Inventory of Aquatic Invasive Species and Water Quality in Lakes in the Lower Truckee River Region: 2012

Inventory of aquatic invasive species and water quality in lakes in the Lower Truckee River Region: 2012

Timothy J. Caldwell and Dr. Sudeep Chandra Aquatic Ecosystems Analysis Laboratory Department of Natural Resources and Environmental Science University of Nevada – Reno 1664 N Virginia St - MS 186 Reno, NV 89557

TABLE OF CONTENTS

TITLE PAGE ...... i

TABLE OF CONTENTS ...... ii

LIST OF TABLES ...... iii

LIST OF FIGURES ...... iv

LIST OF APPENDICIES ...... v

INTRODUCTION ...... 1

METHODS ...... 4

Water quality and limnological profiles ...... 4

Adult invasive invertebrate and plant surveys ...... 4

Quagga and zebra mussel veliger detection ...... 6

Crayfish population dynamics ...... 6

RESULTS ...... 6

Water quality and limnological profiles ...... 6

Adult invasive invertebrate and plant surveys ...... 7

Quagga and zebra mussel veliger detection ...... 8

Calcium levels and quagga mussel invasion potential ...... 9

Crayfish population dynamics ...... 9

DISCUSSION ...... 9

Status of invasive species ...... 9

Calcium levels and dreissenid mussel invasion potential ...... 10

Crayfish population dynamics ...... 14

AKNOWEDGMENTS ...... 32

REFERENCES ...... 33 iii

LIST OF TABLES

TABLE 1. Basic morphological characteristics of the 2012 Truckee River Region study lakes...... 16

TABLE 2. Secchi depth measurements from the Truckee River region lakes during 2010 and 2012...... 17

TABLE 3. Invasive plants and adult invertebrates present in Truckee River region lakes in 2010,2011, and 2012 as determined from UNR shoreline surveys and CFG visual surveys. Species presence is denoted by “X”, a blank space indicates no species were found during the surveys...... 18

TABLE 4. Concentration of calcium (ppm) in the epilimnetic waters of lakes in the Truckee River region during 2012...... 19

LIST OF FIGURES

FIGURE 1. Truckee River Watershed and location of study lakes within the watershed...... 20

FIGURE 2. Temperature, dissolved oxygen and conductivity profiles for lakes in the Truckee River region ...... 21-28

FIGURE 3. Mean concentration of calcium in the epilimnetic waters of the Truckee River Watershed lakes, from 2010, 2011, and 2012...... 29

FIGURE 4. Catch per unit effort (CPUE) for crayfish in the lakes in the Truckee River lakes region. Independence lake is significantly lower than Marlette, Prosser, and Stampede (p<.05, CI=99.42%)...... 30

FIGURE 5. Size distribution of crayfish carapace size (mm) in lakes in the Truckee River region, statistical groupings (p<.05, CI=99.55%) are denoted by letters above boxplots...... 30

FIGURE 6. Comparison of crayfish CPUE from 2010 to 2012 in lakes in the Truckee River region...... 31

LIST OF APPENDICES

Appendix A. Water quality profiles (temperature, dissolved oxygen, and specific conductivity) for each of the Truckee River region study lakes in 2010.a. Donner, b. Spooner, c. Martis Creek L., d. Independence, e. Marlette, f. Webber, g. Prosser, h. Boca, i. Stampede, j. Lahontan, k. Rye Patch, and l. Pyramid...... 35

Appendix B. Invasive species visual shoreline survey data from 2010, 2011, 2012...... 48

INTRODUCTION The introduction of invasive species to aquatic ecosystems can be detrimental to the natural ecology of lakes and be responsible for regional and widespread economic loss. For example, the Laurentian Great Lakes have suffered plant invasions by Eurasian water milfoil

(Myriophyllum spicatum) and zooplankton such as the Spiny waterflea (Bythotrephes longimanu), both have altered natural ecosystem function, and displaced native species (Mills et al. 1994; Riccardi and MacIsaac 2000). More recently, zebra (Dreissena polymorpha) and quagga (Dreissena bugensis) mussels have entered the Great Lakes (Riccardi and MacIsaac

2000), and have continued to spread throughout the United States (Ludyanski et al 1993;

Stockstad 2007) causing ecosystem wide consequences (Hecky et al. 1994; Ludyanski et al.

1993), and economic loss (Leung et al. 2002; Pimentel et al. 2000).

The introduction and establishment of aquatic invasive species throughout the Truckee

River region of California and Nevada is of growing concern to resource managers. Recent research from the region, conducted largely within Lake Tahoe, suggests that invasives cause both ecological and economic impacts (Kamerath et al. 2008; Vander Zanden et al. 2003). For example, the recent introduction of Asian clam (Corbicula fluminea) is thought to facilitate increases in algal blooms in the southeastern part of the lake and have a variety of negative effects (Sousa et al., 2008). While, invasive plants such as water milfoil (Myriophyllum spicatum) can alter nearshore habitats and facilitate the invasion of other species such as warmwater fishes which have drastic impacts on lake ecology (Kamerath et al. 2008). The invasion of species which is facilitated by previous non-natives has been described as

“invasional meltdown” and can cause catastrophic shifts in ecosystems (O.Dowd et al. 2003) 2

The majority of the lakes in the Truckee River Watershed have resisted invasion by many of the exotic species (Rammer and Chandra 2010). However, as aquatic nuisances continue to spread to the western United States (e.g. dreissenid mussels in Lake Mead; Stockstad 2007) they are a risk to lakes and a concern to resource managers in the Truckee River watershed.

Dreissenids have been known to significantly impact water quality, resulting in large scale economic damage by clogging water intake pipes and reducing recreational activity when they establish. Given the ability of dreissenids to spread between systems and the extensive boat traffic (a common vector for aquatic invasions) in the Truckee River watershed, the potential for the establishment of invasive mussels could be significant (Wittmann et al. 2009; Umek et al.

2009).

Researchers have attempted to predict the potential of dreissenid invasion using varying parameters such as ecosystem depth, substrate size and other physiochemical factors

(Bossenboeck et al. 2001; Drake and Bossenboeck 2004, Whittier et al. 2008). For example,

Jones and Riccardi (2005) used depth, substrate size, and calcium concentration to model the distribution of dreissenids in the St. Lawrence River, and suggest that all 3 variables play a role in zebra mussel colonization, while only depth and sediment size are important for quagga mussel establishment, indicating that zebra mussels are more dependent on water calcium levels.

The concentration of calcium in the waters of the Truckee River region is low (Rammer and

Chandra 2010) and suggests that mussels may not be as likely to invade these ecosystems.

However, with the recent invasion of Asian clams to the ultra-oligotrophic and low calcium waters of Lake Tahoe and Donner Lake (Rammer and Chandra 2010), mussels may be able to survive if transported to the Truckee River watershed (Chandra et al. 2009). The concentration of calcium in the sediment pore-water (i.e. water in interstitial space) can be higher than that in 3 the water column (Rammer and Chandra 2010) and could facilitate dressenid invasion, this mechanism deserves further examination.

Currently, boat inspection stations have been put in place along the Truckee River to minimize the risk of transporting species. However, it is important to have information on the current locations of invasive species throughout the watershed, and continue to document recent invasions.

The objective of this project is to identify water bodies within the Truckee River region

(Donner Lake, Stampede Lake, Boca Reservoir, Prosser Reservoir, Marlette Lake, Martis Creek

Lake, Rye Patch Reservoir, Spooner Lake, Lahontan Reservoir) that have already established invasive invertebrate and plant communities, and to identify and document recent invasions.

Additionally, we plan to test the hypothesis that bivalve invasion is dependent not only on calcium concentration in the water column but on the concentration of calcium in sediment pore- water. This is year two of the project and builds upon data collected in 2010 (Rammer and

Chandra 2010). Specifically, our goals were to

1. Use the method developed by Rammer and Chandra (2010) to continue shoreline surveys

for invasive invertebrates (Dreissenid mussels, New Zealand mudsnail, Asian clam, and

crayfish) and invasive plant (Hydrilla and Eurasian water milfoil) species.

2. Sample lakes for the DNA of dreissenid mussel veligers to document invasions using

zooplankton net hauls.

3. Quantify the concentration of calcium in the eplimnetic waters of each lakes.

4. Collect sediment pore-water from locations around Donner Lake to determine if the

spread of Asian clams are influenced by this variable.

METHODS

Study Sites

During the summer of 2012 eight lakes that represent the major recreational water bodies in the Truckee River Watershed region were chosen for invasive species assessment (Table 1).

These include six lakes in California (Independence Lake, Boca Reservoir, Stampede Reservoir,

Prosser Reservoir, Martis Creek Lake, Donner Lake), and two in lakes in Nevada (Marlette Lake and Spooner Lake). These lakes were chosen because of the high frequency of recreational use.

Water quality and limnological profiles

An index sampling station at the deepest part of the lake was selected to determine the physical and chemical nature of each lake. Secchi depth was taken at this location using a standard 30cm multi-colored (black and white) secchi disk. The disk was lowered until it was unable to be seen by the naked eye, and raised till it could be seen again. The mid-point between these two depths was considered the secchi depth. At this location a handheld YSI-85 meter

(YSI Incorporated, Yellow Springs, Ohio) was used to determine a quantitative profile for temperature, dissolved oxygen, and specific conductivity every 4-6 weeks from July to October in 2010 and 2012.

Epilimnetic water samples were collected from each lake to analyze for calcium (Ca).

Because of the presence of Asian clams (Corbicula fluminea) in Donner Lake, sediment pore- water was collected for calcium analysis at 10 sites around Donner Lake. To collect sediment pore-water a sediment sample was taken using a petit-Ponar grab, and water was removed from the interstitial space using a modified-syringe apparatus (Rammer and Chandra 2010). All calcium samples were placed on ice and transported back to the University of Nevada. Each sample was filtered through a 0.7µm Glass Fiber Filter (GFF), then through a 0.45 µm magna- 5 nylon filter. Samples were frozen and shipped overnight to the University of California–Davis plasma mass spectrometry center for analysis.

Adult invasive invertebrate and plant surveys

A protocol was developed to survey lake shoreline area for adult invasive species and invasive plants (Rammer and Chandra 2010). Shoreline area sight surveys were conducted via boat or on foot, depending on feasibility, along the entire lake shoreline. When boating was required, a 14 ft rowboat was driven at a slow and constant speed around the shore. Fifteen transects were chosen in each lake for a detailed evaluation. Transect locations were chosen based on areas where invasive mussel and clam species were likely to be found (i.e., boat launches, public docks, and other hard substrates). Because lake habitat is heterogeneous, our secondary consideration was to choose transects that would be representative of habitat variability in each system. GPS coordinates were recorded for each transect when possible and the location described.

