Ogd

en

Fan

nin

g

Fan

nin

g

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

k

Ke

gesh

oo

k

Salm

on

Salm

on

Nit

rate

(m

g/l)

Lake

August-September Nitrate levels by lake and year2008200920102011201320142015 2016 20172018

No pH data for Provost, Nowlans, Placides, nor Porcupine in 2014 and 2015.

0

1

2

3

4

5

6

7

8

9

10

Ho

urg

lass

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

e

Po

rcu

pin

e

Po

rcu

pin

e

We

ntw

ort

h

We

ntw

ort

h

Par

r

Par

r

Par

r

Ogd

en

Ogd

en

Ogd

en

Fan

nin

g

Fan

nin

g

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

k

Ke

gesh

oo

k

Salm

on

Salm

on

pH

Lake

August-September pH by lake and year2008200920102011201320142015201620172018

0

5

10

15

20

25

30

35H

ou

rgla

ss

Ho

urg

lass

Ho

urg

lass

Pla

cid

es

Pla

cid

es

Pla

cid

es

Po

rcu

pin

e

Po

rcu

pin

e

Po

rcu

pin

e

We

ntw

ort

h

We

ntw

ort

h

Par

r

Par

r

Par

r

Ogd

en

Ogd

en

Ogd

en

Fan

nin

g

Fan

nin

g

Fan

nin

g

Slo

ans

Slo

ans

Slo

ans

Ray

nar

ds

Ray

nar

ds

Vau

ghan

Vau

ghan

Vau

ghan

Pro

vost

Pro

vost

Pro

vost

No

wla

ns

No

wla

ns

No

wla

ns

Ke

gesh

oo

k

Ke

gesh

oo

k

Salm

on

Salm

on

Tem

pe

ratu

re (°C

Lake

August-September Surface Temperatures by lake and year20082009201020112013201420152016

20172018

Appendix 3. Seasonal Variation in Water Quality Parameters for Selected Lakes

Lake Name

Date Secchi

Depth (m) Chlorophyll a

(µg/l)

Total Phosphorus

(mg/l)

Orthophosphate (mg/l)

OrthoP/ Total P ratio

Total nitrate (mg/l)

Total Nitrogen)

(mg/l)

Colour (TCU)

pH

Parr May 4/2013 0.96 7.80 0.025 0.012 0.480 <0.01 0.25 100.4 5.87 July 8/2013 0.55 8.70 0.086 0.068 0.791 0.01 0.50 223.9 5.44 Aug. 12/2013 0.51 6.10 0.105 0.080 0.762 0.04 0.53 199.6 5.71 Oct. 28/2013 0.55 2.30 0.088 0.072 0.818 0.04 0.53 214.3 5.59 May 13/2014 0.90 29.0 0.032 0.024 0.750 <0.01 0.21 92.1 5.67 Aug. 25/2014 0.57 11.0 0.111 0.084 0.757 <0.01 0.49 193.9 5.86 Oct. 20/2014 0.65 4.50 0.084 0.064 0.762 0.02 0.45 169.0 5.98 May 11/2015 1.00 4.90 0.042 0.029 0.690 0.04 0.27 74.0 5.29 Aug. 20/2015 1.80 7.80 0.075 0.047 0.627 <0.01 0.41 123.0 6.26 Oct. 20/2015 0.80 7.30 0.087 0.062 0.713 0.01 0.40 156.0 5.83 May 1/2016 1.00 11.0 0.032 0.011 0.344 <0.01 0.29 90.5 5.70 Aug. 21/2016 1.35 13.7 0.055 0.022 0.400 <0.01 0.34 67.7 6.30 Oct. 16/2016 1.00 6.50 0.052 0.026 0.500 <0.01 0.32 71.0 6.00

May 7/17 1.175 2.75 0.032 0.018 0.5625 <.01 0.26 86.6 6.00

Aug. 20/17 .875

Oct. 15/17 .85 3.61 0.055 0.029 0.527273 <.01 0.42 145 6.1

Apr. 29/18 1.125 4.06 0.026 0.01 0.384615 <.01 0.25 97.7 1.125

Aug. 23/18 0.9 11.9 0.056 0.022 0.392857 <.01 0.32 83 0.9

Oct. 28/18 0.85 2.72 0.07 0.042 0.6 0.02 0.49 120 0.85

Fanning May 5/2013 1.30 9.70 0.017 0.007 0.412 <0.01 0.22 72.4 6.11 July 7/2013 0.90 5.60 0.037 0.022 0.595 <0.01 0.33 128.2 5.81 Aug. 11/2013 1.01 3.80 0.045 0.023 0.511 0.01 0.40 131.4 5.93 Oct. 20/2013 0.58 2.60 0.052 0.039 0.750 0.06 0.42 156.3 5.78 May 11/2014 1.20 6.90 0.019 0.012 0.632 0.03 0.21 68.2 5.65 July 10/2014 1.10 9.69 0.015 5.89 Aug. 24/2014 0.98 8.70 0.027 0.012 0.444 0.02 0.34 99.0 6.07

Lake Name

Date Secchi


(µg/l)

Total Phosphorus

(mg/l)




Total Nitrogen)

(mg/l)

Colour (TCU)

pH

Fanning Oct. 19/2014 1.07 4.00 0.044 0.021 0.477 0.07 0.41 99.3 6.12 May 10/2015 1.70 6.10 0.028 0.024 0.857 0.06 0.30 66.3 5.38 Aug. 16/2015 1.40 14.0 0.019 0.006 0.316 <0.01 0.34 73.6 6.19 Oct. 18/2015 1.35 5.30 0.036 0.017 0.472 0.04 0.34 87.7 6.10

May 1/2016 1.65 6.90 0.022 0.012 0.545 <0.01 0.22 72.7 5.80

Aug. 21/2016 1.55 10.4 0.023 0.003 0.130 0.03 0.32 43.8 6.40 Oct. 16/2016 1.75 7.34 0.020 0.005 0.250 <0.01 0.24 37.8 6.40

May 7/17 1.6 2.7 0.022 0.012 0.545455 <.01 0.24 65.7 6.2

Aug. 23/17 1.5 3.39 0.022 0.01 0.454545 <.01 0.33 82.2 6.4

Oct. 15/17 1.55 3.45 0.031 0.012 0.387097 0.02 0.36 82.3 6.4

Apr. 29/18 1.625 4.95 0.02 0.007 0.35 <.01 0.22 68 6.2

Aug. 27/18 1.8 10.8 0.014 0.004 0.285714 <.01 0.26 41.6 6.6

Oct. 28/18 1.7 4.32 0.027 0.009 0.333333 0.03 0.4 55.4 6.5

Sloans May 6/2013 3.5 2.30 0.003 0.003 0.833 <0.01 0.14 22.0 6.64 July 3/2013 2.65 2.00 0.018 0.006 0.333 <0.01 0.16 29.2 6.81 Aug. 11/2013 3.11 2.40 0.004 0.003 0.625 <0.01 0.14 22.3 6.77 Oct. 20/2013 3.30 2.40 0.002 0.002 1.000 <0.01 0.14 23.0 6.56 May 11/2014 2.35 5.30 0.001 0.001 1.000 <0.01 0.13 29.0 6.63 July 10/2014 2.94 3.35 0.007 6.8 Aug. 24/2014 4.65 1.80 0.004 0.001 0.250 <0.01 0.13 20.1 6.85 Oct. 19/2014 3.69 3.40 0.003 0.001 0.333 <0.01 0.13 14.3 6.75 May 18/2015 4.04 2.80 0.004 0.004 1.000 <0.01 0.17 27.7 6.75 Aug. 16/2015 5.38 2.20 0.004 0.004 1.000 0.02 0.16 21.2 6.60 Oct. 18/2015 4.90 4.10 0.004 0.004 1.000 <0.01 0.13 20.5 6.60 May 1/2016 4.75 1.30 0.004 0.003 0.750 <0.01 0.15 23.5 6.80 Aug. 28/2016 6.25 1.78 0.004 0.004 1.000 0.01 0.14 18.6 6.90 Oct. 16/2016 4.25 2.27 0.003 0.002 0.667 <0.01 0.13 11.4 7.00

Sloans May 7/17 4.25 0.72 0.005 0.003 0.6 <.01 0.19 16.4 6.7

Lake Name

Date Secchi


(µg/l)

Total Phosphorus

(mg/l)




Total Nitrogen)

(mg/l)

Colour (TCU)

pH

Aug. 21.17 4.35 1.35 0.004 0.004 1 <.01 0.15 14.6 7.0

Oct. 15/17 4.6 1.28 0.004 <.002 0.25 <.01 0.14 14.2 6.9 May 7/18 3.75 1.47 0.005 0.002 0.4 0.02 0.17 20.3 7

Aug. 21/8 4.75 1.67 0.003 0.003 1 <.01 0.15 10.5 7.1

Oct. 30/18 4.25 2.48 0.005 0.005 1 <.01 0.16 14 7.1

Raynards May 6/2013 1.52 5.38 0.011 6.17 July 3/2013 1.25 11.83 0.021 6.28 Aug. 11/2013 1.20 26.66 0.021 6.2 Oct. 20/2013 1.08 3.76 0.037 96.369 6.01 May 11/2014 1.41 5.70 0.017 0.010 0.588 0.05 0.23 65.5 5.75 July 10/2014 1.43 7.05 0.0123 6.08 Aug. 24/2014 1.23 16.0 0.0130 0.002 0.154 <0.01 0.27 54.0 6.19 Oct. 19/2014 1.53 8.50 0.0160 0.003 0.188 0.07 0.35 52.0 6.17 May 18/2015 0.96 17.0 0.0200 0.011 0.55 0.03 0.24 55.8 5.92 Aug. 19/2015 1.85 12.0 0.0110 0.004 0.364 <0.01 0.27 47.0 6.44 Oct. 19/2015 1.7 5.10 0.0140 0.004 0.286 0.03 0.24 50.4 6.34 May 2/2016 1.5 9.50 0.0160 0.010 0.625 <0.01 0.24 67.7 6.00 Aug. 24/2016 1.5 4.27 0.0090 0.004 0.444 <0.01 0.2 32.3 6.50 Oct. 16/2016 3.3 3.07 0.0130 0.001 0.077 <0.01 0.2 25.9 6.60

