final peace river basin, florida, dissolved oxygen, nutrient, … · 2017-01-06 · final peace...
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Final Peace River Basin, Florida
Dissolved Oxygen, Nutrient, Turbidity and TSS
Total Maximum Daily Loads
(WBIDs 1501A, 1497,1623K, 1613,1626,1580,1539,1617, 1921,1871)
Prepared by: US Environmental Protection Agency
Region 4 Atlanta, GA
February, 2006
TABLE OF CONTENTS
INTRODUCTION ................................................................................................................................................... 13
PROBLEM DEFINITION FOR THE PEACE RIVER BASIN TMDLS ............................................................ 13
WATERSHED DESCRIPTION ............................................................................................................................ 14
WATER QUALITY STANDARD AND TARGET IDENTIFICATION ............................................................ 16
NUTRIENTS ............................................................................................................................................................ DISSOLVED OXYGEN (DO) .....................................................................................................................................
16 16
BlOCHEMICAL OXYGEN DEMAND (BOD) .......................................................................................................... ! ..... 17 TuRI~IDITY ......................................................................................................................................................... ' ..... 17
EXAMINE WATER QUALITY AND ENVIRONMENTAL DATA .................................................................. 17
SOURCE ASSESSMENT ....................................................................................................................................... 17 I NON-POINT SOURCES .............................................................................................................................................. 18 POINT SOURCES ...................................................................................................................................................... 20
ANALYTICAL APPROACW MODEL SELECTION AND DEVELOPMENT ............................................... 21
STATISTICAL APPROACH ........................................................................................................................................ 21 MECHANISTIC MODEL APPROACH .................................................................................................................... 1 ..... 21
I
LAKE LENA RUN WBID 1501A (SADDLE CREEK SUBBASIN), LOW DO, NUTRIENTS, BOD ....... 1 ..... 26
LENA RUN DESCRIPTION, WATER QUALITY AND ENVIRONMENTAL DATA, AND SOURCE ASSESSMENT ................ 26 LENA RUN ANALYTICAL APPROACH/ MODEL SELECTION AND DEVELOPMENT ..................................................... 35 LENA RUN ALLOCATIONS ....................................................................................................................................... 42 MARGIN OF SAFETY ............................................................................................................................................... 43 CRITICAL CONDITIONS ........................................................................................................................................... 44 SEASONAL VARIATION ........................................................................................................................................... 44
SADDLE CREEK WBID 1497 (SADDLE CREEK SUBBASIN) LOW DO, NUTRIENTS, AND BOD ......... 44
SADDLE CREEK (1497) DESCRIPTION, WATER QUALI f Y AND ENVIRONMENTAL DATA. AND SOURCE ASSESSMENT ............................................................................................................................................................................... 44 SADDLE CREEK (1 497) ANALYTICAL APPROACH/ MODEL SELECTION AND DEVELOPMENT .................................. 49 SADDLE CREEK (1497) ALLOCATIONS ............................................................................................................. i ...... 54 MARGIN OF SAFETY ............................................................................................................................................... 55 CRITICAL CONDITIONS ........................................................................................................................................... 56 SEASONAL VARIATION ........................................................................................................................................... 56
SADDLE CREEK BELOW LAKE HANCOCK (SADDLE CREEK SUBBASIN) WBID 162313 TURBIDITY, TSS .................................................................................................................................................... 56
SADDLE CREEK (1 623K) DESCRIPTION, WATER QUALITY AND ENVIRONMENTAL DATA, AND SOURCE ASSE$SMENT ............................................................................................................................................................................... 56
............................... SADDLE CREEK (1 623K) ANALYTICAL APPROACH/ MODEL SELECTION AND DEVELOPMENT 59 SADDLE CREEK ( I 623K)ALLOCATIONS ............................................................................. ..................................... 68 MARGIN OF SAFETY ........... .................................................................................................................................... 69 CRITICAL CONDITIONS ................................................................................................................................... ...... 69 SEASONAL VARIATION ........................................................................................................................................... 69 RECOMMENDATIONS .............................................................................................................................................. 69
PEACE CREEK TRIB CANAL (PEACE CREEK SUBBASIN) WBID 1613 LOW DO, NUTRIENTS . r ....... 70 PEACE CREEK TRIB CANAL DESCRIPTION, WATER QUALITY AND ENVIRONMENTAL DATA, AND SOURCE ~ ASSESSMENT .......................................................................................................................................................... 70
....... ....... PEACE CREEK TRIBUTARY CANAL ANALYTICAL APPROACH/ MODEL SELECTION AND DEVELOPMENT .i 74 PEACE CREEK TRIB CANAL ALLOCATIONS ............................................................................................................. 77 MARGIN OF SAFETY ............................................................................................................................................... 77 CRITICAL CONDITIONS .......................................................................................................................................... 77 SEASONAL VARIATION .......................................................................................................................................... 78
LIST OF FIGURES
Figure 1 : Peace River Basin (http://www.swfwmd. state . fl.us/waterman/peaceriver/map. html) . This document addresses TMDLs for 6 Peace Creek subbasin WBIDs, 4 Saddle Creek subbasin WBIDs. 1 Peace River WBID stretching from Bartow to Ft . Meade. and 2 tributaries to the Peace River between Zolfo Springs and Arcadia ......................................................................... 15 Figure 2: Lake Lena at outlet ........................................................................................................ 27 Figure 3: Lena Run near inflow to Lake Hancock ........................................................................ 28 Figure 4: Saddle Creek/ Lake Hancock Watershed Aerial Photograph ........................................ 29 Figure 5 : WB ID 1 5 0 1 A. 5 out of 24 DO observations are below 5 mgll ................................. !. .. 30 Figure 6: WBID 1501A. BOD .................................................................................................... Figure 7: WBID 1501A. corrected chlorophyll-a has 2 out of 1 1 above 20 ug/l ........................ Figure 8: WBID 1501A. chlorophyll-a has 2 out of 4 values above 20 ugll ............................... Figure 9: Lena Run average TN is 2.24 mg/l ............................................................................... Figure 10: Lena Run average TP is 0.72 mg/l .............................................................................. Figure 11 : Landuse in the Peace River Basin WBIDs .................................................................
30 31 31 32 32 33
Figure 12: Event Mean Concentrations from Evaluation of Alternative Stormwater Regulations for Southwest Florida (Harper and Baker. 2003) ...................................................................... . . 34 Figure 13: Annual Precipitation Summary for Station WBAN 12876. Winterhaven Florida ..I.... 34 Figure 14: Monthly Precipitation Summary for Station WBAN 12876. Winterhaven ~loridal .... 35 Figure 15: Lena Run (WBID 1501A) and Saddle Creek (WBID 1497) WAM and WASP m del map .............................................................................................................................................. 36 P Figure 16: Lena Run Observed DO. Simulated Existing Condition. Predicted TMDL Condi ion with 80% reduction ..................................................................................................................... 1 39 Figure 17: Lena Run Observed and Predicted Chlorophyll-a ....................................................... 39 Figure 18: Lena Run Observed and Predicted Ammonia ............................................................. 40 Figure 19: Lena Run Predicted Flow ............................................................................................ 40
I Figure 20: Lena Run Observed and Predicted BOD ............................................................... 41 Figure 21: Lena Run Observed and Predicted Nitrate .................................................................. 41 Figure 22: Lena Run Observed and Predicted Total Phosphorus ............................................ 1 .... 42 Figure 23: In WBID 1497. 31 of 40 DO observations were below the 5.0 standard ............... I ..... 46 Figure 24: BOD is mostly at or below detection limits in WBID 1497 .................................. 1 .... 47 Figure 25: Chlorophyll-a in WBID 1497; all values were below 20 ug/l ..................................... 48 Figure 26: Corrected Chlorophyll-a in WBID 1497; 5 out of 27 are above 20 ugll ...............I..... 48 Figure 27: Predicted versus Observed Dissolved Oxygen in Saddle Creek WBID 1497 ...... ! ..... 49 Figure 28: Predicted vs Observed Chlorophyll-a in Saddle Creek W I D 1497 .......................... 50 Figure 29: Predicted vs Observed Ammonia in Saddle Creek WBID 1497 ................................. 50 Figure 30: Predicted vs Observed Flow (cms) in Saddle Creek WBID 1497 .............................. 51 Figure 3 1 : Predicted CBODu versus Observed BOD using a 1.5 CBODu:BOD5 ratio ............. 52 Figure 32: Predicted vs Observed Nitrate and Nitrite in Saddle Creek W I D 1497 .................. 53 Figure 33: Predicted vs Observed Total Nitrogen in Saddle Creek WBID 1497 ........................ 53
Figure 35: Dissolved Oxygen; Existing conditions and TMDL conditions with 95% load .....................
1 Figure 34: Predicted vs Observed Total Phosphorus in Saddle Creek WBID 1497 54
reductions ...................................................................................................................................... 54 Figure 36: Watershed-level nitrogen yields for Peace River sub-basins (data from SWFW$lD).59 Figure 37 . Seasonal TSI values in Lake Arbuckle ............................................................................. 60 Figure 38 . Location of Saddle and Arbuckle Creeks. Polk County. Florida .................................. 62 Figure 39 . Turbidity and TSS measurements in Saddle Creek (WBID 16233) ................................... 63 Figure 40 . Turbidity and flow measured in Saddle Creek below Lake Hancock .................................. I-- 65 Figure 41 . Correlation between Turbidity and Chlorophyll-A in WBID 16233 ............................ 1 ..... 66 Figure 42: Peace Creek Trib Canal 2 ............................................................................................ 71
Figure 43: Peace Creek Trib Canal 3 ......................................................................................... ! . 71 Figure 44: Peace Creek Trib Canal 1 ............................................................................................ 72 Figure 45: 27 of 33 DO observations were below the 5.0 mgll standard ................................... 1 . 72 Figure 46: 6 out of 8 observations exceeded the IWR comparison value for chlorophyll-a . .....,. 73 Figure 47: Only 1 value of 14 observations of Chlorophyll-a corrected was above the IWR ~ comparison value of 20 ug/l ......................................................................................................... 73 Figure 48: The Peace Creek Tributary Canal, WBID 16 13 receives flow from Lake Effie outlet and can flow two directions, through WBID 1626 or directly to the Peace Creek Canal WBID 1539 .............................................................................................................................................. 76 Figure 49: West Wales by Peace Creek Trib Canal Figure 50: West Wales Drainage Canal looking downstream 7 8 Figure 51 : West Wales Drainage Canal at West Wales Rd . looking upstream ........................... 79 Figure 52: The DO standard of 5.0 mgll was violated 26 out of 34 observations in the West Wales Drainage Canal ............................................................................................................... 79 Figure 53: DO observations at each of the stations in WBID 1626 are almost always below t e water quality standard of 5.0 mgll .............................................................................................. 80 Figure 54: WBID 1626 predicted DO vs observed DO based on TP and temp . at station 1 21FLTPA 25020265 ............................................................................................................... 82 Figure 55: Location of the Wahneta Farms Drain Canal Water segment, WBID 1580, and M 'or Geopolitical Features in the Sarasota Bay, Peace River, and Myakka River Basin Group .......... 85 Y Figure 56: Observed vs Predicted DO based on nutrient concentrations and water temperaturk in the Wahneta Farm Drainage Canal WBID 1580 at station 21FLPOLKPCCANAL6 . ...............I.. 87 Figure 57: Observed vs Predicted DO on nutrient concentrations and water temperature in th F Wahneta Farm Drainage Canal WBID 1580 at station 21FLPOLKPCCANAL7 . ....................... 88 Figure 58: Wahneta Farms Drain Canal water quality stations and USGS flow gages ................ 89 Figure 59: 16 out of 66 observations were below the 5.0 mgll standard for DO .......................... 90 Figure 60: Historical DO data in WBID 1580 shows 32 of 35 (91%) below the standard of 5 . mgll ............................................................................................................................................ Figure 61 : Average TN in this WBID is 1.38 mgll ...................................................................... 91 Figure 62: Average TP in this WBID is 0.12 mgll ...................................................................... 1 91 Figure 63: Location of the Peace Creek Drainage Canal Water Segment, WBID 1539, and M!ajor
...... .. Geopolitical Features in the Sarasota Bay, Peace ~ ive ; , and Myakka River Basin Group ./ 94 Figure 64: Peace Creek Drainage Canal Water Segment, and Monitoring Locations .................. 96 Figure 65: In the Peace Creek Drainage Canal 123 of 241 (53%) of the DO observations fro+
.. 1954 to 1983 were below 5.0 mgll ........................................................................................... 98 Figure 66: Fifty Year Trend of Average DO in WBID 1539 ....................................................... 99 Figure 67: Flow in the Peace Creek Drainage Canal shows a 90th percentile of 301. a medi of 35, and a 10th percentile of 5.6 cfs ............................................................................................. 99 Figure 68: In the Peace Creek Drain Canal 91 of 206 (44%) DO observations were below th "! standard of 5.0 mg/l ................................................................................................................. ! 101 Figure 69: The DO percent saturation ranges from zero to 140, indicating nutrients via ~ photosynthesis and respiration are influencing DO . ................................................................. 102 Figure 70: BOD data in the Peace Creek Drain Canal ............................................................... 102
............ Figure 71:14 of 151 (9%) observations of corrected chlorophyll-a were above 20 ugll ................................................... Figure 72: 22 141 of (1 6%) observations were above 20 ugll
........... Figure 73: Observed vs Predicted DO in the Peace Creek Drainage Canal WBID 1539 Figure 74: Ammonia under TMDL predicted conditions in the Peace Creek Drainage Canal .
103 103 104
Segment 1 is upstream. segment 2 receives the point source discharge, and segment 9 is downstream .............................................................................................................................. .,. 104 Figure 75: CBOD under TMDL predicted conditions in the Peace Creek Drainage Canal . Segment 1 is upstream, segment 2 receives the point source discharge, and segment 9 is downstream ................................................................................................................................. 105
Figure 76: Dissolved Oxygen under TMDL predicted conditions in the Peace Creek Drainage Canal . Segment 1 is upstream. segment 2 receives the point source discharge. and segment 9 is downstream ................................................................................................................................. 105 Figure 77: Limestone Creek water quality monitoring stations ................................................ 1 10 I * Figure 78: Limestone Creek looking west .................................................................................. 111 Figure 79: Limestone Creek looking south .................................................................................. 112 Figure 80: Limestone Creek at Roberts Rd . looking downstream ............................................ ! 113 Figure 8 1 : There are 12 violations out of 3 1 DO observations for Limestone Creek. WBID 192 1 . ..................................................................................................................................................... 114 Figure 82: Of the 14 corrected chlorophyll-a observations 9 were below detection limits. 4 were very low. and only one measurement was high at 38 . On the same day. 11/4/2003 at 10:05 My the 3 8 value was detected at station 2 1 FLTPA 272 1 57 1 8 1 5 5423. a value of 2.1 was recorde at station 21FLTPA 2502021 4 ....................................................................................................... 114 Figure 83: There were 15 observations of BOD in Limestone Creek. WBID 1921 . Of these 5. i 13 were recorded as 2 or less. one was 2.8 and one 5.6. The 5.6 value was recorded at the s e station. date and time as the high chlorophyll-a value of 38 ug/l . Also. at that station. same $1 t me and day. the DO was recorded as a low 2.86 mgll ...................................................................... 115 Figure 84: Predicted DO based on TKN and Temperature versus observed DO ........................ 11 6 Figure 85: Alligator Branch at US 17 looking upstream . ........................................................... 11 9 Figure 86: Alligator Branch at US 17 looking downstream . ................................................. 120 Figure 87: Location of WBID 1871. Alligator Branch ............................................................ 1 .. 121 Figure 88: One out of 18 observations exceeded the IWR comparison value of 20 ug/l in th e Alligator Branch WBID .............................................................................................................. 122 Figure 89: 28 out of 50 observations were violations of the 5.0 mgll standard ......................... 122 I Figure 90: The Alligator Branch WBID median for TKN is 1.5 and the average is 1.6 mg/l.i .. 123 Figure 91 : The TP median is 0.68 and average is 0.70. ........................................................... 1 .. 123 Figure 92: Alligator Branch predicted DO vs observed DO based on regression of DO with TOC. nutrients and temperature ........................................................................................................... 125
LIST OF TABLES
! Table 1 : TMDLs developed in this report ...................................................................................... 13 Table 2: Septic Tanks installed since 1970 ............................................................................. ..... 19 Table 3: NPDES facilities in the Peace River Basin WBIDs covered in this report .................... 24 Table 4: Average Nutrients (mgll) in WBID .......................................................................... , . 24 Table 5: Average Nutrients (mgll) for the Sarasota Bay-Peace-Myakka Basins Group ........ 1 ..... 24 Table 6: Biological Assessments Conducted by FDEP (IWR 20) ................................................ 25
..... Table 7: Annual Average Facility Discharge Loads in Lena Run .......................................... , 37 Table 8: Combined Annual Average Daily Continuous Point Source Loads in Lena ~ u n .......... 38
.... Table 9: Combined Point Source Loads as Percent of Non-Point Source Loads in Lena Rut 38 Table 10: Permit limits for Auburndale STP and Florida Distillers Co . ................................?..... 38 Table 1 1 : Estimated Annual Average Daily Non-point Source Loads from the Lena Run 1
...................................................................................................................................... watershed 38 Table 12: Lena Run TMDL allocations ................................................................................. ? ...... 43 Table 13: WBID 1497 Nutrient Concentration Comparison ....................................................... 46 Table 14: Saddle Creek (1497) Estimated Non-point Source Loads ............................................ 49 Table 15: Flow Calibration Statistics for Saddle Creek at Hwy 542 near Lakeland, FL (USGS 022942 17) ..................................................................................................................................... 51 Table 16: Saddle Creek (1497) TMDL allocations ....................................................................... 55
....... Table 17 . Water Quality Data for the Arbuckle Creek at Boat Ramp Station ................................ ; 61
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SUMMARY SHEET Total Maximum Daily Load (TMDL)
1. 303(d) Listed Waterbody Information State: Florida Basin: Peace River Basin
I I I I 1 1501A I Lake Lena Run I Polk I low DO and nutfients /
Impaired Waterbodies for TMDLs (1 998 303(d) List): I
1 I Lake Hancock 1 I 1 1
Segment Name County
11871 ( Alligator Branch I Hardee ( low DO and nu$ients 1
nut:rients
rients
nu..rients
nu.:rients
Peace Creek Trib Polk 1 low DO and
1617 1921
2. TMDL Endpoint (Target): The State of Florida has narrative criteria for nutrients stating that in no case shall nltrient concentrations of a body of water be altered so as to cause an imbalance in natural populatibns of aquatic flora or fauna. The target for these low DO, nutrient and BOD TMDLs is the dis olved oxygen standard of 5.0 mg/l for flowing waters, or a TSI target of 60 for lakes. The target or the turbidity and TSS TMDL is the turbidity standard that states for Class I11 waters, turbidit must be less than or equal to 29 NTU above natural background conditions. i
3. TMDL Approach These TMDLs for nutrients, BOD, and low DO are all addressed by analyzing Statistical regression models and mechanistic models are used to analyze these water bodie develop these TMDLs. A percent reduction in nutrient concentrations was calculated existing conditions and allocated loads. The TSS/turbidity TMDL was developed using a reference stream approach.
low DO and nu-
low DO and
low DO and and BOD
Lake Effie Outlet Limestone Creek
4. TMDL Allocation:
Polk
Polk
Polk
Canal
I WLA I ~
1580
1539
Polk Hardee & DeSoto
West Wales Drainage Canal Wahneta Farms Drain Canal Peace Creek Drainage Canal
nutrients
Stream Name / WBlD
1501A
-
low DO and nutkients
Parameter
TN
Continuous
4.6 kg/d
LA
80% reduction
MS4 (reduction)
80%
TMDL
80% reduction
1
Stream Name ,WBID
1501A
1497
TP
Parameter
BOD
TN
95% reduction
95% reduction
turbidity
I 1626
1626
N/ A
N/ A
N/ A
1613
1613
1580
Continuous
8.8 kg/d
95% reduction
95% reduction
95% reduction
TN
TP
'IN
TP
1539
D W U I reduction I reduction I reduction 1 reduction I
LA
80% reduction
pp
95% reduction
MS4 (reduction)
80%
95% reduction
3 7% reduction -----
75% reduction
75% reduction
TN
1539
TMDL
80% reduction 95%
reduction 95%
reduction 95%
reduction
N/A
1580 1 TP 1 NIA
95% reduction
95% reduction
37% reduction
75% reduction
75% reduction
N/A -----
T N
I r
reduction reduction reduction 1
1 1871 45% 1 45% 1 45% 1
reduction reduction reduction
37% reduction
75% reduction
reduction 75%
reduction
75% reduction
75% reduction
60% reduction
1539 ,
17L I
1871
5. Endangered Species (yes or blank): Yes
6. EPA Lead on TMDL (EPA or blank): EPA
7. TMDL Considers Point Source, Nonpoint Source, or both: Both
75% 75% reduction reduction
75% N'A reduction
75% reduction reduction
75% reduction
nn-
reduction 1 reduction
I
75% reduction
AT/ A 1 0 1 1 11'1
BOD
75% reduction
75% reduction
75% reduction
60% 75% reduction
n 1
75% reduction
I
75% I reduction
reduction
42% l \ / f i
N/A
75% 75%
42% reduction
24% reduction
42% reduction
24% reduction
reduction 24%
reduction
8. Major NPDES Discharges: / s l WBID WBID Name NPDES SIC2D
1497
1 539
1501A
I DRAIN
SADDLE CREEK ABOVE LAKE HANCOCK WAHNETA FARMS
150 1A
CANAL LAKE LENA ) FL000305 1
FLO 13 1385
FL0036048
RUN
LAKE LENA RUN
FL DISTILLERS
POLK NURSERY COMPANY, INC.
