Evaluation of Water Quality Parameters due to Aeration/Bioaugmentation
Efficacy Relative to Baseline Conditions in Maple Lake, Van Buren County,
Michigan
2009 and 2014 Data
Notice: This report is © copyrighted and property of Restorative Lake Sciences. No portion of
this report can be duplicated or used without written consent from the Water Resources
Director at Restorative Lake Sciences (Effective April 29, 2015).
Prepared by: Restorative Lake Sciences
Jennifer L. Jermalowicz-Jones, PhD Candidate
Water Resources Director
18406 West Spring Lake Road
Spring Lake, Michigan 49456
www.restorativelakesciences.com
Restorative Lake Sciences
Maple Lake Aeration Report
2014
Page 2
TABLE OF CONTENTS
SECTION
1.0
2.0
3.0
PAGE
INTRODUCTION & SUMMARY........................................................................................................ 5
1.1
Summary of Maple Lake Aeration Operations ......................................................................... 8
1.2
Summary of Maple Lake Aeration Operation Purpose/Goals ................................................. 8
MAPLE LAKE WATER QUALITY SAMPLING METHODS .......................................................... 8
2.1
Summary of Equipment/Sampling Devices/Replicates/Parameters ......................................... 8
2.2
Sampling Dates and Locations ................................................................................................. 9
MAPLE LAKE WATER QUALITY DATA ANALYSIS AND DISCUSSION .............................. 10
3.1
Dissolved Oxygen.................................................................................................................... 10
3.2
Water Temperature ................................................................................................................. 10
3.3
Conductivity ............................................................................................................................ 11
3.4
Total Dissolved Solids and Total Suspended Solids ............................................................... 11
3.5
Total Phosphorus, Total Nitrogen, and Sediment Nutrients .................................................. 11
3.6
pH ............................................................................................................................................ 12
3.7
Organic Matter Content and Loss .......................................................................................... 13
4.0
MAPLE LAKE AQUATIC PLANT/WATERMILFOIL DISTRIBUTION ...................................... 15
5.0
PAW PAW RIVER/BRIGGS POND MANAGEMENT & RECOMMEND. ................................... 21
6.0
LITERATURE CITED......................................................................................................................... 24
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FIGURES
NAME
PAGE
Figure 1. Map of Maple Lake Depth Contours (RLS, 2014) ........................................................................ 6
Figure 2. Map of Maple Lake Bottom Hardness (RLS, 2014)...................................................................... 7
Figure 3. Map of Maple Lake WQ Sampling Locations (2009 and 2014 Study Sites) ................................ 9
Figure 4. Map of BioBase 2014 Aquatic Plant Biovolume in Maple Lake (RLS, 2014) ........................... 17
Figure 5. Map of Maple Lake 2014 EWM in Maple Lake (RLS, 2014) .................................................... 18
Figure 6. Maple Lake Drain Sampling Location Map ................................................................................ 22
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TABLES
NAME
PAGE
Table 1. 2009 Mean Maple Lake Water Quality Data (Study Locations) .................................................. 14
Table 2. 2014 Mean Maple Lake Water Quality Data (Study Locations) ................................................. 14
Table 3. 2009 Mean Sediment Data (Study Locations) .............................................................................. 15
Table 4. 2014 Mean Sediment Data (Study Locations) .............................................................................. 15
Table 5. 2009 AVAS Data Table ................................................................................................................ 19
Table 6. 2014 AVAS Data Table ................................................................................................................ 20
Table 7. Drain Water Quality Data (November 3, 2014) ............................................................................ 23
Table 8. Drain Water Quality Data (November 17, 2014) .......................................................................... 23
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Maple Lake Aeration Report
2014
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Evaluation of Water Quality Parameters due to Aeration/Bioaugmentation
Efficacy Relative to Baseline Conditions in Maple Lake, Van Buren County,
Michigan
2009 and 2014 Data
1.0
INTRODUCTION AND SUMMARY:
Maple Lake is located in sections 1, 11, 12, 13, and 14 (T.3S, R.14W) of the Village of Paw Paw and
Paw Paw Township, Van Buren County, Michigan (Figure 1). The lake surface area is approximately
172 acres (Michigan Department of Natural Resources, 2001) and may be classified as a eutrophic
lake with one deep basin and a large-sized littoral zone. Maple Lake has a maximum depth of 15.0
feet (Figure 1), and an average depth of 7.0 feet (MDNR, 2005). The lake bottom consists primarily
of sandy substrate and organic matter deposits (Figure 2; RLS, 2014).