May 17/17 1.5 1.67 0.019 0.011 0.578947 0.01 0.25 59.1 6.4

Aug. 14/17 2.25 5.3 0.012 0.004 0.333333 <.01 0.24 43.9 6.5

Oct. 18/17 2.75 2.3 0.015 0.006 0.4 0.01 0.28 47.5 6.6 May 8/18 2 4.57 0.014 0.004 0.285714 <.01 0.21 60.2 6.3

Aug. 26/8 2.5 5.79 0.008 <.002 0.125 <.01 0.2 31.6 6.6

Oct. 28/18 3.5 4.18 0.011 0.003 0.272727 0.01 0.24 30.2 6.6

Vaughan Apr. 30/2013 1.45 4.30 0.0190 0.007 0.368 0.05 0.32 82.4 5.95 July 4/2013 1.5 12.0 0.0150 0.003 0.167 <0.01 0.26 74.1 6.05 Aug. 13/2013 1.17 14.0 0.0200 0.003 0.125 <0.01 0.29 81.0 6.24

Vaughan Oct. 29/2013 1.2 3.30 0.0260 0.008 0.308 0.07 0.42 92.7 6.01

Lake Name

Date Secchi


(µg/l)

Total Phosphorus

(mg/l)




Total Nitrogen)

(mg/l)

Colour (TCU)

pH

May 7/2014 1.34 3.20 0.0200 0.014 0.700 0.07 0.25 62.6 5.79 Aug. 18/2014 1.43 14.0 0.0120 0.003 0.250 <0.01 0.35 54.9 6.32 Oct. 21/2014 1.59 8.60 0.0150 0.003 0.200 0.07 0.38 65.1 6.12 May 12/2015 1.5 9.80 0.0250 0.018 0.720 0.09 0.32 58.6 5.68 Aug. 18/2015 1.8 10.0 0.0100 0.003 0.300 <0.01 0.24 57.0 6.52 Oct. 19/2015 1.9 6.30 0.0140 0.004 0.286 0.04 0.24 50.5 6.20 May 2/2016 1.3 15.0 0.0180 0.009 0.500 <0.01 0.26 65.0 6.10 Aug. 24/2016 1.3 7.87 0.0080 0.003 0.375 <0.01 0.21 41.8 6.40 Oct. 16/2016 2.4 2.27 0.0140 0.006 0.429 0.02 0.22 35.9 6.40

May 10/17 1.55 2.69 0.017 0.008 0.470588 <.01 0.26 59.7 6.4

Aug. 24/17 1.625 14.7 0.015 0.01 0.666667 <.01 0.28 51.2 6.5

Oct. 19/17 1.8 2.16 0.018 0.007 0.388889 0.03 0.29 55 6.6

Apr. 30/18 1.9 7.82 0.016 0.006 0.375 <.01 0.23 56.8 6.4

Aug. 21/18 1.4 2.96 0.01 0.002 0.2 <.01 0.22 53 6.5

Oct. 23/18 3.125 2.61 0.01 0.002 0.2 0.01 0.22 31 6.6

Kegeshook Apr. 30/13 1.45 4.3 0.019 0.007 0.368421 0.05 0.32 82.4 5.95

July 4/13 1.5 12 0.015 0.0025 0.166667 <.01 0.26 74.1 6.05

Aug. 13/13 1.17 14 0.02 0.0025 0.125 <.01 0.29 81 6.24

Oct. 29/13 1.2 3.3 0.026 0.008 0.307692 0.07 0.42 92.7 6.01

May 7/14 1.34 3.2 0.02 0.014 0.7 0.07 0.25 62.6 5.79

Aug. 18/14 1.43 14 0.012 0.003 0.25 <.01 0.35 54.9 6.32

Oct. 21/14 1.59 8.6 0.015 0.003 0.2 0.07 0.38 65.1 6.12

May 12/15 1.5 9.8 0.025 0.018 0.72 0.09 0.32 58.6 5.68

Aug. 18/15 1.8 10.0 0.010 0.003 0.3 <.01 0.24 57 6.52

Oct. 19/15 1.9 6.3 0.014 0.004 0.285714 0.04 0.24 50.5 6.2

May 2/16 1.3 15 0.018 0.009 0.5 <.01 0.26 65 6.1

Aug. 24/16 1.3 7.87 0.008 0.003 0.375 <.01 0.21 41.8 6.4

May 8/18 2.25 2.24 0.006 0.003 0.5 0.01 0.23 55.5 6.4

Aug. 23/18 1.65 4.42 0.006 <.002 0.166667 <.01 0.19 43.1 6.6

Kegeshook Oct. 8/18 2.35 1.63 0.007 0.003 0.428571 <.01 0.2 40.4 6.4

Lake Name

Date Secchi


(µg/l)

Total Phosphorus

(mg/l)




Total Nitrogen)

(mg/l)

Colour (TCU)

pH

Salmon May 19/15 0.7

August 18/15 1.55 4.9 0.014 0.004 0.285714 <.01 0.76 90.4 5.75

Oct. 18/15 1.3 4.7 0.013 0.006 0.461538 0.02 0.34 103 6.16

May 3/16 1.435 2.3 0.01 0.004 0.4 <.01 0.28 84.1 6.08

Aug. 21/16 2.25 9.99 0.016 0.003 0.1875 <.01 0.28 53.3

Oct. 18/16 2.25 2.22 0.015 0.005 0.333333 <.01 0.25 36.3 6.4

May 4/17 1.74 0.88 0.011 0.005 0.454545 <.01 0.26 72.4 6.4

Aug. 17/17 1.38 2.28 0.009 0.004 0.444444 <.01 0.48 108 5.9

Oct. 21/17 1.3 1.39 0.012 0.006 0.5 0.02 0.47 126 6.2

Apr. 30/18 1.375 1.15 0.01 0.004 0.4 0.01 0.26 83.3 6.1

Aug. 27/18 1.625 1.43 0.01 0.006 0.6 0.01 0.35 53 6.4

Oct. 23/18 1.15 1.28 0.02 0.006 0.3 ,02 0.45 107 6.3

0

5

10

15

20

25

30

35

May

4/1

3

Oct

. 28

/13

Oct

. 20

/14

Oct

. 20

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

7/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 30

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 19

/15

Oct

. 16

/16

Oct

. 18

/17

Oct

. 28

/18

July

4/1

3

May

7/1

4

May

12

/15

May

2/1

6

May

10

/17

Ap

r. 3

0/1

8

Oct

. 20

/14

Oct

. 2

0/1

5

Oct

. 16

/16

Oct

. 18

/17

Oct

. 8/1

8

Au

gust

18

/15

Au

g. 2

1/1

6

Au

g. 1

7/1

7

Au

g. 2

7/1

8

Ch

loro

ph

yll a

(µ

g/l)

Date

Seasonal Chlorophyll a levels for Yarmouth County Lakes

Parr

Parr

FanningSloansRaynardsVaughan KegeshookSalmon

0

0.02

0.04

0.06

0.08

0.1

0.12

May

4/1

3

Oct

. 28

/13

Oct

. 20

/14

Oct

. 20

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

7/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 30

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 19

/15

Oct

. 16

/16

Oct

. 18

/17

Oct

. 28

/18

July

4/1

3

May

7/1

4

May

12

/15

May

2/1

6

May

10

/17

Ap

r. 3

0/1

8

Oct

. 20

/14

Oct

. 2

0/1

5

Oct

. 16

/16

Oct

. 18

/17

Oct

. 8/1

8

Au

gust

18

/15

Au

g. 2

1/1

6

Au

g. 1

7/1

7

Au

g. 2

7/1

8

Tota

l P (

mg/

l)

Date

Seasonal Total Phosphorus levels for Yarmouth County Lakes

ParrFanningSloansRaynardsVaughanKegeshookSalmon

0

0.01

0.02

0.03

0.04

0.05

0.06

0.07

0.08

0.09M

ay 4

/13

Oct

. 28

/13

Oct

. 20

/14

Oct

. 20

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

7/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 30

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 19

/15

Oct

. 16

/16

Oct

. 18

/17

Oct

. 28

/18

July

4/1

3

May

7/1

4

May

12

/15

May

2/1

6

May

10

/17

Ap

r. 3

0/1

8

Oct

. 20

/14

Oct

. 2

0/1

5

Oct

. 16

/16

Oct

. 18

/17

Oct

. 8/1

8

Au

gust

18

/15

Au

g. 2

1/1

6

Au

g. 1

7/1

7

Au

g. 2

7/1

8

Ort

ho

-P (

mg/

l)

Date

Seasonal Orthophoaphate levels for Yarmouth County Lakes


0

0.2

0.4

0.6

0.8

1

1.2

May

4/1

3

Oct

. 28

/13

Oct

. 20

/14

Oct

. 20

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

7/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 30

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 19

/15

Oct

. 16

/16

Oct

. 18

/17

Oct

. 28

/18

July

4/1

3

May

7/1

4

May

12

/15

May

2/1

6

May

10

/17

Ap

r. 3

0/1

8

Oct

. 20

/14

Oct

. 2

0/1

5

Oct

. 16

/16

Oct

. 18

/17

Oct

. 8/1

8

Au

gust

18

/15

Au

g. 2

1/1

6

Au

g. 1

7/1

7

Au

g. 2

7/1

8

Ort

ho

-P:T

ota

l P

Date

Seasonal Orthophoaphate:Total Phosphorus Ratios for Yarmouth County Lakes


0

50

100

150

200

250

May

4/1

3

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July

7/1

3

May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July

3/1

3

May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July

3/1

3

May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July

4/1

3

May

7/1

4

May…

May

2/1

6

May…

Apr.…

Oct.…

Oct.…

Oct.…

Oct.…

Oct

. 8/1

8

Augu

st…

Aug.…

Aug.…

Aug.…

Co

lou

r (T

CU

)

Date

Seasonal Colour Levels for Yarmouth County Lakes


0

1

2

3

4

5

6

7

May

4/1

3

Oct

. 28

/13

Oct

. 20

/14

Oct

. 20

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

7/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 30

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 19

/15

Oct

. 16

/16

Oct

. 18

/17

Oct

. 28

/18

July

4/1

3

May

7/1

4

May

12

/15

May

2/1

6

May

10

/17

Ap

r. 3

0/1

8

Oct

. 20

/14

Oct

. 2

0/1

5

Oct

. 16

/16

Oct

. 18

/17

Oct

. 8/1

8

Au

gust

18

/15

Au

g. 2

1/1

6

Au

g. 1

7/1

7

Au

g. 2

7/1

8

Secc

hi D

ep

th (

m)