At each transect, a 5 m2 section was closely examined for the presence of invasive species and evaluated for substrate composition. Within each section, rocks were uprooted and examined for mollusk species and sand was dug up by hand and examined for New Zealand mud snails. Unknown plants and invertebrates were collected and taken back to the laboratory for identification. At each transect, the location, substrate composition, and percent of area where invasive species were present (when applicable) was recorded. Wentworth’s substrate guide

(1922) was modified and used to define general substrate types present at each transect such that rock substrate includes gravel (6.4 mm) to boulder (≥ 610.0 mm), woody structure includes material with a diameter of < 20.5 mm to ≥ 50.9 mm, and fine substrates include anything smaller than gravel (sand, silt, and organic matter). 6

Quagga and zebra mussel veliger detection

Plankton tows were used to detect the presence of zebra and quagga mussel veligers during 2012. During the season each lake was sampled twice following a standard protocol developed by California Fish and Game (CFG 2008). Samples were sent to the California Fish and Game (CFG) laboratory for analysis within the time allotted in the CFG protocol. A 64 micron, 30 cm diameter plankton tow net was used to sample for dreissenid veligers at various locations within each lake. Combinations of vertical and horizontal tows were used depending on water depth and sampling location. Each sample was composed of 2-3 tows from the same location and stored in a 25% by volume 95% reagent grade (non-denatured) ethanol (ETOH) solution. To prevent possible contamination between lakes, all sampling equipment was soaked in vinegar, rinsed, and dried between samplings (California Fish and Game, 2008).

Crayfish population dynamics

To collect the introduced crayfish (Pacifastacus leniusculus), baited minnow traps were set out along depth transects (1m, 5m, 9m) overnight during summer of 2010 and 2012. Catch per unit effort (CPUE) was calculated by dividing total catch by the effort (hours) fished. To determine the size class distribution of crayfish, carapace length was measured using digital calipers to the nearest 0.00mm.

RESULTS

Water quality and limnological profiles

The majority of the lakes surveyed were thermally stratified by the June sampling event

(Figure 2). This trend is different from the previous years (i.e. 2010) when lakes were not stratified until July (Appendix A), this is likely related to the minimal snow pack and early onset of high temperatures early in the season during 2012. Dissolved oxygen levels were typically 6- 7

8 mg/L but were recorded as high as 14 mg/L in Spooner Lake (Figure 2). Conductivity was low

<60 µS in the majority of lakes (Figure 2). However Spooner Lake conductivity levels were

>450 µS, this may be driven by runoff from the nearby highway 50.

Secchi disk readings are presented in Table 2 and were comparable to readings which were taken in 2010 (Table 2), suggesting that productivity levels have been consistent in recent years.

Adult invasive invertebrate and plant surveys

Invasive species were detected in 3 of the 8 lakes which were surveyed (Table 2).

Eurasian water milfoil was noticed at high densities in Martis Creek Lake and Spooner Lake

(Table 2; Appendix A). Asian clams were detected in several parts of Donner Lake and may have spread from the initial clam patch described in 2010 (Rammer and Chandra 2010). Dense patches of clams were detected along the state park beach, and near the outlet at the east end of the lake. Zebra mussels (Dreissena polymorpha), quagga mussels (Dreissena rostriformis), New

Zealand mudsnail snails (Potamopyrgus antipodarum) and hydrilla (Hydrilla verticillata) were not detected in any of the study lakes (Table 3). Shoreline invasive species survey data can be found in Appendix A. A variety of substrates and high use areas were surveyed over the course of the year (Appendix A).

Quagga and zebra mussel veliger detection

Veliger DNA or veligers (via microscopy) were not detected in any of the lakes sampled

(Donner, Stampede, Boca, Prosser, Marlette, Martis Creek Lake, Spooner, and Independence) during 2012 (Table 3), or since this monitoring program began in 2010.

Calcium levels and dreissenid mussel invasion potential

Epilimnetic calcium concentrations were low (< 15ppm) in the majority of lakes. The concentration of calcium in Spooner lake was relatively high (27.28 ± 0.79 ppm) compared to the other lakes (Table 4, Figure 3). Our data suggests that some lakes (Boca, Martis Creek,

Prosser, and Stampede), increased in calcium from early season to late season. This in contrast to data collected in 2010, which showed a decrease in calcium concentration inter-annually

(Rammer and Chandra 2010), and in 2011 where concentrations were similar throughout the year

(Caldwell and Chandra 2012). The increase in calcium concentration this year may be a result of low water levels which would decrease the dilution effect seen in higher water years such as

2011.

Calcium data has been collected since 2010 in the majority of these lakes. This data suggests that the concentration of calcium in some of these waters has been decreasing since

2010 (Figure 3). For example in Boca reservoir the concentration has decreased from 8.04 ±

1.73 ppm in 2010 to 4.85 ± 0.98 ppm in 2012, several other lakes (Donner, Marlette, Martis

Creek, and Stampede) have shown similar patterns (Figure 3). The intra-annual dynamics of calcium concentrations in lakes are difficult to understand but are likely related to weather patterns of each year, lake levels, and geology of the lake, these dynamics deserver further investigation.

The concentration of calcium in sediment pore-water in Donner Lake ranged from 5.65 –

9.78 ppm and averaged 6.27 ± 0.40 ppm (Table 4). This was similar to last years mean (6.19 ±

0.76 ppm; Caldwell and Chandra 2012). Because clams have spread to most parts of the lake we took samples from 10 different locations around the lake. Our results are consistent with the previous years sampling, and we conclude that the high mean concentration presented by 9

Rammer and Chandra (2010), is driven by an outlier (25.36 ppm) collected during this time period. This suggests other variables may be regulating the spread of Asian clams in Donner

Lake.

Crayfish population dynamics

The lowest catch per unit effort (CPUE averaged across depths) recorded for crayfish was at Independence Lake, (0.15±0.06 CPUE), and was highest at Stampede Reservoir (1.77±0.17

CPUE; Figure 4). Independence Lake had significantly lower CPUE than Marlette, Prosser and

Stampede. CPUE generally increased in all lakes from 2010 to 2012 (Figure 6). Crayfish carapace length ranged from 36.5 ± 0.79mm (Donner Lake) to 47.9 ± 0.78mm (Boca Reservoir;

Figure 5). Several significant differences were detected between lakes (p<.0, CI=99.42%) and displayed by grouping in Figure 5.

DISCUSSION

Status of invasive species

The results of the invasive species shoreline surveys suggest show that no new invasive species have arrived since 2010. Additionally, veliger DNA has yet to be detected in any of the lakes indicating that dreissenid mussels have yet to be introduced. This project provides baseline data on the status of invasive species in the lakes of the Truckee River Watershed, and is important to continue this monitoring to document any new invasions. Knowledge of the time of invasions can give researchers and managers the opportunity to document changes in lake processes caused by the invasion of exotic species.

Certain lakes with limited access (e.g. Marlette Lake) are at a reduced risk of an invasion of by aquatic nuisance species. By limiting use, and limiting the type of water craft allowed on 10

Marlette Lake the lake is unlikely to be invaded by any new aquatic invasive species. Given that nearby Spooner Lake is infested with Eurasian Water Milfoil (Myrophillium spicatum; Caldwell and Chandra 2012) it does increase the chances of this nuisance species spreading to Marlette

Lake. We recommend that the State Park launch an awareness/outreach plan to inform anglers of the infestation at Spooner Lake and encourage them to inspect any watercraft or fishing equipment (rods, reels, lines, lures, or waders) for Eurasian Water Milfoil (EWM). Secondly, we recommend that any watercraft destined for Marlette Lake that passes through the main entrance be inspected by those at the entrance, and inform users of infestation of EWM at Spooner and the risk of its spread to Marlette Lake. These simple and low cost tasks will reduce any the risk of spread of EWM from Spooner Lake to Marlette Lake.

Calcium levels and dreissenid mussel invasion potential

Invasive dreissenids, zebra (Dreissena polymorpha) and quagga (Dreissena rostriformis bugensis) mussels, in particular have altered the ecology of lakes and rivers by coupling pelagic and benthic trophic pathways, increasing offshore clarity, stimulating benthic production and altering biodiversity (Makarewicz et al. 1999, Bially and MacIssac 2000, Ricciardi et al. 1998).

In recent years there has been a western range expansion in North America of mussels and it first appeared in western U.S. in Lake Mead, AZ-NV in early 2007 (Stokstad et al. 2007) and has subsequently been found in other major western impoundments including Lakes Powell and

Mohave. The costs of the invasion are already apparent, as the Southern Nevada Water Authority has spent approximately $32 million (US dollars until 2009) to manage quagga biomass impacts on the water intake infrastructure of Lake Mead, a recently invaded reservoir in the Western U.S.

(Peggy Roefer, Southern Nevada Water Authority, pers. communication). These recent invasions 11 have spurred efforts to determine invasion risk posed by zebra and quagga mussels in western waters.

There are a large number of dreissenid mussel establishment risk assessment approaches that have been based on European and Eastern North American invasions that may or may not be appropriate for evaluations of western water ways. Risk assessment for the western U.S. should be based on these approaches, but with careful consideration of western water body characteristics such as differences in water temperature, calcium and other nutrient concentrations as well as food availability and substrate size that may determine different parameters for western waterways. Water column calcium concentration is often used as an index for determining the potential for mollusk establishment, growth, and reproduction with variable requirements depending on the species (Ramcharan et al. 1992, Sousa et al. 2008,

Whittier et al. 2008). Food availability is also an important variable for mollusk establishment, and is often the cause for massive dreissenid mussel population crashes after initial population explosions (Strayer et al. 1996). Since the recent establishments in Lakes Mead, Powell and

Mohave, numerous studies are underway to determine zebra and quagga mussel invasion risk to

Western waterways. Based on empirical information gathered from water quality databases and modeled systems, Whittier et al. (2008) created a watershed-scale risk model for dreissenid species. This model is based on calcium requirements, primarily derived from zebra mussel data due to limited experimental data on quagga mussel survival. Managers have used this model to determine the risk-potential of quagga mussel establishment from invaded water bodies such as

Lake Mead. However, because quagga mussels appear to have different environmental tolerances than zebra mussels, (Jones and Riccardi 2005, Baldwin et al. 2002, Stoeckmann 2003,

Roe and MacIssac 1997, Zhulidov 2004), and possibly in other parts of their range (Domm et al. 12

1993, Antonov and Shkorbatov 1990), the potential risk of invasion to western water bodies may be underestimated by using zebra mussel-based risk assessments.