Maple Lake has a large, immediate watershed of approximately 62,250 acres (97.3 mi 2) consisting of
abundant agricultural land which contributes high quantities of fertile sediments and nutrients to the
lake. The estimated hydraulic retention time depends on the lake water sources and outlet flow rate,
but generally averages 7 days (Southwest Regional Planning Commission 1978). Briggs Pond which
is located in the Village of Paw Paw, is a sedimentation basin which has accumulated large amounts
of sediment that are transported into Maple Lake. The South Branch of the Paw Paw River, which is
upstream of the lake, is also a designated trout stream. Excessive sedimentation has led to the
accumulation of sediments within Maple Lake, as well as increased turbidity, lower dissolved oxygen
levels during late summer and low flow periods, high nutrient loading, and overgrowth of submersed
aquatic vegetation and filamentous algae. Many of the sediments consist of a high fine fraction and
organic matter content since they are derived from a large watershed that is comprised of primarily
Adrian and Houghton Muck organic soils. The outlet for Maple Lake contains a hydropower dam
which was constructed in 1907 and is located at the north end of the lake.
When baseline water quality and sediment data was compared to recently collected data, it was apparent
that recent lake improvement efforts such as the implementation of lake aeration, bioaugmentation,
mechanical harvesting, prior lake drawdowns, and other efforts have improved the water quality of Maple
Lake. Further recommendations are offered in the last section of this report.
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Figure 1. Depth contour map of Maple Lake, Van Buren County, MI (RLS, 2014).
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Figure 2. Bottom hardness map of Maple Lake, Van Buren County, MI (RLS, 2014).
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1.1
Summary of Maple Lake Aeration Operations:
Laminar Flow Aeration (LFA) was installed in the South Basin of Maple Lake in 2011 and has been
evaluated and determined to be effective at improving water quality over the past four years. In 2014,
the Village of Paw Paw environmental council requested that Restorative Lake Sciences (RLS)
compare the original baseline conditions in measured water quality parameters that were collected
during the original lake management plan study in 2009 to the latest collected data set in 2014. Every
effort was made to overlay sampling locations from both dates to assure sampling continuity and
unbiased data comparisons.
1.2
Summary of Maple Lake Aeration Operation Purpose/Goals:
The Maple Lake waterfront residents desired a lake restoration strategy that would make the lake
healthier and accomplish the following objectives:
The primary objectives of the implemented LFA system for Maple Lake include:
1) Reduction of nuisance rooted submersed aquatic vegetation such as milfoil and Curly-leaf
pondweed
2) Increase in top to bottom dissolved oxygen concentrations
3) Increase in water clarity
4) Reduction of filamentous algae
5) Reduction of organic matter and sediment nutrients in problem areas
2.0
MAPLE LAKE WATER QUALITY SAMPLING METHODS
2.1
Summary of Equipment/Sampling Devices/Replicates/Parameters:
Restorative Lake Sciences had sampled 20 locations that became aeration sites in 2011 back in 2009
and also 11 additional sites that remained as non-aerated “control” sites in 2011 and in future years.
Figure 3 shows all of the original sampling locations measured during the lake management study in
2009 and this figure also shows the sampling sites used in the analysis for the 2014 data comparisons.
