Attachment G

– WQBEL Technical Support Document1 Technical Support Document Derivation of the Water Quality Based Effluent Limit (WQBEL) for Phosphorus in Discharges to the Everglades Protection Area

United States Environmental Protection Agency August 24, 2010

This report documents the United States Environmental Protection Agency’s (USEPA) derivation of the Water Quality Based Effluent Limit (WQBEL) to be applied in National Pollutant Discharge Elimination System (NPDES) permits for discharges from the Stormwater Treatment Areas (STAs) into th e Everglades Protection Area (EPA). The WQBEL is calculated to pr otect the designated use 1 of the Everglades by ensuring the State of Florida water quality criter ion for total phosphorus of 10 pa rts per billion (ppb) as a longterm geometric mean is not exceeded in th e receiving waters of the Everglades.

The WQBEL for STAs 1E, 1W, 2, 3/4, 5, 6, and other future STAs, has two components,

both of which must be met. TP concentra tions in the discharge from each STA may not

exceed either:

Part 1: 10 ppb as an annual geometric mean in more than two consecutive years; or Part 2: 18 ppb as an annual flow-weighted mean

Both parts of the WQBEL are n ecessary to assure th at the long-term criterion of 10 ppb is met at each STA. The background and statisti cal approach for derivation of each WQBEL component is described below.

I. The Total Phosphorus Criterion

Since the WQBEL is derived from and must comply with the underlying water quality standard, it is important to understand the unde rlying phosphorus criterion for the Everglades Protection Area. In 2005, the Florida Depart ment of Environmental Protection (FDEP) adopted and USEPA approved a numeric water quality criterion for Total Phosphorus (TP) for the EPA. The TP criterion is a long-term geometric mean of 10 parts per billion (ppb, or micrograms per liter) in surf ace water (Rule 62-302.540(4)(a), Florida Administrative Code (F.A.C.)). The criterion app lies throughout all of the EPA, which includes the Arthur R.

Marshall Loxahatchee National Wildlife Ref uge (Refuge), Water Conservation Areas (WCAs) 2 and 3, and Everglades National Park (Park). The 10 ppb geom etric mean criterion is the numeric interpretation of the FDEP narrative nutrient criterion, which states, “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 or fauna” (Rule 62-302.530(47)(b), (F.A.C.). The FDEP

TP Rule is consistent with the State of Florid a’s Everglades Forever Act that specifies, “In no case shall such phosphorus criteri on allow waters in the Evergl ades Protection Area to be

1 The designated use of Everglades Protection Area is "Recreation, propagation and maintenance of a healthy, well-balanced population of fish and wildlife" (Rule 62-302.540(4)(a), F.A.C., Rule 62-302.400(1)).2 altered so as to cause an imbalance in the natural populations of a quatic flora or fauna” (Florida Statutes 373.4592(4)(e)2).

Surface water TP at reference sites in the Everglades varies spatially across water quality sampling stations and temporally at any given station. TP ha s been measured monthly since

the 1970s at reference 2 locations within the Everglades marsh that are 10-20 miles

downstream of stormwater inflows. TP con centrations at these unimpacted Everglades locations experience natural fluctuations such that annual geometric mean TP can exceed 10 ppb, with individual sample r eadings even higher (FDEP 2000, 2003, 2010a). In deriving the TP criterion, FDEP used data from 9 reference sites in th e Refuge and WCA2A from 1994- 2001, along with data from an additional si te from 1978-2001, for a total of 55 “stationyears” of data (FDEP 2003). Subsequent data verify the appropria teness of the derived criterion - from 1994 to 2008, the arithmetic mean of annual geometric means 3 at the five

reference sites within WCA2A that were used to develop the TP criterion was: E5 7.3 ppb; F5 10.0 ppb; U1 8.0 ppb, U2 7.9 ppb; U3 8.0 ppb (Figure 1). Although annual geometric means varied at an individual site by a f actor of two, and approached 13 ppb to 14 ppb at reference sites F5 and U3, the long-term aver age did not exceed 10 ppb at each site. These sites remain unimpacted (FDEP 2010a).

Figure 1. Natural variation in annual geomet ric mean TP concentration at five marsh reference sites within WCA2A, where the long-t erm 10 ppb criterion is met. These stations

were used to derive the TP criterion.

2 A reference station is a location that identifies the back ground level of water quality in the Everglades. These sites exhibit the unaltered ecosystem structure and functio n that are typical of a lo cation with no evidence of phosphorus impacts or imbalance. Reference sites are routinely used to develop water quality criteria.

