Case studies for monitoring to meet TMDL permit requirements
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Lake Monitoring Case Study: Wirth Lake
The Wirth Lake Excess Nutrients TMDL Report (MPCA, 2010) was approved in 2010 after Wirth Lake was originally listed for excess nutrient (phosphorus) impairment. Wirth Lake is a 38-acre lake with a maximum depth of 26 feet. All known phosphorus sources to Wirth Lake were considered in the development of the TMDL and the Wirth Lake Final TMDL Implementation Plan. These sources include:
- Stormwater runoff from MS4s
- Permitted point sources other than MS4s
- Backflow from Bassett Creek during flood periods
- Atmospheric deposition
- nternal phosphorus loading
Stormwater from approximately 77 percent of the Wirth Lake watershed currently drains through some form of wet detention before it enters Wirth Lake. A significant untreated source of phosphorus to Wirth Lake occurs when flood flows in Bassett Creek backflow to Wirth Lake. Other sources include runoff from highway right-of-ways and sediment release of phosphorus (i.e., internal phosphorus loading).
| Comparison of historical and 10-year (1999-2008) water quality data to applicable water quality standards (MPCA, 2010) | |||
| Water quality parameter | MPCA deep lake eutrophication standards (NCHF Ecoregion) | Wirth Lake historical (1992-2008) growing season average | Wirth Lake 10-year (1999-2008) growing season average |
|---|---|---|---|
| Total phosphorus (ug/L) | < 40 | 55 | 41 |
| Chlorophyll a (ug/L) | <14 | 22 | 18 |
| Secchi disk (m) | < 1.4 | 1.8 | 2.0 |
A watershed P8 model, calculated Bassett Creek backflow phosphorus loads, and observed lake water quality data were used to calibrate the Wirth Lake BATHTUB model to average observed total phosphorus concentration during the 2005-2006 water year. The BATHTUB model calibrated to observed total phosphorus concentration (TP) was used to determine the best models for predicting the observed chlorophyll-a concentration and Secchi disc transparency (SD). The calibrated BATHTUB model was then validated for the 2006-2007 water year (i.e., results generated using the calibrated BATHTUB model were compared to in-lake water quality observations). Table 4 compares in-lake water quality observations to BATHTUB model results for the calibration and validation time periods. The calibrated BATHTUB model was then used to predict how the lake water quality would change if the Wirth Lake outlet were configured to completely prevent backflow from Bassett Creek. Table 4 shows that this improvement option would decrease in-lake TP concentration for the 2005-2006 water year from 46 to 38 μg/L and that both TP and SD would meet the eutrophication criteria for Wirth Lake.
In 2012, a new lake outlet structure was installed to prevent backflow events from Basset Creek from deteriorating Wirth Lake’s water quality. In 2013, the 10-year average of the most recent water quality data (2003-2012) indicated that Wirth Lake met the MPCA deep lake standards for TP and SD. The 10-year average chl-a concentration for Wirth Lake was 14.7 µg/L, which was within 1 µg/L of the 14 µg/L chl-a criteria. If water quality monitoring data from 2013 is considered, the 10-year (2004-2013) average chl-a concentration for Wirth Lake becomes 12.9 µg/L, while the 10-year average TP (32.5 µg/L) and SD (2.56 m) are both significantly better than the respective listing criteria. Additionally, historic water quality data trend analysis indicated that, over the entire water quality monitoring data period (1992-2013), there have been significant improvements for all three water quality criteria at the 95 percent confidence level. The same is true for the trend analysis of the more recent data (2003-2012). Based on this evidence, Wirth Lake was delisted for lake eutrophication/excess phosphorus in 2014 and the tributary MS4s are no longer required to develop a compliance schedule or address this impairment in annual reporting. Wirth Lake average TP concentrations, chl-a concentrations, and SD depths for the period of 1992-2013 are shown in Figure 1.
Stream Monitoring Case Study: Nine Mile Creek
Nine Mile Creek was placed on MPCA’s 303(d) list of Impaired Waters in 2002 after it was determined that 32.5% of the lab turbidity data from the Metropolitan Council Environmental Services (MCES) Watershed Outlet Monitoring Program (WOMP) monitoring location exceeded the 25 NTU turbidity standard, which has since been replaced by ecoregion-based TSS standards. As discussed in Section 4.1.2.1, TSS standards for each use classification may be exceeded no more than ten percent of the time, which is the same frequency that had been specified for the turbidity standard.
Following the 2005 monitoring season, an evaluation of the turbidity data (see Figure 2) indicated that Nine Mile Creek turbidity levels had dropped significantly since the Lower Valley Restoration Project implementation during the winter of 1992/1993.
In 2007, the Nine Mile Creek Watershed District (NMCWD) submitted multi-site turbidity monitoring data and watershed analysis to MPCA for consideration in delisting Nine Mile Creek for turbidity. Continuous probe data from three upstream sites showed that the turbidity standard was exceeded less than 10 percent of the time. However, lab turbidity data from the MCES WOMP monitoring location indicated that the turbidity standard was still exceeded in 26 percent of samples.