Baseline conditions of Maple Lake have been previously reported and extensively documented and
discussed and consisted of excessive invasive aquatic vegetation growth, nuisance filamentous algal
blooms, decreased water clarity and organic muck deposits.
All chemical water samples (such as total phosphorus and total suspended solids) were collected at
middle depth of each of the sampling sites) using a 4-liter VanDorn horizontal water sampler with
weighted messenger (Wildco® brand). Water physical parameters (such as water temperature,
dissolved oxygen, conductivity, total dissolved solids, and pH) were measured with a calibrated
Hanna® multi-probe meter. Total phosphorus was titrated and analyzed in the laboratory according to
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the method by Menzel and Corwin (1965; page 97 in Wetzel and Likens, 2000). Total suspended
solids were analyzed for each sample using ASTM Method D5907.
2.2
Sampling Dates and Locations:
All samples were collected by RLS staff in September of 2009 and 2014 for direct comparisons. For
these dates, all samples were collected from the sampling locations according to Figure 3.
Figure 3. Water quality sampling locations on Maple Lake, Van Buren Co, MI (2009 and 2014).
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3.0
MAPLE LAKE WATER QUALITY DATA ANALYSIS AND DISCUSSION
The water quality parameters listed below were measured by RLS scientists in 2009 prior to
implementation of the lake management plan and again over the past five years. In 2014, another
September data set was collected to directly compare both data sets in both control and aeration zones
during both time periods in order to determine possible effects of laminar flow aeration on the
parameters in question. The data sets for water column and sediment parameters for 2009 and 2014
are shown below in Tables 1-4.
3.1
Dissolved Oxygen
Dissolved oxygen (DO) is a measure of the amount of oxygen that exists in the water column. In
general, DO levels should be greater than 5 mg L-1 to sustain a healthy warm-water fishery or higher
for better overall water quality. DO is generally higher in colder waters and is often higher in flowing
waters. During summer months, DO at the surface is generally higher due to the exchange of oxygen
from the atmosphere with the lake surface, whereas DO is lower at the lake bottom due to decreased
contact with the atmosphere and increased biochemical oxygen demand (BOD) from microbial
activity. A decline in DO may cause increased release rates of phosphorus (P) from lake bottom
sediments if DO levels drop to near zero milligrams per liter.
Under low DO conditions, the imminent accumulation of NH3+ (ammonia) may result in toxicity to
aquatic organisms (Camargo et al., 2005; Beutel, 2006). DO levels in Maple Lake have always been
elevated due to the high flow of water from the Paw Paw River that continuously cycle through the
lake water volume. Statistically speaking, there have been small increases in DO in the aeration zone
compared to the control zone but those increases are modest considering that the DO concentrations
were already > 9.0 mg/L which is considered favorable for an inland lake.
3.2
Water Temperature
The water temperature of lakes varies within and among seasons. In general, shallow lakes such as
Maple Lake will not stratify (except for slight stratification at the north basin) while deeper lakes may
experience single or multiple turnover cycles. Water temperature is measured in degrees Celsius (°C)
or degrees Fahrenheit (°F) with the use of a submersible thermometer. Differences in water
temperatures are due to seasonal effects of sunlight penetration, water level changes, and degree of
particles and color in the water that absorb heat. Evaluation of water temperatures throughout the
operational years of the aeration system in Maple Lake aeration and control zones showed little
change in overall water temperature as a result of the operation of the aeration system relative to preaeration water temperatures in the same sampling locations at the same sampling periods. This
means that the aeration system is not affecting the warm-water fishery present in Maple Lake by
causing any thermal stress. There were also no fish kills reported during the aeration evaluation
period.
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3.3
Conductivity
Conductivity is a measure of the amount of mineral ions present in the water, especially those of salts
and other dissolved inorganic substances. Conductivity generally increases as the amount of
dissolved minerals and salts in a lake increases, and also increases as water temperature increases.