WINTER HAVEN #3 WAHNETA
FL0021466
LAKE LENA
WATER No discharge from this facility
MAJOR, 2.6 C0,AUBURNDALE
AUBURNDALE STP
MINOR
RUN 1 MGD
FLOWERS
ANP FLqRISTS' SU~~PLIES
LAKE LENA RUN
5.0 MGD I
MAJOR, 1.4 MGD
SE@RAGE SY $TEMS
INTRODUCTION I
Section 303(d) of the Clean Water Act requires each state to list those waters within its boundaries for which technology based effluent limitations are not stringent enough to , protect any water quality standard applicable to such waters. Listed waters are prioritized with respect to designated use classifications and the severity of pollution. In accordance( with this prioritization, states are required to develop Total Maximum Daily Loads I (TMDLs) for those water bodies that are not meeting water quality standards. The 1 TMDL process establishes the allowable loadings of pollutants or other quantifiable I parameters for a waterbody based on the relationship between pollution sources and in- stream water quality conditions, so that states can establish water quality based controls to reduce pollution from both point and non-point sources and restore and maintain the quality of their water resources (USEPA, 199 1).
The Florida Department of Environmental Protection (FDEP) has developed 303(d) lists since 1992. The list of impaired waters in each basin, referred to as the Verified List, is also required by the FWRA (Subsection 403.067[4)], Florida Statutes [F.S.]). However, the FWRA (Section 403.067, F.S.) stated that all previous Florida 303(d) lists were for planning purposes only and directed the Department to develop, and adopt by rule, a new science-based methodology to identify impaired waters. After a long rule-making process, the Florida Environmental Regulation Commission adopted the new methodology as Chapter 62-303, Florida Administrative Code (F.A.C.) (Identification of Impaired Surface Waters Rule, or IWR), in April 2001. The TMDLs developed in this report are for impaired waters on the 1998 303(d) list but not on FDEP7s verified list.
This TMDL is being established pursuant to EPA commitments in the 1999 Consent Decree in the Florida TMDL lawsuit (Florida Wildlife Federation, et al. v. Carol Browner, et al., Civil Action No. 4: 98CV356-WS, 1998) that TMDLs be developed for: all of the impairments on the approved 1998 303(d) list. ,
PROBLEM DEFINITION FOR THE PEACE RIVER BASIN TMDLS This document addresses TMDLs for 5 Peace Creek subbasin WBIDs, 3 Saddle Creek subbasin WBIDs, and 2 tributaries to the Peace River between Zolfo Springs and Arcadia. Figure I shows a general view of the Peace River Basin. Table I lists the TMDLs developed in this report.
Table 1: TMDLs developed in this report I
1 Lake Lena Run WBID 1501A (Saddle Creek Subbasin), low DO. nutrients. , - 1 Saddle Creek WBID 1497 (saddle Creek subbasin) low DO, nutrients I
saddle Creek WBID 16%K (Saddle Creek subbasin) turbidity and TSS Peace Creek Trib Canal (Peace Creek subbasin) WBID 16 13 low DO, nutrients I
West Wales ~ r a i n a ~ e Canal (Peace Creek subbasin) WBID 1626 low DO, nutrients 0
I I Peace Creek Drainage Canal (Peace Creek subbasin) WBID 1539 low DO, nutrients, I 1 1 BOD I I
Lake Effie Outlet (Peace Creek subbasin) WBID 16 17 nutrients I - Limestone Creek WBID 192 1. low DO, nutrients I 1 Alligator Branch WBID 1871 low DO, nutrients
I
WATERSHED DESCRIPTION The Peace River Cumulative Impact Assessment is underway and updated information is maintained at the following web site: htt~://www.swfwind.state.fl . u s / w a t e i m a n / . The following four paragraphs ar background information from this web site. The Peace River drainage basin is approximately 2,350 square miles in area. The river flows about 105 miles from the confluence of the Peace Creek Drainage Canal and Saddle Creek to Charlotte Harbor (see Figure 1). Flows from the Peace River are vital t the estuarine health and overall productivity of Charlotte Harbor. Land within the basin
water, but surface water use for public supply is increasing in the southern part of the basin (http://www.swfwmd.state.fl.us/watermadpeaceriver/).
I has been considerably altered from the natural state by phosphate mining, agriculture, and other development. Additionally, considerable amounts of water are withdrawn each dai to support these land uses. Ground water has historically provided the majority of this I
I
A steady, long-term decline in Peace River flows has been observed since the early- , 1960s. The causes of the decline are complex. Average annual rainfall over the last 30 years is about five incheslyear lower than in the previous 30 years. Ground-water withdrawals for public supply, agriculture, and mining have lowered the potentiometric surface of the Floridan aquifer since the early-1 930s which has reversed the hydraulic gradient between the river and underlying confined aquifers. This has caused gravity I drainage of the river into sinkholes in the upper part of the basin 1 I
(http:Nwww.swfwmd.state.fl.uslwaterman~peaceriverl). I The cumulative effects of land use changes due to urbanization, agriculture, and mining, can change stormwater runoff and baseflow contributions to the river. Drainage of wetlands through ditching and canal construction can affect surface water storage and
I runoff patterns. Historic phosphate mining and reclamation of mined lands can alter the I
Figure 1: Peace River Basin (http://www.swfwmd.state.fl.us/waterman/peaceriver/ma~.html). This document addresses TMDLs for 6 Peace Creek subbasin WBIDs, 4 Saddle Creek subbasin WBIDs, Peace River WBID stretching from Bartow to Ft. Meade, and 2 tributaries to the Peace River between Zolfo Springs and Arcadia.
I
timing and magnitude of runoff, surface water storage, recharge, and evapotranspiratio4. All of these factors contribute to changes in hydrology and ecology within the Peace ( River basin (http://www.swfwmd,state.fl.us/watermadpeaceriver/). I
To address the potential effect of these activities in the basin, the Florida Legislature 1 directed the Florida Department of Environmental Protection (DEP) in its 2003 legislative session to assess the cumulative impacts to the Peace River basin. This study called the Peace River Cumulative Impact Assessment, will form the basis for
(not a part of the Peace River Cumulative Impact Assessment) will identify regulatory
I preparation of a resource management plan. The subsequent resource management plan(
and non-regulatory means to minimize future impacts for the basin (http://www.swfwnid. state. fl .us/waterman/peaceriver/).
WATER QUALITY STANDARD AND TARGET IDENTIFICATION Florida's surface waters are protected for five designated use classifications, as follows:
Class I Potable water supplies Class I1 Shellfish propagation or harvesting Class IIT Recreation, propagation, and maintenance of a healthy,
well-balanced population of fish and wildlife Class IV Agricultural water supplies Class V Navigation, utility, and industrial use (there are no state
waters currently in this class)
Waterbodies in the Peace River Basin are classified as freshwater Class 111 waters, with designated use classification for recreation. propagation and maintenance of a healthy, well-balanced population of fish and wildlife. The water quality criteria for protection f Class I11 waters, are established by the State of Florida in the Florida Administrative Code (F.A.C.), Section 62-302.530. The individual criteria should be considered in
302.500 F.A.C. [Surface Waters: Minimum Criteria, General Criteria] that apply to all waters unless alternative or more stringent criteria are specified in F.A.C. Section 62-
1 conjunction with other provisions in water quality standards, including Section 62- 1
I 302.530. In addition, unless otherwise stated, all criteria express the maximum not to be exceeded at any time. The specific criteria are as follows:
Nutriett ts The discharge of nutrients shall continue to be limited as needed to prevent violations of other standards contained in this chapter [Section 62.302 F.A.C.] In no case shall nutrient concentrations of a body of water be altered so as to cause an imbalance in natural populations of aquatic flora and fauna [Section 62.302530 F.A.C.]. I
Dissolved Oxvnen (DO) Dissolved Oxygen (DO) shall not be less than 5.0 milligrams/L. Normal daily and seasonal fluctuations above these levels shall be maintained.
Biochemical Oxvpen Demand (BOD) I I
i BOD shall not be increased to exceed values which would cause dissolved oxygen to ~e depressed below the limit established for each Class and, in no case, shall it be great 1 enough to produce nuisance conditions.
Turbidih) For Class I11 waters, turbidity must be less than or equal to 29 NTU above background conditions.
EXAMINE WATER QUALITY AND ENVIRONMENTAL DATA I
Table 4 lists a summary of water quality nutrient data for each water body ID. Table 5 1 lists a summary of water quality nutrient data for each water type in the Sarasota Bay- Peace-Myakka Basin Group. Table 6 shows the biological assessments performed by th FDEP.
Biological data and chemical water quality data was assessed during the review and listing process. This data is summarized as background information for the TMDL development. The FDEP Water Quality Status Report for Sarasota Bay and Peace and Myakka Rivers (Sept. 2003) assesses the water quality in the Sarasota Bay and Peace Myakka Rivers Basin using quantitative data from a variety of sources, some of which are readily available to the public. These sources include the U.S. Environmental Protection Agency's (EPA) Legacy and "new" STOrage and RETrieval (STORET) databases, the Florida Department of Environmental Protection's IWR database, the U. Geological Survey (USGS), and the Florida Department of Health. The STORET and IWR databases contain water quality data from a variety of sources, including the Department, water management districts, local governments, and volunteer monitoring groups. In order to develop these TMDLs, these data sources and all additional available data was used. The data utilized and displayed in this TMDL report was accessed from, and is stored in IWR version 19.1. In the Water Quality and Environmental data sectior of these TMDLs, EPA reviewed the most current data to assess and discuss the
SOURCE ASSESSMENT 1 An important part of the TMDL analysis is the identification of sources or source I categories in the watershed and the amount of pollutant loading contributed by each of I
i these sources. Sources are broadly classified as either point or non-point sources. I
and
3 .
A point source is defined as a discernable, confined, and discrete conveyance from whi h pollutants are or may be discharged to surface waters. Point source discharges of industrial wastewater and treated sanitary wastewater must be authorized by National
d Pollutant Discharge Elimination System (NPDES) permits. NPDES permitted facilities
impairment. The time period for this was 1/1/1997 and later. The IWR 19.1 database w s used for this assessment, so this time period covered the most recent seven years of available data. These sections of the report show plots of water quality data for this period. In other sections of this report additional data may have been used, if the data f r
well as data collected more recent than that available in the IWR 19.1 database.
1 this seven year period was limited. Data collected prior to 1997 may have been used as
I
including certain urban stormwater discharges such as municipal separate storm sewer, systems (MS4 areas), certain industrial facilities, and construction sites over one acre storm water driven sources that are considered as "point sources" in this report.
Non-point sources of pollution are diffuse sources that cannot be identified as entering waterbody through a discrete conveyance. These include nutrient runoff of agricultural fields and golf courses, septic tanks, and residential developments outside of MS4 area
Non-poirrt sources Non-point sources that ultimately contribute to depletion of in-stream include sources of nutrients such as phosphate mines, animal waste, fertilizer application to agricultural fields, lawns, and golf courses, and onsite sewage treatment and disposal systems or septic tank systems.
There are numerous phosphate mines in the Peace River Basin, and these mines are a source of phosphorous entering surface waters. Phosphate mines are also a potential source of others surface water pollutants, such as acidity, fluorides and heavy metals. Phosphate mining is one of the three largest industries in Florida along with tourism an agriculture. Phosphate rock is a sedimentary rock that consists mainly of calcium phosphate together with other minerals such as calcium carbonate. Phosphate rock is formed from sea shells, corals and the like. As they die, their shells, which are primarily made up of calcium, settle to the bottom of the ocean in layer after layer. Over millions f years large deposits are formed. Millions of years ago, a lot of the earth, that is now dry land, was under water. Florida is a prime example of this. Florida is the leading produce of phosphate rock in the United States. Phosphate rock is used to make much of the
concerns. The process water is highly acidic and spills can cause great harm to aquatic life. The phosphogypsum contains impurities such phosphorus, fluorides and heavy metals like radium and selenium.
9 fertilizers used in agriculture. Phosphogypsum and the process water are environmental
I
Urban development is another major source of pollution in the Peace River Basin. The USGS report, Water-Quality Assessment of Southern Florida-Wastewater Discharges and Runox states that population growth and activities in the south Florida area over th
Agriculture is another potential source for the water quality impairments in the Peace River Basin. The USGS report, Water-Quality Assessment of Southern Florida- Wastewater Discharges and Runofx states that citrus production is a large industry on th Lake Wales Ridge (Highlands and Polk Counties). The Florida Agriculture Statistics Service reports that 119,901 acres of citrus in Polk county and over 55,000 acres in Hardee County. Runoff from these agricultural activities can be significant, especially during rainy seasons when the soil is saturated (USGS, 1998). Some of the largest dairy and cattle operations in the United States are in southern Florida (USGS, 1998). According to the Florida Agriculture Statistics Service, there are 108,126 cattle and calves in Polk County and 94,749 in Hardee County. High nutrient concentrations are attributed to runoff from improved pasture and dairy operations in some areas of southen. Florida (USGS, 1998).
:
past 40 years have resulted in increased water use, changes in the distribution and timhg of flow, and deterioration of water quality. These changes threaten both the remaining1 natural ecosystem and the growing human population. Wetlands and shallow waters i the region are sensitive to increased nutrient and contaminant inputs that are often associated with wastewater discharges and stormwater runoff. The stormwater that collects in retention ponds, canals, or ditches often contains bacteria, viruses, oil and grease, toxic metals, nutrients, and pesticides. These contaminants seep into the groun
discharged from canals into lakes and bays, degrading these waters (USGS, 1998). Landfills are another source of non-point pollutants associated with urban areas.
water quality (USGS, 1998).
I from ponds, canals, and ditches and adversely affect public water supplies, or they are '
Contaminants from landfills leach into the ground and surface waters, adversely
According to the USGS Water-Quality Assessment of Southern Florida-Wastewater Discharges and Runofi septic tanks are mostly used for individual households or smal! commercial establishments (churches, convenience stores, small motels, restaurants, a d campgrounds) that are in rural or remote areas, or in urban areas that are not served by domestic wastewater facility. Water from septic tanks is generally released to the grou d through a subsurface drain field after natural biological treatment. Concentrations of septic tanks are common in highly suburbanized counties, where housing growth often occurs in unincorporated areas immediately adjacent to city limit (Marella, 1994). In 1 many cases, these areas are not served by domestic wastewater facilities. The estimate water released from each septic tank is about 135 galld. Most of the effluent is released to the subsurface through on-site subsurface drain fields or boreholes that allow the water 1 from the tank to percolate into the ground (usually into the surficial aquifers) and either transpire to the atmosphere through surface vegetation or add to the flow of shallow 1 ground water. The USGS report continues to say that the number and density of septic I tanks can have important effects on water quality; waste generated from each tank can 1 add high levels of nitrogen (nearly 24 pounds per year) and phosphorus (9 pounds per year) to the surficial aquifer and adjacent surface water (USGS, 1998).
Some of the analytical methods utilized in development of these TMDLs include speci loading rates for septic tanks. The State of Florida Department of Health (http://www.doh.state.fl.us/environment/OSTDS/statistics/ostdsstatistics.htm) publishes septic tanks data on a county basis. Table 2 summarizes the number of septic systems installed in Hardee and Polk counties since the 1970 census. The data does not reflect septic tanks removed from service.
Table 2: Septic Tanks installed since 1970 1 COUNTY I Total Se~t ic Tanks since 1970 1
Hardee 1 8,293 Polk
Most non-point source pollutant loads were included in the TMDL analysis indirectly through the use of landuseGIs coverages, landuse loading rates, and the observed in- stream water quality data.
In 1982, Florida became the first state in the country to implement statewide regulationb to address the issue of non-point source pollution by requiring new development and I redevelopment to treat stormwater before it is discharged. The Stormwater Rule, as 1 outlined in Chapter 403 Florida Statutes (F.S.), was established as a technology-based program that relies upon the implementation of BMPs that are designed to achieve a specific level of treatment (i.e., performance standards) as set forth in Chapter 62-40, 1 F.A.C.
Florida's stormwater program is unique in having a performance standard for older stormwater systems that were built before the implementation of the Stormwater Rule i 1982. This rule states: "the pollutant loading from older stormwater management systems shall be reduced as needed to restore or maintain the beneficial uses of water" (Section 62-4-.432 (5)(c), F.A.C.).
Nonstructural and structural BMPs are an integral part of the State's stormwater programs. Nonstructural BMPs, often referred to as "source controls", are those that ca be used to prevent the generation of NPS pollutants or to limit their transport off-site. Typical nonstructural BMPs include public education, land use management, preservation of wetlands and floodplains, and minimizing impervious surfaces. Technology-based structural BMPs are used to mitigate the increased stormwater peak
I discharge rate, volume, and pollutant loadings that accompany urbanization.
Landuse in the impaired WBIDs is shown in Figure 11. The spatial distribution and I
acreage of different land use categories were identified using the 1999 land use coveragd (scale 1 :40,000) contained in the FDEPYs GIS library. This dataset was derived from I
Infrared Digital Orthophoto Quadrangle photo interpretations using the Florida Land Us Classification Code System (FLUCCS). Land use categories in the watershed were aggregated using the FLUCCS Level 2 codes.
Point sozirces NPDES facilities in these Peace River Basin WBIDs for which EPA is developing TMDLs are listed in Table 3. Both NPDES facility permit limits and discharge monitoring reports (DMRs) were used in these TMDL analyses.
Also there are municipal separate storm sewer systems (MS4) throughout the Peace ~ i v $ Basin since the area is extensively developed. All waterbodies located within Polk County that collect or receive storm water discharges from regulated Phase I MS4 areas are subject to the appropriate provisions of the NPDES Phase1 MS4 permit. Polk County is the lead applicant in the permit, and is responsible for the coordination of information and efforts to be reported in the Annual reports. Additionally, via interlocal agreements and MOAs, Polk County may be responsible for the actual implementation of stormwater requirements as stated in the permit. However, each permittee covered in the permit is ultimately responsible for the MS4 discharges resulting from their jurisdiction, including TMDLs and WLAs. Since no MS4 water quality data was available, the MS4 pollutant loads were not specifically analyzed. The MS4 loads were indirectly included in the
TMDL analysis through the use of landuse GIs coverages, landuse loading rates for 1 urban areas and the observed in-stream water quality data. ,
ANALYTICAL APPROACH1 MODEL SELECTION AND DEVELOPMENT 1 What type of analysis is appropriate for linking the water quality target and pollutant sources? Methods for linking the target and impairment sources include empirical approaches based on observed information, simple approaches, screening level model analysis, and detailed modeling. TMDLs can include one or more of these approaches t characterize this linkage between a target and source (U.S.Environmenta1 Protection Agency. 2001 Protocol for Developing Pathogen TMDLs. E P A 841-R-00-002. Office f Water (4503F), United States Environmental Protection Agency, Washington, DC. 132 PP.> I i
These TMDLs for nutrients, BOD, and low DO are all addressed by analyzing dissolve oxygen. Statistical regression models and mechanistic models are used to analyze these water bodies and develop these TMDLs. The purpose of utilizing water quality models for the development of DO, nutrient and BOD TMDLs in this river basin is to underst the linkage between the low in-stream DO and the factors that cause the low DO. The models can help determine which factors cause a greater effect than others. Some of the major factors in DO processes include watershed and stream flow and geometry, loads from the watershed, BOD loads from the watershed, in-stream plants and sediment oxygen demand.
Statistical Approach The approaches selected here combine the known kinetic relationships for the sources and sinks of dissolved oxygen with correlation and regression statistics. Based on the known mechanisms of the sources and sinks of DO, simple regression models were developed. The variation in the observed DO is explained by variables such as temperature, BOD, chlorophyll, nutrients, total organic carbon and flow. Statistics were used to explore the relationships at each water quality monitoring station in the impaired WBID depending on the water quality parameters that were recorded. I
Mechanistic Model Approach Water quality simulation models of the complex DO processes were also utilized to analyze and develop some of these TMDLs. The mechanistic model approach here is to model watershed hydrology, nutrient loads, BOD loads, then deliver these flows atid loads to the impaired receiving streams, and finally model the in-stream water quality processes within these receiving streams.