We measured calcium levels and used existing literature to determine the invasion risk of each ecosystem based on these levels using Whittier’s (2008) model to suggest the risk of invasion and comparing to an adult survival study using Lake Tahoe water by Chandra et al.

(2009). Whittier et al. (2008) used literature-based calcium thresholds in create a broad scale, landscape-level approach to determine survival probability for dreissenid mussels in Western watersheds. Thresholds were established based on calcium limitations of zebra mussel, since little calcium-based survival information existed for quagga mussel. Thus, these authors assumed that zebra and quagga mussel requirements were similar because of the genetic proximity of these two closely related taxa. Their findings are still useful however for a 1st order estimate of the invasion potential by dreissenids. They defined risk based on calcium concentrations as: very low (< 12 mg L–1), low (12–20 mg L–1), moderate (20–28 mg L–1), and high (> 28 mg L–1). According to their risk categories, the water bodies with “very low” risk during 2012 include Stampede, Boca, Prosser, Independence, Marlette, Donner and Martis.

Although in 2010 Stampede was marginal in concentration and could be placed in the low category (Rammer and Chandra 2010), this was not the case in 2011 (Caldwell and Chandra

2012), and has declined even further in 2012. Systems with “low” risk were Rye Patch and

Lahontan reservoirs during 2010/2011, while Spooner Lake was classified in “moderate to high” risk in all years. Spooner Lake has had a relatively high concentration of calcium when compared to other lakes in the basin. This is likely caused by its proximity to a major highway, run-off of various road way bi-products may be the driver of these high calcium concentrations. 13

In contrast to the Whittier and colleagues risk assessment, we also utilized another study assessing adult survivability based on Lake Tahoe waters which contain approximately 13 ppm calcium. Chandra et al. (2009) suggests that after a 51 day exposure, quagga adults survive, exhibit positive growth, and may have the potential to release gametes. This study did not have the funding to follow the reproductive cycle of the mussels to determine if they could produce mature veligers. They suggest that the occurrence of veligers in the low calcium waters of

Colorado Lake which are similar to the Truckee River Region suggest the potential for some viable production. Using this study as a benchmark and analyzing risk from another viewpoint, only Spooner Lake is at risk.

According to Whittier’s (2008) risk assessment based on the concentration of calcium in the water column, the majority of systems surveyed in Truckee River Watershed were at relatively low risk for the invasion of dreissenids during 2011. Because this assessment was developed using a biased amount of data for the zebra mussel, it is likely that quagga mussels have different requirements (Jones and Riccardi 2005, Chandra et al. 2009). It is unclear, if adult quagga mussels can reproduce in calcium limited systems, making it difficult to accurately assess their potential to establish in the Truckee River Watershed Lakes. To develop more accurate assumptions research should be devoted to dreissenid reproduction in low calcium waters, and include parameters other than calcium (pH, substrate size, nutrient limitation, food quality, etc.), to lead to better preventative measures, and a decreased chance of dreissenid establishment.

Rammer and Chandra (2010) analyzed the concentration of calcium in sediment pore- water and found variability within each lake. In this study, we chose to examine the variability of concentration in sediment pore-water in Donner Lake because of the presence of Asian clams in the lake. We hypothesized that Asian clam distribution may be influenced by the 14 concentration of calcium in sediment pore-water or in epilmnetic waters. Results from the 2011 study suggest homogeneity of calcium in the sediment pore-water in Donner Lake and no clear pattern was observed between location of clams and density of calcium (Caldwell and Chandra

2012). In contrast to Rammer and Chandra (2010), the calcium concentration in the water column and in the sediment was similar in Donner Lake during 2011 (Caldwell and Chandra

2012), however this could be an artifact of a high water year in 2011. We replicated the study during 2012 and saw similar results to 2011. This suggests that there are other drivers influencing the distribution of Asian clams in Donner Lake besides the concentration of calcium in the epilimnetic waters and the sediment pore-water.

Another interesting pattern detected during the 2012 sampling is the continued decrease in calcium concentration inter-annually. This pattern may be influenced by suite of variables including weather patterns, water year, and the geology of the watershed, and clearly deserves more consideration and research. If this pattern continues during continued sampling, it would appear that these lakes are becoming more resistant to the invasion of dressenid mussels

(Whittier et al. 2008).

Crayfish population dynamics

Crayfish were likely introduced to these systems to increase fish production sometime during the late 1800’s and early 1900’s, about the same time they were introduced into Lake

Tahoe, CA (Abrammason and Goldman 1970). The variability in CPUE between years is likely influence by lake productivity levels, along with year-specific water levels.

Crayfish have the potential to play a role in the flow of energy and nutrients throughout the system often having positive and negative impacts on both algal production and benthic invertebrate production and diversity (Flint and Goldman 1975). At low densities (0.16 ind/m2), 15

Flint (1975) showed that crayfish can stimulate periphyton production by removing old senescent cells, while at higher densities (1.05 ind/m2) they reduce periphyton potentially reducing food for benthic invertebrates. Additionally, crayfish excretion experiments by Flint (1975) indicate that they are a source of nitrogen to the lake, and can result in increased periphyton production.

Given the variety of effects grazing can have on periphyton production, along with their impact on the flow nutrients (Flint 1975; Lodge et al. 1994), the overall role of crayfish in benthic primary production is still not well understood. Thus, their role in primary production in these lakes may be significant and could impact a variety of lake variables.

Recent investigations of crayfish ecology and subsequent increases in their population suggest this consumer is competing and preying upon benthic invertebrates at the bottom of the lake. Preliminary data from pilot research at the University of Nevada Reno suggest that a crayfish are likely controlling the survival of native invertebrates in Lake Tahoe. Given the population of crayfish in these lakes it is possible that they may play a role in the structuring of benthic macro-invertebrates.

Table 1. Basic morphological characteristics of the 2012 Truckee River region study lakes.

Max Depth Surface Shoreline Lakes (m) Area (ha) (km) Donner 70.0 390.0 12.07 Stampede 52.0 1351.7 40.2 Boca 24.0 396.6 24.14 Prosser 24.0 303.5 17.7 Martis Creek L. 6.0 23.4 Na Independence 44.0 252.9 9.3 Spooner 4.0 31.6 Na Marlette 11.0 na Na

Table 2. Secchi depth measurements from the Truckee River region lakes during 2010 and 2012.

LAKE DATE SECCHI (m) 7/6/2010 9 8/16/2010 12.3125 Donner 9/15/2010 12.1875 8/23/2012 12.9 10/2/2012 12.5 7/20/2010 2.4775 8/19/2010 2.375 Spooner 9/22/2010 1.5 1 6/12/2012 NA 1 7/23/2012 NA 7/15/2010 3.4875 8/16/2010 3.5 Martis Creek L. 9/15/2010 3.75 6/14/2012 3.5 8/16/2012 3.25 7/27/2010 11.0375 8/31/2010 8.5625 9/24/2010 11.875 Independence 6/14/2012 6.9 8/16/2012 10 10/1/2012 10.5 7/23/2010 7.8125 8/19/2010 7.4375 9/22/2010 3.6875 Marlette 6/12/2012 8.5 7/23/2012 4* 10/4/2012 3.5 8/3/2010 4.75 Webber 9/24/2010 4.875 7/17/2010 5.25 9/13/2010 4.25 Prosser 6/13/2012 6.1 8/7/2012 4.2 9/27/2012 4.1 7/14/2010 5.81 9/13/2010 4.44 Boca 6/13/2012 3.1 2 8/8/2012 NA 9/24/2012 2.5 7/7/2010 6.56 9/13/2010 5.31 Stampede 6/13/2012 6.2 8/17/2012 3.1 9/26/2012 4.8 1 To many weeds to make accurate measurement 2 To windy to obtain accurate measurement * Choppy waters may have influenced measurement

Table 3. Invasive plants and adult invertebrates present in Truckee River region lakes in 2010,2011, and 2012 as determined from UNR shoreline surveys and CFG visual surveys. Species presence is denoted by “X.” A blank space indicates no species were found during the surveys.

Adult Invertebrates Plants Lakes Quagga Zebra NZMS Corbicula EWM Hydrilla Marlette Donner X Stampede Boca Prosser Martis Creek L. X Independence Spooner X

Table 4. Concentration of calcium (ppm) in the epilimnetic waters of lakes in the Truckee River region during 2012. Lake Date n Average SE Boca 13-Jun-12 3 3.09 1.30 Boca 24-Sep-12 3 6.60 0.21 Donner 25-Jul-12 1 5.34 NA Donner 4-Oct-12 3 5.16 0.71 Donner* 14-Nov-12 10 6.27 0.40 Independence 14-Jun-12 3 3.99 0.12 Independence 1-Oct-12 3 3.98 0.13 Marlette 12-Jun-12 3 3.07 0.90 Marlette 4-Oct-12 3 3.94 0.33 Martis Ck 14-Jun-12 3 5.53 0.05 Martis Ck 16-Aug-12 3 8.67 0.81 Prosser 13-Jun-12 3 4.03 0.82 Prosser 28-Sep-12 3 6.74 0.24 Spooner 12-Jun-12 3 28.64 11.55 Spooner 4-Oct-12 3 25.92 1.74 Stampede 13-Jun-12 3 2.75 0.05 Stampede 26-Aug-12 3 6.10 0.30 * Average sediment pore water concentration of calcium from Donner lake

Lake 1. Donner 10 2. Stampede 3. Boca 4. Prosser 5. Martis Creek L. 6 6. Webber 7 2 11 34 7. Independence 1 5 8. Spooner 89 9. Marlette 10. Pyramid 11. Lahontan 12. Rye Patch

Figure 1. Truckee River Watershed and location of study lakes within the watershed.