Conductivity is measured in micro-Siemens per centimeter (µS cm-1) with the use of a conductivity
probe and meter. This parameter is likely to fluctuate greatly as the concentration of salts and solutes
varies from the riverine inputs and would be dependent on flow rates. The conductivity of Maple
Lake has traditionally been moderately high for an inland lake. Mean values for the control region
(north basin) in 2009 pre-aeration were 540±7.6 mS/cm and mean values for the aeration zone (south
basin) in 2009 pre-aeration were 613±31 mS/cm. Mean values for the control region (north basin) in
2014 post-aeration were 511±37 mS/cm and mean values for the aeration zone (south basin) in 2014
post-aeration were 535±56 mS/cm. The overall trend for both regions of the lake is that the
conductivity has declined slightly with time with use of the LFA system. The reason for this effect is
unclear but the result may be beneficial.
3.4
Total Dissolved Solids and Total Suspended Solids
Total Dissolved Solids (TDS) is a measure of the amount of dissolved organic and inorganic particles
in the water column. Particles dissolved in the water column absorb heat from the sun and raise the
water temperature and increase conductivity. Total dissolved solids are often measured with the use
of a calibrated meter in mg L-1. This number can fluctuate numerous times daily due to scattering of
light on particles in the water and re-suspension of fine particles from the lake bottom during the time
of measurement. The TDS mean concentration in the control zone remained close the same in 2014 as
in 2009 at 276±23 mg/L and 260±22 mg/L, respectively. However, the mean TDS concentration in
the aeration zone in 2009 was higher at 307±16 mg/L compared to 264±30 mg/L in 2014 which
means that the aeration system may be influencing TDS by reducing it in the south basin.
Total Suspended Solids (TSS) is a measure of the amount of suspended particles in the water column.
Particles suspended in the water column absorb heat from the sun and raise the water temperature.
Total suspended solids are often measured in mg L-1 and analyzed in the laboratory. The lake bottom
contains many fine sediment particles that are easily perturbed from winds and wave turbulence. All
of the TSS samples collected in Maple Lake in 2009 and 2014 were < 12.0 mg/L which is considered
low. These samples were taken during good weather and may have been much higher if collected
after a heavy rainfall event. The aeration system does not seem to be increasing TSS and may be
processing organic loads in the water column as they enter from the Paw Paw River as evidenced by
increases in water clarity.
3.5
Total Phosphorus, Total Nitrogen, and Sediment Nutrients
Total phosphorus (TP) is a measure of the amount of phosphorus (P) present in the water column.
Phosphorus is the primary nutrient necessary for abundant algae and aquatic plant growth. Lakes
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which contain greater than 20 µg L-1 of TP are defined as eutrophic or nutrient-enriched. TP
concentrations are usually higher at increased depths due to higher release rates of P from lake
sediments under low oxygen (anoxic) conditions. Phosphorus may also be released from sediments
as pH increases. Total phosphorus is measured in micrograms per liter (µg L-1) or in milligrams per
liter (mg L-1).
When phosphorus enters Maple Lake from the atmosphere, runoff, the Paw Paw River, or Briggs
Pond, it falls to the bottom and seeps into the sediment pore water where it is assimilated by the
aquatic plant roots, especially milfoil, pondweeds, and lily pads. This is why the sediment TP and
TKN (nitrogen) concentrations are much higher than the water column concentrations throughout the
entire lake. Nutrients adhere to sediment particles and solubilize in the pore water where they can be
directly assimilated by plant roots for metabolism and growth. Sediment TP is measured in
milligrams per kilogram (mg kg-1). A study by Krogerus and Ekholm (2003) measured the release
rates of P from sediment in shallow, open, agriculturally-impacted lakes and found that the mean
daily rate of gross sedimentation was 0.04-0.18 g m-2 day-1 of phosphorus.
The sediment TP concentrations of both the control region and the aeration zone have declined with
time presumably due to assimilation by rooted aquatic vegetation for growth over the years. It will be
interesting to see if these values continue to decline if rooted aquatic vegetation also declines over
time given that they would not be present to utilize the sediment phosphorus and nitrogen sources.