3 The arithmetic mean of annual geometric means at marsh stations is the calculation method that was used to derive the 10 ppb long-term geometric mean TP criterion (FDEP 2003). It is also the calculation method used to determine compliance with the TP criterion (FDEP 2006). 4 5 6 7 8 9 1 0 1 1 1 2 1 3 1 4

1994 1995 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 2006 2007 2008MarshTPppb E5

F5

U1

U2

U3

10 ppb3 II. The Total Phosphorus Criterion Assessment Methodology for the Everglades

Protection Area

The TP criterion rule for the EPA, approved by the USEPA, includes a four-part assessment methodology (four-part test) deve loped by FDEP (FDEP 2003, 2005a). The purpose of this

test is to serve as an assessment method to determine whether the long-term (decades) 10 ppb geometric mean criterion is bei ng achieved on a short-term (annual) basis. The four-part test places upper limits on TP concentration in the Everglades marsh using certain temporal and spatial scales to limit the variability in measured TP concentrations throughout the Everglades to the variability observed at the unimpacted marsh reference sites. USEPA’s

evaluations of this test have concluded that attaining these four concentra tion requirements together assures that the long-term TP c oncentration does not exceed the 10 ppb geometric mean criterion throughout the entire marsh (USEPA 2005, Walker 2004, 2005a).

The TP criterion is expressed as a geometric mean at ambient marsh stations. The geometric mean is often used to represent the central tendency of environmen tal data that are lognormally distributed and/or have a positive skew , as do phosphorus levels in the Everglades. The geometric mean has been used since the 1990s in the Everglades to determine compliance with phosphorus levels within the Refuge using da ta from 14 marsh stations (SFWMD 1992a; U. S. District Court, 2001).

The first three parts of the f our-part test allow concentratio ns to be averaged across the network of marsh monitoring sites within the Everglades waterbody to address the natural spatial and temporal variability within the EPA. The fourth part of the test provides an

annual maximum concentration not to be exceeded at any individual site (FDEP 2005a). The TP criterion was derived using data from Ev erglades freshwater open water sloughs, and, therefore, the four-part test is applied to mars h stations in these same aquatic habitats (62- 302.540 (4)(d)1. FAC). Below are the four parts of the TP criterion assessment methodology.

Part one : the five-year average of annual geometric means is not to exceed 10 ppb , averaged across the network of marsh mon itoring stations within the Everglades. This criterion was derive d based on the central tendency and upper

95% confidence interval of the annual geometric mean TP concentrations measured at a group of reference sites in WCA2A and the Refuge over six to eight year periods of record (FDEP 2003, 2005a). This part of the test is supplemented by three additional parts wh ich limit the allowable spatial and temporal variability.

Part two: the annual geometric mean, when averaged across stations, is less than or equal to 11 ppb each year . This value was derived as the upper 95 th percent confidence limit using a pooled value of spatially averaged annual variances

from individual sites within reference ar eas, and is intended to limit the temporal range of annual concentra tions across the network of monitoring stations to the range exhibited by the network of reference sites.4 Part three: the annual geometric mean, when averaged across stations, is less than or equal to 10 ppb for three of five years. This is intended to limit the allowable temporal variability on a frequency of exceedance basis.

Part four: the annual geometric mean at all individual stations is less than or equal to 15 ppb. This value is the 95 th percentile of long- term annual geometric

means estimated from annual values at five WCA2A reference sites (47 stationyears of data, FDEP 2003, 2005a). The inclusion of an additional 25 stationyears of data from five reference sites in the Refuge resulted in the same 15 ppb limit (FDEP 2003). FDEP concluded that an annual geometric mean above 15 ppb has less than a 5% chance (type I erro r) of occurring within the expected range of annual values from a long-te rm reference distribution of phosphorus data which is centered at 10 ppb (FDEP 2005a ). In other words, if the annual geometric mean exceeds 15 ppb, then it is highly unlikely (<5% chance) that the long-term criterion is met. This part of the four-part test provides an upper bound for allowable annual geometric mean s at individual monitoring stations every year and is necessary to ensure that averaging across stations alone does not mask problems at individual sites, thereby allowing areas of the EPA to become impacted without detection.

Independent evaluation of th e four-part test developed by FDEP found it to be an effective and protective methodology for dete rmining attainment of the long-term phosphorus criterion on a short-term basis (Walker 2004, 2005a; USEPA 2005).