A. Spooner Lake

Temperature (°C) 0 5 10 15 20 25 0

4 6/12/2012 7/23/2012 10/4/2012

Dissoloved oxygen (mg/L) 0 5 10 15 20 0

4 6/12/2012 7/23/2012 10/4/2012

Conducvity (µS) 0 100 200 300 400 500 600 700 0

4 6/12/2012 7/23/2012 10/4/2012

B. Marlette Lake

Temperature (°C) 0 5 10 15 20 0 2 4 6 8 10 12 14 6/12/2012 7/23/2012 10/4/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 10 12 0 2 4 6 8 10 12 14 6/12/2012 7/23/2012 10/4/2012

Conducvity (µS) 0 20 40 60 80 100 0 2 4 6 8 10 12 14 6/12/2012 7/23/2012 10/4/2012

C. Boca Reservoir

Temperature (°C) 0 5 10 15 20 0

20 6/13/2012 9/24/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 10 12 0

20 6/13/2012 9/24/2012

Conducvity (µS) 0 20 40 60 80 0

20 6/13/2012 9/24/2012

D. Stampede Reservoir

Temperature (°C) 0 5 10 15 20 25 0 5 10 15 20 25 30 35 6/13/2012 8/17/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 10 12 0 5 10 15 20 25 30 35 6/13/2012 8/17/2012

Conducvity (µS) 0 10 20 30 40 50 60 70 0 5 10 15 20 25 30 35 6/13/2012 8/17/2012

E. Prosser Reservoir

Temperature (°C) 0 5 10 15 20 25 0

20 6/13/2012 8/7/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 0

20 6/13/2012 8/7/2012

Conducvity (µS) 0 10 20 30 40 50 60 70 0

20 6/13/2012 8/7/2012

F. Independence Lake

Temperature (°C) 0 5 10 15 20 0

30 6/14/2012 10/1/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 10 0

30 6/14/2012 10/1/2012

Conducvity (µS) 0 10 20 30 40 50 0

30 6/14/2012 10/1/2012

G. Martis Creek Lake

Temperature (°C) 0 5 10 15 20 25 30 0

6 6/14/2012 8/16/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 10 0

6 6/14/2012 8/16/2012

Conducvity (µS) 0 50 100 150 200 0

6 6/14/2012 8/16/2012

H. Donner Lake

Temperature (°C) 0 5 10 15 20 25 0 5 10 15 20 25 30 35 8/23/2012 10/2/2012

Dissoloved oxygen (mg/L) 0 2 4 6 8 10 12 0 5 10 15 20 25 30 35 8/23/2012 10/2/2012

Conducvity (µS) 0 20 40 60 80 100 0

40 8/23/2012 10/2/2012

Figure 2. Temperature, dissolved oxygen and conductivity profiles for lakes in the Truckee River region.

20 2010 15 2011 10 2012 Calcium concentron (ppm) 5

Figure 3. Mean concentration of calcium in the epilimnetic waters of the Truckee River Watershed lakes, from 2010, 2011, and 2012.

AB 2.5 AB

1.5

CPUE 1

0.5

Figure 4. Catch per unit effort (CPUE) for crayfish in the lakes in the Truckee River lakes region. Independence lake is significantly lower than Marlette, Prosser, and Stampede (p<.05, CI=99.42%).

70 Averages Outliers 60 C BC A B 50

30 Carapace length (mm) 20

0 Marlee Donner Boca Stampede Prosser Independence n = 50 n = 65 n = 40 n = 60 n = 21 n = 10

Figure 5. Size distribution of crayfish carapace size (mm) in lakes in the Truckee River region, statistical groupings (p<.05, CI=99.55%) are denoted by letters above each boxplot. 31

2.5

1.5

1 2010

2012 0.5

Figure 6. Comparison of crayfish CPUE from 2010 to 2012 in lakes in the Truckee River region.

ACKNOWLEDGMENTS

We would like to thank all cooperating agencies and personnel for contributing to the successful completion of this project: Jim Gaither, David Mandrella, and Gina Rammer at the

The Nature Conservancy provided access and field support at the Independence Lake preserve.

The California Fish and Game for analysis of veliger DNA. Sami Evanson was a wonderful technician and was of great help as was the entire staff at the University of Nevada’s Aquatic

Ecosystem and Analysis Laboratory. Special thanks to Kim Boyd and Dave Roberts at the

Tahoe Resource Conservation District (TRCD) for submitting an application for funding and guiding the overall project. This project was funded by the Truckee River Fund to TRCD to S.

Chandra at the University of Nevada- Reno.

REFERENCES

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Ramcharan C.W., Padilla D.K., Dodson, S.I. 1992. Models to predict potential occurrence and density of the zebra mussel Dreissena-polymorpha. Canadian Journal of Fisheries and Aquatic Sciences. 49: 2611-2620. Rammer, G., Chandra, S., 2010. Inventory of aquatic invasive species and water quality in lakes in the Lower Truckee River Region: 2010. Riccardi, A., MacIsaac, H.J., 2000. Recent mass invasion of the North American Great Lakes by Ponto-Caspian species. Trends in Ecology and Evolution. 15 (2): 62-65. Ricciardi, A; Neves, RJ; Rasmussen, JB. 1998. Impending extinctions of North American freshwater mussels (Unionoida) following the zebra mussel (Dreissena polymorpha) invasion. Journal of Animal Ecology 67: 613-61). Roe, S.L. and H.J. MacIsaac. 1997. Deepwater population structure and reproductive state of quagga mussels (Dreissena bugensis) in Lake Erie. Canadian Journal of Fisheries and Aquatic Sciences. 54: 2428–2433. Sousa, R., Antunes, C., and L. Guilhermino. 2008. Ecology of the invasive Asian clam Corbicula fluminea (Muller, 1774) in aquatic ecosystems: an overview. Annales de Limnologie-International Journal of Limnology 44: 85-94. Stoeckmann, A. 2003. Physiological energetics of Lake Erie Dreissenid mussels: a basis for the displacement of Dreissena polymorpha by Dreissena bugensis. Canadian Journal of Fisheries and Aquatic Sciences. 60: 126-134. Stokstad, E. 2007. Feared Quagga mussel turns up in Western United States. Science 315:453. Strayer, D.L., Powell, J., Ambrose, P. Smith, L.C. Pace, M.L. Fischer, D.T. 1996. Arrival, spread, and early dynamics of a zebra mussel (Dreissena polymorpha) population in the Hudson River estuary. Canadian Journal of Fisheries and Aquatic Sciences. 1144-1153. Umek, J., Chandra, S., and Brownstein, J. 2009. Limnology and food web structure of a large terminal ecosystem, Walker Lake (NV, USA). Natural Resources and Environmental Issues: Vol 15:15. Vander Zanden, M.J., Chandra, S., Allen, B.C., Reuter, J.E., Goldman, C.R., 2003. Historical food web structure and restoration of native aquatic communities in the Lake Tahoe (California-Nevada) Basin. Ecosystems. 6(3): 274-288. Whittier, T.R., Ringold, P.L., Herlihy, A.T., and Pierson, S.M. 2008. A calcium-based invasion risk assessment for zebra and quagga mussels (Dreissena spp). Front Ecol Environ 6(4): 180-184 Wittmann, M., J. Reuter, G. Schladow, S. Hackley, B Allen, S Chandra, A. Caires.Unpublished: January 2008. Asian Clam (Corbicula fluminea) of Lake Tahoe: Preliminary scientific findings in support of a management plan. Zhulidov, A.V., D.F. Pavlov, T.F. Nalepa, G.H. Scherbina, D.A. Zhulidov, T. Yu. Gurtovaya. 2004. Relative Distributions of Dreissena bugensis and Dreissena polymorpha in the Lower Don River System, Russia. International Review of Hydrobiology. 89(3): 326- 333.

Appendix A. Water quality profiles (temperature, dissolved oxygen, and specific conductivity) for each of the Truckee River region study lakes in 2010. a. Donner, b. Spooner, c. Martis Creek L., d. Independence, e. Marlette, f. Webber, g. Prosser, h. Boca, i. Stampede, j. Lahontan, k. Rye Patch, and l. Pyramid. a. Donner Lake

Temperature (oC) 0 5 10 15 20 25 0

Depth (m) 30

Dissolved Oxygen (mg/l) 0 2 4 6 8 10 12 14 0

Depth (m) 40

60 36

Specific Conductivity (mS) 88 90 92 94 96 98 100 102 0

Depth (m) 40

60 7/6/2010 8/16/2010 9/15/2010 b. Spooner Lake

Temperature (oC) 0 5 10 15 20 25 0 0.5 1 1.5 2 2.5 Depth (m) 3 3.5 4 4.5

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 10 0 0.5 1 1.5 2 2.5 Depth (m) 3 3.5 4 4.5

Specific Conductivity (mS) 400 500 600 700 800 900 1000 1100 0 0.5 1 1.5 2 2.5 Depth (m) 3 3.5 4 4.5

7/20/2010 8/19/2010 9/22/2010 c. Martis Creek L.

Temperature (oC) 0 5 10 15 20 25 0 1 2 3

Depth (m) 4 5 6

Dissolved Oxygen (mg/l) 0 2 4 6 8 10 0

Depth (m) 4

7 38

Specific Conductivity (mS) 100 150 200 250 300 350 0 1 2 3 4 Depth (m) 5 6 7

7/15/2010 8/16/2010 9/15/2010

d. Independence Lake

Temperature (oC) 0 5 10 15 20 25 0 5 10 15 20

Depth (m) 25 30 35 40

Dissolved Oxygen (mg/l) 0 2 4 6 8 10 12 0 5 10 15 20

Depth (m) 25 30 35 40 39

Specific Conductivity (mS) 37 38 39 40 41 42 0 5 10 15 20

Depth (m) 25 30 35 40

7/27/2010 8/31/2010 9/24/2010 10/21/2010

e. Marlette Lake

Temperature (oC) 0 5 10 15 20 25 0

6 Depth (m) 8

14 40

Dissolved Oxygen (mg/l) 0 2 4 6 8 10 0 2 4 6 Depth (m) 8 10 12 14

Specific Conductivity (mS) 43 44 45 46 47 48 49 50 0 2 4 6 8 Depth (m) 10 12 14

7/23/2010 8/19/2010 9/22/2010

f. Webber Lake

Temperature (oC) 0 5 10 15 20 25 0 5 10 15 20 Depth (m) 25 30 35 41

Dissolved Oxygen (mg/l) 0 2 4 6 8 10 12 0 5 10 15 20 Depth (m) 25 30 35

Specific Conductivity (mS) 0 10 20 30 40 50 60 70 80 0 5 10 15 20 Depth (m) 25 30 35

8/3/2010 9‐24‐10 L1 9‐24‐10 L2

*L1 and L2 represent two different sampling locations on 9-24. The second location had an increased depth of fine sediments from 20 to 31 m.

g. Prosser Reservoir 42

Temperature (oC) 0 5 10 15 20 25 0

Depth (m) 20

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 0

Depth (m) 20

Specific Conductivity (mS/cm) 40 42 44 46 48 50 52 54 56 0

Depth (m) 20

30 7/17/2010 9/13/2010

h. Boca Reservoir 43

Temperature (oC) 0 5 10 15 20 25 0

Depth (m) 15

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 10 0

15 Depth (m)

Specific Conductivity (mS/cm) 0 0.02 0.04 0.06 0.08 0.1 0.12 0

15 Depth (m)

25 8/21/2010 10/14/2010

i. Stampede Reservoir 44

Temperature (oC) 0 5 10 15 20 25 0

30 Depth (m) 40

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 10 0

Depth (m) 40

Specific Conductivity (uS/cm) 0 0.02 0.04 0.06 0.08 0.1 0

Depth (m) 40

60 8/21/2010 10/14/2010 j. Lahontan Reservoir 45

Temperature (oC) 0 5 10 15 20 25 30 0 2 4 6 8

Depth (m) 10 12 14 16 18 20

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 10 0 2 4 6 8 10 Depth (m) 12 14 16 18 20

Specific Conductivity (uS/cm) 0.224 0.225 0.226 0.227 0.228 0.229 0.23 0.231 0.232 0.233 0.234 0.235 0 2 4 6 8 10 12 Depth (m) 14 16 18 20 8/19/2010 k. Rye Patch Reservoir 46

Temperature (oC) 0 5 10 15 20 25 0

6 Depth (m) 8

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 10 0

Depth (m) 8

Specific Conductivity (us/cm) 0.75 0.76 0.77 0.78 0.79 0.8 0.81 0.82 0.83 0.84 0.85 0.86 0

Depth (m) 8

12 8/21/2010 10/13/2010

l. Pyramid Lake 47

o Temperature ( C) 0 5 10 15 20 25 0

30 Depth(m) 40

Dissolved Oxygen (mg/l) 0 1 2 3 4 5 6 7 8 9 10 0

Depth(m) 40

Specific Conductivity (mS/cm) 7.8 7.85 7.9 7.95 8 8.05 8.1 8.15 8.2 8.25 0

Depth(m) 40

60 8/20/2010 7/22/2010 10/15/2010

Appendix B. Invasive species visual shoreline survey data from 2010, 2011, 2012.