Sediment phosphorus was not determined to be statistically reduced in the aeration zone between
2009 and 2014 due to the large standard error; however, it is worth noting that this finding of decline
in sediment TP overlaps with observed reduced milfoil growth prior to treatment in 2014 which could
be attributed to aeration and is discussed in Section 4.0 below.
Total Kjeldahl Nitrogen (TKN) is the sum of nitrate (NO3-), nitrite (NO2-), ammonia (NH4+), and
organic nitrogen forms in freshwater systems. Much nitrogen (amino acids and proteins) also
comprises the bulk of living organisms in an aquatic ecosystem. Nitrogen originates from
atmospheric inputs (i.e. burning of fossil fuels), wastewater sources from developed areas (i.e. runoff
from fertilized lawns), agricultural lands, septic systems, and from waterfowl droppings. It also enters
lakes through groundwater or surface drainage, drainage from marshes and wetlands, or from
precipitation (Wetzel, 2001). In lakes with an abundance of nitrogen (N: P > 15), phosphorus may be
the limiting nutrient for phytoplankton and aquatic macrophyte growth. The mean TKN was
statistically slightly lower at 0.52±0.1 mg/L in the aeration zone in 2014 relative to baseline values in
the same sampling locations in 2009 with a mean of 0.55±0.1 mg/L.
3.6
pH
pH is the measure of acidity or basicity of water. The standard pH scale ranges from 0 (acidic) to 14
(alkaline), with neutral values around 7. Most Michigan lakes have pH values that range from 6.5 to
9.5. Acidic lakes (pH < 7) are rare in Michigan and are most sensitive to inputs of acidic substances
due to a low acid neutralizing capacity (ANC). pH is measured with a pH electrode and pH-meter in
Standard Units (S.U). The pH of Maple Lake water has remained remarkably consistent throughout
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the evaluation of the LFA system compared to the baseline pH values measured during the 2009 lake
study with a mean range of 7.8-8.0 S.U. Thus, the LFA system does not appear to be influencing pH.
3.7
Organic Matter Content and Loss
Organic matter (OM) contains a high amount of carbon that is derived from biota such as decayed
plant and animal matter. Detritus is the term for all dead organic matter which is different than living
organic and inorganic matter. OM may be autochthonous or allochthonus in nature where it
originates from within the system or external to the system, respectively. Sediment OM is measured
with the ASTM D2974 method and is usually expressed in a percentage (%) of total bulk volume.
Maple Lake sediment samples were collected at the sampling locations with the use of an Ekman
hand dredge. Statistically speaking, the sediment OM has not changed much in the control or aeration
sampling areas relative to baseline values. This may be due to low organic matter readings that
already existed in both the original control and “aeration” zones that were sampled again in 2014 and
were still low. Other areas in Maple Lake such as the southernmost region of the South Basin contain
higher percentages of organic matter and have showed more reduction in OM over the past few years
of aeration. It is also important to realize that this variable may change rapidly with inputs from the
Paw Paw River since many deposits may be high in organics during periods of high rainfall that carry
Houghton Mucks from farm lands to the lake but at other times deposits may consist of silt and
mineral content.
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Location
DO
pH
-1
Cond.
-1
TDS
-1
TSS
TKN
-1
TP
(mg L )
(S.U.)
(µS Cm )
(mg L )
(mg L-1)
(mg L )
(mg L-1)
Control
9.1± 0.9
8.0±0.5
540.0±7.6
260± 22
10.0± 0.0
0.50±0.0
0.019±3.9
Aeration
9.7± 1.0
7.8± 0.1
613±31.0
307± 16.0
11.6± 4.5
0.55±0.1
0.025±10.8
Table 1. Summary statistics for major water column water quality parameters collected at control and
aeration zone sites in 2009 (Pre-Aeration).
Location
DO
pH
Cond.