III. NPDES requirements

Where technology-based permit effluent limits are not adequate to a ttain the water quality criterion of a waterbody, the CWA and impl ementing regulations for the CWA’s National Pollutant Discharge Elimination System (NPDES ) program require that discharge limits in NPDES permits be set at levels to meet water quality standards (see CWA section 301(b)(1)(C) and 40 CFR § 122.44(d)(1) and (5)). Th ese limits are known as WQBELs.

The NPDES regulations further require that WQBELs “derive from and comply with” all applicable water quality standards (see 40 CFR § 122.44(d)(1)(vii)(A)). USEPA

recommends the use of statistical procedures that translate un derlying water quality criteria into defensible, enforceable and protect ive WQBELs (USEPA 1996). Based on this underlying regulation and as a result of the translation, WQ BELs may differ from the underlying water quality criterion. WQBELs are often expressed as both a long-term value

and a short-term value. The simultaneous use of both values ensures that a given facility’s long-term performance is maintained, while st ill allowing for some short-term variability (USEPA 1991).

NPDES regulations require that a WQBEL be expressed as maximum daily and monthly averages, unless impractical (see 40 CFR § 122.45( d)). However, as a technical matter, USEPA understands that expres sing permit effluent limitations for nutrients like phosphorus5 over shorter terms (for example, as a daily ma ximum, weekly average, or monthly average) may be impractical and supports expression as annual permit limits since the effects of nutrients are expressed far afield and over longer time periods. Recent USEPA guidance for Chesapeake Bay permitting recognized this issu e (USEPA 2004). USEPA is following the same approach for the WQBEL in this situati on. Given the weekly and monthly variability in biological wetland treatment systems such as the STAs, monthly and daily limits are not appropriate.

IV. The two-part WQBEL for the Evergla des Protection Area and its derivation

The WQBEL for STA 1E, 1W, 2, 3/4, 5, and 6 ha s two components, both of which must be met. Compliance with the WQBEL is determined on an annual basis. TP concentrations in the discharge from each STA may not exceed either:

Part 1: 10 ppb as an annual geometric mean in more than two consecutive years; or Part 2: 18 ppb as an annual flow-weighted mean

The WQBEL was derived by using the statistica l methods described below to apply the 10 ppb long-term geometric mean (GM) TP criterion directly to the discharge for each STA. The objective of the WQBEL is to determ ine whether the long-term (decades) 10 ppb criterion is met at the point of discharge on a short-term (annual) basis. If the WQBEL is met at each STA discharge, phosphorus will not be discharged into the Everglades at

concentrations that will result in exceeding the criterion ove r the long-term (decades), nor

will short-term exceedances be allowed that would result in local degradation of the receiving waters near the disc harge points. The two-part WQ BEL allows for expected yearto-year variability in the STA discharge TP c oncentration, as observed at the marsh reference sites used to develop the TP criterion, wh ile attaining the long-term TP criterion.

A. Assumptions

The WQBEL derivation is base d on several assumptions.

1) The two-part WQBEL will be applied to each STA on an annual water year (WY) basis (May – April). 4 In the case of multiple discharge structures from a STA, the maximum annual FWM limit (18 ppb) will be applied to the FWM TP concentration across all discharge points and pump stations sampled as identified in the permit, resulting in one annual FWM reported for the STA. The annua l GM limit (10 ppb) will be applied to the GM of grab samples collected at each out flow structure on days when discharge is occurring, resulting in one annual GM reporte d for the STA. The present number of

4 A Water Year is defined as May through April: WY 2010 is May of 2009 through April 2010. This reflects the annual hydrologic cycle in south Florida with th e initiation of the wet season about May. This WY designation is used to calculate the annual marsh geomet ric mean TP values used to assess compliance with the TP criterion in the EPA. The May to April WY is also used to measure compliance with the EAA best management practice (BMP) regulatory rule and the C-1 39 Basin regulatory rule. The May to April WY also has been used to assess compliance with perm it effluent limits for the STAs since 1996.6 outflow structures for each STA is as follo ws: 1- STA1E; 2- STA1W; 1- STA2; 6 - STA3/4; 6- STA5; and 3- STA6.