Because the MCES WOMP monitoring station is biased to higher flows, Barr Engineering Co. (Barr) completed an analysis of collected monitoring data and developed a relationship between flow and lab turbidity. This relationship was applied to all MCES flow records collected between 1993 and 2005, and demonstrated that the standard would have been exceeded less than 9 percent of the time at the MCES WOMP monitoring station. Based on this analysis, the MPCA developed a future plan to reevaluate impairment status based on continuous turbidity probe data NMCWD collected at the WOMP monitoring station.
A regression relationship was used to translate continuous turbidity measurements collected in 2008 using the DTS-12 (continuous) probe into NTU units for direct comparison to the 25 NTU turbidity standard. The resulting turbidity estimates were plotted along with observed stream flow rates (), and showed that the turbidity standard would have been exceeded less than 3 percent of the time during 2008.
Because 2008 was a dry year, Barr compared the flow duration characteristics from 2008 to the longer-term dataset (1993-2005) from the Nine Mile Creek WOMP site. This analysis confirmed that considerably lower flows occurred during 2008 compared to the period of 1993-2005. By applying the identified turbidity-flow rate relationship to the long-term (1995-2003) flow dataset, Barr’s analysis confirmed that the 25 NTU standard would be met more than 90% of the time and approach 95% compliance. In 2010, Nine Mile Creek was delisted for turbidity/TSS impairment.
5.3 Case Study: Outfall Monitoring
| Full water quality station 2015 summary (CRWD, 2015) | ||
| Full water quality station | Subwatershed Area (ac) | TSS Annual Yield (lbs/ac/year) |
|---|---|---|
| East Kittsondale | 1,116 | 342 |
| Hidden Falls | 167 | 419 |
| Phalen Creek | 1,433 | 355 |
| St. Anthony Park | 3,418 | 125 |
| Trout Brook-East Branch | 932 | 139 |
| Trout Brook-West Branch | 2,379 | 1,059 |
| Trout Brook Outlet | 5,028 | 536 |
| Villa Park Outlet | 753 | 16 |
| Como 3 | 517 | 76 |
| Como 7 | 793 | 28 |
The South Metro Mississippi River TSS TMDL report (MPCA, 2015) was approved in 2016 to address aquatic life impairment related to excess turbidity (TSS). The report established TSS TMDLs for five stream reaches in the South Metro – Mississippi River (South Metro) watershed, extending from River Mile 844 (the confluence with the Minnesota River), to River Mile 780 (downstream of the confluence with the Rush River, Wisconsin) as shown in Figure 4. All known sources of TSS loading were considered in the development of the TMDL and general implementation strategy. These sources include:
- Stormwater runoff from MS4s
- Permitted point sources other than MS4s (e.g., wastewater treatment facilities)
- Agricultural sources
- Internal loading (i.e., resuspension of sediments)
- Streambank erosion
- Natural background loading
A large number of MS4s exist within the area tributary to the impaired reaches shown in Figure 4. For this reason, rather than develop individual WLAs for each MS4, the TMDL establishes a categorical WLA of 154 lbs/acre/year for all MS4s within the impaired watershed.
One method of evaluating compliance with the categorical TSS areal loading rate WLA established in the TMDL (i.e., 154 lbs/acre/year) is to monitor major outfalls (Section 5.0) that discharge to the Mississippi River within the South Metro watershed. An example of how outlet monitoring can be used to evaluate compliance with an areal loading rate WLA is provided in the CRWD 2015 Stormwater Monitoring Report (CRWD, 2015).
The CRWD 2015 Stormwater Monitoring Report (CRWD, 2015) a detailed description of monitoring operations (e.g., period of operation, operation of automated ISCO samplers, area-velocity sensors used to monitor flow, etc.), sampling and laboratory analysis (e.g., delivery of sample for laboratory analysis, QAQC procedures, etc.) and total discharge and pollutant load calculations (e.g., baseflow partitioning analysis, calculation of event load and baseload, flow-weighted average concentration calculations, and pollutant yield (lbs/acre), etc.)
Additionally, the document provides a detailed summary of outfall monitoring efforts conducted throughout 2015. Full water quality stations (i.e., automated sampling stations collecting flow and water quality data) were installed at ten (10) locations listed below and shown in Figure 5.
- East Kittsondale
- Hidden Falls
- Phalen Creek
- St. Anthony Park
- Trout Brook-East Branch
- Trout Brook-West Branch
- Trout Brook Outlet
- Villa Park Outlet
- Como 3
- Como 7
Using 2015 monitoring data collected at the ten (10) full water quality monitoring stations and flow and loading calculation procedures outlined in the report (CRWD, 2015), CRWD developed summary pollutant loading tables for the watershed district, including the TSS areal loading (lbs/acre/year) calculated at each station (see Table 5.1, of the CRWD 2015 Stormwater Monitoring Report; CRWD, 2015). Table 6 summarizes data collected at the ten (10) full water quality monitoring stations presented in the monitoring report. As shown in Table 6, 5 of the 10 full water quality monitoring stations are meeting the categorical TSS areal loading rate WLA established in the South Metro Mississippi River TSS TMDL report (MPCA, 2015) (i.e., 154 lbs/acre/year). Figure 6 provides a spatial summary of monitored TSS areal loading rate throughout the CRWD. Results presented in Table 6 and Figure 6 are a valuable watershed management tool, and can be used to identify and prioritize individual watersheds and drainage areas for BMP implementation.