In the Peace River EPA's simple approach from the BASINS PLOAD model was utiliz d to estimate non-point source pollutant loadings. In Saddle Creek and Lena Run the Watershed Assessment Model (WAM) was utilized to simulate the watershed hydrolog 1 and water quality loadings. Water Quality Analysis Simulation Program (WASP) models were set up to examine the DO processes in the Peace River, Peace Creek, Saddle Creek, and Lena Run. The WAM model was used to predict flows and loads which were then linked to the WASP models. I
The following summary on of the WAM model is from EPA7s Watershed and Water 1 Quality Modeling Technical Support Center web site (http://www.epa.gov/athens/wwqtsc/WAMView.pdf). WAM7s interface uses ESR17s ArcView 3.2a with Spatial Analyst 1.1 (or 2.0). WAM was developed to allow engineers and planners to assess the water quality of both surface water and groundwater based on land use, soils, climate, and other factors. The model simulates the primary physical processes important for watershed hydrologic and pollutant transport. The WAM GIS- based coverages include land use, soils, topography, hydrography, basin and sub-basin boundaries, point sources and service area coverages, climate data, and land use and soil description files. The coverages are used to develop data that can be used in the simulation of a variety of physical and chemical processes.
i WAM was developed based on a grid cell representation of the watershed. The grid cell representation allows for the identification of surface and groundwater flow and phosphorus concentrations for each cell. The model then "routes" the surface water and groundwater flows from the cells to assess the flow and phosphorus levels throughout the watershed. The model simulates the. following elements: surface water and ground water flow allowing for the assessment of flow and pollutant loading for a tributary reach at both the daily and hourly time increment as necessary; water quality including particulate and soluble phosphorus, particulate and soluble nitrogen (N03, NH4, and organic N), total suspended solids, and biological oxygen demand.
WAM was linked to WASP (SWET, 2003), which enables the simulation of dissolved ~ oxygen and chlorophyll-a. The WAM model simulates the hydrology of the watershed using other imbedded models including "Groundwater Loading Effects of Agricultural Management Systems" (GLEAMS; Knisel, 1993), "Everglades Agricultural Area Model" (EAAMod; Botcher et al., 1998; SWET, 1999), and two submodels written specifically for WAM to handle wetland and urban landscapes. Dynamic routing of flows is I
accomplished through the use of an algorithm that uses a Manning's flow equation based' technique (Jacobson et al., 1998). Attenuation is based on the flow rate, characteristics of the flow path, and the distance of travel. The model provides many features that improve' its ability to simulate the physical features in the generation of flows and loadings including:
Flow structures simulation Generation of typical farms BMPs Rain zones built into unique cells
definitions, which also allows use with NEXRAD Data
Full erosion/deposition and in-stream routing -is used with ponds and reservoirs Closed basins and depressions are simulated Separate simulation of vegetative areas in residential and urban Simulation of point sources with service areas Urban retention ponds Impervious sediment buildup/washoff !
Shoreline reaches for more precise delivery to rivers, lakes, and estuaries Wildlife diversity within wetlands Spatial map of areas having wetland assimilation protection Indexing submodels for BOD, bacteria, and toxins
The overall operation of the model is managed by the ArcView-based interface. The interface allows the user to view available data, modify land use conditions, execute the model, and view results.
In order to evaluate the effect of BOD, nutrients, algae, and other oxygen demanding substances on DO processes Water Quality Analysis Simulation Program (WASP) models were setup. The Water Quality Analysis Simulation Program version 7 (WASP )
1984; Ambrose, R.B. et al., 1988). This model helps users interpret and predict water quality responses to natural phenomena and man-made pollution for various pollution
1 is an enhancement of the original WASP (Di Toro et al., 1983; Connolly and Winfield,
management decisions. WASP7 is a dynamic compartment-modeling program for aquatic systems, including both the water column and the underlying benthos. The time-varying processes of advection, dispersion, point and diffuse mass loading, and boundary exchange are represented in the basic program. Water quality processes are represented in special kinetic subroutines that are either chosen from a library or written by the user. WASP is structured to permit easy substitution of kinetic subroutines into the overall package to form problem-specific models. WASP7 comes with two such models -- TOXI for toxicants and EUTRO for conventional water quality. Earlier versions of WASP have been used to examine eutrophication of Tampa Bay; phosphorus loading to Lake Okeechobee; eutrophication f the Neuse River and estuary; eutrophication and PCB pollution of the Great Lakes (Thomann, 1975; Thomann et al., 1976; Thomann et al, 1979; Di Toro and Connolly,
I 1980), eutrophication of the Potomac Estuary (Thomann and Fitzpatrick, 1982), kepone I
pollution of the James River Estuary (O'Connor et al., 1983), volatile organic pollution Of the Delaware Estuary (Ambrose, 1987), and heavy metal pollution of the Deep River, ! North Carolina (JRB, 1984). In addition to these, numerous applications are listed in Dil Toro et al., 1983.
I
The flexibility afforded by the Water Quality Analysis Simulation Program is unique. 1 WASP7 permits the modeler to structure one, two, and three-dimensional models; allods the specification of time-variable exchange coefficients, advective flows, waste loads a d water quality boundary conditions. The eutrophication module of WASP7 was applied n the development of these TMDLs.
1 I
The following sections discuss the impairments in each water body ID (WBID) and ' describes the water quality data in each of these WBIDs. Each section also describes the/ applied analytical approach and develops the TMDL for the pollutant-WBID I
combination.
above lake hancock
FL0036048 farms drain
Table 3: NPDES facilities in the Pea
canal
WRID WBID Name ; NPDES I
e River Basin WBIDs co FACILITY NAME
I I
POLK NURSERY
1501 A
COMPANY, INC.
WINTER HAVEN #3 WAHNETA
lake lena nin
FL DISTILLERS C0,AUBURNDALE AUBURNDALE STP FL0021466
ered in this re RECEIVING WATER No discharge from this facility
LAKE LENA RUN LAKE LENA RUN
Table 4: Average Nutrients (mgll) in WBID
1623K 1623K 1626
Table 5: Average Nutrients (mgll) for the Sarasota Bay-Peace-Myakka Basins 1 Basin Group I Water Type I Nutrient I Average 1
1626 1626
SADDLE CK Below L HANCOCK SADDLE CK Below L HANCOCK WEST WALES DRAINAGE CA
MINOR FLOWERS AND FLORISTS'
o r t . 1
WEST WALES DRAINAGE CA WEST WALES DRAINAGE CA
SUPPLIES
MAJOR-ID
TN TP TKN
MAJOR, 2.6 IST, RECTIFIED
MAJOR, 1.4 SEWERAGE YSTEMS
1 SIC2D i
2.4 1 0.56 1.85
TN TP
I Sarasota Bay - Peace - Myakka 1 BLACKWATER I TKN 1 1.650 1
1.99 0.1 1
I Sarasota Bav - Peace - Mvakka I COASTAL I TP 1 0.100
Sarasota Bay - Peace - Myakka Sarasota Bay - Peace - Myakka Sarasota Bav - Peace - Mvakka
BLACK WATER^ COASTAL COASTAL
Sarasota Bay - Peace - Myakka Sarasota Ray - Peace - Myakka
Group
Sarasota Bay - Peace - Myakka Sarasota Bay - Peace - Myakka Sarasota Bay - Peace - Myakka
--
TP TKN TN
-
ESTUARY ESTUARY
0.405 0.66 1 0.205
ESTUARY LAKE LAKE
TKN TN
. .
0.687 1.129
TP TKN TN
0.228- 1.503 1.475
1 61 1
1 LI
I LI
I L 1 SZ 6 1
1 1 E
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LAKE LENA RUN WBID 1501A (SADDLE CREEK SUBBASIN), LOW DO, NUTRIENTS, BOD
Lena Run description, Water Quality And Environmental Data, and Source Assessment WBID 1501A is on the 1998 303(d) list as impaired for nutrients and low DO. A TM for BOD is also developed here since it is related to the low DO. There are two permitted discharges to Lena Run, Auburndale Allred WWTP NPDES FL0021466, an Florida Distillers Co at Auburndale NPDES FL000305 1. A third facility, Coca Cola Foods, discharged to Lena Run until around Dec. 1993 when the permit There was a water quality based effluent limit analysis performed on Lena Run for permitting purposes in 1985. Several municipalities near the WBID stormwater runoff to Lena Run under the Polk County MS4 permit.
1 '5 \,
29
1 ; 2 \
Figure 4 is an aerial photograph showing Lake Lena and Lena Run within the Saddle Creek Watershed. Lake Lena Run originates in Auburndale and enters Lake Hancock o the northeast side (SWFWMD, 2004). During wet seasons, Lake Lena may discharge
b into Lake Lena Run through the Southwest Florida Water management District control structure P-1 (see Figure 2). However, neither nutrients (TN, TP) nor chlorophyll-a observed data shows clear relationships to the levels in the upstream Lake Lena. Figure 5 shows that 21 percent of the DO observations are below the 5.0 mgll standard. Figure 9 and Figure 10 show the TN and TP data from Lena Run. Figure 7 and Figure 8 show 4 chlorophyll-a observations above 20 ug/l in Lena Run. A query of the USEPA ecoregio
mgll and TKN of 1.1 mgll (http:Nwww.epa.gov/waterscience/criteridn~~trient/database/select ecoregion.htm1). EPA "reference conditions for aggregate ecoregion XI1 streams" are 0.56 mgll TKN an 0.040 mg/l TP and 0.58 mgll for TN. The average TKN in the Lena Run observations (IWR 19.1) from 1992 through 2003 is 1.30 mgll, which is higher than the ecoregion
I nutrient data for ecoregion XI1 rivers and streams in Florida shows an average TP of 1.4
value and the average TP is 0.53 mgll, about one third the EPA ecoregion value. The average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the FDEP IWR 19.1 database (entire database period of record which is 1992 through or early 2004) is 1.17 and the average TP is 0.45 mgll.
1
1626
192 1 192 1 1921
Nitrogen is usually the limiting nutrient when the TN/TP ratio is less than 7.2 based on phytoplankton stoichiometry. For this dataset the TNITP ratio was 3.6. This seems reasonable since this area of the Peace River Basin is known for high phosphorus content in its soil and bedrock. This area of Florida has many phosphate mines, although none aru documented in the Lena Run watershed. Because of the high phosphorus and the
SCI
SCI BIORECON SCI
W. WALES DRAINAGE CANAL @ CREWS RD. OFF CR640 Limestone Crk Test Limestone Crk Test Limestone Crk Test
Poor
Excellent Suspect Good
7/23/2003
2/25/1998 2/25/1998 7/10/2003
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7
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r 7
Figure 11 shows that the Lake Lena Run WBID is a highly developed area with 20 percent of the area residential and 26 percent commercial, industrial. Table 7 the loads discharged by the two permitted discharges in the WBID, Florida at Auburndale industrial wastewater FL000305 1 and Auburndale Allred municipal wast water treatment plant FL002 1466.
Figure 12: Event Mean Concentrations from Evaluation of Alternative Stormwater Regulations for 1 Southwest Florida (Harper and Baker, 2003) I
Annual Preap~tatlon Summary for Statlon WBAN 12876. W~nlerhaven Flor~da
!
70
1997 1998 1999 2000 2001 2002 2003 ~ Figure 13: Annual Precipitation Summary for Station WBAN 12876, Winterhaven Florida 1
Precipitation I
' 2 2 2 2 p 3 8 , 0 " J v o " J $ ED) .p c~a $" *a' $,.P'~~Q p P ,*p g ,., oG ,~$p<9,s40E4,~p90p<p0,~900&90,ap9D)p<99, b :, , \* vQ
Figure 14: Monthly Precipitation Summary for Station WBAN 12876, Winterhaven Florida
Lena Run Analvtical Approach/Model Selection And Development
WAM was used to estimate the non-point source loads and the flow for Lena Run. The WASP was used for estimating the effects of non-point source and point source loads o dissolved oxygen. Figure 15 shows the WAM and WASP model map for Lena Run. Th location of the continuous point source discharges is shown. i Table 11 shows the non-point source loads (MS4 load estimations are included in these non-point source loads) estimated by WAM for the Lena Run watershed, and Table 7 shows the continuous point source loads. Reported actual discharge loads from both poi source facilities are summarized in Table 8. A comparison of these combined point source loads to the non-point source loads is shown in Table 9. The BOD point source loads range from 6 to 19 percent of the non-point source loads, the nitrogen loads range from 13 to 16 percent, and the phosphorus loads ranged from 14 to over 200 percent of the non-point source loads. Overall, the nitrogen and BOD point source loads are a sma part of the loadings to Lena Run. For the TMDL analysis the NPDES surface water permitted loads from the point sources are evaluated because the facilities are allowed t discharge these quantities. The permitted point source loads are summarized in Table 1( and they are greater than the existing discharges. In this TMDL analysis, the permitted point source loads and the estimated non-point source loads are reduced until the water quality standard for DO is met.
Figure 16 through Figure 22 show the predicted versus observed water quality in Lena Run. Figure 16 shows that the DO is improved to meet the 5.0 mgll water quality ~ standard with an eighty percent reduction in all nutrient and BOD loads. ~
WAM and WASP models for Saddle Creek, WBlD 1497 and Lena Run, WBlD 1501A 1
m Npdesdischarges.shp $$/ Lenarunl50lawasp.shp Subbas~ns
Banana Lake 0 Cabbage Branch I Eagle Lake 0 I-Ville D~tch
B Lake Lena Run Lake Parker I Lower Saddle Creek 0 Middle Saddle Creek
4 0 4
0 Upper Saddle Creek
Figure 15: Lena Run (WBID 1501A) and Saddle Creek (WBID 1497) WAM and WASP model map
Table 7: Annual Average Facility Discharge Loads in Lena Run Facility Name
AUBURNDALE STP AUBURNDALE STP AUBURNDALE STP AUBURNDALE STP
Facility ID
FL002 1466 FL002 1466
AUBURNDALE STP AUBURNDALE STP AUBURNDALE STP
FL002 1466 FL0021466
AUBURNDALE STP AUBURNDALE STP
1 FL DISTILLERS / FL0003051 / 12.76 1 1 1 1991 1 1
BOD (kg/d) 2.35 0.52
FL002 1466 FL002 1466 FL0021466
AUBURNDALE STP FL DISTILLERS
COYAUBURNDALE FL DISTILLERS FL000305 1 1992 CO-AUBURNDALE
1.96 1.86
FL002 1466 FL0021466
1 FL DISTILLERS
TN (kgld)
4.90 2.75
1.38 1.95 2.83
FL002 1466 FL000305 1
1 COYAUBURNDALE FL DISTILLERS
1995 1 1996 i
5.64 11.66
1.27 4.41
TP (kgld)
1997 1998
2.48 2.79 4.18
4.19 9.52
YEAR
9.30 8.46
FL DISTILLERS C0,AUBURNDALE FL DISTILLERS
1.96 10.82
3.10
C0,AUBURNDALE FL DISTILLERS
1999 2001 1 2002 I
6.34 4.95
FL000305 1
1 FL0003051
C0,AUBURNDALE FL DISTILLERS CO.AUBURNDALE
2003 2004
3.94
FL DISTILLERS C0,AUBURNDALE
2005 1990
1.97
4.57 I
2003 1 FL000305 1
FL000305 1
3.19
FL000305 1
2.45
2.06
2.87 2004 I
12.26
0.14
0.14
2005
200 1
2002 i
Table 8: Combined Annual Average Daily Continuous Point Source Loads in Lena Run YEAR 1999
Table 9: Combined Point Source Loads as Percent of Non-Point Source Loads in Lena Run
TN (kg/d) 4.68
BOD
1 Table 10: Permit limits for Auburndale STP and Florida Distillers Co.
Discharge Limit AUBURNDALE STP
TP 1 YEAR
FL DISTILLERS C0,AUBURNDALE
TP (kgld) 0.365
' TN
1 Surface Water
--- 14.76
Table 11: Estimated Annual Average Daily Non-point Source Loads from the Lena Run watershed 1
BOD (kgld) 5.95 !
TP (kgld) TN (kg/d)
8.33
BOD (kgld)
No limit
BOD load (kg/d) ' 32.1 24.3
Year 1999 2000
No limit
19.681 24.6
TN load (kgld) 28.5 27.2
-
TP load (kgld) 2.7 2.2
I
...... I Eal *h~pCo~~d ido~~n . 2 IF IRXKLEtU RIIH CREEKII . >lFLSWFDFLCk3327 j l I P L I P A M I O I I 1
. .. . THC1 Conel8icn
Figure 16: Lena Run Observed DO, Simulated Existing Condition, Predicted TMDL Condition witq 80% reduction I
Figure 17: Lena Run Observed and Predicted Chlorophyll-a 1
~ MO[~ pap!paq una euaq :61 a~nZ!d
! VOOZ COOZ ZOOZ LOOZ OOOZ 666L
e!uourury pappa~d pue paalasqo una euaq :g~ a~n9!d
POX - L6BL
PO02 EOOZ ZOO1 LOO2 0002 666L 8661
I alt!.q!N pap!paJd put! pauasqo unH sua? :TZ a~nz!~
9002 - L661 COO2 ZOOZ COOZ OOOZ 666L 8661
0
z
c -
I'
9
9
116~
i (108 pappaJd put! paAJasq0 unH sua? :OZ a~nz!~
I aoe
TOM Phosphorus I
Figure 22: Lena Run Observed and Predicted Total Phosphorus 1
Lena Rrrn Allocations The TMDL process quantifies the amount of a pollutant that can be assimilated waterbody, identifies the sources of the pollutant, and recommends regulatory or actions to be taken to achieve compliance with applicable water quality standards on the relationship between pollution sources and in-stream water quality conditions. TMDL can be expressed as the sum of all point source loads (Waste Load non-point source loads (Load Allocation), and an appropriate margin of which takes into account any uncertainty concerning the relationship limitations and water quality:
TNIDL = C WLAs + C LAs + MOS I I
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR in terms of mass per time (e.g. kilograms The TMDL for Lena Run, WBID 1501A, the LA and storm water WLA. The
Table 12: Lena Run TMDL allocations I I I I I
WLA
Waste Load Allocations (Regulated with treatment plant and stormwater permits)
LA I MOS
There are two continuous point source facility permits and a MS4 permit in the Lena Ri watershed. The TMDL for nutrients targets nitrogen because the TNITP ratio of 3.6 indicated a nitrogen limitation. An eighty percent reduction in TN and BOD is recommended to achieve the water quality standard for DO. For the continuous point sources these reductions are from the permitted point source loads. The TMDL pollut; loads to the two facilities is allocated by reducing each existing permit limit by 80 percent such that the WLA is achieved. This TMDL also allows the total pollutant allocation to be apportioned differently between the two facilities as long as the total WLA is achieved. The MS4 allocation is expressed as a percent reduction since these storm-water loads that vary with the antecedent conditions and the intensity and durati of the storm.
I Pollutant 1 TMDL 1 continuous 1 MS4
implicit
implicit
Total Nitrogen
BOD
Load Allocations (Non- Regulated) As discussed above, for nutrients the target is total nitrogen, and an eighty percent reduction in TN is recommended to achieve the water quality standard for DO. An eig percent reduction in BOD is also recommended to achieve the standard for DO. The 1c allocation is expressed as a percent reduction since these are storm-water loads that va with the antecedent conditions and the intensity and duration of the storm.
reduction 80% 4.6 kgld 80% reduction reduction 80%
Margin O f SafeQ A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDI the following information was considered in determining the margin of safety.
The worst case condition in the 5 year simulation was addressed to meet stand: However, the boundary DO was assumed to be 5 mgll which is not always tru~ (These boundaries are the inflows to the model at the upstream end and throughout the modeled stream segments via tributaries and direct runoff that a not affected by the model.) Decreases in the watershed loads are expected to also improve the DO at the model boundaries There are no flow records to which to calibrate the model The downstream most reach was selected for the analysis in order to avoid modeling inaccuracies due to low or zero flow (low volume and depth) conditi~
The two worst cases for DO occurred in 2000 and 2002, which represent a dry year an wet year in this 5 year period (see Figure 13). The reductions required to meet the 5.0 : standard in an average precipitation year such as 2003 is 60 percent. If the boundary D is assumed to be 3 then even with complete removal of sources Lena Run would not
reduction 80% 80%
reduction 8.8 kgld 80% reduction
recover to the 5.0 mg/l DO standard even in 2003 conditions. What does all this mean? Basically, there are unknowns that may have significant implications on this analysis, an1 these cannot all be quantified. Rather than assign an arbitrary explicit margin of safety, the TMDL should be reevaluated after reductions have been implemented and additional data has been collected. The margin of safety for this TMDL is implicit by basing the TMDL reductions on the worst case in the 5 year analysis period, and by specifying nutrient reductions that would result in TKN concentrations near or below the EPA ecoregion reference conditions. For example, the median observed TKN was 1.3, and 20 percent of this is 0.26, which is less than the EPA recommended reference condition of 0.56 mg/l.