Date

Seasonal Secchi Depths for Yarmouth County Lakes

ParrFanningSloansRaynards VaughanKegeshookSalmon

0

0.1

0.2

0.3

0.4

0.5

0.6

0.7

0.8

May

4/1

3

Oct

. 28

/13

Oct

. 20

/14

Oct

. 20

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

7/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 28

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 18

/15

Oct

. 16

/16

Oct

. 15

/17

Oct

. 30

/18

July

3/1

3

May

11

/14

Oct

. 19

/14

Oct

. 19

/15

Oct

. 16

/16

Oct

. 18

/17

Oct

. 28

/18

July

4/1

3

May

7/1

4

May

12

/15

May

2/1

6

May

10

/17

Ap

r. 3

0/1

8

Oct

. 20

/14

Oct

. 2

0/1

5

Oct

. 16

/16

Oct

. 18

/17

Oct

. 8/1

8

Au

gust

18

/15

Au

g. 2

1/1

6

Au

g. 1

7/1

7

Au

g. 2

7/1

8

Tota

l N (

mg/

l)

Date

Seasonal Total Nitrogen Levels for Yarmouth County Lakes

ParrFanningSloansRaynards VaughanKegeshookSalmon

0

1

2

3

4

5

6

7

8May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July…

May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July…

May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July…

May…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

July…

May…

May…

May…

May…

Apr.…

Oct.…

Oct.…

Oct.…

Oct.…

Oct.…

Augu

…

Aug.…

Aug.…

Aug.…

pH

Date

Seasonal pH for Yarmouth County Lakes ParrFanningSloansRaynardsVaughanKegeshookSalmon

Appendix 4. Comparison of Surface and Bottom Parameters for Selected Lakes

Database

Lake_ID Level and

Year Date

Secchi Depth

(m)

Chlorophyll a (µg/l)

Total Phosphorus

(mg/l)


Orthophosphate/ Total Phosphorus

ratio

Total Nitrate (mg/l)

Total Nitrogen

(mg/l)

Colour (TCU)

pH

Hourglass Surface08 Aug.

13/2008 1.3 15 0.069 0.034 0.493 0.03 0.57 60 6.20

Hourglass Surface10 Sept.

25/2010 1.25 13 0.05 0.022 0.440 0.01 0.35 58 6.80


13/2011 1.4 2.1 0.045 0.018 0.400 0.04 0.64 89 6.80


12/2013 0.63 7 0.056 0.029 0.518 <0.01 0.56 161.7 6.07


18/2014 0.8 44 0.067 0.037 0.552 <0.01 0.45 145.2 6.31

Hourglass Surface 15 Aug.

17/2015 0.93 19 0.065 0.038 0.585 <0.01 0.4 105 6.35


21/2016 0.925 44.9 0.08 0.026 0.325 <0.01 0.39 66.5 6.50


24/17 1 49.8 0.073 0.028 0.383562 <.02 0.41 80.4 6.7


28/18 1 24.1 0.118 0.056 0.474576 <.01 0.49 67.2 6.9

Hourglass Bottom08 Aug.

13/2008 1.3 15

Hourglass Bottom10 Sept.

25/2010 1.25 13


13/2011 1.4 2.1 0.39 0.33 0.846 0.01 167


12/2013 0.63 7 0.374 0.172 0.460 <0.01 2.19 270.8 6.07


18/2014 0.8 44 0.564 0.454 0.805 <0.01 1.35 316.4 6.31


17/2015 0.93 0.429 0.383 0.893 0.02 1.05 280 6.10

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH


21/2016 0.925 0.442 0.357 0.808 <0.01 0.97 166 7.00


24/17 1 0.651 0.52 0.798771 <.01 1.86 205 7.1


28/18 1 0.975 0.844 0.865641 <.01 3.63 174 7.2

Placides Surface08 Aug.

13/2008 1.3 20 0.74 0.58 0.784 0.35 1.69 68 6.50

Placides Surface10 Sept.

26/2010 0.7 15.5 0.82 0.705 0.860 0.47 1.23 90 6.90


22/2011 2.8 0.96 0.786 0.819 0.58 1.83 117 6.80


6/2013 0.4 52 0.792 0.764 0.965 0.52 1.34 227.8 6.80


25/2014 0.625 32 0.806 0.611 0.758 <0.01 0.57 149.5

Placides Surface 15 Aug.

26/2015 0.95 22 0.698 0.592 0.848 <0.01 0.5 126


30/2016 1.4 15.05 0.624 0.5725 0.917 <0.01 0.38 66 6.90


22/17 3.375 8.28 0.618 0.506 0.81877 <.01 0.46 98.6 6.2


29/17 1 4.01 0.609 0.512 0.840722 <.01 0.48 96.8 6.8


29/18 1.3 14.1 0.583 0.481 0.825043 <.01 0.45 69.4 6.9

Placides Bottom08 Aug.

13/2008 1.3 20 5.2 5.2 1.000 0.02 2.95 202 6.30

Placides Bottom10 Sept.

26/2010 0.7 15.5 0.83 0.652 0.786 0.54 1.28 97 6.90


22/2011 2.8 2.1 1.78 0.848 0.16 4.32 132.7

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH


6/2013 0.4 52 2.600 2.600 1.000 0.35 1.68 393.9 7.10


25/2014 0.625 39 4.46 3.92 0.879 <.01 3.22 305.6

Placides Bottom 15 Aug.

26/2015 0.95 291 4.32 4.06 0.940 <.01 2.8 291

Placides Bottom 16 Aug.

30/2016 1.4 3.02 2.78 0.920 0.01 1.47 148 7.20


22/17 3.375 0.661 0.528 0.79879 <.01 0.54 106 6.9


29/17 1 0.615 0.522 0.84878 <.01 0.46 97.3 6.8


29/18 1.3 1.896 1.516 0.799578 <.01 1.33 160 7.3

Porcupine Surface08 Aug.

12/2008 2.5 7.8 0.012 0.005 0.417 0.01 0.22 25 6.60

Porcupine Surface10 Sept.

26/2010 1.95 2.8 0.021 0.005 0.238 0.01 0.25 39 6.80


14/2011 0.9 3.4 0.014 0.005 0.357 0.01 0.3 46.6 6.90


6/2013 0.59 7 0.032 0.014 0.436 0.02 0.42 105.3 6.90


25/2014 1.63 6.9 0.016 0.005 0.313 <.01 0.28 73.2


26/2015 1.9 7.3 0.016 0.003 0.188 <.01 0.24 53.2

Porcupine Surface 16 Aug.

30/2016 2.3 3.2 0.018 0.0055 0.306 <.01 0.255 30.55 6.80


22/17 0.875 2.41 0.017 0.013 0.764706 <.01 0.29 44.7 6.9


29/17 2.5 1.13 0.013 0.004 0.307692 <.01 0.3 38.3 6.8


29/18 1.9 5.53 0.01 0.003 0.3 <.01 0.26 23.9 7.0

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

Porcupine Bottom08 Aug.

12/2008 2.5 7.8 0.021 0.005 0.238 0.01 0.4 87 6.30

Porcupine Bottom10 Sept.

26/2010 1.95 2.8 0.13 0.01 0.26 6.80


14/2011 0.9 3.4 0.08 72.3


6/2013 0.59 0.044 0.027 0.614 0.14 0.5 89.5 6.90


25/2014 1.63 0.058 0.038 0.655 0.17 0.61 111.6

Porcupine Bottom 15 Aug.

26/2015 1.9 0.062 0.039 0.629 0.14 0.61 102


30/2016 2.3 0.056 0.034 0.607 <.01 0.44 47.8 7.00


22/17 0.875 0.065 0.024 0.369231 0.05 0.46 52 6.9


29/17 2.5 0.016 0.006 0.375 0.04 0.29 45.1 6.8


29/18 1.9 0.138 0.096 0.695652 <.01 0.9 102 7.2

Wentworth Surface13 Aug.

12/2013 0.46 14 0.16 0.138 0.863 0.01 0.58 250.6 5.58


18/2014 0.33 13 0.187 0.14 0.749 <.01 0.54 304.1 5.64

Wentworth Surface 15 Aug.

17/2015 0.6 11 0.13 0.111 0.854 <.01 0.37 182 6.00

Wentworth Surface 16 Aug.

21/2016 1.57 3.9 0.154 0.146 0.948 0.06 0.51 115 6.10


21/17 0.625 4.63 0.084 0.082 0.97619 <.01 0.46 158 6.3


28/18 1 14.7 0.128 0.089 0.695313 <.01 0.48 128 6.5

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

Wentworth Bottom13 Aug.

12/2013 0.46 14 0.174 0.144 0.828 0.02 0.58 252.5 5.54


18/2014 0.33 13

Wentworth Bottom 15 Aug.

17/2015 0.6 0.139 0.123 0.885 <.01 0.53 192 5.72

Wentworth Bottom 16 Aug.

21/2016 1.57 0.154 0.104 0.675 0.06 0.53 117 6.10


21/17 0.625 0.128 0.092 0.71875 <.01 0.46 164 6.1


28/18 1 0.139 0.093 0.669065 <.01 0.45 127 6.4

Parr Surface08 Aug.

14/2008 1.5 11 0.033 0.012 0.364 0.01 0.27 64 6.20

Parr Surface10 Aug.

24/2010 1 6.7 0.075 0.075 1.000 0.01 0.03 97.2 6.20

Parr Surface11 Sept.

26/2010 0.75 13 0.061 0.031 0.508 0.01 0.33 86 6.20

Parr Surface13 Aug.

12/2013 0.51 6.1 0.105 0.08 0.762 0.04 0.53 199.6 5.71

Parr Surface14 Aug.

25/2014 0.57 11 0.111 0.084 0.757 <.01 0.49 193.9 5.86

Parr Surface 15 Aug.

20/2015 1.8 7.8 0.075 0.047 0.627 <.01 0.41 123 6.26


21/2016 1.35 13.7 0.055 0.022 0.400 <.01 0.38 67.7 6.30


23/18 0.9 11.9 0.056 0.022 0.392857 <.01 0.32 83 6.4

Parr Bottom08 Aug.

14/2008 1.5 11

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

Parr Bottom10 Sept.

27/2010 1 6.7

Parr Bottom11 Aug.

25/2011 0.75 13 0.076 0.046 0.605 0.01 0.036 99

Parr Bottom13 Aug.

12/2013 0.51 6.1 0.107 0.082 0.766 0.04 0.54 216.6 5.54

Parr Bottom14 Aug.