Marlette Lake LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 9.889 119 53.833 100F 0 0 0 0 0 0 2 39 9.864 119 53.882 95R 5F 0 0 0 0 0 0 3 39 9.675 119 53.888 5W 5R 90F 0 0 0 0 0 0 4 39 9.845 119 54.075 10W 30F 60R 0 0 0 0 0 0 5 39 10.366 119 54.413 50R 50F 0 0 0 0 0 0 6 39 10.116 119 54.208 30F 10W 60R 0 0 0 0 0 0 7 39 10.572 119 53.890 50R 50F 0 0 0 0 0 0 22-Jul-10 8 39 10.589 119 54.210 50W 20F 30R 0 0 0 0 0 0 9 39 10.779 119 53.934 90R 10F 0 0 0 0 0 0 10 39 10.801 119 52.011 95F 5R 0 0 0 0 0 0 11 39 10.797 119 54.157 95R 5W 0 0 0 0 0 0 12 39 10.750 119 55.251 90R 10F 0 0 0 0 0 0 13 39 10.516 119 54.417 80R 20F 0 0 0 0 0 0 14 39 10.417 119 53.840 95 R 5F 0 0 0 0 0 0 15 39 10.414 119 54.338 100R 0 0 0 0 0 0 1 39 10.767 119 53.911 100F 0 0 0 0 0 0 2 39 10.774 119 53.944 40R 10W 50F 0 0 0 0 0 0 3 39 10.740 119 53.898 60R 40F 0 0 0 0 0 0 4 39 10.712 119 53.910 75R 25F 0 0 0 0 0 0 5 39 10.393 119 54.391 5W 35R 60F 0 0 0 0 0 0 6 39 10.373 119 54.440 50R 50F 0 0 0 0 0 0 7 39 10.380 119 54.455 25R 75F 0 0 0 0 0 0 22-Sep-10 8 39 10.380 119 54.324 20W 50R 30F 0 0 0 0 0 0 9 39 9.681 119 53.892 100F 0 0 0 0 0 0 10 39 9.694 119 53.931 80W 10R 10F 0 0 0 0 0 0 11 39 9.11 119 53.817 50R 50F 0 0 0 0 0 0 12 39 9.906 119 53.865 90R 10F 0 0 0 0 0 0 13 39 9.881 119 53.854 25R 75F 0 0 0 0 0 0 14 39 9.867 119 53.872 90R 10F 0 0 0 0 0 0 15 39 9.875 119 53.899 100R 0 0 0 0 0 0

Marlette Lake (continued) 1 39 9.8887 119 53.8539 100F 0 0 0 0 0 0 2 39 9.8739 119 53.8870 70R 30F 0 0 0 0 0 0 3 39 9.8285 119 53.8236 80F 10W 10R 0 0 0 0 0 0 4 39 9.6796 119 53.8875 100F 0 0 0 0 0 0 5 39 9.7455 119 53.9864 80F 10W 10R 0 0 0 0 0 0 6 39 9.8894 119 54.0213 50R 50F 0 0 0 0 0 0 7 39 10.1475 119 54.2386 80F 20R 0 0 0 0 0 0 30-Jul-12 8 39 10.3679 119 54.3221 80F 20R 0 0 0 0 0 0 9 39 10.3694 119 54.4387 90R 10F 0 0 0 0 0 0 10 39 9.9101 119 53.8130 95F 5R 0 0 0 0 0 0 11 39 9.9568 119 53.7649 95F 5R 0 0 0 0 0 0 12 39 9.9939 119 53.7649 60F 40R 0 0 0 0 0 0 13 39 10.0315 119 53.7194 70F 30W 0 0 0 0 0 0 14 39 10.0765 119 53.6953 100F 0 0 0 0 0 0 15 39 10.2560 119 53.6382 100F 0 0 0 0 0 0 1 39 10 22.47-119 54 26.37 95F 5R 0 0 0 0 0 0 2 39 10 23.60-119 54 23.36 90R 10F 0 0 0 0 0 0 3 39 10 22.94-119 54 19.38 75F 25R 0 0 0 0 0 0 4 39 10 15.46-119 54 16.19 100F 0 0 0 0 0 0 5 39 10 12.69-119 54 15.35 90F 5R 5W 0 0 0 0 0 0 6 39 10 10.92-119 54 15.40 90F 5R 5W 0 0 0 0 0 0 7 39 10 05.99-119 54 11.77 50F 50R 0 0 0 0 0 0 5-Oct-12 8 39 09 58.80 -119 54 7.58 90F 10R 0 0 0 0 0 0 9 39 09 54.94-119 54 05.96 100F 0 0 0 0 0 0 10 39 09 47.92-119 54 01.5410W 80F 10R 0 0 0 0 0 0 11 39 09 41.49-119 56 53.50 60F 40R 0 0 0 0 0 0 12 39 09 51.92-119 56 52.62 70R 30F 0 0 0 0 0 0 13 39 09 54.38-119 56 51.94 80F 20R 0 0 0 0 0 0 14 39 09 53.85-119 56 49.47 100F 0 0 0 0 0 0 15 39 09 56.02-119 56 46.87 100F 0 0 0 0 0 0

Boca Reservoir LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 24.466 120 5.498 50R 50F 0 0 0 0 0 0 2 39 24.902 120 5.349 90R 10F 0 0 0 0 0 0 3 39 25.233 120 5.234 80R 10W 10F 0 0 0 0 0 0 4 39 25.210 120 5.350 100R 0 0 0 0 0 0 5 39 25.094 120 5.845 90F 10W 0 0 0 0 0 0 6 39 24.756 120 6.029 90F 10W 0 0 0 0 0 0 7 39 24.432 120 6.102 90R 10F 0 0 0 0 0 0 13-Jul-10 8 39 24.441 120 6.474 10W 90F 0 0 0 0 0 0 9 39 24.440 120 6.515 90R 10F 0 0 0 0 0 0 10 39 24.229 120 6.293 90R 10F 0 0 0 0 0 0 11 39 23.907 120 6.481 50R 50F 0 0 0 0 0 0 12 39 23.903 120 6.512 80F 20R 0 0 0 0 0 0 13 39 23.693 120 6.167 90F 10R 0 0 0 0 0 0 14 39 23.376 120 5.841 100R 0 0 0 0 0 0 15 39 23.530 120 5.565 90R 10F 0 0 0 0 0 0 1 39 23.844 120 6.402 25R 75F 0 0 0 0 0 0 2 39 23.912 120 6.455 5R 95F 0 0 0 0 0 0 3 39 23.911 120 6.478 10R 90F 0 0 0 0 0 0 4 39 23.919 120 6.490 5R 95F 0 0 0 0 0 0 5 39 23.931 120 6.470 100F 0 0 0 0 0 0 6 39 23.394 120 5.869 5R 95F 0 0 0 0 0 0 7 39 23.382 120 5.834 100R 0 0 0 0 0 0 16-Aug-10 8 39.23.392 120 5.795 100R 0 0 0 0 0 0 9 39 23.486 120 5.577 100R 0 0 0 0 0 0 10 39 23.464 120 5.588 80R 20F 0 0 0 0 0 0 11 39 23.766 120 5.478 90R 10F 0 0 0 0 0 0 12 39 23.841 120 5.436 50R 50F 0 0 0 0 0 0 13 39 24.665 120 5.475 25R 15W 60F 0 0 0 0 0 0 14 39 24.911 120 5.333 95R 5F 0 0 0 0 0 0 15 39 25.053 120 5.365 100F 0 0 0 0 0 0 1 39 24.186 120 6.1333 100F 0 0 0 0 0 0 2 39 24.1825 120 6.0985 80F 20R 0 0 0 0 0 0 3 39 24.1141 120 6.1385 100F 0 0 0 0 0 0 10-Jan-12 4 39 24.0509 120 6.1522 100F 0 0 0 0 0 0 5 39 24.0037 120 6.1646 100F 0 0 0 0 0 0 6 39 23.9429 120 6.2310 80F 20R 0 0 0 0 0 0 7 39 23.9388 120 6.1502 90F 10R 0 0 0 0 0 0