Critical Conditions Critical conditions were considered by analyzing five years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed in this 1999 through 2003 , period. I I
Seasonal Vuriation 1 Seasonal variation was considered by analyzing five years containing all seasons, wet, 1 normal, and dry conditions.
SADDLE CREEK WBID 1497 (SADDLE CREEK SUBBASIN) LOW DO, NUTRIENTS, AND BOD
Saddle Creek (1497) description, Water Or~ality Artd Envirorzrnentnl Data, and Source Assessment This WBID is on the 1998 303(d) list as impaired for low DO and nutrients. EPA is developing TMDLs for WBID 1497 for low DO, nutrients, and BOD. BOD is included because it is a suspected contributor to the low DO impairment. The landuse in this WBID is 25 percent urban, 11 percent agriculture or rangeland, 21 percent wetlands, an
I 32 percent barren or extractive (see Figure 1 1). There is one permitted point source facility in this WBID, Polk Nursery Company, Inc. permit number FLO13 1385. This Saddle Creek WBID is a portion of one of the three watersheds contributing to Lake Hancock. Upstream of this WBID, Lakes Bonny and Parker are two nutrient-impaired
I Lakes contributing to Saddle Creek. Lake Bonny has an outlet to Lake Parker and Lake 1 Parker has a managed outlet to this Saddle Creek WBID. According to the Southwest
! Florida Water Management District Lake Bonny is approximately 350 acres in size wit a watershed of approximately 2.8 square miles, and the average depth of the lake is 8 feet. Lake Parker is approximately 2,270 acres in size, and it is located just northeast of
mostly comprised of a mixture of commercial and residential land uses. The average
6 downtown Lakeland. The watershed of Lake Parker is about 24 square miles, and is 1 ~ water depth for Lake Parker is 10 feet. The watersheds of both lakes have experienced dramatic population growth during the last 50 years (SWFWMD, 2005 Lake Parker, L e Bonny, and Banana Lake). f Lake Bonny's water quality has varied between eutrophic (TSI values 60 to 70) and hypereutrophic (TSI values > 70) classifications for the past several decades (Figure 3),
Lake Parker's water quality has been consistently classified as hypereutrophic, with TSI values in excess of 70 since the late 1960's (S WFWMD, 2005 Lake Parker, Lake Bonny? and Banana Lake). i
According to the Southwest Florida Water Management District, a number of stormwat treatment projects are either ongoing or in the design phase for Lake Parker. These projects are: Lake Parker Southwest Outfall Retrofit, which is expected to reduce 55 % f the TSS load, 16 % of the TN load, and 46 % of the TP load from this 595 acre drainage basin when the final project is completed. The Lake Parker Northwest Tributary
stormwater treatment ponds by expanding the wet and dry retention ponds to allow for
is the Alternative Stormwater BMP's for Lake Parker Southwest Basin. This project seeks to provide for additional stormwater treatment in the Southwest Basin of Lake
I Stormwater Retrofit, which should enhance the nutrient removal of already-existing 1 greater amount of flow to be treated prior to discharge into Lake Parker. Another projec f Parker "upstream" of the point of discharge of stormwater into the wet detention treatment ponds mentioned above. The performance of these downstream treatment 1 ponds would be enhanced if stormwater could be treated at multiple locations within th watershed, as a form of "treatment train" for stormwater in this highly urbanized 4 watershed. This project is in the conceptual design stage, and will proceed in cooperatibn with the City of Lakeland once land becomes available for stormwater treatment (SWFWMD, 2005 Lake Parker, Lake Bonny, and Banana Lake).
The dissolved oxygen in this WBID was below the 5.0 mg/l standard 78 percent of the time (see Figure 23). These DO observations show that DO saturation ranged from 2 to 72 percent. As an indication of imbalance of natural flora or fauna, FDEP's IWR states a maximum annual mean value of chlorophyll-a should not exceed 20 ug/l or annual meaL chloropl~yll-a values should not have increased by more than 50% over historical value i for at least two consecutive years. Corrected chlorophyll-a exceeded 20 ug/l 18 percentlof the time and un-corrected chlorophyll-a never exceeded 20 ug/l (see Figure 25 and Fig@ 26). As shown in Figure 24, BOD is relatively low, near detection limits. Nutrients can( affect the DO through algae production and respiration. An excess of algae growth can imbalance the natural system and cause large DO swings from high supersaturation to low levels. Additionally, the algae populatibn can reach a limiting level of nutrients or light and then experience a large die-off that can then result in DO consumption and lo in-stream DO. The average TKN is 1.18 mgll, 1.61 for TN and the average TP value is
1.6 mg/l TP and the TKN value is comparable to the ecoregion value of 1.1 mg/l
W 0.54 mgll. The total phosphorus value is less than one third the EPA ecoregion average of
according to a query of the USEPA ecoregion nutrient data for ecoregion XI1 rivers an d streams in Florida 1 (http://www.epa.gov/waterscience/criteridnutrient/database/select ecorepion.htm1). E ~ A "reference conditions for aggregate ecoregion XI1 streams" are 0.56 mgll TKN and 0. 40 mg/l TP and 0.58 mg/l for TN. 9 Average nutrient values from the Florida IWR Upper Peace Planning Unit data are 0.2~1 mg/l TP and 1.58 mgll TKN. The average TKN for streams in the Sarasota Bay-Peacet Myakka Basins Group from the FDEP I WR 19.1 database is 1.17 and the average TP s 0.45 mg/l. For blackwater streams in this basins group the average TKN is 1.65 and th b
average TP is 0.41 mgll. The average color of Saddle Creek is 108 platinum cobalt units. ~ FDEP performed four bioassessments analyzed according to the Stream Condition Index ~ (SCI) in WBID 1497 with scores ranging from suspect to good (2005. Florida I Department Of Environmental Protection, IWR 20) (see Table 6). I
/ EPA Ecoregion XI1 average I 1.1 I
1 1.6
Table 13: WBID 1497 Nutrient Concentration Comparison
WBID 1497
I Sarasota Bay-Peace-Myakka Basins Group streams 1 1.17 1 0.45 1 1 EPA Ecoregion XI1 recommended reference condition Upper Peace Planning Unit
TN:TP ratio is 3.0 for the WBID. Based on phytoplankton stoichiometry, a TN:TP ratio less than 7.2 generally indicates a nitrogen limitation and a high ratio indicates that nitrogen is abundant and the system is phosphorus limited. This ratio of 3.0 indicates a
TKN I TN 1.18 1 1.61
nitrogen limitation.
TP 0.54
0.56 1.58
1497 Water Quality Data r . - - p . .-
I + Dissolved Oxygen (mgll) - WaterQualityCriteria I 1 L-- . _ - ~ 1
0.58
I I Figure 23: In WBID 1497,31 of 40 DO observations were below the 5.0 standard I
0.04 0.21
-
1 WBID 1497 Water Quality Data 1 L + Chlorophyll (ugm -Water -- Quality - - ~ o m ~ a r i s o d
- - ----- -- + I
--j +
8
7 I
912711997 1/5/1998 411511 998 712411 998 1111 11 998 21911 999 - -- - -- -- ----- - - --
Figure 25: Chlorophyll-a in WBID 1497; all values were below 20 ugll
-- FBID 1497 Water Quality ~ a t a ]
1 + Chlorophyll Corrected (ugll) -Water Quality Comparison 1 L - - . _ _ ~ . . ~ - ~ p - - - - 1
Figure 26: Corrected Chlorophyll-a in WBID 1497; 5 out of 27 are above 20 ug/l.
Saddle Creek (1497) Analvtical Approach/Model Selection And Develoament WAM was used to estimate the non-point source loads and the flow for Saddle Creek. Then WASP was used for estimating the effects of all nutrient and oxygen consuming
I loads on dissolved oxygen. Figure 15 shows the WAM and WASP model map for Sad Creek. The location of the USGS flow gage is also shown.
Table 14 shows the non-point source loads (MS4 load estimations are included in thesei non-point source loads) estimated by WAM for the Saddle Creek watershed. Figure 27 through Figure 34 show the predicted vs observed water quality in Saddle Creek. Figur 35 shows that the DO is improved to meet the 5.0 mgll water quality standard with a 95
not necessarily achievable, but such reductions would be necessary to meet the current water quality standard for DO. If the FDEP develops a site specific alternate water quality criterion for this water body, the TMDL can be revised.
i percent reduction in all nutrient and BOD loads. It is recognized that these reductions ate
Table 14: Saddle Creek (1497) Estimated Non-point Source Loads
Figure 27: Predicted versus Observed Dissolved Oxygen in Saddle Creek WBID 1497 I I
Year 1999
TN load (kgld) 64.2
TP load (kgld) 30.9
BOD load (kgld) 120.8
Figure 30: Predicted vs Observed Flow (cms) in Saddle Creek WBID 1497
Table 15: Flow Calibration Statistics for Saddle Creek at Hwy 542 near Lakeland, FL (USGS 02294217)
Root Mean Square Error (RMSE) 1 2.02609 Mean Predicted 1 1.56324
Mean Error Mean Absolute Error (MAE)
1 Standard Deviation Predicted 1 2.9096
0.731981 1.01737
Mean Observed 1 Standard Deviation Observed
Table 15 shows the calibration statistics for flow in Saddle Creek near Lakeland, FL.
0.831257 1 .go525
Correlation Coefficient, RA2 Forecast Efficiency
Mean absolute error, root mean square error, and forecast efficiency are measures that incorporate both systematic error and random error (Maidment, David R. 1993. Hydrologic Forecasting. Handbook of Hydrology.). The mean error, mean error absolut~ and root mean squared error are measures of the size of the discrepancies between
0.602405 0.488868
predicted and observed values. Values near zero indicate a close match. If the RMSE is significantly greater than the MAE then there are instances where the prediction error is significantly greater than the average prediction error. The means and standard deviatioi show the central tendency and the spread of the predicted and observed values. In this model the mean flow is over-predicted mostly at low-flow conditions. Figure 30 shows that the general trend and most storms are predicted well. The correlation coefficient measures the tendency of the predicted and observed flows to vary similarly. The forecc efficiency measures how well a model predicts relative to the average of the observatior The forecast efficiency ranges from negative infinity to one, with higher values indicatii
I 'IlaM ICpg
SMOU a8r!~a~r! ayl sr! IIaM sr! sICal~r!~ pur! syr!ad slxpald Iapour sry~ .sluauraal8r! lallaq
I -
&.a,*" n~ll"X*0mLr:~LL"l . : + I L ( B z L C O I . ,8',YFA ,5vz,m . 28FL?PA>?t2?>57 . 2,,L:#~.>w<,x,:.,T,<,
PODO mor 1897 -2003
Figure 34: Predicted vs Observed Total Phosphorus in Saddle Creek WBID 1497 1
- RsdlrtedTUCL rond. . llFLPOLKSACOLE CREEK r IIFLIL'IFDFLOOOY . 2ITLTPA 2502O249
2lFLrPb 210202ST 1
Figure 35: Dissolved Oxygen; Existing conditions and TMDL conditions with 95% load reductions 1 I
Saddle Creek (1497) Allocations i The TMDL process quantifies the amount of a pollutant that can be assimilated in1 a waterbody, identifies the sources of the pollutant, and recommends regulatory or ot er actions to be taken to achieve compliance with applicable water quality standards bas d on the relationship between pollution sources and in-stream water quality conditions. I A TMDL can be expressed as the sum of all point source loads (Waste Load Allocatio ), non-point source loads (Load Allocation), and an appropriate margin of safety (MO 1 ),
which takes into account any uncertainty concerning the relationship between effluent limitations and water quality:
TMDL = C WLAs + C LAs + MOS I
The objective of a TMDL is to allocate loads throughout a watershed so that appropriate water quality standards achieved. 40 CFR $130.2 (i) states in terms of mass per time (e.g. kilograms per day), toxicity, The TMDL for Saddle Creek, W I D 1497, is expressed in for the LA and WLA.
Table 16: Saddle Creek (1497) TMDL allocations
WLA 17
Nitrogen and Total Phosphorus) I BOD
TMDL
95% reduction
Waste Load Allocations (Regulated with treatment plant and stormwater permits) There is one permitted continuous point source facility in the Saddle Creek (1497) watershed. It is Polk Nursery Company, Inc. permit number FLO13 1385. However, this facility has had no discharge in the period of record of 2003 through 2005 in the EPA PCS database. The permit requirements require monitoring only with no specific limits given. According to this TMDL analysis, there is no available assimilative capacity in Saddle Creek, and thus there should be no discharge of nutrients or oxygen consuming wastes. This 95% reduction applies to the permitted discharge, or existing discharge if there is no permit limit.
95% reduction
Load Allocations (Non- Regulated) The LA for DO is equal to the water quality standard of a minimum of 5 mgll. For nutrients the target is total nitrogen and total phosphorus, and a 95 percent reduction in both nutrients and BOD is recommended to achieve the water quality standard for DO.
Marnin Of Safetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMD
I the following information was considered in determining the margin of safety. 4
The worst case condition in the 5 year simulation was addressed to meet standa 1. ds However, the boundary DO was assumed to be 5 mgll which is not always trud (These boundaries are the inflows to the model at the upstream end and I
throughout the modeled stream segments via tributaries and direct runoff that 4 e not affected by the model.) I
Continuous
95%
95% reduction
MS4
95%
LA ' MOS
reduction 95%
95% reduction
reduction reduction I implicit
95% reduction implicit
Decreases in the watershed loads are expected to also improve the DO at the model boundaries i A 95% reduction results in average TP of 0.09 mgll and average TN of 0.16 mg1l.l This TN of 0.16 is below the EPA recommended ecoregion reference condition of' 0.58 and is likely not achievable. Model predictions show that a reduction to this 'IN reference value of 0.58 does not result in the DO meeting the water quality standard.
The two worst cases for DO occurred in 2000 and 2002, which represent a dry year and a wet year in this 5 year period (see Figure 13). If the boundary DO is assumed to be 3 ther even with complete removal of sources Saddle Creek would not recover to the 5.0 DO standard. What does all this mean? Basically, there are unknowns that may have significant implications on this analysis, and these cannot all be quantified. Rather than assign an arbitrary explicit margin of safety, the TMDL should be reevaluated after reductions have been implemented and additional data has been collected. The margin of safety for this TMDL is implicit by basing the TMDL reductions on the worst case in the 5 year analysis period, and by specifyiilg nutrient reductions that would result in TN and TP concentrations near or below the EPA ecoregion reference conditions.
Critical Conditions Critical conditions were considered by analyzing several years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed.
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, wet, normal, and dry conditions.
SADDLE CREEK BELOW LAKE HANCOCK (SADDLE CREEK SUBBASIN) WBID 1623K TURBIDITY, TSS
Saddle Creek (1 623K) description, Water Oiialitv And Environmental Data, and Source Assessment
i
I W I D 1623K is on the 1998 303 (d) list as impaired for total suspended solids (TSS) anh turbidity. Because one of the prime factors affecting turbidity is TSS, the factors affectiqg TSS will also affect turbidity. In addition, organic matter contributes to turbidity. Typical non-point sources of turbidity include:
High flow rates and flooding Soil erosion Aquatic plants Urban development (outside of Phase I or I1 MS4 discharges)
There are no facilities permitted to discharge effluent to surface waters in WBID 1623 . However, WBID 1623K (Saddle Creek below Lake Hancock) lies within the jurisdicti n of a Phase I MS4 permit (FLS000015) which includes the City of Bartow, Florida, P Ik County, and FDOT District 1. 1
In response to storm events, Municipal Separate Storm Sewer Systems (MS4s) discharge pollutants that cause elevated TSS and turbidity. Currently, MS4s serving populations greater than 100,000 people are required to obtain a storm water permit. Small MS4s serving urbanized areas were required to obtain permit under the Phase I1 storm water regulations. An urbanized area is entity with a residential population of at least 50,000 people and an density of 1,000 people per square mile.
Debris from roads and other impervious surfaces may be carried to streams during storm events and contribute to elevated turbidity and TSS concentrations. Erosion of nearby soils and the stream's bed and banks may also release sediment that contributes to turbidity and suspended solids. High nutrient loadings may cause imbalances in flora an fauna, which elevate turbidity via increased frequency and intensity of algae blooms.
Almost half of the land area in the Saddle Creek watershed is used for agriculture (45.8%), though wetlands (21%), forest (14%), and barren/extractive uses (12%) also constitute significant fractions. The lack of association between turbidity1TSS and high flows, and the significant association between turbidityITSS and chlorophyll, suggest th t nutrients are important non-point source pollutants contributing to elevated turbidity an TSS in Saddle Creek. WBID 1623K is also 303(d)-listed for nutrient and D.O. impairment. TMDLs for those parameters are detailed in a separate document. ! The flow rate of a waterbody may be a prime factor influencing turbidity and running water can carry more particles and larger-sized sediment. Heavy up sand, silt, clay, and organic particles from the land surface and carry surface waters. Flow rates are higher in streams draining proportion of impervious surfaces since natural settling areas allows sediment previously trapped by vegetation to be Particulate matter from bottom sediments may become when the speed or direction of the water current levels.
Flooding may also contribute to elevated turbidity and TSS concentrations. ~ncrea+d flow rates cause erosion of stream beds and banks. During flood events, stream b s become saturated and as the flow recedes, forces are no longer present to balance p re pressures in the stream bank soils. Over time stream banks fail through mass-wast'ng "; processes as the channel widens in an attempt to compensate for the increased volume. As flow waters recede, they will also carry inorganic and organic particles the land surface back to the stream. As discussed above, elevated turbidity and WBID 1623K are not strongly associated with high flows. In fact, many of the high turbidity were associated with low flow conditions.
Soil erosion can be caused by disturbance of a land surface, such as construction activities, forest fires, logging and mining. In the absence of adequate sediment and erosion control measures, the eroded soil particles can be carried by stormwater to a stream, resulting in elevated amounts of suspended particles and adding to turbidity.
Stormwater runoff from urban areas can be a significant source of TSS loadings to a stream. Watersheds with a large percentage of impervious land cover experience increased peak stormwater discharge rates and volumes resulting in erosion of the streambed and failure of stream banks.
Algae can contribute to elevated turbidity levels. Nutrients allow algae and other plants to grow in streams, a process which is beneficial to some extent. However, chronic enrichment with excess nutrients can promote overgrowth. Algae may out-compete wit other aquatic plants, causing an imbalance in the flora and fauna, and algae may absorb too much dissolved oxygen from the water, leading to eutrophic conditions. Algal production is enhanced when nutrients are released from bottom sediments during seasonal turnovers and changes in water current. Because algae also require light, too
Saddle Creek in WBID 1623K receives flows from Lake Hancock, a large (4,500 acres) hypereutrophic lake north of Bartow and southeast of Lakeland. These flows are regulated via a weir which was completed in 1962 and is designated Structure P-1 1. Saddle Creek then joins with Peace Creek to form the Peace River just northeast of the City of Bartow. The Peace River then travels inore than 100 miles until it empties into Charlotte Harbor, a SWIM priority water body, and an "estuary of national significance' via its inclusion in the U.S. EPA's National Estuary Program.
I
Lake Hancock has long been characterized as one ofthe most polluted lakes in Florida. Concerns about the lake's poor water quality date back to at least the 1950's (ERD, 1999). Water discharged from Lake Hancock has been identified as a major impact to both the Peace River and Charlotte Harbor (Coastal Environmental, 1995; ERD, 1999).
much turbidity may limit algal growth. Fast flow rates inhibit algae, because they are n able to maintain their position near the surface (where there is more available light) in turbulent water. In addition, decaying plants and animals present in a waterbody releas suspended organic particles and can contribute to turbidity.
Water quality in Lake Hancock has remained "poor" over the past 30 years, with TSI values consistently well above the hypereutrophic TSI threshold value of 70. The influence of Lake Hancock discharges has contributed to poor water quality in South Saddle Creek and the Upper Peace River based on elevated chlorophyll-a concentrations, high BOD values, and low DO (SWFWMD, 2000).
According to the Southwest Florida Water Management District, not only do discharges from Lake Hancock adversely affect water quality in south Saddle Creek and the upper Peace River, nitrogen loads in the upper Peace River (above Bartow) were estimated to contribute about 21 percent of the total point and non-point source loads for the entire Peace River (Coastal Environmental, 1995). Further work by the SWFWMD has supported the importance of Lake Hancock discharges on water quality in Charlotte Harbor, as nitrogen yields (kg TN / ha / yr) from the Lake Hancock watershed (see P-1 1 in Figure 36) are more than twice as high as most sub-basins in the Peace River.
TN Yields wl different watersheds (WY 2003)
I I
Figure 36: Watershed-level nitrogen yields for Peace River sub-basins (data from SWFWMD).
Saddle Creek (1 623K) Analvtical Avproach/Model Selection And Develovment An excessive amount of material suspended in a water column can cause various water quality issues. Measurements of total suspended solids (TSS) account for particles sucll as silt and clay, algae, fine organic debris, and other particulate matter that will not pas:; through a 2-micron filter. Turbidity is a measure of how much this suspended material decreases the passage of light through the water (i.e. water clarity).