25/2014 0.57 11 0.124 0.091 0.734 <.01 0.46 203.1 5.81

Parr Bottom 15 Aug.

20/2015 1.8 0.134 0.099 0.739 <.01 0.56 211 5.71

Parr Bottom16 Aug.

21/2016 1.35 0.069 0.035 0.507 0.02 0.4 76.2 6.30

Parr Bottom18 Aug.

23/18 0.9 0.059 0.022 0.372881 <.01 0.34 74.4 6.5

Ogden Surface08 Aug.

14/2008 1.8 10 0.014 0.005 0.357 0.01 0.25 39 6.10

Ogden Surface10 Sept.

27/2010 0.95 18.8 0.029 0.008 0.276 0.05 0.35 58 6.30


24/2011 1.2 12.5 0.022 0.005 0.227 0.01 0.28 59.2 6.10


6/2013 0.6 9.4 0.052 0.035 0.673 0.02 0.41 145.3 6.40


25/2014 0.66 26 0.046 0.021 0.457 <.01 0.44 126.5 6.20

Ogden Surface 15 Aug.

20/2015 1.17 11 0.022 0.004 0.182 <.01 0.32 83.2 6.53


21/2016 1.25 4.46 0.024 0.004 0.167 0.02 0.33 41.6 6.30


26/18 1.375 16.8 0.018 <.002 0.055556 <.01 0.31 55.2 6.6

Ogden Bottom08 Aug.

14/2008 1.8 10 0.097 0.051 0.526 0.01 0.8 152 5.90

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

Ogden Bottom10 Sept.

27/2010 0.95 18.8 0.26 0.194 0.746 0.01 1.79 206 7.00

Ogden Bottom11 Aug.

24/2011 1.2 12.5 0.094 0.038 0.404 0.02 0.74 107.1

Ogden Bottom13 Aug.

6/2013 0.6 9.4 0.960 0.720 0.750 0.13 0.58 141.9 6.40

Ogden Bottom14 Aug.

25/2014 0.66 26 0.102 0.074 0.725 0.02 0.75 198.4 5.95

Ogden Bottom15 Aug.

20/2015 1.17 0.058 0.041 0.707 0.08 0.48 88.1 5.52

Ogden Bottom16 Aug.

21/16 1.25 0.205 0.138 0.673 <.01 0.74 126 6.90

Ogden Bottom18 Aug.

26/18 1.375 0.038 0.009 0.236842 <.01 0.37 65.4 6.7

Fanning Surface08 Aug.

16/2008 2.3 5.8 0.011 0.005 0.455 0.01 0.21 31 6.40

Fanning Surface09 Sept.

12/2009 0.75 1.3 0.056 0.037 0.661 0.06 0.4 120 5.90

Fanning Surface10 Sept.

29/2010 1.15 21.9 0.021 0.005 0.238 0.06 0.35 55 6.40


17/2011 1.3 19.2 0.023 0.005 0.217 0.01 0.05 63.1 6.20


11/2013 1.01 3.8 0.045 0.023 0.511 0.01 0.4 131.4 5.93


24/2014 0.98 8.7 0.027 0.012 0.444 0.02 0.34 99 6.07


16/2015 1.4 14 0.019 0.006 0.316 <.01 0.34 73.6 6.19

Fanning Surface 16 Aug.

21/2016 1.55 10.4 0.023 0.003 0.130 0.03 0.32 43.8 6.40


23/17 1.5 3.39 0.022 0.01 0.454545 <.01 0.33 82.2 6.4


27/18 1.8 10.8 0.014 0.004 0.285714 <.01 0.26 41.6 6.6

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

Fanning Bottom08 Aug.

16/2008 2.3 5.8 0.097 0.055 0.567 0.01 0.62 137 6.50

Fanning Bottom09 Sept.

12/2009 0.75 1.3 0.06 0.037 0.617 0.06 0.4 122 5.90

Fanning Bottom10 Sept.

29/2010 1.15 21.9


17/2011 1.3 19.2 0.082 0.054 0.659 0.01 0.045 202.2


11/2013 1.01 3.8 0.044 0.026 0.591 0.02 0.38 130.6 5.82


24/2014 0.98 8.7 0.036 0.02 0.556 0.02 0.4 105.7 5.89


16/2015 1.4 0.039 0.023 0.590 <.01 0.28 95.2 5.27


21/2016 1.55 0.041 0.016 0.390 0.02 0.46 65.2 6.60


23/17 1.5 0.01 0.005 0.5 <.01 0.33 91.8 6.4

Fanning Bottom 18 Aug.

27/18 1.8 0.086 0.068 0.790698 <.01 0.52 119 7.0

Sloans Surface09 Sept.

12/2009 3.8 1.9 0.005 0.005 1.000 0.01 0.18 20 6.90

Sloans Surface10 Sept.

30/2010 4.3 4.3 0.009 0.005 0.556 0.01 0.12 12 7.00

Sloans Surface11 Aug.

15/2011 4.6 4.6 0.005 0.005 1.000 0.01 0.13 15.3 7.00


11/2013 3.11 2.4 0.004 0.0025 0.625 <0.01 0.14 22.3 6.77


24/2014 4.65 1.8 0.004 0.001 0.250 <0.01 0.13 20.1 6.85

Sloans Surface 15 Aug.

16/2015 5.375 2.2 0.004 0.004 1.000 0.02 0.16 21.2

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH


28/2016 6.25 1.78 0.004 0.004 1.000 0.01 0.14 18.6 6.90


21/17 4.35 1.35 0.004 0.004 1 <.01 0.15 14.6 7.0


27/18 4.75 1.37 0.003 0.003 1 <.01 0.15 10.5 7.1

Sloans Bottom09 Sept.

12/2009 3.8 1.9 0.007 0.000 0.06 0.09 15 6.80

Sloans Bottom10 Sept.

30/2010 4.3 4.3 0.007 0.005 0.714 0.01 0.08 18 6.90

Sloans Bottom11 Aug.

15/2011 4.6 4.6 0.01 0.005 0.500 0.02 0.12 16.9 6.90


11/2013 3.11 2.4 0.004 0.0025 0.625 0.02 0.18 18.7 5.90


24/2014 4.65 1.8 0.008 0.001 0.125 0.01 0.17 32.9 5.93


16/2015 5.375 0.005 0.005 1.000 0.06 0.22 31 6.84


28/2016 6.25 0.032 0.005 0.156 0.03 0.27 25 7.00


21/17 4.35 0.006 0.006 1 0.04 0.21 15.3 6.9


27/18 4.75 0.006 0.006 1 0.03 0.17 12.7 7.0

Raynards Surface13 Aug.

11/2013 1.2 26.65797 0.021262 6.20


24/2014 1.23 16 0.013 0.002 0.153846 <0.01 0.27 54 6.19


19/2015 1.85 12 0.011 0.004 0.364 <0.01 0.27 47 6.44


24/2016 1.5 4.27 0.009 0.004 0.444 <0.01 0.2 32.3 6.50

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

Raynards Surface 17 Aug.

14/17 2.25 5.3 0.012 0.004 0.333333 <.01 0.24 43.9 6.5

Raynards Surface 18 Aug.

26/18 2.5 5.79 0.008 <.002 0.125 <.01 0.2 31.6 6.6

Raynards Bottom13 Aug.

11/2013 1.2 5.66


24/2014 1.23 0.017 0.010 0.588 0.05 0.23 65.5 5.75


19/2015 1.85 0.014 0.004 0.286 <0.01 0.46 81.6 6.20


24/2016 1.4 0.009 0.004 0.444 <0.01 0.22 33.7 6.60


14/17 2.25 0.024 0.008 0.333333 <.01 0.3 56.3 6.6


26/18 2.5 0.008 <.002 0.125 <.01 0.19 31 6.6

Vaughan Surface08 Sept.

4/2008 3 3.9 0.012 0.005 0.417 0.01 0.17 22 7.20

Vaughan Surface10 Sept.

30/2010 1.2 2.8 0.019 0.005 0.264 0.04 0.34 69 6.20

Vaughan Surface11 Aug.

16/2011 1.9 2.6 0.01 0.005 0.5010 0.01 0.22 63 6.20


13/2013 1.17 14 0.02 0.0025 0.125 <0.01 0.29 81 6.24


18/2014 1.43 14 0.012 0.003 0.250 <0.01 0.35 54.9 6.32


18/2015 1.8 10 0.01 0.003 0.300 <0.01 0.24 57 6.52

Vaughan Surface 16 Aug.

24/2016 1.3 7.87 0.008 0.003 0.375 <0.01 0.21 41.8 6.40


24/17 1.625 14.7 0.015 0.01 0.666667 <.01 0.28 51.2 6.5

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH


21/18 1.4 2.96 0.01 0.002 0.2 <.01 0.22 53 6.5

Vaughan Bottom08 Sept.

4/2008 3 3.9 0.045 0.005 0.111 0.01 0.73 148 6.30

Vaughan Bottom10 Sept.

30/2010 1.2 2.8 0.078 0.043 0.551 0.01 0.5 181 7.10

Vaughan Bottom11 Aug.

16/2011 1.9 2.6 0.087 0.061 0.701 0.01 0.65 112 7.20


13/2013 1.17 14 0.015 0.0025 0.167 <0.01 0.27 79.8 6.43


18/2014 1.43 14 0.04 0.02 0.500 <0.01 0.56 108.5

Vaughan Bottom 15 Aug.

18/2015 1.8 0.083 0.05 0.602 <0.01 0.81 238 6.28


24/2016 1.3 0.053 0.041 0.774 <0.01 0.53 88.1 7.00


24/17 1.625 0.136 0.103 0.757353 <.01 0.91 189 7.2


21/18 1.4 0.081 0.057 0.703704 <.01 0.8 142 7.1

Provost Surface08 Aug.

14/2008 1.7 18 0.011 0.005 0.455 0.01 0.45 32 6.10

Provost Surface10 Sept.

30/2010 1.7 20.3 0.016 0.005 0.313 0.04 0.29 36 6.00


14/2011 0.6 19.6 0.011 0.005 0.455 0.01 0.03 43.8 6.00


13/13 0.99 32 0.016 0.0025 0.156 0.05 0.48 74.3 5.96


24/2014 1.05 31 0.016 0.006 0.375 0.02 0.52 82.6

Provost Surface 15 Aug.