Boca Reservoir (continued) 1 39 24.0433 120 6.2567 100F 0 0 0 0 0 0 2 39 24.0760 120 6.3152 80F 20R 0 0 0 0 0 0 3 39 23.9048 120 6.4859 50R 50F 0 0 0 0 0 0 4 39 23.8399 120 6.4084 90R 10F 0 0 0 0 0 0 5 39 23.8348 120 6.1549 50R 50F 0 0 0 0 0 0 6 39 23.7664 120 6.1782 90R 10F 0 0 0 0 0 0 7 39 23.5886 120 5.9916 100R 0 0 0 0 0 0 2-Aug-12 8 39 23.3773 120 5.8311 100R 0 0 0 0 0 0 9 39 23.4868 120 5.5688 100R 0 0 0 0 0 0 10 39 23.7810 120 5.4370 95R 5F 0 0 0 0 0 0 11 93 24.1400 120 5.4077 100R 0 0 0 0 0 0 12 39 24.3073 120 5.4898 100R 0 0 0 0 0 0 13 39 24.4600 120 5.5009 20R 80F 0 0 0 0 0 0 14 39 24.6281 120 5.4643 50R 50F 0 0 0 0 0 0 15 39 24.9973 120 5.2802 100R 0 0 0 0 0 0 1 39 23 48.30 120 5 28.65 90R 10F 0 0 0 0 0 0 2 39 23 33.06 120 5 33.76 80R 20F 0 0 0 0 0 0 3 39 24 8.06 120 5 27.90 60R 40F 0 0 0 0 0 0 4 39 24 22.85 120 5 31.12 100P 0 0 0 0 0 0 5 39 24 34.50 120 5 26.43 90P 5R 5F 0 0 0 0 0 0 6 39 24 49.21 120 5 30.39 80F 20R 0 0 0 0 0 0 7 39 25 7.38 120 5 17.23 90R 10F 0 0 0 0 0 0 24-Sep-12 8 39 25 1.63 120 5 51.89 90F 10R 0 0 0 0 0 0 9 39 24 43.34 120 6 0.29 50R 50F 0 0 0 0 0 0 10 39 24 25.20 120 6 4.76 50R 50F 0 0 0 0 0 0 11 39 23 54.87 120 6 8.85 60F 40R 0 0 0 0 0 0 12 39 23 44.89 120 6 8.17 60F 40R 0 0 0 0 0 0 13 39 23 33.78 120 5 56.97 90F 10R 0 0 0 0 0 0 14 39 23 23.84 120 5 49.45 100R 0 0 0 0 0 0 15 39 23 53.16 120 6 22.05 60F 30R 10P 0 0 0 0 0 0

Stampede Reservoir LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 27.991 120 8.298 95F 5R 0 0 0 0 0 0 2 39 27.808 120 9.308 25W 25R 50F 0 0 0 0 0 0 3 39 28.199 120 9.523 75F 25R 0 0 0 0 0 0 4 39 28.537 120 10.036 50F 50R 0 0 0 0 0 0 5 39 28.916 120 8.700 50R 50F 0 0 0 0 0 0 6 39 29.417 120 7.893 90F 10R 0 0 0 0 0 0 7 39 29.396 120 7.074 95R 5F 0 0 0 0 0 0 6-Aug-10 8 39 28.968 120 6.484 100R 0 0 0 0 0 0 9 39 29.253 120 6.317 40R 60F 0 0 0 0 0 0 10 39 29.203 120 6.174 10W 70F 20R 0 0 0 0 0 0 11 39 28.617 120 6.236 20W 70F 10R 0 0 0 0 0 0 12 39 28.284 120 6.587 70R 30F 0 0 0 0 0 0 13 39 28.258 120 7.356 100R 0 0 0 0 0 0 14 39 28.275 120 8.018 90F 10R 0 0 0 0 0 0 15 39 28.275 120 8.018 80F 20R 0 0 0 0 0 0 1 39 28.261 120 6.616 100R 0 0 0 0 0 0 2 39 28.252 120 6.657 10R 90F 0 0 0 0 0 0 3 39 28.332 120 6.513 75R 25F 0 0 0 0 0 0 4 39 28.392 120 6.395 50R 50F 0 0 0 0 0 0 5 39 28.390 120 6. 302 60R 40F 0 0 0 0 0 0 6 39 28.404 120 6.312 30R 70F 0 0 0 0 0 0 7 39 28.441 120 6.285 100R 0 0 0 0 0 0 28-Sep-10 8 39 28.450 120 6.190 100R 0 0 0 0 0 0 9 39 28.222 120 7.836 5R 95F 0 0 0 0 0 0 10 39 28.263 120 8.047 100F 0 0 0 0 0 0 11 39 28.264 120 8.033 10R 90F 0 0 0 0 0 0 12 39 28.268 120 8.104 95F 5R 0 0 0 0 0 0 13 39 27.990 120 8.275 25R 75F 0 0 0 0 0 0 14 39 29.541 120 5.951 50R 50F 0 0 0 0 0 0 15 39 29.519 120 5.957 50R 50F 0 0 0 0 0 0 1 39 29.8432 120 5.5745 50F 50R 0 0 0 0 0 0 2 39 29 .7197 120 5.8008 50F 30R 20W 0 0 0 0 0 0 3 39 29.6072 120 5.9484 40F 40R 20W 0 0 0 0 0 0 10-Jan-12 4 39 29.3598 120 6.0100 80R 20R 0 0 0 0 0 0 5 39 29.3302 120 6.2779 50F 50R 0 0 0 0 0 0 6 39 29.0369 120 6.5455 90R 10F 0 0 0 0 0 0 7 39 29.3352 120 6.6245 100R 0 0 0 0 0 0

Stampede Reservoir (continued) 8 39 29.5371 120 7.1053 30F 70R 0 0 0 0 0 0 9 39 30.0592 120 7.9351 100F 0 0 0 0 0 0 10 39 28.6801 120 9.3135 50F 50R 0 0 0 0 0 0 11 39 28.5461 120 9.9979 100R 0 0 0 0 0 0 10-Jan-12 12 39 28.3890 120 6.3729 100R 0 0 0 0 0 0 13 39 28.1531 120 7.8794 30F 70R 0 0 0 0 0 0 14 39 28.2548 120 8.0308 90R 10W 0 0 0 0 0 0 15 39 27.9574 120 8.0983 50F 50R 0 0 0 0 0 0 1 39 28.6039 120 6.2307 100R 0 0 0 0 0 0 2 39 28.3927 120 6.3459 20R 80F 0 0 0 0 0 0 3 39 28.2142 120 6.8306 95F 5R 0 0 0 0 0 0 3-Aug-12 4 39 28.3583 120 7.0033 80F 20R 0 0 0 0 0 0 5 39 28.2418 120 8.0303 10R 90F 0 0 0 0 0 0 6 39 28.2144 120 7.9373 50R 50F 0 0 0 0 0 0 7 39 27.9716 120 8.1440 20R 80F 0 0 0 0 0 0 8 NA NA 50F 50R 0 0 0 0 0 0 9 NA NA 70F 30R 0 0 0 0 0 0 10 NA NA 90R 10F 0 0 0 0 0 0 11 NA NA 50F 50R 0 0 0 0 0 0 17-Aug-12 12 NA NA 80R 20F 0 0 0 0 0 0 13 NA NA 50F 50R 0 0 0 0 0 0 14 NA NA 80F 20R 0 0 0 0 0 0 15 NA NA 100R 0 0 0 0 0 0 1 39 23 52.94 120 6 22.09 70F 30R 0 0 0 0 0 0 2 39 28 14.92 120 8 3.43 70F 30R 0 0 0 0 0 0 3 39 28 13.33 120 7 58.04 80F 20R 0 0 0 0 0 0 4 39 28 37.40 120 6 13.82 80F 20R 0 0 0 0 0 0 5 39 28 23.26 120 6 19.96 10R 90F 0 0 0 0 0 0 6 39 28 19.89 120 6 57.43 95F 5W 0 0 0 0 0 0 7 39 28 11.28 120 7 23.01 95F 5R 0 0 0 0 0 0 26-Sep-12 8 39 27 55.80 120 08 01.10 90F 10R 0 0 0 0 0 0 9 39 27 57.38 120 08 12.83 95F 5R 0 0 0 0 0 0 10 39 28 49.92 120 7 38.24 75R 25F 0 0 0 0 0 0 11 39 28 46.16 120 7 19.15 70R 25F 5W 0 0 0 0 0 0 12 39 28 20.36 120 7 08.04 90R 10F 0 0 0 0 0 0 13 39 28 05.16 120 7 29.92 90R 5F 5W 0 0 0 0 0 0 14 39 28 07.96 120 7 47.34 50F 50R 0 0 0 0 0 0

Prosser Reservoir LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 22.657 120 8.447 100R 0 0 0 0 0 0 2 39 22.781 120 8.283 100R 0 0 0 0 0 0 3 39 23.042 120 8.50 90R 10W 0 0 0 0 0 0 4 39 23.283 120 8.757 90F 10R 0 0 0 0 0 0 5 39 23.160 120 8.894 50R 50F 0 0 0 0 0 0 6 39 22.974 120 8.786 90F 10R 0 0 0 0 0 0 7 39 23.285 120 9.568 20R 80F 0 0 0 0 0 0 16-Jul-10 8 39 23.313 120 10.442 80R 20F 0 0 0 0 0 0 9 na na 100F 0 0 0 0 0 0 10 na na 40R 60F 0 0 0 0 0 0 11 na na 90F 10R 0 0 0 0 0 0 12 na na 90F 10R 0 0 0 0 0 0 13 na na 100R 0 0 0 0 0 0 14 na na 100F 0 0 0 0 0 0 1 39 22.388 120 9.274 50R 50F 0 0 0 0 0 0 2 39 22.490 120 9.239 50R 50F 0 0 0 0 0 0 3 39 22.346 120 9.280 70R 30F 0 0 0 0 0 0 4 39 22.639 120 8.757 80F 20R 0 0 0 0 0 0 5 39 22.666 120 8.552 95F 5R 0 0 0 0 0 0 6 39 22.658 120 8.478 100F 0 0 0 0 0 0 7 39 22.659 120 8.441 100R 0 0 0 0 0 0 17-Sep-10 8 39 22.806 120 8.251 100R 0 0 0 0 0 0 9 39 22.828 120 8.270 20R 80F 0 0 0 0 0 0 10 39 23.241 120 8.752 100F 0 0 0 0 0 0 11 39 23.246 120 8.805 100F 0 0 0 0 0 0 12 39 23.280 120 8.792 100F 0 0 0 0 0 0 13 39 23.232 120 8.718 100F 0 0 0 0 0 0 14 39 23.175 120 8.698 100F 0 0 0 0 0 0 15 39 23.137 120 8.670 40R 60F 0 0 0 0 0 0 1 39 23.1017 120 8.6878 90F 10R 0 0 0 0 0 0 2 39 23.0329 120 8.5801 100R 0 0 0 0 0 0 3 39 22.9986 120 8.5023 30F 70R 0 0 0 0 0 0 10-Jan-12 4 39 23.1300 120 9.4862 90R 10F 0 0 0 0 0 0 5 39 23.0730 120 9.4572 50F 50R 0 0 0 0 0 0 6 39 23.0198 120 9.4586 70F 30R 0 0 0 0 0 0 7 39 23.0415 120 8.7081 100F 0 0 0 0 0 0