The Southwest Florida Water Management District has spent considerable time and resources examining nutrient budgets and water quality restoration strategies for both Lake Hancock and the waters downstream from Lake Hancock. They have decided to develop a Lake Hancock outfall treatment project. This project involves constructing a treatment system to improve water quality leaving the lake. The first step in the process to investigate the feasibility of various water treatment methods, which may include constructed wetlands, sand filter systems, chemical treatment followed by settling, aquatic plant-based water treatment technology or other physical treatment processes. The second step involves the final design, engineering, environmental permitting, and preparation of the construction documents for the selected treatment methods. Construction of the treatment system could commence after the permits are issued. The treatment system is to be constructed on the Old Florida Plantation property purchased
is
-)y the District in 2003. This treatment system along with the other water quality projects f+r Lake Parker and Banana Lake (diversion of the City of Lakeland's wastewater plant outfall, and whole-lake sediment removal project) will help improve the water quality in Saddle Creek and the Peace River. The elevated turbidity and TSS values in Saddle Creek are a direct result of algal biomass and resuspended sediment 1999).
The F.A.C. does not have specific criteria for Total Suspended Solids (TSS). In lieu o TSS criteria, turbidity is used as a surrogate to assess waters for TSS. For Class 111 waters, turbidity must be less than or equal to 29 NTU above natural background conditions. Typically, an unimpaired reference stream with similar characteristics to th impaired stream is used to establish natural background turbidity and set the TMDL target. Due to the abundance of residential and urban development, agriculture, minin and other such landuses in the area, most of the streams that serve as lake outlets are unsuitable for use as a reference. Other streams that seem like promising candidates do not have turbidity or TSS data available for them. The best potential reference for whi data are available appears to be Lake Arbuckle.
At approximately 3,800 acres, Lake Arbuckle is considered one of Polk healthier waterbodies. The lake's trophic state index (TSI) and other water support this claim. The TSI is a scale of numbers between 0- 100 that are biological productivity of lakes based on their concentrations of total phosphorus, and chlorophyll. The average TSI of Lake Arbuckle is 53, lake in the "good" category, fully supporting its uses (Figure 37). TSI and 69 are considered "fair" while values above 70 are considered
I Seasonal TSI values in Lake ~rbuckle I
winter
fall
summ r
- t Year
L - - . _ . - - -- - - -
Figure 37. 'Seasonal TSI values in Lake Arbuckle. I,
Arbuckle Creek receives water from the south end of Arbuckle Lake (Figure 38). Although Arbuckle Creek is much longer than Saddle Creek below Lake Hancock, and its nutrient concentrations increase by the time it flows into Lake Istokpoga (Highland County), the portion of Arbuckle Creek just below the outlet from Lake Arbuckle is a suitable turbidity reference for Saddle Creek, which receives its water from the approximately 4,500 acre Lake Hancock (Figure 38). Based on the available water quality data, Arbuckle Creek is not impaired for turbidity, dissolved oxygen or nutrient
at the Arbuckle Creek Boat Ramp station (2lFLAVONAPAFRTMDLl) near its headwaters. The chlorophyll A values are low, ranging from 1 to 21 pgll and 3.3 pg/l. These low chlorophyll values do not indicate the presence of algal blooms, which would increase the chlorophyll concentration. Dissolved oxygen levels are all above the standard of 5.0 mg/l. The turbidity measurements do not indicate a problem with excessive suspended materials, as only 1 of the 20 measurements is Table 17 is a summary of the available water quality data for this station. All of the dat was collected between 3/30/2004 and 3/17/2005.
Table 17. Water Quality Data for the Arbuckle Creek at Boat Ramp Station.
I Chlorophyll A (mg/l) 1 2 1 3.3 4.8 1
STN: 2 lFLAVONAPAFRTMDL1
I Dissolved Oxygen (mg/l) 5.7 9.8 7.5 1.4 7.5 1
Minimum
The background turbidity concentration used to develop a target for Saddle Creek belo Lake Hancock is the 5oth percentile value observed at Station 2 1 FLAVONAPAFRTMDL 1 in Arbuckle Creek. The 5oth turbidity value there is 5.2 NTTJ (Table 17 or Table 19). for Saddle Creek would equate to 29 NTTJ above the background value 34.2 NTU. A margin of safety (MOS) of 10 percent is applied to the account for uncertainty in the analysis, resulting in a final target of 30.8 NTTJ. This target is not appreciably higher than 29 NTU, which is the water background turbidity is considered. Consequently, the approximately the same TMDL as setting the target background allowance as an implicit MOS.
Nitrogen Total as N (mgll) Phosphorus, Total as P (mgll) Turbidity (NTU)
Maximum
0.78
0.04 0.0
Mean
2.27
0.23 37.4
Standard Deviation Median
1.27
0.1 1 8.2
0.4 1
0.05 9.0
1.17
0.10 5.2
$0 ' 0
20
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In order to use turbidity as a surrogate for TSS in Saddle Creek, the data should show a correlation between the two parameters. A review of the data indicates that high TSS concentrations are measured during times of elevated turbidity levels. The correlation between TSS and turbidity concentrations in Saddle Creek is shown in Figure 39. A linear trend-line is drawn'through the data, and the equation defining the line and the coefficient of correlation are shown. The higher the coefficient of correlation, the greai confidence there is that the regression line describes the data well. The TSS target for Saddle Creek may be calculated using the trend-line equation shown in Figure 39 and a turbidity target of 30.8 NTTJ. The resulting TSS target is 58.6 mg/L. TSS data for Arbuckle Creek were not available.
1623K Saddle Creek Below Lake Hancock Correlation between Turbidity and TSS
0 50 100 150 200 2 50
TSS (mgll)
Figure 39. Turbidity and TSS measurements in Saddle Creek (WBID 1623K) 1
FDEP maintains ambient monitoring stations throughout the Saddle Creek basin. All data collected at monitoring stations within WBID 1623K (Saddle Creek below Lake Hancock) are used in the analysis (Table 18). The monitoring station on Arbuckle Cre k that was used as a reference is also listed. Data collected during the Group 3 listing cy le (i.e., January 1997 through December 2003) and any more recent data, if available, are considered in the data assessment for both Saddle and Arbuckle Creeks. Table 19
from the turbidity and TSS targets in Saddle Creek.
I provides a statistical summary of the data and includes the percent of samples that devi
Table 18. Monitoring Stations used in the Development of TSS TMDL I I I A . . I I I
Number Samples I I Station ID/Name
Impaired Stream: Saddle Creek (WBID 162330 2 1 FLP0LKP.C. CANAL9 PC Canal 1 Mi W. Old Bartwlegle LK Cutoff Rd. 2 1FLSWFDFLO 3 7 72 0 Saddle Creek 21FLSWFDFL00118 Saddle Creek at STR P-1 1 21FLTPA 27552158149358 TP- 166 Saddle Creek Reference Strea:m: Arbtlckle Creek (WBID 1685A) 2 1 FLAVONAPAFRTMDL 1 Arbuckle Creek Boat Ramp
In many streams, high turbidity occurs in response to rainfall events, due to sediment runoff and/or elevated stream flow. To evaluate the strength of this association for Saddle Creek below Lake Hancock, turbidity measurements were compared against rainfall measured at the National Oceanic and Atmospheric Administration (NOAA) Station 3855 (COOP #: 080478) near Bartow, FL, and against flow measured at the United States Geologic Survey (USGS) gage 02294491 (Saddle Creek at Structure P-11 Near Bartow, FL). While rainfall events were associated with elevated flow, there was no clear association between rainfall and turbidity or flow and turbidity. Excursions of the turbidity target occur even under low flow conditions. In some instances, turbidity i elevated above the target at moderate flows. More often, increased flow rates are
measured in Saddle Creek below Lake Hancock and flow measured at USGS gage associated with a decrease in turbidity. Figure 40 shows the correlation between turbidi y
Creek.
1 02294491 (Structure P-1 l), a weir located at the outlet of Lake Hancock into Saddle ~
I
Parameter Evaluated
TSS, Turbidity
TSS, Turbidity
TSS, Turbidity
TSS, Turbidity
Turbidity
- t 8
WBlD
Impaired
1623K
Reference
1685A
AVBIIB ule Sampling
Period
1997 - 2004
1997 - 2002
1997 - 1998
2003 - 2003
2004 - 2005
Note: Turbidity target: 30.8 NTU; TSS target = 58.6 mg/L Min = minimum value; Max = maximum value; Mean = average value
Parameter
Stream: Saddle
TSS (mg/L)
Turbidity (NTU)
Strea:m:
Turbidity (NTU)
3 8
76
16
4
20
No. of Samples
Creek
9 3
122
Arbuckle Creek
2 0
I
Min.
(WBID
1
0.8
(WBID
0.0
Mean
49
26
8.2
Max.
1623K)
278
240
1685A)
37.4
5oth percentile
33
22
5.2
# Samples Exceeding
Target
2 6
3 7
-
Percer Exceeding
Target
28%
30%
1 WBID 1623K Saddle Creek below Lake ~ a n c o c k l
----- rz; . Turbidity -Turbidity Target ' -- A --
Figure 40. Turbidity and flow measured in Saddle Creek below Lake Hancock. Note: The scale for turbidity excludes one very high measurement of 240 NTU from 8191200 1
Elevated turbidity in WBID 1623K (Saddle Creek below Lake Hancock) appears to be due, in large part, to algae. WBID 1623K recei;es water directly from Lake Hancock, ~ which is known to be hypereutrophic and have extremely poor water quality. Accordi d g to FDEP's 2003 Basin Status Report for the Peace River, water discharged from Lake ~ Hancock has high concentrations of phytoplankton (microscopic, single-celled algae th t float). Saddle Creek is also verified as impaired for dissolved oxygen and nutrients (FDEP, 2003).
a The data for WBID 1623K support an association between turbidity and chlorophyll A (Figure 4 1). Chlorophyll is the green pigment in plants that allows them to create ener y from light. Higher concentrations of chlorophyll in water are indicative of algal bloo s.
in Saddle Creek below Lake Hancock. The F-distribution statistic was 12.18 and the
,B An F-test was performed to compare the variances of turbidity and chlorophyll measur d e critical F(0.05,1,85) was 4.0, indicating that there is a relationship between turbidity add chlorophyll-A at an alpha of 0.05. The probability that this relationship occurred by 1 chance is low- only 0.00077. Nutrient and dissolved oxygen (D.O.) TMDLs for Lake Hancock and Saddle Creek are discussed in a separate report.
1623K Saddle Creek Below Hancock I 1 Correlation between Turbidity and chlorophyll-A 1 -
Figure 41. Correlation between Turbidity and Chlorophyll-A in WBID 1623K.
This TMDL assumes that it is infeasible to calculate numeric water quality-based efflue limitations for turbidity and TSS from storm water discharges. Therefore, in the absenc of information presented to the permitting authority showing otherwise, the WLA for th City of Bartow is expressed in narrative form (e.g., as best management practices), provided that (1) the permitting authority explains in the permit fact sheet the reasons it expects the chosen BMPs to achieve the aggregate wasteload allocation for these stormwater discharges; and (2) the state will perform ambient water quality monitoring for TSS and turbidity for the purpose of determining whether the BMPs in fact are achieving such aggregate wasteload allocation.
The percent reduction calculated for all nonpoint sources is assigned to the MS4 as loadings from both sources typically occur in response to storm will be responsible for reducing only the loads associated with stormwater outfalls it owns, manages, or otherwise has responsible control. MS4s are not responsible for reducing other nonpoint source loads within its jurisdiction. All future MS4s the area are automatically prescribed a WLA equivalent to the percent to the LA.
The calculation of a TMDL for turbidity and TSS in Saddle Creek below Lake follows a reference stream, approach to develop a turbidity target. By reducing and TSS in Saddle Creek WBID 1623K to levels observed in a non-impaired stream, water quality standards for those parameters should be attained in the impaired WBID. The TMDL is expressed as the percent reduction necessary to achieve the reference target. In lieu of specific TSS criteria, and given the strong relatioilship and TSS, the TMDL percent reduction is applicable to both parameters. It is expected
that actions taken to reduce turbidity will result in reduction of suspended solids (TSS), 1 and vice versa.
The TMDL for Saddle Creek WBID 1623K is expressed as a percent reduction. Following this method, the percent reduction required for the existing condition of the waterbody to meet the target condition is calculated using the following equation:
Percent Reduction (%) = (existing condition -target) / existing condition * 100 1 The 9oth percentile concentration of all turbidity measurements in WBID 1623K is used to represent its existing condition. The 9oth percentile implies 90 percent of the values are lower than this level, and that 10 percent are higher. EPA 303(d) listing guidance allows criteria to be exceeded in less than 10 percent of the samples. The targe condition was determined from the reference stream as described above.
The TMDL process quantifies the amount of a pollutant that can be assimilated in a waterbody, identifies the sources of the pollutant, and recommends regulatory or other actions to be taken to achieve compliance with applicable water quality standards based on the relationship between pollution sources and in-stream water quality conditions. A TMDL can be expressed as the sum of all point source loads (Waste Load Allocations), non-point source loads (Load Allocations), and an appropriate margin of safety (MOS), which takes into account any uncertainty concerning the relationship between effluent limitations and water quality:
TMDL = C WLAs + C LAs + MOS 1
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 9 130.2 (i) states that TMDLs can be express in terms of mass per time (e.g. pounds per day), toxicity, or other appropriate measure. Because the target is based on turbidity, which is not a concentration but rather a of water clarity, the TMDL for Saddle Creek is expressed in terms of a percent
Existing conditions are characterized by the 9oth percentile of all in WBID 1623K (Saddle Creek below Lake Hancock). The 901h TSS levels in Saddle Creek WBID 1623K are about 49 NTU and 99
Background conditions in Saddle Creek are based on the 5oth percentile (median) turbidity measured in the Arbuckle Creek reference stream, which is 5.2 NTU.
Saddle Creek (1 623K)Allocations
The TMDL components are expressed as the percent reduction required to meet the turbidity target. By achieving this reduction in turbidity, the TSS concentrations in Saddle Creek WBID 1623K should be reduced to levels necessary for attainment of the designated uses of the stream. There are currently no NPDES facilities discharging in Saddle Creek below Lake Hancock and therefore a continuous WLA is not assigned. The TMDL components for WBID 1623K (Saddle Creek below Lake Hancock) are summarized in Table 20.
Saddle Creek below Lake Hancock TurbidityITSS
(WBID 1623K) reduction
Waste Load Allocations (Regulated with treatment plant and stormwater permit$ 1 There are no regulated continuous point sources currently discharging to WBID 1623K (Saddle Creek below Lake I-Iancock), so a WLA for continuous facilities was not applicable (NIA). Any future facility permitted to discharge TSS and turbidity in the 1
I Saddle Creek watershed will be required to meet end-of-pipe limits that do not cause or contribute to turbidity and TSS impairment in the stream. I WLAs are expressed separately for continuously discharging facilities and MS4 areas as the former may discharge during all weather conditions whereas the later discharges in response to storm events. The Waste Load Allocation (WLA) for the MS4 is expressed in terms of percent reduction. Given the available data, it is not possible to estimate loadings coming exclusively from the MS4 area. Although the aggregate wasteload allocation for storm water discharges is expressed in numeric form, as a percent reduction, based on the information available today, it is infeasible to calculate numeric WLAs for individual storm water outfalls because discharges from these sources can be highly intermittent, are usually characterized by very high flows occurring over relative] short time intervals, and carry a variety of pollutants whose nature and extent varies according to geography and local land use. Water quality impacts, in turn, also depend on a wide range of factors, including the magnitude and duration of rainfall events, the time period between events, soil conditions, fraction of land that is impervious to rainfal other land use activities, and the ratio of storm water discharge to receiving water flow.
Phase I MS4 permit FLSOOOO15, which covers the City of Bartow, Polk County, and FDOT District 1 (as well as other co-permittees) overlaps with WBID 1623K. The WLh assigned to the MS4 area is expressed as the percent reduction in turbidity required to attain the target. With the available water quality data it is not possible to calculate the WLA in terms of a load, or to isolate the load discharging exclusively from the MS4 ar
Load Allocations (Non- Regulated) Nonpoint sources may contribute excess nutrients and sediment to the stream during storm events. Modification of the landuse from pervious to impervious surfaces results higher peak flow rates that wash soil particles and other debris into the stream and erod the stream bed and banks. Instream production of algae is a significant source of turbidity and TSS in Saddle Creek. Much of the land in WBID 1623K is used for agriculture, and it receives water from Lake Hancock, which is known to be hypereutrophic and have poor water quality due to nutrient impairment.
The load allocation for WBID 1623K (Saddle Creek below Lake Hancock) is expressed as the percent reduction in turbidity necessary to achieve water quality standards. By achieving this reduction in the sources contributing to turbidity, the TSS concentrations in Saddle Creek WBID 1623K should also be reduced.
Marnin Of Safety There are two methods for incorporating a MOS in the analysis: a) implicitly incorpora the MOS using conservative model assumptions to develop allocations; or b) explicitly specify a portion of the TMDL as the MOS and use the remainder for allocations. An
(from 34.2 to 30.8 NTU). An implicit MOS was also included in the analysis by using
I explicit MOS was used in the analysis as the target turbidity was reduced by 10 percent
the 90" percentile turbidity concentration to represent existing conditions in the stream. This is considered somewhat conservative as this value is exceeded in less than 10 percent of the samples. EPA 303(d) listing guidance allows criteria to be exceeded in less than 10 percent of the samples. The reference stream approach yields approximate:.y the same TMDL as setting the target turbidity at 29 NTU and reserving the background allowance as an implicit MOS.
Critical Conditions Critical conditions for turbidity and TSS are usually created during and shortly after storm events. However, in Saddle Creek WBID 1623K, turbidity is elevated even at lo flows. Elevations in turbidity and TSS appear to be related to algal concentrations. Although algal blooms are more likely to occur during low flow conditions, loading of the excess nutrients that promote them may occur during storm events. Controlling nutrient concentrations in Lake Hancock will be critical to achieving water quality standards for turbidity and TSS in Saddle Creek below the lake.
Recommendations Since the turbidity and TSS impairment appears to be a bi-product of the nutrient impairment, controlling sources contributing to nutrient impairment should be the focu of implementing this TMDL. Control of algal blooms resulting from excess nutrients i
Seasonal Variation Seasonal variation was incorporated in the analysis by using the entire period of record data collected in the WBID. Water quality data was collected at various flow regimes during all seasons.
of
the stream should lower turbidity and TSS concentrations. A TNIDL for nutrients and 1 dissolved oxygen in WBID 1623K is described in a separate document.
FDEP employs the Basin Management Action Plan (B-MAP) as the mechanism for developing strategies to accomplish the necessary load reductions. Components of a B- MAP are:
Allocations among stakeholders Listing of specific activities to achieve reductions Project initiation and completion timeliness Identification of funding opportunities Agreements Local ordinances Local water quality standards and permits Follow-up monitoring
PEACE CREEK TRIB CANAL (PEACE CREEK SUBBASIN) WBID 1613 LOW 1 DO, NUTRIENTS
Peace Creek Trib Canal description, Water Quality Ant1 Environmental Data, and Sorirce Assessment WBID 1613 is on the 1998 303 (d) list as impaired for nutrients and low DO. This area overlaps the MS4 area from the town of Lake Wales and may receive discharges from these storm sewer systems. There are no NPDES permitted facilities discharging directly into this W I D . The landuse in WBID 161 3 is 15.5 percent urban, 49.1 percent agriculture, 4.4 percent rangeland, 6.5 percent forest, and 19.9 percent wetlands. Figure 48 shows the stream network for this watershed that includes WBIDs 16 1 3, 1626, 16 17, 1580, and 1539.
r reuen qu.1, xaa.n aaeaa :PP aan8r.q
E l 6 1 3 Water Quality ad i Chloro~hvll (un/ll -Water Quality Comparison 1
Figure 46: 6 out of 8 observations exceeded the IWR comparison value for chlorophyll-a.
~ B I D 1613 Water Quality Data] * Chlorophyll Corrected (ugll) -Water Quality cornparisol( -.-pp-pp--p-pp--
Figure 47: Only 1 value of 14 observations of Chlorophyll-a corrected was above the IWR comparison value of 20 ugll.