25/2015 2.65 4.8 0.016 0.002 0.125 <0.01 0.25 42.1

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH


30/2016 2.4 5.675 0.017 0.0045 0.265 <0.01 0.27 19.7 6.30


22/17 2.2 4.15 0.008 0.004 0.5 <.01 0.29 34.3 6.4


30/17 3 4.7 0.012 0.001 0.083333 <.01 0.27 34 6.2


30/18 2.35 3.79 0.009 0.002 0.111111 <.01 0.24 23.8 6.5

Provost Bottom08 Aug.

14/2008 1.7 18

Provost Bottom10 Sept.

30/2010 1.7 20.3


14/2011 0.6 19.6 0.016 0.005 0.313 0.01 0.03 55.4


13/2013 0.99 32 0.014 0.0025 0.179 0.05 0.54 86.4 5.59


24/2014 1.05 31 0.166 0.098 0.590 <0.01 2.7 431


25/2015 2.65 0.091 0.045 0.495 <0.01 1.51 372


30/2016 2.4 0.022 0.006 0.273 <0.01 0.36 39.6 6.50


22/17 2.2 0.014 0.003 0.214286 <.01 0.26 36.1 6.5


30/17 3 0.045 0.014 0.311111 <.01 1.2 114 7.0


30/18 2.35 0.017 0.006 0.352941 <.01 0.68 89.5 7.0

Nowlans Surface 15 Aug.

25/2015 0.625 90 0.497 0.43 0.865 <0.01 0.77 58.9

Nowlans Surface16 Aug.

31/2016 0.85 73.9 0.556 0.525 0.944 <0.01 n/a 15.3 7.35

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH


29/17 1 48.6 0.553 0.437 0.790235 0.01 n/a 25.4 7.3


30/18 0.85 47.1 0.464 0.409 0.881466 <.01 n/a 14 9.1

Nowlans Bottom15 Aug.

25/2015 0.625 2.16 1.98 0.917 <0.01 2.6 89.7


31/2016 0.85 4.18 3.73 0.892 <0.01 5.6 130 7.30


29/17 1 0.764 0.522 0.683246 0.02 1.28 24.2 7.3


30/18 0.85 4.942 2.845 0.575678 <.01 6.03 191 7.4

Kegeshook Surface 14 August

21/2014 1.97 3.4 0.005 0.001 0.200 <0.01 0.18 60.8

5.96

Kegeshook Surface/15 August

24/2015 2.215 5.1 0.006 0.004 0.667 <0.01 0.19 64.2

6.04

Kegeshook Surface 16 August

21/2016 1.87 14.9 0.007 0.003 0.429 <0.01 0.18 38.2

6.4

Kegeshook Surface 17 Aug.

28/17 1.25 2.75 0.005 0.003 0.6 <.01 0.21 56.5 6.3

Kegeshook Surface 18 Aug.

23/18 1.65 4.42 0.006 <.002 0.166667 <.01 0.19 43.1 6.6

Kegeshook Bottom 14 August

21/2014 1.97 0.013 0.005 0.385 <0.01 0.02 88.2

5.42

Kegeshook Bottom15 August

24/2015 2.215 0.009 0.009 1.000 0.02 0.2 55.6

5.34

Kegeshook Bottom 16 August

21/2016 1.87 0.008 0.003 0.375 <0.01 0.18 45.1

6.4

Kegeshook Bottom17 Aug.

28/17 1.25 0.051 0.006 0.117647 <.01 0.22 60.7 6.6

Kegeshook Bottom18 Aug. 1.65 0.143 0.004 0.027972 <.01 0.28 39.6 6.5

Lake_ID Level and

Year Date

Secchi Depth

(m)


Total Phosphorus

(mg/l)



ratio


Total Nitrogen

(mg/l)

Colour (TCU)

pH

23/18

Salmon Surface 15 Aug.

18/2015 1.55 4.9 0.014 0.004 0.286 <0.01 0.76 90.4

6.16

Salmon Surface 16 Aug.

21/2016 2.25 9.99 0.016 0.003 0.188 <0.01 0.28 53.3

6.4

Salmon Surface17 Aug.

17/17 1.38 2.28 0.009 0.004 0.444444 <.01 0.48 108 6.2

Salmon Surface18 Aug.

27/18 1.625 5.3 0.01 0.006 0.6 <.01 0.35 53 6.4

Salmon Bottom 15 Aug.

18/2015 1.55 0.015 0.006 0.400 <0.01 0.77 98.5

5.69

Salmon Bottom 16 Aug.

21/2016 2.25 0.018 0.004 0.222 <0.01 0.28 52.7

6.3

Salmon Bottom17 Aug.

17/17 1.38 0.01 0.001 0.1 <.01 0.38 106 6.3

Salmon Bottom18 Aug.

27/18 1.625 0.01 0.006 0.6 <.01 0.29 53 6.6

No bottom phosphorus data for 2008 nor 2010.

0

0.2

0.4

0.6

0.8

1

1.2P

ho

sph

oru

s (

mg/

l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Hourglass

0

1

2

3

4

5

6P

ho

sph

oru

s (

mg/

l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Placides

No bottom phosphorus data for 2010 nor 2011.

0

0.02

0.04

0.06

0.08

0.1

0.12

0.14

0.16

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Porcupine

0

0.02

0.04

0.06

0.08

0.1

0.12

0.14

0.16

0.18

0.2

Surface13 Surface14 Surface 15 Surface 16 Surface17 Surface 18 Bottom13 Bottom14 Bottom 15 Bottom 16 Bottom17 Bottom18

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Wentworth

*No bottom phosphorus data for 2008 nor 2010.

0

0.02

0.04

0.06

0.08

0.1

0.12

0.14

0.16

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Parr

0

0.2

0.4

0.6

0.8

1

1.2P

ho

sph

oru

s (

mg/

l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Ogden

No bottom phosphorus data available for 2010.

0

0.02

0.04

0.06

0.08

0.1

0.12

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Fanning

0

0.005

0.01

0.015

0.02

0.025

0.03

0.035

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Sloans

0

0.005

0.01

0.015

0.02

0.025

0.03

Surface13 Surface14 Surface15 Surface16 Surface 17 Surface18 Bottom13 Bottom14 Bottom15 Bottom16 Bottom17 Bottom18

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Raynards

0

0.02

0.04

0.06

0.08

0.1

0.12

0.14

0.16

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Vaughan

No bottom phosphorus data available for 2008 nor 2010.

0

0.02

0.04

0.06

0.08

0.1

0.12

0.14

0.16

0.18P

ho

sph

oru

s (

mg/

l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Provost

0

1

2

3

4

5

6

Surface 15 Surface16 Surface17 Surface18 Bottom15 Bottom16 Bottom17 Bottom18

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Nowlans

0

0.02

0.04

0.06

0.08

0.1

0.12

0.14

0.16

Surface 14 Surface/15 Surface 16 Surface 17 Surface18 Bottom 14 Bottom15 Bottom 16 Bottom17 Bottom18

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Kegeshook

0

0.002

0.004

0.006

0.008

0.01

0.012

0.014

0.016

0.018

0.02

Surface 15 Surface 16 Surface17 Surface18 Bottom 15 Bottom 16 Bottom17 Bottom18

Ph

osp

ho

rus

(m

g/l)

Depth and Year

August-September Surface and Bottom Total phosphorus levels by Year: Salmon

Appendix 5: Comparison of Selected Spring Parameters at Inlets, Deep Stations, and Outlets on Parr and Fanning

LAKE Date Station Secchi (m)

Chlorophyll a (µg/L)

Color (TCUs)

Turbidity (NTUs)

Total Phosphorus (mg/L)

Orthophosphate (mg/L)

Total Nitrogen (mg/L)

pH (from lab)