TDS
TSS
TKN
TP
(mg L-1)
(S.U.)
(µS Cm-1)
(mg L-1)
(mg L-1)
(mg L-1)
(mg L-1)
Control
10.0± 0.8
7.8±0.2
511±37
276± 23
10.1± 0.3
0.50±0.0
0.018±5.4
Aeration
10.1± 0.7
7.9± 0.1
535±56*
264± 30*
10.4± 1.2*
0.52±0.1*
0.020±7.9
Table 2. Summary statistics for major water column water quality parameters collected at control and
aeration zone sites in 2014 (Post-Aeration). *denotes significant reductions
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Location
% OM
TP
mg/kg
Control
14.4± 11.3
429±296
Aeration
20.7± 14.5
515± 315
Table 3. Summary statistics for major sediment parameters collected at control and aeration zone
sites in 2009 (Pre-Aeration).
Location
% OM
TP
mg/kg
Control
13.4± 7.0
375±229
Aeration
19.0± 11.9
353± 217
Table 4. Summary statistics for major sediment parameters collected at control and aeration zone
sites in 2014 (Post-Aeration).
4.0
Maple Lake Hybrid Watermilfoil Distribution, Aquatic Vegetation Biovolume, and
Comparisons of Aquatic Vegetation in 2009 (Pre-lake management plan) and 2014 (Post-lake
management plan)
On May 27 of 2014, a Lowrance® 50-satellite GPS HDS 8 WAAS-enabled unit (accuracy within 2
feet) was used to scan the entire bottom of Maple Lake and record all of the aquatic vegetation
throughout Maple Lake and to generate a complete lake aquatic vegetation aquatic biovolume map
(Figure 4). The red and orange colors indicate dense growth, while the yellow is moderate growth and
green is light growth and blue color is no growth.
From this map and using Point-Intercept aquatic plant data collected by RLS scientists,
approximately 47 acres of hybrid Eurasian Watermilfoil was found primarily north of the aeration
system and of the south basin (Figure 5). This indicates that the aeration system has been quite
effective at reducing milfoil as has been noted on many other lakes. The aeration system has had a
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tough time treating the milfoil in Turtle Bay likely due to the sediment type that consists of a more
consolidated sediment type per the sediment scan conducted by RLS in 2014. Other nuisance aquatic
plants such as Coontail, Thin-leaf Pondweed, and Elodea were still abundant in the south basin and
have required rigorous contact herbicide treatments and mechanical harvesting removal.
In 2009, before the lake management plan was implemented, there were only 10 native aquatic plant
species noted with 30.7% of the lake surface area covered with Eurasian Watermilfoil and 22.6% of
the lake covered with Curly-leaf Pondweed (Table 5). By 2014, five years post-management, there
were 15 native aquatic plant species noted with 1.5% of the lake surface area covered with Eurasian
Watermilfoil and 1.0% of the lake covered with Curly-leaf Pondweed after treatment in September of
2014 (Table 6). The increase in native aquatic plant species is undoubtedly a result of the decline in
milfoil which smothers out light from favorable natives and limits their growth.
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Figure 4. Maple Lake aquatic plant biovolume map showing high biovolume locations (5/27/14).
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Figure 5. Map showing milfoil areas before treatment in 2014. Note the lack of milfoil in the
aeration zones (exception is Turtle Bay area).
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Table 5. 2009 aquatic vegetation AVAS data sheet for Maple Lake.
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Table 6. 2014 aquatic vegetation AVAS data sheet for Maple Lake.