The average TN:TP ratio at station 21FLPOLKPCCANAL3 is 6.8 and this indicates th system is borderline nitrogen limited or co-limited by nitrogen and phosphorus. The average TKN is 3.29 mgll and the average TP value is 0.50 mgll (see Figure 90 and Figure 91). The total phosphorus value is less than one third the EPA ecoregion averag t
of 1.6 mgll TP and the TKN value is about three times higher than the ecoregion value of j 1.1 mgll according to a query of the USEPA ecoregion nutrient data for ecoregion XI1 , rivers and streams in Florida , (l~ttp://www.epa.govlwaterscience/criteria~nutrient/databaselselect ecoregion.htm1). The average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the ~ FDEP IWR 19.1 database is 1.17 and the average TP is 0.45 mgll (see Table 5). For blackwater streams in this basins group the average TKN is 1.65 and the average TP is , 0.41 mgll. ~ Figure 45 shows 82 percent of the DO observations were below the 5.0 mgll standard. ~ Figure 46 and Figure 47 show 7 chlorophyll-a observations were above 20 ugll. Most of the water quality observations were recorded before 2000, with only about nine observations since. Because there is limited data in this WBID, additional data from the watershed was used to develop the TMDL. This water body drains to the Peace Creek I Drainage Canal WBID 1539 as shown in Figure 48, and the TMDL is based on this ;
whole watershed. Historic data in the watershed show that the DO has been commonly 1 below the 5.0 mgll standard for at least the past fifty years. The low DO in this canal system is likely a result of natural processes in the wetlands and groundwater draining into this canal, with further degradation from anthropogenic sources. Even though much of the problem is non-anthropogenic, a TMDL needs to show the amount of pollutants a
I water body can receive and still meet the water quality standard. It is recommended that site specific alternative criterion for the whole Peace Creek Drainage Canal watershed b developed. However, until a more appropriate criterion is developed the 5.0 mgll
i standard will be targeted, and this TMDL calculation will target the 5.0 mgll.
Pence Creek Tribtrtnw Cnnnl Altcilvtical Appronclt/Moclel Selection And Developmen
The regression approach selected here combines the known kinetic relationships for the 1 sources and sinks of dissolved oxygen with'correlation and regression statistics. Based o the known mechanisms of the sources and sinks of DO, a simple regression model is n developed. The variation in the observed DO is explained by variables such as temperature, BOD, chlorophyll, nutrients, organic carbon, and flow. Statistics are used t explore the relationships at each water quality monitoring station in the watershed depending on the water quality parameters that were recorded.
The relationship between DO and temperature is well known, and the relationship between DO, TOC and nutrients can be explained by plant nutrient uptake, photosynthesis, respiration, growth and death and decay. These kinetic relationships arel part of the principal components of the DO budget, and these are the mechanisms typically included in mechanistic models of DO. The presence of plants in the Peace Creek Tributary Canal (see Figure 42 and Figure 44), and the observed wide variations DO saturation (observed data show DO saturation ranging from 2 to 78 percent), that the DO is greatly influenced by plant photosynthesis and respiration. Due to the limited data in this WBID, and since this WBID is part of the Peace Creek Drainage Canal Watershed, the TMDL is based on the larger Peace Creek Drainage Canal
Watershed. Figure 48 shows the Peace Creek Tributary Canal (WBID 16 1 3) and other WBIDs that are included in the Peace Creek Drainage Canal Watershed.
As described in the Peace Creek Drainage Canal, WBID 1539 section, the TMDL analysis indicates that a 75 percent reduction in TN and TP will result in DO meeting the standard of 5.0 mg/l all of the time. It is recognized that these reductions are not necessarily achievable, but such reductions would be necessary to meet the current water quality standard. If a site specific alternative water quality criterion is developed for this water body, the TMDL can be revised.
A / Saddle Creek
1 0 1 2 Miles - WBlDs
Figure 48: The Peace Creek Tributary Canal, WBID 1613 receives flow from Lake Effie Outlet and can flow two directions, through WBID 1626 or directly to the Peace Creek Canal WBID 1539.
Peace Creek Trib Canal Allocations The TMDL process quantifies the amount of a pollutant that can be waterbody, identifies the sources of the pollutant, and recommends actions to be taken to achieve compliance with applicable water on the relationship between pollution sources and in-stream TMDL can be expressed as the sum of all point source non-point source loads (Load Allocation), and an which takes into account any uncertainty limitations and water quality:
TMDL = C WLAs + C LAs + MOS I
The objective of a TMDL is to allocate loads among all of the known pollutant sourc&s throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 8130.2 (i) states that TMDLs can be expre in terms of mass per time (e.g. kilograms per day), toxicity, or other The TMDL for Peace Creek Tributary Canal, WBID 161 3, is percent reduction for the LA and storm-water WLA.
Table 21: WBID 1613 Peace Creek Trib Canal TMDL allocations
WLA 7
Waste Load Allocations (Regulated with treatment plant and stormwater permits) 1 There are no regulated continuous point source facilities in the Peace Creek Trib Cana watershed. Permitted MS4 discharges are allocated the same percent reductions as the non-point source load.
Pollutant TMDL Continuous Nutrients (Total 75%
Nitrogen and Total reduction NIA
Load Allocations (non- Regulated) 1 I
LA
75% reduction
MS4
75% reduction
For nutrients the target is total nitrogen and total phosphorus, and a 75 percent reducti is recommended to achieve the water quality standard for DO.
MOS
implicit
Marpin Of Safe4 A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDh the margin of safety is considered to be implicit since very large reductions are recommended. 1 I Critical Conditions Critical conditions were considered by analyzing several years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed.
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, t, normal, and dry conditions. XI WEST WALES DRAINAGE CANAL (PEACE CREEK SUBBASIN) WBID 162 LOW DO, NUTRIENTS t West Wales Drainage Canal description, Water Orialitv And Environmental Dntn, nnrt Source Assessment WBID 1626 is on the 1998 303 (d) list as impaired for low DO and nutrients. Near the town of Lake Wales, but not in the MS4 area, and there are no other NPDES facilities discharging in this WBID. The landuse in WBID 1626 is about 60 percent agriculture, and 30 percent wetlands. Figure 48 shows the stream network for the West Wales Drainage Canal. This canal receives flow from Lake Effie Outlet via the Peace Creek Tributary Canal and then empties to the Peace Creek Drainage Canal.
Figure 49: West Wales by Peace Creek Trib Canal Figure 50: West Wales Drainag Canal looking downstream 1
5/7/90 1/31/93 1 0128195 7/24/98 411 9/01 1 11 4/04 1 011 0106
date 1 I
Figure 53: DO observations at each of the stations in WBID 1626 are almost always below the water quality standard of 5.0 mgll.
Figure 52 and Figure 53 show 76 percent of the DO observations were below the 5.0 mgl'l standard. IWR data also shows that 3 out of 13 observations of chlorophyll-a were above 20 ugll. The average TKN is 1.86 mgll and the average TP value is 0.1 1 mgll (see Figure 90 and Figure 91). The total phosphorus value is less than one tenth the EPA ecoregion average of 1.6 mgll TP and the TKN value is higher than the ecoregion value of 1.1 mgll according to a query of the USEPA ecoregion nutrient data for ecoregion XI1 rivers and streams in Florida (http://www.epa.~ov/waterscience/criterialnutrient/database/select ecoreaion.htm1). The average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the FDEP I WR 19.1 database is 1.17 and the average TP is 0.45 mgll. For blackwater streams in this basins group the average TKN is 1.65 and the average TP is 0.41 mgll.
West Wales Drainnne Canal Analytical Approach/ Model Selection And Development What type of analysis is appropriate for linking the water quality target and pollutant sources? Methods for linking the target and impairment sources include empirical approaches based on observed information, simple approaches, screening level model analysis, and detailed modeling. TMDLs can include one or more of these approaches to ,
characterize this linkage between a target and source (U.S.Environmenta1 Protection Agency. 2001 Protocol for Developing Pathogen TMDLs. EPA 841-R-00-002. Office f Water (4503F), United States Environmental Protection Agency, Washington, DC. 132 PP .) I The approach selected here combines the known kinetic relationships for the sources an sinks of dissolved oxygen with correlation and regression statistics. Based on the kno mechanisms of the sources and sinks of DO, a simple regression model is developed. variation in the observed DO is explained by variables such as temperature, BOD, chlorophyll, nutrients, and flow. Statistics are used to explore the relationships at each water quality monitoring station in the impaired W I D depending on the water quality parameters that were recorded. The relationship between DO and temperature is well known, and the relationship between DO and nutrients can be explained by plant uptake, photosynthesis, respiration, growth and death and decay.
Data collected at station 2 1 FLTPA 25020265 indicates that DO can be reasonably predicted with TP, and temperature. The F-distribution statistic was determined to be 13.286 and the critical F(0.05,2,4) is 6.9, meaning that there is a relationship between observed DO values and known values of water temperature and TP, at an alpha of 0.05 Also, the probability that this data relationship occurred by chance is only 0.017. Data from station 2 lFLPOLKP.C.CANAL4 also shows a relationship between DO and temperature and TP. However, the relationship to TP isn't strong enough to explain the low DO. That is, the regression equation indicates that a decrease in TP improves DO, but not enough to meet the 5.0 mgll all of the time.
The targeted nutrient was TP since the TN:TP ratio was high. Based on phytoplankton I stoichiometry, a TN:TP ratio less than 7.2 generally indicates a nitrogen limitation and high ratio indicates that nitrogen is abundant and the system is phosphorus limited. For station 21FLTPA 25020265 the TN:TP ratio was 23, and data from station 21FLPOLKP.C.CANAL4 also shows a high TN:TP ratio of 24. According to this analysis based on Station 21FLTPA 25020265 and shown in Figure 54 a fifty percent reduction of TP would result in attainment of the 5.0 mgll DO standard. However, because there is limited data in this WBID, and since this WBID is part of the Peace
1. Creek Drainage Canal Watershed, the TMDL is based on the larger Peace Creek Drainage Canal Watershed.
I As described in the Peace Creek Drainage Canal, WBID 1539 section, the analysis indicates that a 75 percent reduction in TN and TP will result in DO meeting the standar of 5.0 mgll all of the time. It is recognized that these reductions are not necessarily achievable, but such reductions would be necessary to meet the current water quality standard. If a site specific alternative water quality criterion is developed for this water body, the TMDL can be revised.
Predicted DO versus Observed DO \ I
Figure 54: WBID 1626 predicted DO vs observed DO based on TP and temp. at station 21FLTPA 25020265 1
I West Wnles Dminn.~e Cnnnl Alloccrtions The TMDL process quantifies the amount of a pollutant that can be waterbody, identifies the sources of the pollutant, and recommends actions to be taken to achieve compliallce with applicable water quality standards on the relationship between pollution sources and in-stream water quality conditions. TMDL can be expressed as the sum of all point source loads (Waste Load non-point source loads (Load Allocation), and an appropriate margin of which takes into account any uncertainty concerning the relationship between efflue limitations and water quality:
TMDL = C WLAs + C LAs + MOS 1 The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 5130.2 (i) states that TMDLs can be expressed in terms of mass per time (e.g. kilograms per day), toxicity, or other appropriate measure. The TMDL for West Wales Drainage Canal, WBID 1626, is expressed in terms of a percent reduction for the LA and storm-water WLA.
Table 22: WBID 1626 West Wales Drainage Canal TMDL allocations
WLA I I
Waste Load Allocations (Regulated with treatmentplant and stormwaterpermits) There are no regulated continuous point source facilities in the West Wales Drainage Canal watershed. Permitted MS4 discharges are allocated with the same percent reduction as the non-point source loads.
Pollutant Nutrients (Total
Nitrogen and Total Phosphorus)
Load Allocations @on- Regulate4 The LA for nutrients is a 75 percent reduction to achieve the water quality standard for DO. I
M a r ~ i n Of Safetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDL the margin of safety is considered to be implicit since a large reduction is recommende and the nutrient reductions would result in TN and TP concentrations below the EPA ecoregion reference conditions. In this WBID the average TKN is 1.86 mgll (25% of th s is 0.465) and the average TP value is 0.1 1 (25% of this is 0.028). The EPA "reference 1 conditions for aggregate ecoregion XI1 streams" are 0.56 mgll TKN and 0.040 mg/l TP.
TMDL
75% reduction
Critical Conditions Critical conditions were considered by analyzing several years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed.
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, w normal, and dry conditions.
WAHNETA FARMS DRAIN CANAL (PEACE CREEK SUBBASIN) WBID 158 LOW DO AND NUTRIENTS
Wahneta Farms Drain Canal description, Water Oualitv And Environmental Data, and Source Assessment WBID 1580, shown in Figure 55, is on the 1998 303 (d) list as impaired for low DO an nutrients. Wahneta Farms Drain Canal receives flow from the Winter Haven Chain of Lakes and is located near the town of Wahneta, which has an MS4 permit that may discharge to the canal. The landuse in WBID 1580 is mostly 36.7% urban, 41.3%
d agriculture, 1.6% rangeland, 6.1% forest, and 12.6% wetlands. Figure 48 shows the stream network for this watershed.
Continuous
NIA
LA
75% reduction
MS4
75% reduction
MOS
implicit
Dissolved oxygen data from 1997 to present, (based on IWR 19. I), shows 16 of 66 (24%) below the 5.0 standard (Figure 59). Dissolved oxygen data from EPAYs Legacy STORET database was used to understand the background DO in the Wahneta Farms Drainage Canal. Thirty-two of 35 DO observations between 1954 and 1982 are below th standard of 5.0 mgll (Figure 60). The median DO was 1.3 mgll in this period. Figure 59 and Figure 60 show that there is no apparent decrease in DO from 1954 to 2004. It is recommended that a site specific criteria for the whole Peace Creek Drainage Canal watershed be developed, since the current 5.0 mgll standard is likely not reasonably attainable.
: The average TN is 1.38 mgll, the average TKN is 0.99 mgll, and the average TP value is
' 0.12 mgll (see Figure 6 1 and Figure 62). The total phosphorus value is less than one tent the EPA ecoregion average of 1.6 mgll TP and the TKN value is slightly lower than the ecoregion value of 1.1 mgll according to a query of the USEPA ecoregion nutrient data for ecoregion XI1 rivers and streams in Florida
h (http://www.epa.gov/waterscience/criteria/nutsient/database/select ecoregion.htin1). EP "reference conditions for aggregate ecoregion XI1 streams" are 0.56 mgll TKN and 0.04 mgll TP and 0.58 mgll for TN. Average nutrient values from the Florida IWR Upper Peace Planning Unit data are 0.21 mgll TP and 1.58 mgll TKN. The average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the FDEP IWR 19.1 database is 1.17 and the average TP is 0.45 mgll. For blackwater streams in this basins group the average TKN is 1.65 and the average TP is 0.41 mgll. ? TN:TP ratios are 13.4 and 18.4 at stations 21FLPOLKPCCANAL6 and 21FLPOLKPCCANAL7, respectively. Based on phytoplankton stoichiometry, a TN:TP ratio less than 7.2 generally indicates a nitrogen limitation and a high ratio indicates that nitrogen is abundant and the system is phosphorus limited. This system would be considered co-limited. 1
Figure 55: Location of the Wahneta Farms Drain Canal Water segment, WBID 1580, and Major Geopolitical Features in the Sarasota Bay, Peace River, and Myakka River Basin Group
Wahneta Farms Drain Canal Analvtical Approach/ Model Selection And ~evelopmeht The first approach selected here combines the known kinetic relationships for the sourcks and sinks of dissolved oxygen with correlation and regression statistics. Data collected t
station 21FLPOLKPCCANAL6 indicates that DO can be reasonably predicted with TN, ( TP, and temperature. The F-distribution statistic was determined to be 41 and the critical) F(0.05,3,45) is 2.8, meaning that there is a relationship between observed DO values and known values of water temperature, TN and TP, at an alpha of 0.05. Also, the probabilit that this data relationship occurred by chance is only 5.8621 E-13. Data from station 1 21FLPOLKPCCANAL7 also shows a relationship between DO and temperature and TP with an F-statistic of 34.8, critical F of 3.3, and 7.4943E-09 probability of the relationshlb, occurring by chance. These regression equation indicates that a decrease in nutrients improves DO, but not enough to meet the 5.0 mgll all of the time. These results indicate that other factors such as BOD, SOD, flow, velocity and depth are also important in the DO budget. Next, a second approach was explored. This analysis estimates the effect of anthropogenic sources on runoff loadings of nutrients and oxygen demanding substance in the watershed. BOD and nutrient loads are reduced to natural background levels
6 consistent with undeveloped conditions. It is presumed that this undeveloped condition represents a condition which cannot be controlled or abated and would have been established as an alternative dissolved oxygen criterion if the watershed had not developed. The DO level resulting from this natural condition is not specified in this document, however, the levels of nutrients and BOD are determined and the reductions necessary to attain this natural condition are specified. Estimated BOD, nitrogen, and phosphorus loads for Wahneta Farms Drainage Canal are shown in Table 23. These wele calculated by the EPA Simple method formula shown in Table 32 from the BASINS PLOAD version 3.0 model (EPA, 2001) using EMC values for Florida compiled by Harper, 2003 (see Figure 12). Landuse was based on the SWFWMD 1999 land uselcov r features categorized according to the Florida Land Use and Cover Classification Syste (FLUCCS). The features were photointerpreted from 1 : 12,000 UGSG color infrared (CIR) digital orthophoto quarter quadrangles (DOQQs). These can be downloaded fro the internet at http:l/www.swfwmd.state.fl,us/data/gis/libraries/physical~dense.htm.
.T 1
Next the urban and agriculture landuse is changed to wetlands, which is an undevelope , e nonanthropogenic landuse, and loadings were estimated for this undeveloped condition (shown in Table 24). The difference in the existing condition and undeveloped conditio watershed loadings is the reduction required for the TMDL. This results reductions of kgld of BOD (54% reduction), 2.8 kgld of TN (54% reduction), and 0.5 kgld of TP reduction).
Table 23: Estimated Existing Non-point Source Loads in WBID 1580 Parameter BOD
Table 24: Estimated Undeveloped Non-point Source Loads in WBID 1580
Total Load (kgld) 12.7
Parameter BOD TN TP
TN 5.12 TP 0.73
Total Load (kgld) 5.80
P
2.36 0.21 -L-
the water quality standard. The first analysis of these stations demonstrates that variat. in levels of nutrients, and temperature explain some of the variation in dissolved oxyg However, this analysis failed to determine pollutant reductions that would result in meeting the DO water quality standard all of the time. The second analysis demonstra the nutrient and BOD reductions necessary to attain undeveloped conditions, but does quantify the link between these parameters and DO. Because of this and because the downstream WBID has a much larger dataset, the TMDL for Wahneta Farms Drain Canal is based on the analysis of the downstream receiving canal, WBID 1539. A sin analysis of this downstream canal, WBID 1539, shows that a 75 percent reduction of 1 nitrogen and total phosphorus will result in DO meeting the water quality standard all the time. Details of the analysis are described in the section for WBID 1539. ,- --- -.
A TMDL needs to show the amount of pollutants a water body can receive and still meet 'o$ ,enl.
i Predicted DO versus Observed DO
Figure 56: Observed vs Predicted DO based on nutrient concentrations and water temperature ii Wahneta Farm Drainage Canal WBID 1580 at station 2lFLPOLKPCCANAL6.
Predicted DO versus Observed DO
Figure 57: Observed vs Predicted DO on nutrient concentrations and water temperature in the Wahneta Farm Drainage Canal WBID 1580 at station 21FLPOLKPCCANAL7.
- FDOT US Rartes
* S f o ~ t Stetions
8 USGS Owing Statlons
Figure 58: Wahneta Farms Drain Canal water quality stations and USGS flow gages.
'Oa -101 plepueqs 1/9.10-j aq1 MoIaq alaM suo!yaMasqo 99 JO yno 91 :6s a.rnZ!a
I --
WBID 1580 Water Quality ~ a t a l
+ Nitrogen Total as N (mg/l) --
Figure 61: Average TN in this WBID is 1.38 mgll.
WBID 1580 Water Quality ~ a t a l
I+ Phosphorus Total as P (mgtl) 1
Figure 62: Average TP in this WBID is 0.12 mgtl.
I
Wahneta Farms Drain Canal Allocations ~
Pollutant TMDL MS4 Nutrients (Total
Nitrogen and Total reduction
75% 75% reduction 75% reduction implicit Phosphorus)
Table 25: WBID 1580 Wahneta Farms Drain Canal TMDL allocations
Waste Load Allocations (Regulated wit11 treatment plnnt and stormwater permits) There are no regulated continuous point source facilities in the Wahneta Farms Drain Canal watershed. For nutrients the target is total nitrogen and total phosphorus, and a percent reduction in TN and TP is recommended to achieve the water quality DO. The waste-load allocation for regulated storm-water sources of total nitrogen and total phosphorus is expressed as a 75 percent reduction.
WLA
Load Allocations w o n - Regulated) For nutrients the target is total nitrogen and total phosphoms, and a 75 percent reduction in TN and TP is recommended to achieve the water quality standard for DO. The load allocation for non-regulated non-point sources of total nitrogen and total phosphorus is expressed as a 75 percent reduction.
LA I MOS 1
Critical Conditions Critical conditions were considered by analyzing several years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed.
Margin O f Safetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDL the margin of safety is considered to be implicit since the nutrient reductions would resl in TlV and TP concentrations near or below the EPA ecoregion reference conditions.