Parr Oct. 22/09 PARL-INA 0.1 142 0.018 0.006 0.38 6

Sept. 27/10 PARL-INA 3.4 111 1.66 0.099 0.069 0.35 6.1

Aug. 25/11 PARL-INA 117.9 0.097 0.068 0.42

Parr Aug. 21/16 PARL-INA 71.8 2.64 0.06 0.023 0.38

Aug. 20/17 PARL-INA 0.875 1.08 213 1.27 0.04 0.026 0.58 5.2

Apr. 29/18 PARL-INA 1.125 104 1.23 0.027 0.012 0.26 5.7

Parr Oct. 22/09 PARL-INB 0.1 130 0.011 0.005 0.3 5

Sept. 27/10 PARL-INB 0.1 115 0.23 0.012 0.005 0.32 5.9

Aug. 25/11 PARL-INB 103.3 0.076 0.036 0.48

Aug. 21/16 PARL-INB

Parr Aug. 20/17 PARL-INB 1.05 216 1.5 0.016 0.007 0.61 4.9

Apr. 29/18 PARL-INB 1.125 104 0.86 0.022 0.008 0.37 5.7

Parr Oct. 22/09 PARL-INC 0.1 183 0.016 0.005 0.33 5

Sept. 27/10 PARL-INC 6.8 72 2.65 0.057 0.028 0.4 6.6

Aug. 25/11 PARL-INC 106.8 0.012 0.005 0.32

Parr Aug. 21/16 PARL-INC 71.2 2.3 0.063 0.027 0.35

Aug. PARL-INC 0.31 296 1.05 0.02 0.008 0.67 4.7

20/17

Apr. 29/18 PARL-INC 1.125 90.1 1.26 0.039 0.012 0.3 5.9

Parr Oct. 22/09

PARL-DS1Surface 176 0.96 0.075 0.56 5.4

Sept. 28/10

PARL-DS1Surface 13 86 1.88 0.061 0.031 0.33 6.2

Aug. 25/11

PARL-DS1Surface 6.7 97.2 0.075 0.075 0.034

Parr Aug. 21/16

PARL-DS1Surface 1.35 13.7 67.7 2.71 0.055 0.022 0.38 6.3

Aug. 20/17

PARL-DS1Surface 0.875

Apr. 29/18

PARL-DS1Surface 0.9 4.06 97.7 1.16 0.026 0.01 0.25 5.9

Parr Apr. 29/18 PARL-PE 1.125 32.9 0.46 0.007 0.003 0.17 6.4

Parr Oct. 22/09 PARL-OL1 168 0.076 0.059 0.52 5.5

Sept. 28/10 PARL-OL1 3.8 80 1.58 0.054 0.029 0.29 6.2

Aug. 25/11 PARL-OL1 92.1 0.062 0.033 0.33

Parr Aug. 21/16 PARL-OL1 58.3 2.19 0.038 0.008 0.34 6.3

Aug. 20/17 PARL-OL1 1.5 2.78 113 1.6 0.06 0.04 0.36 6.2

Apr. 29/18 PARL-OL1 1.125 86.9 0.96 0.023 0.01 0.24 6

Fanning Oct. 14/09 LF-IN1 1 130 0.064 0.043 0.46 5.9

Oct. 1/10 LF-IN1 1.9 50 1.15 0.24 0.005 0.41 6.6

Aug. 18/11 LF-IN1 70.2 4.64 0.018 0.005 6.1

Fanning Aug. 21/16 LF-IN1 47.4 0.52 0.026 0.011 0.31 6.4

Aug. 23/17 LF-IN1 2 105 1.12 0.03 0.017 0.37 6.2

Apr. 29/18 LF-IN1 1.625 76.8 0.79 0.021 0.008 0.22 6

Fanning Oct. 14/09 LF-IN2 1.2 113 0.02 0.005 0.38 6.3

Oct. 1/10 LF-IN2 1.9 43 0.54 0.008 0.005 0.21 6.7

Aug. 18/11 LF-IN2 45 0.61 0.007 0.005 0.2 6.8

Fanning Aug. 21/16 LF-IN2 31.4 0.44 0.011 0.006 0.2 6.9

Aug. 23/17 LF-IN2 2.45 92 0.94 0.011 0.004 0.34 6.4

Apr. 29/18 LF-IN2 1.625 55.8 0.53 0.009 0.004 0.19 6.2

Fanning Oct. 14/09 LF-IN3 0.7 37 0.007 0.005 0.26 6.4

Oct. 1/10 LF-IN3 23.9 0.32 0.005 0.005 0.14 6.6

Aug. 18/11 LF-IN3 23.9 0.32 0.005 0.005 0.14 6.6

Fanning Aug. 21/16 LF-IN3

Fanning Aug. 23/17 LF-IN3 0.95 33.5 0.4 0.004 0.004 0.19 6.6

Apr. 29/18 LF-IN3 1.625 34.4 0.6 0.006 0.003 0.18 6.5

Fanning Oct. 13/09

LF-DS1Surface 1.3 120 0.056 0.037 0.4 5.9

Sept. 30/10

LF-DS1Surface 21.9 55 2.82 0.021 0.005 0.35 6.4

Aug. 18/11

LF-DS1Surface 19.2 63.1 4.06 0.023 0.005 6.2

Fanning Aug. 21/16

LF-DS1Surface 1.55 10.4 43.8 2.11 0.023 0.003 0.32 6.4

Aug. 23/17

LF-DS1Surface 1.5 3.39 82.2 1.06 0.022 0.01 0.33 6.4

Apr. 29/18

LF-DS1Surface 1.625 4.95 68 0.89 0.02 0.007 0.22 6.2

Fanning Oct. 14/09 LF-OL 1.1 120 0.059 0.03 0.45 6

Oct. 1/10 LF-OL 6.5 42 2.17 0.019 0.005 0.31 6.5

Aug. 18/11 LF-OL 61.5 4.35 0.015 0.005 6.2

Fanning Aug. 21/16 LF-OL

Aug. 23/17 LF-OL 2.09 76.8 1.06 0.022 0.012 0.33 6.4

Apr. 29/18 LF-OL 1.625 65.9 0.9 0.018 0.006 0.21 6.1

0

0.2

0.4

0.6

0.8

1

1.2

Tota

l P (

mg/

l)

Date

Total phoshorus , Inlets, Outlet and Mid-Lake, ParrINAINBINCDeep stationPete's Inlet

Outlet

0

0.05

0.1

0.15

0.2

0.25

0.3

Tota

l P (

mg/

l)

Date

Total phoshorus , Inlets, Outlet and Mid-Lake, Fanning

IN1IN2IN3Deep stationOutlet

0

0.1

0.2

0.3

0.4

0.5

0.6

0.7

0.8

Tota

l N (

mg/

l)

Date

Total Nitrogen, Inlets, Outlet and Mid-Lake, Parr

INAINBINCDeep stationPete's Inlet

0

0.05

0.1

0.15

0.2

0.25

0.3

0.35

0.4

0.45

0.5

Tota

l N (

mg/

l)

Date

Total nitrogen, Inlets, Outlet and Mid-Lake, Fanning IN1IN2IN3Deep station

Outlet

0

50

100

150

200

250

300

350

Co

lou

r (T

CU

's)

Date

Colour, Inlets, Outlet and Mid-Lake, ParrINAINBINCDeep stationPete's InletOutlet

0

20

40

60

80

100

120

140

Co

lou

r (T

CU

's)

Date

Colour, Inlets, Outlet and Mid-Lake, Fanning IN1IN2IN3Deep station

Outlet

Appendix 6: Data on Cyanobacterial Abundance, Genus Composition and Microcystin

Lake Date Percent composition

Microcystin

(µg/l)

Anab

ae

na

Apah

niz

om

en

on

Apha

nocapsa

Apha

noth

ece

Chro

ococcus

Coelio

sph

ae

ri

um

Eucap

sis

Gom

ph

osp

ha

eria

Mic

rocystis

Meris

mop

edia

Oscilla

toria

Pla

nkto

lyn

gby

a

Pla

nkto

thrix

Spiru

lina

Woro

nic

hin

ia

Pseud

oa

na

ba

ena

Total Free Total

Provost Aug. 27/08 98.374 1.626 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

Oct. 27/09 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000

Oct. 1/10 21.053 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 78.947 100.000

Aug. 15/11 57.778 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 42.222 100.000

Aug. 25/15 3.819 0.000 6.205 0.000

0.000 0.000 8.592 0.000 0.000

0.000 0.000 81.384 100.000 <.20 <.20

Aug. 30/16 100.000 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 30/17 22.222 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 77.778 100.000

<.2

July 4/18 43.4 0 0 0 0 0 0 0 0 0 0 0 0 0 0 56.6 100

Aug. 30/18 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 <.2

Nowlan's Aug. 28/08 1.415 0.575 0.000 0.000

75.566 22.443 0.000 0.000 0.001

0.000 0.000 0.000 100.000 0.3

Oct. 15/08 1.652 0.620 0.000 0.000

96.872 0.857 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 15/09 0.000 98.815 1.185 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Sept. 26/10 0.047 11.696 0.000 0.000

0.000 88.097 0.000 0.000 0.000

0.000 0.000 0.160 100.000 0.3

Aug. 26/11 0.236 0.152 0.000 0.000

0.000 98.280 0.000 0.000 1.332

0.000 0.000 0.000 100.000 <.2 11.82

Aug. 7/13 1.049 2.380 4.513 0.000

0.000 92.058 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 25/15 2.423 9.546 0.000 0.000

0.000 8.893 0.000 0.000 0.000

0.000 79.138 0.000 100.000

0.37

Aug. 31/16 2.586 21.160 73.668 0.000

0.000

1.293 1.293 0.000 0.000 0.000

0.000 0.000 0.000 100.000

0.27

Nowlans Aug. 29/17 22.293 48.819 2.953 0.000 0.000 0.000 0.000 0.000 25.935 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

<.2

July 4/18 0 93.2 0 0 0 0 0 0.18 6.7 0 0 0 0 0 0 0 100

Aug. 30/18 11.1 7.6 0 0 0 0 0 6.9 68.0 0 0 0 0 0 0 6.4 100 <.2

Hourglass Aug. 27/08 0.000 100.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 20/09 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 100.000

0.000 0.000 0.000 100.000 <.2

Sept. 26/10 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 0.000

0.000 0.000 0.000 100.000 <.2

Aug. 14/11 0.000 0.000 0.000 0.000

0.000 34.483 0.000 0.000 48.276

0.000 0.000 17.241 100.000 <.2 <.2

Aug. 12/13 #DIV/0! #DIV/0! #DIV/0! #DIV/0!

#DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0!

#DIV/0! #DIV/0! #DIV/0! #DIV/0!

<.2

Aug. 17/15 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000

<.2

Aug. 22/16 86.916 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 13.084 100.000

<.2

July 5/17 #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0! #DIV/0!

Aug. 15/17 25.029 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 74.971 100.000

<.2

July 4/18 0 0 0 0 0 0 0 0 0 0 21.4 7.1 60.7 0 0 10.7 100

Aug. 15/18 100 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 100 <.2

Placides Aug. 27/08 0.000 100.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 21/09 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 84.670

0.000 0.000 15.330 100.000 <.2

Sept. 27/10 #DIV/0! #DIV/0! #DIV/0! #DIV/0!


#DIV/0! #DIV/0! #DIV/0! #DIV/0! <.2



#DIV/0! #DIV/0! #DIV/0! #DIV/0! <.2 <.2



#DIV/0! #DIV/0! #DIV/0! #DIV/0!

<.2

Aug. 26/15 12.162 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 87.838 100.000

<.2

Aug. 30/16 0.000 0.000 100.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

July 5/17 0.000 0.000 96.430 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 3.570 100.000

Aug. 29/17 0.000 0.000 23.077 76.923 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

<.2

July 4/18 12.09 0 0 44.2 0 0 0 0 0 0.38 0 0 0 0 0 43.3 100

Aug. 29/18 4.4 0 0 66. 7 0 0 0 0 0 0 0 26. 7 0 0 0 2.2 100 <.2

Porcupine Aug. 28/08 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 27/09 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 100.000

0.000 0.000 0.000 100.000 <.2

Sept. 27/10 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000 <.2

Aug. 15/11 60.920 0.000 0.000 0.000

5.747 0.000 0.000 11.494 0.000

0.000 0.000 21.839 100.000 <.2 <.2

Aug. 5/13 90.865 0.000 0.000 0.000

0.000 0.000 0.000 4.327 1.923

0.000 0.000 2.885 100.000

<.2

Aug. 26/15 0.257 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 99.743 100.000

<.2

Aug. 30/16 0.000 0.000 0.000 0.000

90.909

0.000 0.000 0.000 9.091 0.000

0.000 0.000 0.000 100.000

<.2

July 5/17 100.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

Aug. 29/17 0.000 4.762 0.000 95.238 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

<.2

July 4/18 90.9 0 0 0 0 0 0 0 0 0 0 0 0 0 0 9.1 100

Aug. 29/18 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 <.2

Wentwort

h Aug. 17/15 #DIV/0! #DIV/0! #DIV/0! #DIV/0!


#DIV/0! #DIV/0! #DIV/0! #DIV/0!