2) The WQBEL is applied directly at the disc harge from each STA. Changes in surface

water TP concentration between the STA di scharge point and the location where the discharge enters the marshes of the EPA are ignored for several reasons. For example, little water exists in the marshes during th e dry season. Additionally, USEPA interprets Florida water quality standards to not allo w mixing zones or credit for dilution for nutrients. Also, STA1E and STA1W discha rge into a canal that flows unimpeded directly into the Refuge rim canal and marsh. At present, the othe r STAs discharge into

canals which flow several miles before th e water can enter EPA marshes. After hydropattern restoration efforts are in place, STA2 and STA3/4 will also discharge directly into EPA marshes. An STA discha rge into a canal may be mixed with other water with a higher or lower TP con centration, and may al so be subject to biogeochemical processes which could eith er increase (e.g., refl ux of phosphorus from the sediment) or decrease (e.g., assimilation or adsorption) the TP concentration in the water prior to entry in the Everglades mars h. These potential changes are not considered in the application of the WQB EL. Thus, USEPA is neither considering the loss of, or the addition of, phosphorus between the discharge po int and the Everglades marsh itself.

3) The derivation of the 18 ppb FWM WQBEL annual limit uses the 90 th percentile of the data distribution for STA discharge data that are adjusted to simulate an STA facility discharging at the long-term TP criterion of 10 ppb. This ap proach is consistent with NPDES program guidance (USEPA 1991) and with the derivation of previous discharge limits in the Everglades (Walker 2000; Near hoof et al. 2005; Goforth et al. 2007; FDEP 2010b). Since the 18 ppb annual limit was derive d from weekly TP data, it is assumed that future calculations of STA annual average TP will use weekly data.

4) It is assumed that the Everglades marsh does not have a long-term net assimilative capacity above the TP criterion

. This is consistent with the assumptions made to develop and adopt the 10 ppb long-term geometric mean criterion and previous determinations by USEPA and FDEP that a 10 ppb criterion is sufficiently protective and is not overly protective (USEPA 1999, 2005; FDEP 2003).

B. Database Development

Derivation of the 18 ppb FWM annual discharge limit requires a sta tistical model that accounts for the variability in TP at the STA discharge, and it requires determining the relationship between the annual geometric mean TP and flow-weighted mean TP at STA discharges. Each STA has daily flow data. Th ere are two sets of TP concentration data at each STA discharge. TP concentrations were determined for water samples collected weekly in two ways: grab samples and flow-proportiona l samples. Annual geometric mean outflow TP concentrations were calculated over the peri od of record for each STA, using weekly TP data from grab samples collected at each outfl ow structure or pump on days when discharge was occurring. This approach is consistent with the grab-sampling methodology used in deriving the phosphorus criterion and testing compliance at marsh sites. Weekly TP data7 from flow-weighted composite samples were used along with discha rge data to compute annual flow-weighted TP means. SFWMD pr ovided annual flows and flow-weighted-mean discharge concentrations over the period of record for each STA. These were computed by SFWMD using the same datasets and procedur es used in reporting compliance with the existing discharge limits (SFWMD, 2010a).

USEPA uses over 90% of the available “S TA-years” of data generated from May 1995 through April 2010 for the seven STAs. This da ta set includes data from the Everglades Nutrient Removal Project (ENRP - a 3700-acre prototype STA which was operated with nearly uniform TP and hydraulic loading a nd later was expanded to become STA1W), STA1W itself, STA1E, STA2, STA3/4, STA5, a nd STA6 (Appendix 1). The performance of some STAs has been adversely influenced by excessive phosphorus loadings, extreme droughts (2001, 2007-2008), repair of damage su stained in severe hurricanes (STA1W 2005- 2007) and initial construction problems (STA 1E 2010). Performance has also been temporarily affected by partial operation due to implementation of measures designed to optimize performance, such as internal le vee construction, vegetation management, and accompanying stabilization. The above factors are likely to have increased the variability of these STA discharges relative to that e xpected under long-term operations, although

occasional future disturbances would be e xpected due to maintenance and vegetation management practices. However, in order not to have extreme values in the dataset which are not representative of stab le STA operation, the data used for WQBEL derivation were screened in the following manner:

(1) STA startup periods were excluded;

(2) Data were excluded for STA1W fo r WY2005-2007 when performance was significantly impaired due to phospho rus overloading, hurricane damage, and

construction associated with repair and optimization; and

(3) Data were excluded for STA1E in WY 2010 because of vegetation loss and deterioration in performance due to construction problems resulting in excessive water depths.