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, w t, normal, and dry conditions. 1
It
PEACE CREEK DRAINAGE CANAL (PEACE CREEK SUBBASIN) WBID 15 LOW DO, NUTRIENTS, BOD
Peace Creek Drninnne Canal description, Wnter Oelality And En.vironmentn1 Datn, Source Assessment This document describes the development of TMDLs for WBID 1539 which is shown Figure 63. The Peace Creek Drainage Canal is on the 1998 303 (d) list as impaired for low DO, nutrients, and BOD. Peace Creek Drainage Canal receives flow from the Winter Haven Chain of Lakes and is located near the town of Wahneta, which has an MS4 permit and may discharge stormwater to the canal. The city of Winter Haven WWTP
and
in
ft3,
Wahneta, NPDES FL0036048, is an activated sludge domestic waste water treatment - facility (secondary treatment) with a permit capacity of 5 MGD applied to the land
through an irrigation sprayfield and overland flow treatment system. The overland flow treatment system ultimately is discharged to an unnamed tributary of the Peace Creek Drainage Canal (WBID 1539). The City of Winter Haven WWTP #2, Conine Plant, NPDES No. FL0021849, possessed a permit for a limited wet weather discharge to the Peace Creek Drainage Canal, but the outfall was never utilized. The locations of these facilities are shown in Figure 64.
- Interstates
Figure 63: Location of the Peace Creek Drainage Canal Water Segment, WBID 1539, and Major Geopolitical Features in the Sarasota Bay, Peace River, and Myakka River Basin Group
Table 26: Permit limits for Winter Haven #3. July monthly average values are shown. 1 Surface Water NH3 (mgll) 1 1 FLOW
-
Discharge Limit Winter Haven #3
Water quality data from the stations shown in Figure 64 is discussed next. The dissolve oxygen in this WBID was below the 5.0 mgll standard 44 percent of the time (see Figur 68). Corrected chlorophyll-a exceeded 20 ugll nine percent of the time and un-corrected chlorophyll-a exceeded 20 ugll 16 percent of the time (see Figure 71 and Figure 72). Th average TKN is 1.46 mgll, 1.86 for TN and the average TP value is 0.34 mgll. The total 1
Table 27: Average discharge for Winter Haven #3. Year 2004 average reported values from DMR.
phos~horus value. is less than one fifth the EPA ecoregion average of 1.6 m i l l . ~ ~ and t TKN value is higher than the ecoregion value of 1.1 mgll according to a query of the USEPA ecoregion nutrient data for ecoregion XI1 rivers and streams in Florida
5.0
Surface Water Discharge Limit Winter Haven #3
(h t t p : / /m .e~a . eov /wa te r sc i ence / c r i t e r i&t r i en t / da tb ecoreeion.htm1). EP "reference conditions for aggregate ecoregion XI1 streams" are 0.56 mgll TKN and 0.0 0 mgll TP and 0.58 mgll for TN. k I
Average nutrient values from the Florida IWR 19.1 Upper Peace Planning Unit data (entire period of record in the database) are 0.2 1 mgll TP and 1.58 mgll TKN. The average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the FDEP IWR 19.1 database is 1.17 and the average TP is 0.45 mgll. For blackwater streams in this basins group the average TKN is 1.65 and the average TP is 0.41 mgll. Another set of nutrient values that may be useful for comparison are the event mean concentrations for southwest Florida compiled by Harper and Baker. The nutrient concentrations estimated for wetlands could be considered natural background conditions. These EMC values for wetlands are included in
No limit
Table 28 and a list of these EMC values for other landuse types is shown in Figure 12.
NH3 (mgll)
0.485
10.0
TP (mgll)
0.153
BOD (mgll)
2.97
(MGD) 5.0
TN (mgll)
2.3 1
Flow (MGD)
4.65
I suo!)e>oq 8u!~o)!uom pue '~uaur%a~ ~a)e~ leue3 a%eu!e~~ yaa~3 axad :pg a~nz!~
Table 28: WBID 1539 Nutrient Concentration Comparison
WBID 1539 EPA Ecoregion XI1 average EPA Ecoregion XI1 recommended reference condition
TN:TP ratio is 11.5 for the WBID. Based on phytoplankton stoichiometry, a TN:TP ratio less than 7.2 generally indicates a nitrogen limitation and a high ratio indicates that nitrogen is abundant and the system is phosphorus limited. This ratio of 11.5 indicates co-limitation. !
TKN 1.46
u
Upper Peace Planning Unit Sarasota Bay-Peace-Myakka Basins Group streams Event Mean Concentration for Wetlands
FDEP performed four bioassessments analyzed according to the Stream Condition (SCI) in WBID 1539 with scores ranging from poor to excellent (Florida Environmental Protection, Division of Water Resource Management, Water Quality Status Report, Sarasota Bay and Peace and Myakka Rivers, September 2003) (see Tab1 6). The poor scores were at locations south of highway 60, while the scores were north of this highway.
1.1 0.56
The Peace Creek Canal is basically a wetland with a canal through it. Wasteload allocation documents for the Cities of Lake Wales and Winter Haven describe sections f the canal as completely overgrown with water hyacinth and Lemna, the channel was about 10 feet wide and one foot deep. Site specific alternative criteria (SSAC) were
5.0 mgll criterion, high levels of organic matter and high BOD in the groundwater that
I approved for sections of the Peace Creek Canal in 1985 based on
provides the base flow in this system. The City of Lake Wales flowing southward to the western section line of Section 15, Township 30 South, 27 East. The SSAC for the City of Winter Haven applies from points of #2 from the City's underdrained spray irrigation system and extends 3 miles downstrea in the Canal for the months of June, July and September, and 5 miles downstream in August. These SSAC's are documented in EPA and FDEP correspondence letters and internal EPA memorandums (Patton, March 19, 1985; Ravan, August 20, 1985; Kutzman, July 15, 1985; Kutzman, March 19, 1985).
TN 1.86
1.58 1.17
In addition to these wasteload allocations and documents from the 1 9809s, dissolved ~ oxygen data from EPA's Legacy STORET database was used to understand the background DO in the Peace Creek Drainage Canal. Figure 65 shows that from 1954 1983 dissolved oxygen was frequently below 5.0 mgll. The median DO was 4.8 mgll i that period. Figure 66 shows that there is no apparent decrease in DO from 1954 to 200f.
TP 0.34
0.58 1.6 1 0.04 1
1.01
0.21 0.45 0.09
1
-- -- -- - --a-
+ PEACE CR CANAL GANDY BR PEACE CR CANAL RIFLE RANGE RD
A PEACE CR CANAL BR 114 X PEACE CRK CNL4 3 MI E OF ALTURA
A
X A
12 -- -- --
X
7---
- ->--r&---- 6 A -7-
1 -Jan-54 24-Jun-59 14-Dec-64 6-Jun-70 27-Nov-75 19-May-81
Figure 65: In the Peace Creek Drainage Canal 123 of 241 (53%) of the DO observations from 1954 t 1983 were below 5.0 mgll.
I Average DO in the Peace Creek Drainage Canal
Figure 66: Fifty Year Trend of Average DO in WBID 1539 ~ Flow at USGS 02293987, Peace Creek Drainage Canal near Wahneta
800
Figure 67: Flow in the Peace Creek Drainage Canal shows a 90th percentile of 301, a median of 35, and a 10th percentile of 5.6 cfs.
The water quality data show that the DO is frequently low and has been for at least the last fifty years. However, a TMDL analysis needs to determine the amount of pollutants water body can receive and still meet the water quality standard. The information on this canal indicates the standard of 5.0 mg/l has historically been met only about half of the
99 of 129
a
time. The data from the 1950's through early 1980's represents a period of lower population and development than now, and the low DO during that time indicate that a daily average not to exceed 5.0 mg/l is a standard that cannot be met even with little impact from industry and urbanization. For this reason, it is recommended that a site specific criterion for the whole Peace Creek Drainage Canal watershed be developed. Until a more appropriate criterion is developed the 5.0 mg/l standard will be targeted, an this TMDL calculation will target the 5.0 mg/l.
I Peace Creek Draina~e Canal Analytical Approaclt/Model Selection And Development For the portion of this watershed upstream of the Winter Haven discharge, (upstream of the highway 60 bridge), a regression model was applied to develop the TMDL. For the portion receiving the influence of the City of Winter Haven discharge, (downstream of the highway 60 bridge), a steady state model was applied to better evaluate the impact of this discharge. The regression approach selected here combines the known kinetic relationships for the sources and sinks of dissolved oxygen with correlation and regression statistics. Based on the known mechanisms of the sources and sinks of DO, a simple regression model is developed. The variation in the observed DO is explained by variables such as temperature, BOD, chlorophyll, nutrients, organic carbon, and flow. Statistics are used to explore the relationships at each water quality monitoring station in the watershed depending on the water quality parameters that were recorded.
The relationship between DO and temperature is well known, and the relationship between DO, TOC and nutrients can be explained by plant nutrient uptake, photosynthesis, respiration, growth and death and decay. These kinetic relationships are part of the principal components of the DO budget, and these are the mechanisms typically included in mechanistic models of DO.
Data collected at all stations in WBID 1539 indicates that DO can be reasonably predicted with TN, TP, TOC, and temperature (see Figure 73). The F-distribution statistic was determined to be 54 and the critical F(0.05,4,101) is 2.5, meaning that there is a relationship between observed DO values and known values of water temperature, TOC, TN and TP, at an alpha of 0.05. Also, the probability that this data relationship occurred by chance is only 2.4E-24. The regression equation indicates that a decrease in nutrients and the corresponding decrease in TOC improves DO. Specifically, the data at indicates that a 75 percent reduction in TN and TP will result in a 53 percent decrease in TOC and DO meeting the standard of 5.0 mg/l all of the time. It is recognized that these reductions are not necessarily achievable, but such reductions would be necessary to meet the current water quality standard. If a site specific alternative water quality criterion is developed for this water body, the TMDL can be revised.
A steady state WASP model of critical low flow conditions was used for estimating the effects of non-point source and point source loads on dissolved oxygen for the lower section of the Peace Creek Drainage Canal shown in the rectangle in Figure 48. This section extends from just south of highway 60 to the confluence with the Peace River.
Table 26 shows the continuous point source permit limits for nutrients and BOD, and t& reported actual discharge loads from point source facilities are summarized in Table 27. For the TMDL analysis the surface water permitted loads from the point sources are evaluated because the facilities are allowed to discharge these quantities. The modeled
WBID 1539 Water Quality Data1
critical conditions include upstream 7410 flow of about 0.06 cubic meters per second, cfs), with the point soufce continuous discharge of 0.219 crns, (5 mgd), Wahneta Farms Drainage Canal flow of 0.0039 crns and Gaskin Brook flow of 0.0064 crns. These critical conditions were based on the 1988 Florida Department of Environmental Regulation water quality based effluent limitation analysis. The water quality concentrations associated with the upstream and tributary flows were set to median observed values. In this TMDL analysis, the permitted point source loads and the non-point source loads are reduced until the water quality standard for DO is met. Figure 74 through Figure 76 show the predicted water quality in Peace Creek Drainage Canal. Figure 76 shows that the DO is improved to meet the 5.0 mg/l water quality standard with a sixty percent reduction in all nutrient and BOD loads.
1 + Dissohled Oxygen (mgll) -WaterQualityCriteria (
(2
I I
Figure 68: In the Peace Creek Drain Canal 91 of 206 (44%) DO observations were below the standard of 5.0 mgll.
DO Percent Saturation at USGS 02293987 (21FLSWFDFLOl9191O) PEACE CREEK DRAINAGE
CANAL NEAR WAHNETA FL
9% QT d'9 4TQ
6' 2 ' 4'
Figure 69: The DO percent saturation ranges from zero to 140, indicating nutrients via photosynthesis and respiration are influencing DO.
I
WBlD 1539 Water Quality Data
BOD 5-Day (mgll) 1 . - - - -- .
L ~ 1
Figure 70: BOD data in the Peace Creek Drain Canal
WBID 1539 Water Quality Data1 i
L + Chbrophy -. . - ll Corrected (ugil) -Water Quality
1. -- I
Figure 71:14 of 151 (9%) observations of corrected chlorophyll-a were above 20 ugll.
-- --
~ I D 1539 Water Quality Data1
( + Chlorophyll (ugll) -Water Quality Comparison 1 L -
I
Figure 72: 22 141 of (16%) observations were above 20 ugll.
Figure 75: CBOD under TMDL predicted conditions in the Peace Creek Drainage Canal. Segment is upstream, segment 2 receives the point source discharge, and segment 9 is downstream.
Figure 76: Dissolved Oxygen under TMDL predicted conditions in the Peace Creek Drainage Can: Segment 1 is upstream, segment 2 receives the point source discharge, and segment 9 is downstreal
Peace Creek Drainage Canal Allocations The TMDL' process quantifies the amount of a pollutant that can be assimilated ir waterbody, identifies the sources of the pollutant, and recommends regulatory or otl actions to be taken to achieve compliance with applicable water quality standards bas on the relationship between pollution sources and in-stream water quality conditions. TMDL can be expressed as the sum of all point source loads (Waste Load Allocatio non-point source loads (Load Allocation), and an appropriate margin of safety (MC)
which takes into account any uncertainty concerning the relationship between effluer limitations and water quality: '
TMDL = C WLAs + C LAs + MOS
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR § 130.2 (i) states that TMDLs can be expresse in terms of mass per time (e.g. kilograms per day), toxicity, or other appropriate measure The TMDL for Peace Creek Drainage Canal, WBID 1539, is expressed in terms of a percent reduction for the LA and WLA.
BOD
Table 29: WBID 1539 Peace Creek Drainage Canal Upstream of Hwy. 60 TMDL allocations
1 reduction 75% 1 reduction "% 175% r e d u ~ t i o n I ~ ~ ~ ~ ~ ~ ~ implicit I
Pollutant Nutrients (Total Nitrogen and Total Phosphorus)
Waste Load Allocations (Regz~laterl with treatment plant and storm water permits) The WLA for this WBID requires reductions of total nitrogen (TN), total phosphorus (TP) and BOD in order to meet the DO water quality standard. Allocations are recommended for both nutrients because the TN to TP ratio is 11.5 which indicates a co- limitation of nitrogen and phosphorus. This WBID was analyzed in two parts. The section upstream of the effects of the continuous point source, (upstream of the highway 60 bridge), will require a 75 percent reduction in permitted MS4 discharge loads of total nitrogen, total phosphorus, and oxygen demanding substances to meet the DO standard. There is one regulated continuous point source facility in the Peace Creek Drainage Canal watershed. The segments of the creek receiving this discharge, ( from just south o highway 60 to the confluence with the Peace River ), will require a 60 percent reduction in nutrients and BOD. This reduction applies to the permitted discharge, or existing discharge if there is no permit limit. The average existing discharge of BOD is only a b o ~ 30 percent of the permitted discharge, so reductions in actual discharges may not be necessary. Similarly, the existing ammonia discharge is 0.485 mgll on average, which is only about 10 percent of the permit limit.
Load Allocations (Non- Regulated) The LA for nutrients and BOD is a 75 percent reduction to achieve the water quality standard for DO.
TMDL 75%
reduction
Margin Of Safetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDL
LA 75%
MOS
implicit
WLA Continuous. FL0036048 MS4
"% 75%reductionreduction reduction
the margin of safety is considered to be implicit since the nutrient reductions would resu t in TN and TP concentrations near or below the EPA ecoregion reference conditions. Twenty-five percent of the average TN and TP in the Peace Creek Drainage Canal is , 1.86*.25 = 0.465, and 0.34*.25 = 0.085. These compare to 0.58 and 0.04 for TN and TP recommended reference conditions.
I Critical Conditions For non-point sources and storm sewer point sources critical conditions were considered by analyzing several years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed. A high temperature, low flow critical condition was analyzed for the effluent dominated section of the Peace Creek Drainage Canal.
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, we , normal, and dry conditions. I Lake Effie Outlet description, Water Oualitv And Environmental Data, and Source Assessment Lake Effie Outlet was listed on Florida's 1998 303(d) list as impaired for nutrients. The basis for this listing was that median values for nitrogen, phosphorous, and TSI exceede FDEP thresholds. However, there is no water quality data for Lake Effie Outlet in the Florida IWR database or in STORET. The sampling data that resulted in the listing wer from four samples collected from one sample station, 2 1 FLPOLKEFFIE I, in 1987. Th station was named Lake Effie Center. The station coordinates locate the station out in Lake Effie proper ( W I D 1617A), not in the Lake Effie Outlet (WBID 1617). A revie
1 61 7A) and not Lake Effie Outlet (WBID 1 61 7).
I of current data, 1989-2004, reveals the fact that no samples have been collected in Lake Effie Outlet ( W I D 161 7), however, a few samples have been collected from Lake Effi proper. Therefore, the original listing was likely meant to represent Lake Effie (WBID
Based on the limited more recent samples collected in Lake Effie the chlorophyll and nitrogen levels in the lake remain quite high. Since this is a small lake and the Lake Ef e Outlet receives waters directly from the lake, the high nutrient levels observed in the 1 e are likely transported to the outlet at high water levels. Water from Lake Effie Outlet eventually flows to Peace Creek Drainage Canal.
4 I
u A 1982 FDEP wasteload allocation document for the city of Lake Wales discusses a 1. 9 '
MGD discharge from Lake Wales to Lake Effie that in turn discharged to Peace Creek Drainage Canal (1 982, Bureau of Water Analysis). The NPDES permit expired in 1996, and FDEP records show this facility no longer operates, so now there are no permitted discharges to the lake. Figure 11 shows that the landuse in this W I D is 53% develope and 27% agriculture with only 14% undeveloped or water. The city of Lake Wales is permitted to discharge municipally separated storm sewer system water under the Polk
County MS4 permit, and these discharges as well as other urban runoff likely enter the WBID.
Lake Effie Outlet and ~nalv t ical ~pproaclt/ ~ o d e l Selection And Development There are no data available from the outlet canal and very limited data from Lake Effie, so the TMDL is based on an analysis of the Peace Creek Drainage Canal watershed. LaE Effie Outlet is a part of this watershed as can be seen in Figure 48. As discussed in the Peace Creek Drainage Canal section, a regression analysis indicates that a decrease in nutrients and the corresponding decrease in TOC improves DO. Specifically, the analysi indicates that a 75 percent reduction in TN and TP will result in a 53 percent decrease ir TOC and attainment of the DO water quality standard of 5.0 mgll.
Lake Effie Outlet Canal Allocations The TMDL process quantifies the amount of a pollutant that can be assimilated in waterbody, identifies the sources of the pollutant, and recommends regulatory or 0th actions to be taken to achieve compliance with applicable water quality standards basc on the relationship between pollution sources and in-stream water quality conditions. TMDL can be expressed as the sum of all point source loads (Waste Load Allocatior non-point source loads (Load Allocation), and an appropriate margin of safety (MO? which takes into account any uncertainty concerning the relationship between efflue limitations and water quality:
TMDL = C WLAs + C LAs + MOS
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 91 30.2 (i) states that TMDLs can be express in terms of mass per time (e.g. kilograms per day), toxicity, or other appropriate measur The TMDL for Lake Effie Outlet Canal, WBID 1617, is expressed in terms of a percent reduction for the LA and WLA.
Table 30: WBID 1617 Lake Effie Outlet Canal TMDL allocations I I I I I I
Waste Load Allocations (Regulated with treatment plant and stormwater permits) There are no regulated point source facilities in the Lake Effie Outlet Canal watershed. This TMDL analysis indicates that a 75 percent reduction in permitted storm sewer discharge loads of nutrients is necessary to attain the DO standard in the Peace Creek Drainage Canal watershed and Lake Effie Outlet.
Pollutant Nutrients (Total
Nitrogen and Total Phosphorus)
TMDL
75% reduction
WLA MS4
75% reduction
LA
75% reduction
MOS
implicit
Load Allocations (Non- Regulated) I
I
For nutrients the target is total nitrogen and total phosphorus, and a 75 percent reduction 1 is recommended to achieve the water quality standard for DO.
I
Margin OfSafetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDL the margin of safety is considered to be implicit since the nutrient reductions would resu in TN and TP concentrations near or below the EPA ecoregion reference conditions. , Critical Conditions Critical conditions were considered by analyzing several years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed.
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, we normal, and dry conditions.
LIMESTONE CREEK WBID 1921, LOW DO, NUTRIENTS 1 Limestone Creek description. Water Oualitv And Environmental Data, and Source Assessment Limestone Creek is on the 1998 303 (d) list as impaired for low dissolved oxygen and nutrients, and a TMDL is required. In addition to the DO and nutrient issues, fish consumption advisories have been issued for largemouth bass, bowfin, and gar for Limestone Creek. Limestone Creek has been verified as impaired due to mercury in fish tissue by FDEP, and they will develop a TMDL for mercury. This document addresses the low DO and nutrient impairments.
The landuse in Limestone Creek WBID 1921 is 53.1 percent agriculture, 7.5 percent rangeland, 21.4 percent forest and 17.5 percent wetlands. There are no point sources in this watershed. The WBID boundary is essentially the entire watershed to limestone creek, so there are no other sources contributing to this impaired WBID.