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5.0
Paw Paw River and Briggs Pond Management Recommendations
The drains empting into the Paw Paw River have been monitored over the past few years for nutrients
and various water quality parameters. Data from these sampling locations (Figure 6) is shown below
for 2014 in Tables 7 and 8. In general, the water quality of these drains indicates that the water is
adequate in dissolved oxygen, especially since they are sampled in late fall. Additionally, the drains
are high in nutrients such as phosphorus and nitrogen and specific conductance and total dissolved
solids. The total suspended solids has traditionally been lower and indicates that most solids are
settling out and in the dissolved form. The S1 and S6 drain sites appear to have the highest nutrient
levels. Due to the fluctuating nature of these drains and dependence of rainfall for flowage, flow rates
are often difficult to obtain, but RLS will once again try to obtain a precise loading rate of these
drains in 2015 to calculate loading rates and use this data to incorporate into a loading model that
adds the nutrient loading from the Paw Paw River confluence and Briggs Pond contributions. RLS
will also utilize data obtained from the Village of Paw Paw Public Works Department which includes
phosphorus concentrations and monthly loading of phosphorus in pounds as a condition of the
NPDES limit for local industrial outputs to the Paw Paw River.
RLS recommends that a filtration buffer device be placed at the confluence of the Paw Paw River as
it enters La Cantina Basin. In addition, RLS recommends a sediment reduction and bioaugmentation
technology approach for Briggs Pond in 2015 in the absence of dredging funds and as a sustainable
approach for biological organic sediment reduction. RLS will measure baseline sediment and
nutrient loads within these two locations before and after solution implementation to precisely
measure solution efficacy.
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Figure 6. Maple Lake Drain sampling locations (November, 2014).
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Drain
Water
DO
pH
Cond.
Total
Total
Total
Total
Sampling
Temp
mg L-1
S.U
µS cm-1
Suspen.
Diss.
Phos.
Nitr.
Location
ºF
Solids
Solids
mg L-1
mg L-1
-1
mg L
mg L-1
S1
48.9
8.5
8.6
725
22
275
0.040
0.4
S2
49.3
8.1
8.3
719
16
311
< 0.010
0.6
S3
47.1
7.6
8.5
733
42
332
0.020
0.5
S4
49.0
8.0
8.7
716
22
319
0.022
0.4
S5
48.6
8.1
7.9
744
37
371
0.025
0.5
S6
49.2
7.9
8.1
627
42
299
0.030
0.4
S7
49.7
8.2
8.4
537
11
178
< 0.010
0.4
Table 7. Maple Lake drain water quality data (November 3, 2014)
Drain
Water
DO
pH
Cond.
Total
Total
Total
Total
Sampling
Temp
mg L-1
S.U
µS cm-1
Suspen.
Diss.
Phos.
Nitr.
Location
ºF
Solids
Solids
mg L-1
mg L-1
-1
mg L
mg L-1
S1
47.1
8.4
8.4
722
19
272
0.030
0.5
S2
48.4
8.2
8.1
728
11
318
0.010
0.7
S3
47.5
7.7
8.4
719
14
329
0.025
0.6
S4
48.2
7.9
8.5
710
9
294
0.020
0.5
S5
47.4
7.7
7.8
724
26
321
0.030
0.4
S6
48.0
7.4
8.0
698
38
348
0.040
0.5
S7
48.6
8.0
8.3
520
13
210
0.025
0.4
Table 8. Maple Lake drain water quality data (November 17, 2014).
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6.0
SCIENTIFIC LITERATURE CITED
Beutel, M.W. 2006. Inhibition of ammonia release from anoxic profundal sediments in lakes
using hypolimnetic oxygenation. Ecological Engineering 28(3): 271-279.
Camargo, J.A., A. Alonso, and A. Salmanca. 2005. Nitrate toxicity to aquatic animals: a review with
new data for freshwater invertebrates. Chemosphere 58: 1255-1267.
Krogerus, K., and P. Ekholm. 2003. Phosphorus in settling matter and bottom sediments in lakes
loaded by agriculture. Hydrobiologia 429: 15-28.
Nicholls, K.H. 1979. A simple tubular phytoplankton sampler for vertical profiling in lakes.
Freshwater Biology 9:85-89.
Prescott, G.W. 1970. Algae of the western great lakes areas. Pub. Cranbrook Institute of Science
Bulletin 33:1-496.
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