<.2

Aug. 22.16 100.000 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

July 5/17 0.000 0.000 100.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

August 15/17 40.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 60.000 100.000

<.2

July 4/18 0 0 100 0 0 0 0 0 0 0 0 0 0 0 0 0 100

Aug. 15/18 40 0 0 0 0 0 0 0 0 0 0 0 0 0 0 60 100 <.2

Parr Sept. 4/08 0.000 62.782 37.218 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 22/09 0.000 2.247 0.000 0.000

0.000 0.000 0.000 0.000 61.049

0.000 0.000 36.704 100.000 <.2

Sept. 27/10 21.569 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

78.431 0.000 0.000 100.000 <.2

Aug. 24/11 88.390 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 11.610 100.000 <.2 <.2

Aug. 12/13 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 20/15 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 22/16 100.000 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

July 5/17 89.130 0.000 10.870 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

August 15/17 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000 100.000

<.2

July 4/18 99.0 0 0 0 0 0 0 0 0 0 0 0.1 0 0 0 0 100

Aug. 15/18 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 <.2

Ogden Aug. 15/08 77.558 21.122 0.000 0.000

0.000 0.000 .00.000 1.320 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 22/09 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 33.333

0.000 0.000 66.667 100.000 <.2

Sept. 28/10 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Aug. 24/11 52.357 0.000 0.000 0.000

7.692 0.000 0.000 0.000 0.000

0.000 0.000 39.950 100.000 <.2 <.2

Aug. 6/13 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 20/15 99.748 0.000 0.000 0.168

0.084 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 22/16 100.000 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

July 11/17 100.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

Aug. 15/17 100.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

<.2

July 4/18 100 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 100

Aug. 15/18 100 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 100

Fanning Aug. 28/08 18.750 56.250 0.000 0.000

0.000 0.000 0.000 25.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 15/08 99.670 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.330

0.000 0.000 0.000 100.000 <.2

Oct. 13/09 0.000 20.000 0.000 0.000

0.000 0.000 0.000 0.000 80.000

0.000 0.000 0.000 100.000 <.2

Sept. 30/10 94.654 0.000 0.273 0.000

0.000 0.000 0.000 5.074 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 12/10 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Aug. 16/11 54.779 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 45.221 100.000 <.2 <.2

Aug. 11/13 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 16/15 100.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 22/16 #DIV/0! 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 #DIV/0!

<.2

July 11/17 97.189 0.000 1.606 0.000 1.205 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

Aug. 15/17 98.923 0.000 0.000 0.000 0.000 0.000 1.077 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

<.2

July 4/18 99.8 0.1 0 0 0 0 0 0.1 0 0 0 0 0 0 0 0 100

Aug. 15/18 8.9 0 0 0 0 0 14.3 67.9 0 0 0 0 0 0 0 8.9 100 <.2

Sloans Sept. 9/09 0.000 0.000 0.000 44.914

47.824 0.000 0.000 0.000 5.363

0.000 0.000 1.900 100.000 <.2

Nov. 5/09 0.000 1.156 14.451 28.902

55.491 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 1/10 0.000 0.000 28.777 7.194

25.180 0.000 0.000 0.000 0.000

0.000 0.000 38.849 100.000 <.2

Aug. 16/11 0.000 0.000 11.682 0.000

75.935 11.682 0.000 0.000 0.000

0.000 0.000 0.701 100.000

<.2

Aug. 11/13 0.000 0.000 0.000 45.455

54.545 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

Aug. 16/15 0.000 0.000 0.000 40.816

51.020 0.000 0.000 0.000 0.000

0.000 0.000 8.163 100.000

<.2

Aug. 22/16 0.000 0.000 0.000 28.571

0.000

71.429 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000

<.2

July 5/17 0.000 0.000 10.582 17.637 0.176 0.000 0.000 62.610 0.000 8.995 0.000 0.000 0.000 0.000 0.000 0.000 100.000

Aug. 15/17 0.000 0.000 0.000 43.103 0.000 0.000 0.000 51.724 0.000 0.000 0.000 0.000 5.172 0.000 0.000 0.000 100.000

<.2

July 4/18 0 0 16.9 54.8 0 0 0 4. 7 0 18.0 0 3.7 0 0 0 2.0 100 <.2

Aug. 15/18 0 0 45.6 27.5 0 0 0 26.9 0 0 0 0 0 0 0 0 100

Raynards Aug. 19/15 96.970 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 3.030 100.000

<.2

Aug. 22/16 0.000 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000

<.2

July 5/17 100.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

Aug. 15/17 100.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000

<.2

July 4/18 100 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 100

Aug. 15/18 0 0 0 0 0 0 76.2 0 0 0 0 0 0 0 0 23.8 100 <.2

Vaughan Sept. 5/08 0.000 100.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 100.000 <.2

Oct. 28/09 #DIV/0! #DIV/0! #DIV/0! #DIV/0!


#DIV/0! #DIV/0! #DIV/0! #DIV/0! <.2

Sept. 30/10 0.000 0.000 0.000 0.000

0.000 0.000 0.000 30.769 0.000

0.000 0.000 69.231 100.000 <.2

Aug. 17/11 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000 <.2 <.2

Aug. 13/13 83.333 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 16.667 100.000

<.2

Aug. 19/15 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000

<.2

Aug. 22/16 0.000 0.000 0.000 0.000

0.000

0.000 0.000 0.000 0.000 0.000

0.000 0.000 100.000 100.000

<.2

July 5/17 97.597 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.364 0.000 0.000 0.000 0.000 2.039 100.000

Aug. 15/17 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 100.000 100.000

<.2

July 4/18 100 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 100

Aug. 15/18 0 0 0 100 0 0 0 0 0 0 0 0 0 0 0 0 100 <.2

Kegeshook June 27/17 2.633 0.000 0.311 92.247 0.000 0.000 0.000 0.643 0.000 4.115 0.000 0.000 0.000 0.000 0.000 0.052 100.000

July 3/18 2.8 0 0 0 0 0 0 56.7 0 36.3 0 0 0 0 0 4.2 100

Aug. 20/18 0 3.2 64.5 0 0 0 0 32.3 0 0 0 0 0 0 0 0 100 <.2

Salmon July 4/17 0.000 0.000 0.000 0.000 0.000 0.000

0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000 #DIV/0!

July 3/18 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0

Aug. 20/18 0 0 17.0 0 0 0 76.2 0 0 0 0 0 0 0 0 6.8 100 <.2

1Averaged among more than one collecting site

Appendix 7: Calculated Carlson Trophic State Indices, based on August Data

Year Provost Nowlans Hourglass Placides Porcupine Wentworth Parr Ogden Fanning Sloans Raynards Vaughan Kegeshook Salmon

2018 42.4 74.5 64.9 69.6 45.2 65.5 59.5 53.2 49.2 30.4 42.9 44.6 42.7 45.8

2017 43.3 74.6 65.0 66.9 39.9 56.8 48.5 32.2 45.1 51.1 41.6 43.3

2016 46.7 76.8 65.5 69.8 45.3 58.1 58.0 50.7 52.2 31.3 44.9 47.1 46.8 48.5

2015 52.1 78.4 61.6 79.7 48.3 64.2 56.2 53.5 52.7 32.7 48.3 47.4 41.9 47.4

2014 55.9 66.2 82.6 48.9 67.7 63.1 61 54.6 32.8 52 50.3 40.1

2013 56.3 55.9 84.9 57.1 66.8 59.8 56.9 51.4 35.5 53.9

2011 55.3 50.7 48.8 58.6 53.8 55.1 42.7

2010 77.1 57.7 80.2 46.4 61.1 57.6 55.6

2008 50 74.9 59.5 71.9 45.8 54.3 49 44.9 38.5

Numbers in red reflect cases where colour was over 125 TCU’s; therefore, Secchi depth was not included in the TSI Calculation.

TSI Range Trophic Status

<40 Oligotrophic (nutrient-poor)

40-50 Mesotrophic

50-70 Eutrophic (nutrient rich)

>70 Hypereutrophic

0

10

20

30

40

50

60

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Provost

72

73

74

75

76

77

78

79

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Nowlans

0

10

20

30

40

50

60

70

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Hourglass

0

20

40

60

80

100

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Placides

0

20

40

60

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Porcupine

50

55

60

65

70

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Wentworth

48

50

52

54

56

58

60

62

64

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Parr

0

10

20

30

40

50

60

70

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Ogden

0

10

20

30

40

50

60

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Fanning

26

28

30

32

34

36

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Sloans

0

10

20

30

40

50

60

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Raynards

0

10

20

30

40

50

60

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Vaughan

0

10

20

30

40

50

60

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Kegeshook

40

42

44

46

48

50

2008 2010 2011 2013 2014 2015 2016 2017 2018

Car

lso

n T

SI I

nd

ex

Year

Carlson TSI Summer Indices, Salmon

Appendix 8:

Mann-Kendall trend analysis on select parameters for August surface composite sample results

Watershed Lake

Parameter

Chlorophyll a TP Secchi Orthophosphate Total Nitrogen Colour Temperature

Trend Peak

Concentration Year

Peak Concentration

(µg/L)

Start Year

# of Years

Trend Peak

Concentration Year

Peak Concentration

(mg/L)

Start Year

# of Years

Trend Trend Trend Trend Peak

Concentration Year

Peak Concentration

(TCU)

Start Year

# of Years

Trend

Carleton

Hourglass INCREASING 2017 49.8 2008 8 INCREASING 2018 0.118 2008 8 No Trend No Trend DECREASING No Trend 2013 161.7 2008 8 INCREASING

Porcupine DECREASING 2008 7.8 2008 8 No Trend 2013 + 0.032 2008 8 No Trend No Trend No Trend No Trend 2013 + 105.3 2008 8 No Trend

Placides No Trend 2013 * 52 2008 8 DECREASING 2011 0.96 2008 8 No Trend DECREASING DECREASING No Trend 2013 * 227.8 2008 8 INCREASING

Wentworth No Trend 2018 14.7 2013 6 DECREASING 2014 + 0.187 2013 6 INCREASING No Trend No Trend DECREASING 2014 + 304.1 2013 6 No Trend

Parr No Trend 2016 13.7 2008 7 No Trend 2014 0.111 2008 7 No Trend No Trend No Trend No Trend 2013 199.6 2008 7 No Trend

Ogden No Trend 2014 26 2008 7 No Trend 2013 + 0.052 2008 7 No Trend DECREASING No Trend No Trend 2013 + 145.3 2008 7 INCREASING