FDEP performed three bioassessments in Limestone Creek. One bio-recon resulted in 2
"suspect" rating. However, two assessments analyzed according to the Stream Conditic Index (SCI) resulted in scores of good and excellent (FDEP, 2003) (see Table 6). DO data shows 39 percent below the 5.0 mgll standard, however there was only one high chlorophyll-a observation. A query of the USEPA ecoregion nutrient data for ecoregiol XI1 rivers and streams in Florida shows an average TP of 1.6 mgll and TKN of 1.1 mg/ (http://www.epa.gov/waterscience/criteria~nutrient/databaselselect~ecoregion.html). WBID 1921, Limestone Creek has average TP of 0.41 mgll and TKN of 1.4 mgll. The average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the FDEP IWR 19.1 database is 1.17 and the average TP is 0.45 mgll. EPA "reference conditions for aggregate ecoregion XI1 streams" are 0.56 mgll TKN and 0.040 mgll TP and 0.5 8 mgll for TN.
'PIZOZoSZ uo!lels le PaPJo3aJ SeM 1.2 Jo anIcA 'CZ~CS~~~LSIZLZ VdL'IBIZ uO!)Els le PaPalaP SeM 'my SO:O~ )e ~ooz/P/~~ 'dep auras aq) uo -8s )e q%!q sm luaurarnsaaur auo dluo pue 'MOI
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1 BOD 5-Day (mgll) Water Quality Comparison
Figure 83: There were 15 observations of BOD in Limestone Creek, WBID 1921. Of these 15,13 we recorded as 2 or less, one was 2.8 and one 5.6. The 5.6 value was recorded at the same station, date and time as the high chlorophyll-a value of 38 ug/l. Also, at that station, same time and day, the DO was recorded as a low 2.86 mgll.
Limestone Creek Creek Analytical Approach/Model Selection And Development
Data collected at stations 2 1 FLS WFDFL00073 (which also includes station 21FLGWFL00073) indicates that DO can be reasonably predicted with TKN, and temperature using a statistical regression analysis. The F-distribution statistic was determined to be 12.867 and the critical F(0.05,1,18) is 4.4, meaning that there is a relationship between observed DO values and known values of water temperature and TKN, at an alpha of 0.05. Also, the probability that this data relationship occurred by chance is only 0.002 1.
The relationship between DO and temperature is well known, and the relationship between DO and nutrients can be explained by plant nutrient uptake, photosynthesis, respiration, growth and death and decay. Therefore the relationships indicated by the statistics are expected, and the predictive equation is based on physics and biology. This equation was used to develop necessary reductions in nutrients. Nitrogen is usually the limiting nutrient when the TNiTP ratio is less than 7.2 based on phytoplankton stoichiometry. For this dataset the TNiTP ratio was 4.1. This seems reasonable since thi area of the Peace River Basin is known for high phosphorus content in its soil and bedrock. This area of Florida has many phosphate mines, although none are documentec in the Limestone creek watershed. Because of the high phosphorus and the potential for entering Limestone Creek, and the observed low TN to TP ratio, nitrogen is the targeted nutrient.
A TMDL was developed based on the following equation used in Figure 84;
DO = -0.20197 X Water Temperature in degrees C + -2.45829 X TKN in mg/l + 13.56997 I A 42 percent reduction of TKN results in DO meeting the water quality standard of 5.0 mg/l. This equation was developed with ambient trend water quality monitoring data and therefore reflects the conditions at the time of monitoring. Since DO varies diurnally, an these data were primarily daytime grab samples, the lowest DO of the late night or early morning are not necessarily represented. Additional water quality monitoring could improve the equation and the TMDL accuracy.
I I
Predicted DO versus Observed DO I
I I 1
5 10 15 -- J
Figure 84: Predicted DO based on TKN and Temperature versus observed DO
Limestone Creek Allocations The TMDL process quantifies the amount of a pollutant that can be assimilated in waterbody, identifies the sources of the pollutailt, and recommends actions to be taken to achieve compliance with applicable water quality standards on the relationship between pollution sources and in-stream water quality conditions. TMDL can be expressed as the sum of all point source loads' (Waste Load non-point source loads (Load Allocation), and an appropriate margin of which takes into account any uncertainty concerning the relationship limitations and water quality:
TMDL = C WLAs + C LAs + MOS 1
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 5 130.2 (i) states that TMDLs can be expres: in terms of mass per time (e.g. kilograms per day), toxicity, or other appropriate measu The TMDL for Limestone Creek, WBID 192 1, is expressed in terms of a percent reduction for the LA and WLA (see Table 3 1).
Table 31: Limestone Creek TMDL allocations
1 Pollutant I TMDL
Waste Load Allocations (Regulated with treatment plant and stormwater permits) There are no regulated continuous point source facilities in the Limestone Creek watershed. The regulated storm water discharges of total nitrogen should be reduced b! 42 percent to attain the water quality standard for DO.
Nutrients (Total 42% 1 Nitrogen) reductionl 42% reduction
Load Allocations (Non- Regulated) For nutrients the target is total nitrogen, and a 42 percent reduction in TN is recommended to achieve the water quality standard for DO.
WLA MS4
42% reduction I implicit I
Marnin Of Safetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDI the margin of safety is implicit since the recommended 42 percent reduction would res in TKN (1.4*(1-0.42) = 0.812) approaching the EPA "reference conditions for aggrega ecoregion XI1 streams" of 0.56 mg/l TKN.
Critical Conditions Critical conditions were considered by analyzing all available data representing severa years containing wet, normal, and dry conditions. Both wet events and dry events were analyzed.
LA
Seasonal Variation Seasonal variation was considered by analyzing several years containing all seasons, v, normal, and dry conditions.
MOS
ALLIGATOR BRANCH WBID 1871 LOW DO, NUTRIENTS
Allinator Branch description, Water Qualitv And Environmental Data, and Source Assessment Alligator Branch, shown in Figure 87, is on the 1998 303 (d) list as impaired for low 1: and nutrients, and TMDLs are required by the USEPA. The landuse in WBID 1871 is 55.6 percent agriculture, 6.7 percent rangeland, 10.0 percent forest and 23.5 percent
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wetlands. Zolfo Springs has a MS4 permit and may discharge to the Alligator Branch watershed since part of this town is in the Alligator Branch WBID, but there are no othc permitted NPDES discharges in the watershed. The average color is 169 indicating a blackwater stream. The dark water and the watershed are visible in Figure 85 and Figur~ 86. Alligator Branch watershed lies within the phosphate mineable limit area. This area of the Peace River Basin is known for high phosphorus content in its soil and bedrock. This area of Florida has many phosphate mines, although none are documented in the Alligator Branch watershed. Because of the high phosphorus and the potential for it entering Alligator Branch, and the observed low TN to TP ratio of 2.8, nitrogen is the targeted nutrient.
FDEP performed no bioassessments in Alligator Branch. The average TKN is 1.59 mg/ and the average TP value is 0.75 mg/l (see Figure 90 and Figure 91). The total phosphorus value is less than half the EPA ecoregion average of 1.6 mg/l TP and the TKN value is higher than the ecoregion value of 3.1 mg/l according to a query of the USEPA ecoregion nutrient data for ecoregion XI1 rivers and streams in Florida (http://www.epa.gov/waterscience/criteridnutrient/database/select ecorenion.htm1). Th, average TKN for streams in the Sarasota Bay-Peace-Myakka Basins Group from the FDEP IWR 19.1 database is 1.17 and the average TP is 0.45 mgll. For blackwater streams in this basins group the average TKN is 1.65 and the average TP is 0.41 mg/l. Figure 88 shows that only one chlorophyll-a observation was above the IWR threshold 20 ug/l. Figure 89 shows that 56 percent of the DO observations were below the water quality standard.
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in TKN and TP. A regression equation based on this relationship indicates that a decreas in TKN by 33 percent would decrease the chlorophyll-a to below 20 ugll. However, this is a blackwater stream and observed corrected chlorophyll-a values were not high (see Figure 88), with only one value above the IWR comparison value of 20 ugll. Since this analytical approach address the nutrient impairment, but does not address the low DO impairment, other approaches were explored. Data collected at all stations in Alligator Branch, WBID 1871, indicates that DO can be reasonably predicted with TN, TOC, and temperature (see Figure 92). The F-distribution statistic was determined to be 22 and the critical F(0.05,4,10 1) is 3.2, meaning that there is a relationship between observed DO values and known values of water temperature, TOC, and TN at an alpha of 0.05. Also, the probability that this data relationship occurred by chance is only 2.95 178E-06. The regression equation indicates that a decrease in nutrients and the corresponding decrease in TOC improves DO. However, the equation developed from this relationship is not sensitive enough to nutrients and TOC to improve DO to the 5.0 mgll standard all of the time. These results indicate that other factors such as BOD, SOD, flow, velocity and depth are also important in the DO budget.
Predicted Chlorophyll-a versus Observed Chlorophyll-a
Predicted DO versus Observed DO
1 9
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Figure 92: Alligator Branch predicted DO vs observed DO based on regression of DO with TOC, nutrients and temperature.
A TMDL needs to show the amount of pollutants a water body can receive and still mee the water quality standard. Because this data analysis did not determine pollutant reductions that would result in meeting the DO water quality standard all of the time, a third approach was explored. This analysis estimates the effect of anthropogenic sources on runoff loadings of nutrients and oxygen demanding substances in the watershed. BOI and nutrient loads are reduced to natural background levels consistent with undeveloped conditions. It is presumed that this undeveloped condition represents a condition which cannot be controlled or abated and would have been established as an alternative dissolved oxygen criterion if the watershed had not developed. The DO level resulting from this natural condition is not specified in this document, however, the levels of nutrients and BOD are determined and the reductions necessary to attain this natural condition are specified. Estimated BOD, nitrogen, and phosphorus loads for Alligator Branch are show in Table 33. These were calculated by the EPA Simple method forrnuli shown in Table 32 from the BASINS PLOAD version 3.0 model (EPA, 2001) using EMC values for Florida compiled by Harper, 2003 (see Figure 12). Landuse was based on the SWFWMD 1995 land uselcover features categorized according to the Florida Land Use and Cover Classification System (FLUCCS). The features were photointerpreted from 1 : 12,000 UGSG color infrared (CIR) digital orthophoto quarter quadrangles (DOQQs). These can be downloaded from the internet at http:llwww.swfwmd.state.fl.us/data~gis/libraries/physical~dense.htm. Next the urban and agriculture landuse is changed to wetlands, which is an undeveloped nonanthropogenic landuse, and loadings were estimated for this undeveloped condition
(shown in Table 34). The difference in the existing condition and undeveloped watershed loadings is the reduction required for the TMDL. This results in a
(65% reduction). 6.2 kgld BOD (24% reduction), 6.48 kgld of TN (45% reduction), and 1.26 kgld of TP
Table 32: Pollutant Load Equation from EPA BASINS PLOAD users manual LP = Cu (P * PJ* RVU * Cu* Au * 2.72 1 12) Where: LP = Pollutant load, Ibs P = Precipitation, incheslyear PJ = Ratio of storms producing runoff (default = 0.9) RVu= Runoff Coefficient for land use type u, inches of runofflinches of rain RVu=0.05 + (0.009 * lu); lu = percent imperviousness Cu = Event Mean Concentration for land use type u, milligramslliter Au = Area of land use type u, acres
Table 33: Alligator Branch Estimated existing watershed loads. I Parameter I Total load (kgldav)
Table 34: Alligator Branch Estimated undeveloped (no urban or agriculture landuse) watershed 1
BOD TN
loads. [ Parameter 1 Total load (kglday)
25.8 14.5
Alliaator Branch Allocations The TMDL process quantifies the amount of a pollutant that can be assimilated i a waterbody, identifies the sources of the pollutant, and recommends regulatory or ot er actions to be taken to achieve compliance with applicable water quality standards ba ed on the relationship between pollution sources and in-stream water quality conditions. A TMDL can be expressed as the sum of all point source loads (Waste Load Allocati n), non-point source loads (Load Allocation), and an appropriate margin of safety (MOS), which takes into account any uncertainty concerning the relationship between efflu nt limitations and water quality: I BOD TN
TMDL = C WLAs + C LAs + MOS
19.6 8.02
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 8 130.2 (i) states in terms of mass per time (e.g. kilograms per day), toxicity,
I (shown in Table 34). The difference in the existing condition and undeveloped condition, watershed loadings is the reduction required for the TMDL. This results in a reduction of 6.2 kgld BOD (24% reduction), 6.48 kgld of TN (45% reduction), and 1.26 kgld of TP (65% reduction). I Table 32: Pollutant Load Equation from EPA BASINS PLOAD users manual
LP = &(P PJ* RVU CU* AU 2.72 / 12) Where: LP = Pollutant load, Ibs P = Precipitation, inchestyear PJ = Ratio of storms producing runoff (default = 0.9) RVU= Runoff Coefficient for land use type u, inches of runoff/inches of rain CU = Event Mean Concentration for land use type u, milligramstliter AU = Area of land use type u, acres
Table 33: Alligator Branch Estimated existing watershed loads. Parameter BOD
Alligator Branch Allocations The TMDL process quantifies the amount of a pollutant that can be assimilated waterbody, identifies the sources of the pollutant, and recommends regulatory or actions to be taken to achieve compliance with applicable water quality standards on the relationship between pollution sources and in-stream water TMDL can be expressed as the sum of all point source loads (Waste non-point source loads (Load Allocation), and an appropriate margin which takes into account any uncertainty concerning the relationship limitations and water quality:
Total load (kglday) 25.8
Table 34: Alligator Branch Estimated undeveloped (no urban or agriculture landuse) watershed loads.
TMDL = C WLAs + C LAs + MOS
Parameter BOD TN
The objective of a TMDL is to allocate loads among all of the known pollutant sources throughout a watershed so that appropriate control measures can be implemented and water quality standards achieved. 40 CFR 9130.2 (i) states in terms of mass per time (e.g. kilograms per day), toxicity,
Total load (kglday) 19.6 8.02
The TMDL for Alligator Branch, WBID 1871, is expressed in terms of a percent reduction for the LA and WLA (see Table 35).
Table 35: Alligator Branch TMDL allocations I I I I I 1
Biochemical Oxygen 2 4 % 1 NIA I 24% 1 24% 1 implicit 1 1 Demand(B0D) reduction reduction reduction
Pollutant
1 Nutrients (Total Nitroaen) red;:onl NIA I
Waste Load Allocations (Regulated with treatment plant and stormwater permits)
TMDL
There are no regulated continuous point source facilities in the Alligator Branch watershed. The waste load allocation (WLA) for storm water loads from municipal separate storm sewer systems are shown as a percent reduction. Because of the high phosphorus and the potential for it entering Alligator Branch, and the observed low TN TP ratio of 2.8, nitrogen is the targeted nutrient. A 45 percent reduction of total nitroge is recommended to attain a DO level consistent with natural conditions. Also, a 24 percent reduction of BOD is recommended to attain a DO level consistent with natural conditions.
Load Allocations (Nun- Regulated)
WLA Continuoud MS4
The LA is also specified as a percent reduction. A 45 percent reduction of total nitroge is recommended to attain a DO level consistent with natural conditions. Also, a 24 percent reduction of BOD is recommended to attain a DO level consistent with natural conditions.
Marnin Of Safetv A margin of safety is used to account for any lack of knowledge concerning the relationship between effluent limitations and the in-stream water quality. In this TMDI the margin of safety is implicit due to reductions of nitrogen and BOD to levels consistent with natural conditions.
LA
Critical Conditions Critical conditions were considered by estimating nutrients and BOD on an annual average basis. The reductions of nutrients and BOD apply to all conditions.
MOS
Seasonal Variation Seasonal variation was considered by applying the reductions of nutrients and BOD to seasons.
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REFERENCES
ERD. 1999. Lake Hancock Water and Nutrient Budget and Water Quality Improvemen. Project. Final Report. December 1999. Prepared for SWFWMD by H. H. Harper, J.L. Herr, D. M. Baker. Environmental Research and Design, Inc.
Florida Administrative Code (F.A.C.). Chapter 62-302, Surface Water Quality Standards.
Florida Department of Environmental Regulation, Bureau of Water Analysis, Water Quality Analysis Section. Water Quality Technical Series. Voulme 2. No. 68. City of Lake Wales STP Wasteload Allocation Documentation. 1982.
Florida Department of Environmental Regulation, Bureau of Surface Water Manageme Point Source Evaluation Section. Water Quality Technical Series. Voulme 2. No. 116. Peace Creek Canal, Water Quality Based Effluent Limitation Documentation, City of Winterhaven. 1 988.
Florida Department of Environmental Protection. February 1,200 1. A Report to the Governor and the Legislature on the Allocation of Total Maximum Daily Loads in Florida. Tallahassee, Florida: Bureau of Watershed Management.
FDEP, 2003. Water Quality Status Report Sarasota Bay and Peace and Myakka Rivers. Florida Department of Environmental Protection, Division of Water Resource Management. Southwest District. Group 3 Basin. September 2003.
Florida Department of Environmental Protection (FDEP), 2000. 2000 Water Quality Assessment for the State of Florida. Section 305(b) Main Report.
FDEP, 2005.TMDL Report, Nutrient TMDL for Winter Haven Chain of Lakes (WBID, 1521K, 1521H, 1521G,1521F, 1521E, 1521D, 1521B, 1521,1488C, 1488A). Kevin Petrus. September 13, 2005
Florida Agriculture Statistics Service. 2002. United States Department of Agriculture, National Agriculture Statistics Service, Florida Field Office. 2002 Census of Agricultui State and County Profiles. http://www.nass.usda.gov/fl/.
Harper, H. H. and D.M. Baker. 2003. Evaluation of Alternative Stormwater Regulatio for Southwest Florida. Environmental Research & Design, Inc. (Table 7).
McCary, J.P., and M.A. Ross. 2005. Winter Haven Chain of Lakes PLRG Study. Fin; Report to Southwest Florida Water Management District. University of South Florida, Center for Modeling Hydrologic and Aquatic Systems, Tampa, FL.
SWET. 2002. WAM Training Manual. Developed for EPA Region IV Training.
Published by: Soil and Water Engineering Technology, Inc., Gainesville, FL. ~ I
SWFWMD. 2005. Peace River Cumulative Impact Assessment. Southwest Florida Water Management District. http://www.swfwmd.state.fl.us/wateman~peaceriver/. I SWFWMD. 2005. Lake Parker, Lake Bonny, and Banana Lake, MS Word document forwarded by the FDEP.
SWFWMD. 2004. Lake Hancock Lake Level Modification Preliminary Evaluation Dra Final Report Produced for: Southwest Florida Water Management District Prepared by: BCI Engineers & Scientists, Inc, May 2004
USEPA. 1991. Guidance for Water Quality -based Decisions: The TMDL Process. U. Environmental Protection Agency, Office of Water, Washington, DC. EPA-44014-91- 001, April 1991.
US Environmental Protection Agency - Region 4 Atlanta, GA. 2001, Water Quality Analysis Simulation Program (WASP) Version 6.0 DRAFT: User's Manual By Tim A. Wool, Robert B. Ambrose, James L. Martin, Edward A. Comer
USEPA. 2001. BASJNS PLOAD Version 3.0 Users Manual. U.S. Environmental Protection Agency, Office of Water, Washington, DC. 2001.
USEPA. Patton, March 19, 1985. Internal memorandum from Patton to Kutzman.
USEPA. Ravan, August 20,1985. Correspondence from Ravan, EPA Regional Administrator to Tschinkel, Secretary FDEP. i USEPA.Kutman, July 15, 1985. Internal memorandum from Kutzman to Wagener.
USEPA.Kutman, March 19, 1985. Correspondence from Kutzman, EPA Water Qualit Section Chief to Goren, Florida Dept. Envir. Regulation Environmental Specialist. 1 USGS. 1998. National Water-Quality Assessment Program. Water-Quality Assessment of Southern Florida-Wastewater Discharges and Runoff. USGS Fact Sheet FS-032-98.
I
Final Peace River Basin, Florida i
I Dissolved Oxygen, Nutrient, Turbidity and TSS , I
Total Maximum Daily Loads
(WBIDs 1501 A, 1497,1623K, 1 61 3,1626,1580,1539,161 1, 1921,1871) ~
Prepared by: US Er~vironrnental Protection Agency
Region 4 Atlanta, GA
January, 2006
united States firtvironmeratal Protedmn Agenty
In compliance with the provisions of the Federal Clean Water Act, 33 U.S.C $1251 et. seq., as amended by the Water Quality Act of 1987, P.L. 400-4, the U.S Environmental Protection Agency is hereby establishing the Total Maximum Daily Load (TMDL) for dissolved oxygen, nutrients, turbidity, and TSS Peace River Basin (WBIDs 1501 A, 1497, 1623K, 16 13, 1626, 1580, 1539, 1617, 1921 and 1871). Subsequent actions must be consistent with this TMDL.
James D. Giattina, Director Water Management Division
CONCURRANCES:
A. Bartlett
G. Mitchell
Date
J. Giattina