Prosser Reservoir (continued) 8 39 22.9882 120 8.6535 100F 0 0 0 0 0 0 9 39 22.6504 120 8.6755 90F 10R 0 0 0 0 0 0 10-Jan-12 10 39 22.6454 120 8.7404 50F 50R 0 0 0 0 0 0 11 39 22.6776 120 8.8292 80F 20R 0 0 0 0 0 0 1 39 23.1130 120 8.6711 40R 60F 0 0 0 0 0 0 2 39 23.0388 120 8.5282 80R 20F 0 0 0 0 0 0 3 39 22.8144 120 8.2460 50R 50F 0 0 0 0 0 0 4 39 22.7492 120 8.3387 100R 0 0 0 0 0 0 5 39 22.6729 120 8.4490 100R 0 0 0 0 0 0 6 39 22.6536 120 8.6851 70F 30R 0 0 0 0 0 0 7 39 22.7080 120 9.0695 80F 20R 0 0 0 0 0 0 7‐Aug‐12 8 39 22.4738 120 9.2360 60F 40R 0 0 0 0 0 0 9 39 22.5687 120 9.4524 10R 90F 0 0 0 0 0 0 10 39 22.7552 120 9.2588 100F 0 0 0 0 0 0 11 39 22.8142 120 9.4296 90F 10R 0 0 0 0 0 0 12 39 22.9708 120 10.0809 90F 10R 0 0 0 0 0 0 13 39 23.0589 120 9.6627 95F 5R 0 0 0 0 0 0 14 39 22.9692 120 8.7706 70F 30R 0 0 0 0 0 0 15 39 23.2621 120 8.7217 50F 50R 0 0 0 0 0 0 1 39 23 2.67 120 8 36.64 50R 50F 0 0 0 0 0 0 2 39 22 58.96 120 8 39.68 80F 20P 0 0 0 0 0 0 3 39 22 45.62 120 8 19.89 100R 0 0 0 0 0 0 4 39 22 40.21 120 8 26.75 100R 0 0 0 0 0 0 5 39 22 39.16 120 8 43.92 50R 50F 0 0 0 0 0 0 6 39 22 42.84 120 9 02.22 60F 40R 0 0 0 0 0 0 7 39 22 58.08 120 8 59.37 70F 30R 0 0 0 0 0 0 27‐Sep‐12 8 39 23 04.41 120 9 29.28 100F 0 0 0 0 0 0 9 39 23 04.51 120 9 51.12 100R 0 0 0 0 0 0 10 39 23 6.44 120 10 4.71 50R 50F 0 0 0 0 0 0 11 39 22 53.11 120 9 42.79 80R 20F 0 0 0 0 0 0 12 39 22 50.74 120 9 25.93 50R 50F 0 0 0 0 0 0 13 39 22 45.81 120 9 41.67 100F 0 0 0 0 0 0 14 39 22 31.80 120 9 22.72 100F 0 0 0 0 0 0 15 39 22 20.32 120 9 23.76 70F 30R 0 0 0 0 0 0

Independence Lake LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 N 39 27.097 W 120 17.754 90R 10W 0 0 0 0 0 0 2 N 39 26.943 W 120 18.085 5F 95R 0 0 0 0 0 0 3 N 39 26.842 W 120 18.509 100R 0 0 0 0 0 0 4 N 39 26.678 W120 18.923 5F 95R 0 0 0 0 0 0 5 N 39 26.392 W120 19.345 20F 80R 0 0 0 0 0 0 6 N 39 26.110 W120 19.646 80F 20R 0 0 0 0 0 0 7 N 39 25.937 W120 19.704 100F 0 0 0 0 0 0 31-Aug-10 8 N 39 25.930 W120 19.753 100F 0 0 0 0 0 0 9 N39 25.890 W120 19.785 100F 0 0 0 0 0 0 10 N 39 25.838 W120 18.636 100F 0 0 0 0 0 0 11 N 39 26.143 W120 18.928 25W15F60R 0 0 0 0 0 0 12 N 39 26.502 W120 18.037 10F 90R 0 0 0 0 0 0 13 N 39 27.099 W120 17.413 20F 80R 0 0 0 0 0 0 14 N 39 27.075 W120 17.457 100R 0 0 0 0 0 0 15 N 39 27.024 W120 17.253 100R 0 0 0 0 0 0 1 39 27.078 120 17.439 75R 25F 0 0 0 0 0 0 2 39 27.074 120 17.461 100R 0 0 0 0 0 0 3 39 27.078 120 17.548 50R 50F 0 0 0 0 0 0 4 39 27.114 120 17.762 100R 0 0 0 0 0 0 5 39 26.813 120 18.591 100R 0 0 0 0 0 0 6 39 26.551 120 19.153 100R 0 0 0 0 0 0 7 39 26.114 120 19.642 90R 10F 0 0 0 0 0 0 29-Sep-10 8 39 26.005 120 19.706 10W 90F 0 0 0 0 0 0 9 39 25.925 120 19.679 5W 95W 0 0 0 0 0 0 10 39 25.900 120 19.674 10W 90F 0 0 0 0 0 0 11 39 26.256 120 18.774 40W 20R 40F 0 0 0 0 0 0 12 39 26.539 120 17.929 100R 0 0 0 0 0 0 13 39 26.996 120 17.290 10W 90F 0 0 0 0 0 0 14 39 26.988 120 17.263 75R 25F 0 0 0 0 0 0 15 39 27.102 120 17.406 75R 25F 0 0 0 0 0 0 1 39 26.9751 120 17.3782 100R 0 0 0 0 0 0 2 39 27 4.56 120 17 32.31 50F 50R 0 0 0 0 0 0 3 39 26 8460 120 17.4448 60F 40R 0 0 0 0 0 0 14-Dec-11 4 39 26.8088 120 17.5069 70F 30R 0 0 0 0 0 0 5 39 26.7427 120 17.6037 70F 30R 0 0 0 0 0 0 6 39 26.6653 120 17.7087 50F 50R 0 0 0 0 0 0

Independence Lake (continued) 1 39 26.7580 120 18.7534 80R 20F 0 0 0 0 0 0 2 39 26.6758 120 18.9017 80R 20F 0 0 0 0 0 0 3 39 26.4216 120 19.3074 65R 30F 5W 0 0 0 0 0 0 4 39 26.2045 120 19.5577 75R 20F 5W 0 0 0 0 0 0 5 39 25.9677 120 19.6506 60F 40R 0 0 0 0 0 0 6 39 25.8345 120 19.5549 95F 5W 0 0 0 0 0 0 7 39 25.9417 120 19.2951 60F 30R 10W 0 0 0 0 0 0 14-Jun-12 8 39 26.2106 120 18.9095 95R 5F 0 0 0 0 0 0 9 39 26.3867 120 18.5472 90R 10F 0 0 0 0 0 0 10 39 26.5103 120 18.0406 95R 5F 0 0 0 0 0 0 11 39 26.7274 120 17.6156 100R 0 0 0 0 0 0 12 39 26.9275 120 17.3577 60R 40F 0 0 0 0 0 0 13 39 29.9951 120 17.3769 90R 10F 0 0 0 0 0 0 14 39 26.9500 120 18.0417 90R 10F 0 0 0 0 0 0 15 39 27.0989 120 17.7796 80R 20F 0 0 0 0 0 0 1 39 26 55.63 120 18 7.08 80R 20F 0 0 0 0 0 0 2 39 26 50.11 120 18 29.60 75R 25F 0 0 0 0 0 0 3 39 26 31.30 120 19 9.00 50R 50F 0 0 0 0 0 0 4 39 26 15.50 120 19 31.59 80R 20F 0 0 0 0 0 0 5 39 26 4.61 120 19 38.02 80R 10F 10W 0 0 0 0 0 0 6 39 26 00.53 120 19 40.62 90F 10R 0 0 0 0 0 0 7 39 25 54.77 120 19 23.60 70F 30R 0 0 0 0 0 0 1-Oct-12 8 39 26 3.74 120 19 7.96 50R 50F 0 0 0 0 0 0 9 39 26 11.16 120 18 56.37 80R 20F 0 0 0 0 0 0 10 39 26 17.98 120 18 43.72 85F 15R 0 0 0 0 0 0 11 39 26 34.80 120 19 51.69 95R 5F 0 0 0 0 0 0 12 39 26 59.52 120 17 22.29 100R 0 0 0 0 0 0 13 39 27 2.54 120 17 30.01 100R 0 0 0 0 0 0 14 39 27 6.05 120 17 46.35 90R 10F 0 0 0 0 0 0 15 39 27 4.50 120 17 48.12 95R 5F 0 0 0 0 0 0

Donner Lake LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 19.321 120 17.368 100F 0 0 0 0 0 0 2 39 19.229 120 17.417 95R 5F 0 0 0 0 0 0 21-Jul-10 3 39 19.158 120 15.220 50R 50F 0 0 0 0 0 0 4 39 19.485 120 16.923 10R 10W 80F 0 0 0 0 0 0 5 39 19.483 120 16.577 10R 10W 80F 0 0 0 0 0 0 1 39 19.587 120 15.918 90R 5F 5W 0 0 0 0 0 0 2 39 19.479 120 17.010 70R 30F 0 0 0 0 0 0 3 39 19.501 120 18.001 85R 15F 0 0 0 0 0 0 4 39 19.393 120 94.706 60R 40F 0 0 0 0 0 0 5 39 19.383 120 14.650 80F 10R 10W 0 0 0 0 0 0 6 39 19.381 120 14.618 100F 0 0 0 0 0 0 7 39 19.385 120 14.481 10W 90F 0 0 0 0 0 0 15-Sep-10 8 39 19.243 120 15.126 10W 50R 40F 0 0 0 0 0 0 9 39 19.194 120 15.136 100F 0 0 0 0 0 0 10 39 19.162 120 15.154 100F 0 0 0 0 0 0 11 39 19.225 120 17.417 40R 60F 0 0 0 0 0 0 12 39 19.162 120 15.221 30R 70F 0 0 0 0 0 0 13 39 19.474 120 16.802 50R 50F 0 0 0 0 0 0 14 39 19.488 120 16.576 60R 40F 0 0 0 0 0 0 15 39 19.492 120 16.542 75R 15F 10W 0 0 0 0 0 0 1 39 19.587 120 15.918 10W 40F 50R 0 0 0 0 0 0 2 39 19.479 39 17.010 80F 20R 0 0 0 0 0 0 3 39 19.1577 120 17.2539 100F 0 0 0 0 0 0 4 39 19.0894 120 15.1660 100F 0 0 0 0 0 5% 5 39 19.2173 120 15.1660 90F R 0 0 0 0 0 5% 6 39 19.4325 120 14.5866 100F 0 0 0 0 0 2% 7 39 19 4395 120 14.4288 100F 0 0 0 0 0 15% 9-Dec-12 8 39 19.5240 120 14.3977 70F 30W 0 0 0 0 0 5% 9 39 19.6410 120 14.8572 98F 2R 0 0 0 0 0 10% 10 39 19.7061 120 15.3925 95F 5R 0 0 0 0 0 2% 11 39 19.1644 120 15.5588 60F 40R 0 0 0 0 0 0 12 39 19.0923 120 16.2859 60F 40R 0 0 0 0 0 2% 13 39 19.0562 120 16.7091 90R 10F 0 0 0 0 0 0 14 39 19.4801 120 16.3608 90F 10R 0 0 0 0 0 0 15 39 19.4440 120 16.7233 90F 10R 0 0 0 0 0 0