Fanning No Trend 2011 19.2 2008 9 No Trend 2009 0.056 2008 9 No Trend No Trend No Trend No Trend 2013 131.4 2008 9 No Trend

Sloans DECREASING 2011 ~ 4.6 2009 8 DECREASING 2011 ~ 0.005 2009 8 INCREASING No Trend No Trend DECREASING 2013 22.3 2009 8 INCREASING

Raynards No Trend 2014+ 16 2014 5 No Trend 2014+ 0.013 2014 5 INCREASING No Trend No Trend DECREASING 2014 54 2014 5 No Trend

Vaughan No Trend 2017 14.7 2008 8 No Trend 2013 + 0.02 2008 8 No Trend No Trend No Trend No Trend 2013 + 81 2008 8 No Trend

Meteghan Nowlans DECREASING 2013 100 2008 6 No Trend 2016 0.56 2008 6 No Trend No Trend n<4 No Trend 2015 58.9 2008 6 No Trend

Sissiboo Provost DECREASING 2013 32 2008 8 No Trend 2015 + 0.029 2008 8 INCREASING No Trend No Trend No Trend 2015 + 127.55 2008 8 No Trend

Tusket Kegeshook No Trend 2016 14.9 2014 5 No Trend 2016 0.007 2014 5 No Trend No Trend No Trend No Trend 2014 60.8 2014 5 No Trend

Salmon River No Trend 2016 9.99 2015 4 No Trend 2016 0.016 2015 4 No Trend No Trend No Trend No Trend 2017 108 2015 4 No Trend

Notes:

All trend analysis - 90% confidence interval

BOLD - increasing or decreasing trend observed

n<4 - less than four samples available (Nowlans - historic total nitrogen analysis interference in samples collected)

* - Peak concentration in chlorphyll a and total nitrogen occurs in same year + - Peak concentration in chlorophyll a, total phosphorus and total nitrogen occurs in the same year

~ - Peak concentration in total phosphorus and total nitrogen occurs in the same year

Mann-Kendall trend analysis on select parameters for spring surface composite sample results

Watershed Lake

Parameter

Chlorophyll a TP Secchi Orthophosphate Total Nitrogen Colour

Trend

Peak

Concentration

Year

Peak

Concentration

(µg/L)

Start

Year

# of

Years Trend

Peak

Concentration

Year

Peak

Concentration

(mg/L)

Start

Year

# of

Years Trend Trend Trend Trend

Peak

Concentration

Year

Peak

Concentration

(TCU)

Start

Year

# of

Years

Carleton

Parr No Trend 2014 29 2013 4 No Trend 2015 0.042 2013 4 No Trend No Trend No Trend No Trend 2018 97.7 2013 4

Fanning DECREASING 2013 9.7 2013 6 No Trend 2015 0.028 2013 6 No Trend No Trend No Trend No Trend 2016 72.7 2013 6

Sloans No Trend 2014 5.3 2013 6 INCREASING 2017-2018 0.005 2013 6 No Trend No Trend No Trend No Trend 2014 29 2013 6

Raynards No Trend 2015 17 2014 5 No Trend 2015 0.020 2014 5 No Trend No Trend No Trend No Trend 2016 67.7 2014 5

Vaughan No Trend 2016 15 2014 5 DECREASING 2015 0.025 2014 5 No Trend DECREASING No Trend No Trend 2016 65 2014 5

Tusket Kegeshook No Trend 2015 18 2014 5 No Trend 2015 - 2018 0.010 2014 5 No Trend No Trend No Trend No Trend 2016 57.7 2014 5

Salmon River n<4 2016 2.3 2016 3 n<4 2017 0.011 2016 3 n<4 n<4 n<4 n<4 2016 84.1 2016 3

Notes:




- All sample events, except 2018 thermally stratified

- All sample events, except 2016 thermally stratified

Mann-Kendall trend analysis on select parameters for fall surface composite sample results

Watershed Lake

Parameter

Chlorophyll a TP Secchi Orthophosphate Total Nitrogen Colour

Trend

Peak

Concentration

Year

Peak

Concentration

(µg/L)

Start

Year

# of

Years Trend

Peak

Concentration

Year

Peak

Concentration

(mg/L)

Start

Year

# of

Years Trend Trend Trend Trend

Peak

Concentration

Year

Peak

Concentration

(TCU)

Start

Year

# of

Years

Carleton

Parr No Trend 2015 7.3 2009 7 DECREASING 2009 0.96 2009 7 INCREASING DECREASING No Trend DECREASING 2013 214.3 2009 7

Fanning No Trend 2016 7.34 2009 6 DECREASING 2009 0.056 2009 6 INCREASING DECREASING No Trend DECREASING 2013 156.3 2009 6

Sloans No Trend 2015 4.1 2009 8 No Trend 2010 0.009 2009 8 No Trend No Trend No Trend No Trend 2013 23 2009 8

Raynards No Trend 2014 8.5 2014 5 No Trend 2014 0.016 2014 5 INCREASING No Trend No Trend No Trend 2014 52 2014 5

Vaughan No Trend 2014 8.6 2009 7 DECREASING 2009 0.033 2009 7 INCREASING DECREASING DECREASING DECREASING 2013 92.7 2009 7

Tusket Kegeshook No Trend 2015 4.7 2015 4 No Trend 2018 0.020 2015 4 No Trend No Trend No Trend No Trend 2018 107 2015 4

Salmon River No Trend 2015 4.7 2015 4 No Trend 2018 0.02 2015 4 No Trend No Trend No Trend No Trend 2017 126 2015 4

Notes:




- Sloans was thermally stratified for the 2013 to 2017 monitoring events

Appendix 9: Yarmouth May to October Precipitation (Climate Normal, and 2008 to 2018)

Year Precipitation (mm)

May June July August September October May-June May-July May-Aug June-Aug July-Aug June-July

Climate Normal (1981 – 2010) 100.9 94.8 88.4 84.3 94.9 112.5 195.7 284.1 368.4 267.5 172.7 183.2

2008 102.4 38 46.8 49.2 155.1 109.2 140.4 187.2 236.4 134 96 84.8

2009 119.8 127.8 117.4 162.8 55.8 158 247.6 365 527.8 408 280.2 245.2

2010 55.8 82.6 117 36 57.8 131.8 138.4 255.4 291.4 235.6 153 199.6

2011 112.4 77.8 158 68.2 59.8 212.6 190.2 348.2 416.4 304 226.2 235.8

2013 132.6 173 141.8 54.8 144.4 76.2 305.6 447.4 502.2 369.6 196.6 314.8

2014 63 102.2 111.4 53.8 82.6 170 165.2 276.6 330.4 267.4 165.2 213.6

2015 59.2 169.8 49.6 34.4 113.2 95.8 229 278.6 313 253.8 84 219.4

2016 111.6 23.4 43.4 19.8 72.6 102.2 135 178.4 198.2 86.6 63.2 66.8

2017 151.8 127.7 48.6 150.2 54.9 56.7 279.5 328.1 478.3 326.5 198.8 176.3

2018 48.4 75.2 2.8 29.2 142.8 172.2 123.6 126.4 155.6 107.2 32 78

2008 vs. Climate Normal Total 1.5 -56.8 -41.6 -35.1 60.2 -3.3 -55.3 -96.9 -132 -133.5 -76.7 -98.4

% 1% -60% -47% -42% 63% -3% -28% -34% -36% -50% -44% -54%

2009 vs. Climate Normal Total 18.9 33 29 78.5 -39.1 45.5 51.9 80.9 159.4 140.5 107.5 62

% 19% 35% 33% 93% -41% 40% 27% 28% 43% 53% 62% 34%

2010 vs. Climate Normal Total -45.1 -12.2 28.6 -48.3 -37.1 19.3 -57.3 -28.7 -77 -31.9 -19.7 16.4

% -45% -13% 32% -57% -39% 17% -29% -10% -21% -12% -11% 9%

2011 vs. Climate Normal Total 11.5 -17 69.6 -16.1 -35.1 100.1 -5.5 64.1 48 36.5 53.5 52.6

% 11% -18% 79% -19% -37% 89% -3% 23% 13% 14% 31% 29%

2013 vs. Climate Normal Total 31.7 78.2 53.4 -29.5 49.5 -36.3 109.9 163.3 133.8 102.1 23.9 131.6

% 31% 82% 60% -35% 52% -32% 56% 57% 36% 38% 14% 72%

2014 vs. Climate Normal Total -37.9 7.4 23 -30.5 -12.3 57.5 -30.5 -7.5 -38 -0.1 -7.5 30.4

% -38% 8% 26% -36% -13% 51% -16% -3% -10% 0% -4% 17%

2015 vs. Climate Normal Total -41.7 75 -38.8 -49.9 18.3 -16.7 33.3 -5.5 -55.4 -13.7 -88.7 36.2

% -41% 79% -44% -59% 19% -15% 17% -2% -15% -5% -51% 20%

2016 vs. Climate Normal Total 10.7 -71.4 -45 -64.5 -22.3 -10.3 -60.7 -105.7 -170.2 -180.9 -109.5 -116.4

% 11% -75% -51% -77% -23% -9% -31% -37% -46% -68% -63% -64%

2017 vs. Climate Normal Total 50.9 32.9 -39.8 65.9 -40 -55.8 83.8 44 109.9 59 26.1 -6.9

% 50% 35% -45% 78% -42% -50% 43% 15% 30% 22% 15% -4%

2018 vs. Climate Normal Total -52.5 -19.6 -85.6 -55.1 47.9 59.7 -72.1 -157.7 -212.8 -160.3 -140.7 -105.2

% -52% -21% -97% -65% 50% 53% -37% -56% -58% -60% -81% -57%

- Drought conditions observed (June to August)

- Wet spring/early summer conditions observed (May/June to July)

- Similar to climate normal year (May/June to July; June to August) (+/-15%) Source: Government of Canada. Historical Climate and Climate Normal Data: http://climate.weather.gc.ca/.

http://climate.weather.gc.ca/

Figure 9.1. Monthly total precipitation values from May to August for Climate Normal (1981 to 2010) and monitoring years (2008 to 2018).

0

20

40

60

80

100

120

140

160

180

200

Cl imate Normal (1981

– 2010)

2008 2009 2010 2011 2013 2014 2015 2016 2017 2018

Pre

cip

ita

tio

n (m

m)

May June July August

Prepared for Carleton River Watershed Area Water Quality ...

Documents

Transcript of Prepared for Carleton River Watershed Area Water Quality ...