Donner Lake (continued) 1 39 19.63 120 14.66 90F 10R 0 0 0 0 0 0 2 39 19.71 120 15.45 50F 50R 0 0 0 0 0 0 3 39 19.5994 120 15.8868 50F 50R 0 0 0 0 0 5% 4 39 19.4926 120 16.3166 30F 70R 0 0 0 0 0 0 5 39 19.4702 120 16.6188 50F 50R 0 0 0 0 0 0 6 39 19.4788 120 16.9422 100R 0 0 0 0 0 0 7 39 19.4806 120 17.0239 100R 0 0 0 0 0 0 6-Aug-12 8 39 19.2367 120 17.3193 50F 50R 0 0 0 0 0 5% 9 39 19.0343 120 16.9822 50F 50R 0 0 0 0 0 5% 10 39 19.0480 120 16.5819 60F 40R 0 0 0 0 0 0 11 39 19.0898 120 16.0197 80R 20S 0 0 0 0 0 0 12 39 19.1787 120 15.4525 50F 50R 0 0 0 0 0 0 13 39 19.4186 120 14.7693 50F 50R 0 0 0 0 0 5% 14 39 19.2096 120 15.2015 50F 50R 0 0 0 0 0 0 15 39 19.3263 120 15.0015 100R 0 0 0 0 0 0 1 39 19 29.78 -120 17 3.52 90R 10F 0 0 0 0 0 1% 2 39 19 29.08 -120 16 59.33 80R 20F 0 0 0 0 0 0 3 39 19 28.08 -120 16 47.32 95R 5F 0 0 0 0 0 5% 4 39 19 29.10 -120 16 28.64 95R 5F 0 0 0 0 0 0 5 39 19 35.15 -120 15 55.78 100R 0 0 0 0 0 0 3-Oct-12 6 39 19 37.75 -120 14 33.91 90R 10F 0 0 0 0 0 2% 7 39 19 20.16 -120 14 17.58 95F 5R 0 0 0 0 0 1% 8 39 19 23.12 -120 14 37.85 100F 0 0 0 0 0 1% 9 39 19 22.91 -120 14 51.80 50R 50F 0 0 0 0 0 0 10 39 19 11.54 -120 15 8.40 100F 0 0 0 0 0 0

Martis Creek Lake LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 19.195 120 6.893 75R 25F 100% 0 0 0 0 0 2 39 19.224 120 6.833 25R 75F 50% 0 0 0 0 0 3 39 19.268 120 6.827 50R 50F 20% 0 0 0 0 0 4 39 19.244 120 6.895 100F 100% 0 0 0 0 0 5 39 19.301 120 6.855 80R 20F 100% 0 0 0 0 0 7/9/2010 6 39 19.458 120 6.823 10R 90F 60% 0 0 0 0 0 7 39 19.503 120 6.862 50R 50F 5% 0 0 0 0 0 8 39 19.034 120 7.025 60R 40F 50% 0 0 0 0 0 9 39 18.892 120 7.034 20R 80F 100% 0 0 0 0 0 10 39 18.925 120 7.001 50R 50F 95% 0 0 0 0 0 1 39 19.191 120 6.898 20R 5W 75F 5% 0 0 0 0 0 2 39 19. 185 120 6.902 50F 25R 25W 40% 0 0 0 0 0 3 39 19.166 120 6.898 60R 40F 85% 0 0 0 0 0 4 39 19.134 120 6.919 20R 80F 25% 0 0 0 0 0 5 39 19.198 120 6.878 30R 70F 50% 0 0 0 0 0 6 39 19.270 120 6.82 50F 50R 0 0 0 0 0 0 7 39 19.266 120 6.825 40R 10W 50F 15% 0 0 0 0 0 9/14/2010 8 39 19.271 120 6.831 5R 95F 100% 0 0 0 0 0 9 39 18.858 120 7.79 100F 0 0 0 0 0 0 10 39 18.866 120 7.064 100F 0 0 0 0 0 0 11 39 18.904 120 7.013 100F 0 0 0 0 0 0 12 39 18.905 120 7.025 100F 90% 0 0 0 0 0 13 39 18.896 120 7.064 100F 50% 0 0 0 0 0 14 39 14.401 120 6.762 100F 95% 0 0 0 0 0 15 39 19.021 120 6.970 10R 70F 20W 80% 0 0 0 0 0

Martis Creek Lake (continued) 1 39 19.1951 120 6.8890 95F 5R 40% 0 0 0 0 0 2 39 19.1079 120 6.9427 90F 10R 100% 0 0 0 0 0 3 39 18.9577 120 7.0294 100F 0 0 0 0 0 0 4 39 18.9005 120 7.0342 70F 20W 10R 20% 0 0 0 0 0 5 39 18.9263 120 6.9640 100F 0 0 0 0 0 0 6 39 18.9784 120 6.8788 100F 0 0 0 0 0 0 7 39 19.0345 120 6.8404 95F 5R 85% 0 0 0 0 0 15‐Jun‐12 8 39 19.0769 120 6.7497 100F 100% 0 0 0 0 0 9 39 19.2074 120 6.7212 85R 15F 25% 0 0 0 0 0 10 39.19.3143 120 6.7411 90R 10F 40% 0 0 0 0 0 11 39 19.4531 120 6.7335 100F 90% 0 0 0 0 0 12 39 19.5408 120 6.8881 80F 20R 65% 0 0 0 0 0 13 39 19.4797 120 6.8376 50F 50R 85% 0 0 0 0 0 14 39 19.4613 120 6.8122 70R 30F 95% 0 0 0 0 0 15 39 19.3767 120 6.7865 75R 25F 90% 0 0 0 0 0

Spooner Lake LOCATION SUB INVASIVES Date T N W % Type EWM Hydrilla Zebra Quagga NZMS Corbicula 1 39 6.232 119 54.449 100F 0 0 0 0 0 0 2 39 6.267 119 54.448 50W 50F 0 0 0 0 0 0 3 39 6.292 119 54.464 50R 50F 0 0 0 0 0 0 4 39 6.285 119 54.487 100F 0 0 0 0 0 0 5 39 6.280 119 54.624 100F 0 0 0 0 0 0 6 39 6.349 119 54.743 100F 0 0 0 0 0 0 7 39 6.431 119 54.687 10R 90F 5% 0 0 0 0 0 10-Jul-10 8 39 6.451 119 54.779 20R 80F 20% 0 0 0 0 0 9 39 6.460 119 54.783 40R 10W 50F 15% 0 0 0 0 0 10 39 6.468 119 54.776 90R 10F 5% 0 0 0 0 0 11 39 6.489 119 54.645 40R 60F 95% 0 0 0 0 0 12 39 6.655 119 54.505 100F 10% 0 0 0 0 0 13 39 6.486 119 54.333 100F 0 0 0 0 0 0 14 39 6.285 119 54.350 10W 90F 0 0 0 0 0 0 15 39 6.233 119 54.379 100F 0 0 0 0 0 0 1 n/a n/a 20R 80F 90% 0 0 0 0 0 2 n/a n/a 95F 5R 70% 0 0 0 0 0 3 n/a n/a 20W 80F 30% 0 0 0 0 0 4 n/a n/a 95F 5R 60% 0 0 0 0 0 5 n/a n/a 95F 5R 95% 0 0 0 0 0 6 n/a n/a 100F 10% 0 0 0 0 0 7 n/a n/a 100F 80% 0 0 0 0 0 20-Sep-10 8 39 6.455 119 54.783 20W 20R 60F 80% 0 0 0 0 0 9 39 6.439 119 54.672 50R 50F 10% 0 0 0 0 0 10 39.6.334 119 54.695 100F 15% 0 0 0 0 0 11 39 6.287 119 54.608 100F 5% 0 0 0 0 0 12 39 6.293 119 54.473 5W 5R 90F 0 0 0 0 0 0 13 39 6.270 119 54.442 60W 40F 0 0 0 0 0 0 14 39 6.232 119 54.386 100F 0 0 0 0 0 0 15 39 6.232 119 54. 386 10W 20R 70F 20% 0 0 0 0 0

Spooner Lake (continued) 1 39 6.4316 119 54.9606 90F 10R 10% 0 0 0 0 0 2 39 6.3746 119 54.7201 100F 20% 0 0 0 0 0 3 39 6.2994 119 54.6471 100F 10% 0 0 0 0 0 4 39 6.2806 119 54.5037 100F 5% 0 0 0 0 0 5 39 6.2330 119 54.4953 100F 0 0 0 0 0 0 6 39 6.2816 119 54.3514 90F 10R 5% 0 0 0 0 0 7 39 6.3860 119 54.2874 100R 0 0 0 0 0 0 12-Jun-12 8 39 6.4246 119 54.7857 80R 20W 80% 0 0 0 0 0 9 39 6.5341 119 54.3563 100F 5% 0 0 0 0 0 10 39 6.6630 119 54.5192 100F 60% 0 0 0 0 0 11 39 6.5949 119 54.5812 100F 40% 0 0 0 0 0 12 39 6.5577 119 54.6137 100F 50% 0 0 0 0 0 13 39 6.4967 119 54.6464 100F 60% 0 0 0 0 0 14 39 6.4618 119 54.6967 100F 70% 0 0 0 0 0 15 39 6.4699 119 54.7784 60R 40F 90% 0 0 0 0 0 1 39 6 26.06 -119 54 40.73 95F 5R 90% 0 0 0 0 0 2 40 6 24.65 -119 54 41.63 100F 90% 0 0 0 0 0 3 41 6 22.92 -119 54 42.89 100F 90% 0 0 0 0 0 4 42 6 26.22 -119 54 43.22 100F 90% 0 0 0 0 0 5 43 6 27.58 -119 54 46.83 100F 100% 0 0 0 0 0 4-Oct-12 6 44 6 27.62 -119 54 41.63 90F 10R 100% 0 0 0 0 0 7 45 6 29.28 -119 54 38.73 100F 100% 0 0 0 0 0 8 46 6 32.53 -119 54 37.68 100F 100% 0 0 0 0 0 9 47 6 35.93 -119 54 34.82 100F 90% 0 0 0 0 0 10 48 6 37.37 -119 54 27.54 100F 90% 0 0 0 0 0