Data were included from th e initial phase of STA-1W (ENRP WY 1996-2000), which was operated at relatively st eady flows that may not be representative of all future STAs. Data

also were included for STA5 in WY2007 and STA6 in WY 2007-2008 when the coincidence of extreme drought, construction, and implementa tion of optimization measures contributed to elevated TP concentrations in the discharg es. Retaining these da ta from STA1W, STA5 and STA6 in the data set used for WQBEL deri vation provide a broader basis for calibration and a range of variability to account for future performance and disturbances. These retained

data are indicative of conditions that USEPA reasonably expects to recur. The resulting period of record STA data used to devel op the WQBEL (50 STA-years) is sufficient compared with the number of stat ion-years of data used to de rive the TP criterion (55) and the four-part test (72). The STA outflow da ta that were used for WQBEL derivation are shown in Appendix 1.8 C. The requirement not to exceed a geometric mean of 10 ppb in more than two consecutive

years.

The first part of the WQBEL requires that 10 pp b as an annual geometric mean (GM) is not exceeded in more than two consecutive years. Th is part of the test is based directly upon the long-term TP criterion and is i ndependent of the historical STA discharge data. This part of the WQBEL is expressed as a geometric mean because the criterion is expressed as a geometric mean. As noted above, the geometric mean is often used to represent the central tendency of environmental data th at are log-normally distributed and/or have a positive skew, as do phosphorus levels in the Everglades. The annual geometric mean will be computed using weekly grab samples collected at each disc harge structure on days when there is flow. The use of the weekly grab samples to compute the annual geometric mean is consistent with

how marsh data were used to derive the TP cr iterion and are used to assess compliance with the four-part test.

This two consecutive year requirement is non-para metric and is insensit ive to the variability in the STA discharge concentration since it is based on the central tendency (the geometric mean) of the long-term criterion. Three years of data are required to determine compliance with this WQBEL requirement. A WQBEL te st based on three years of data makes it possible to determine compliance with a criteri on that is expressed as a long-term value (decades) in a shorter time period (three year s), thereby providing protection against nonattainment of the water quality criterion in advance of a longer term measurement period such as five years.

Assuming random and statistically independent variations in the annual GMs, if an STA is discharging at the long-term criterion of 10 ppb, the probability of exceeding 10 ppb in 3 (more than 2) successive years would be 0.13 (= 0.5 N where N = number of years). This type I error rate of 0.13 is consistent with the 0.10 type I error rate (90 th percentile) used to derive the annual limit (see page 21). The re quirement of not exceeding a limit in more than two consecutive years is already used in the TP control regul atory rules for the EAA basin and the C-139 basin (SFWMD 2010b).

D. Derivation of the requirement not to exceed 18 ppb flow-weighted annual average in any

year

1) Use of the flow-weighted mean

The flow-weighted mean (FWM) is the most commonly used statistical expression of the central tendency to account fo r total phosphorus at discharge st ructures in the Everglades. All of the phosphorus limits and water quality st andards applied at wate r discharge structures in the Everglades use FWM TP values. For th e Park, FDEP’s phosphorus rule specifies that achievement of the criterion will use phosphorus lim its that are applied as FWM TP values at structures that discharge into the Park (Rule 62-302.540(4)(c), F.A.C.; SFWMD 1992a; Walker 1999; U. S. District Court 2001) . The FWM concentration is the average9 concentration of phosphorus in the water, we ighted proportionally for the volume of flow during the time of sampling:



## ∑ ∑ ×

= Flow ion Concentrat Flow FWM ] [

Phosphorus data are collected weekly at STA di scharge structures, and water flow rate is measured daily. Phosphorus samples taken dur ing weeks when the flow is high are given proportionally greater weight in the calculation of the flow-wei ghted mean than are samples taken when the flow is low. Acute, high fl ow events result in a higher load of phosphorus discharged into the Everglades, as compared to weeks with the same concentration but less flow. Other statistical expressi ons of the central tendency or mean do not consider the flow

rate when the TP concentrati on is sampled. Without the consid eration of flow, mass loading of phosphorus is absent. Concentration alone wi thout flow does not account for flow events that can affect the cumulative delivery of phosphorus to the receiving water body.

For the Everglades marsh, the loading of nutri ents such as phosphorus is an important consideration in evaluating and addressing the impacts on the water body. The naturally nutrient-poor marshes of the Everglades are a ffected by both the concentration and the load of phosphorus. Once phosphorus is discharged into the Everglades, this mass or load of TP cycles within the Everglades marsh where it can continue to impact Everglades flora and fauna. The higher total load received from higher flows may accumulate in the marsh and affect the long-term observed concentrations in the marsh. 5

Stormwater Treatment Area efflue nt TP and water volume tend to vary seasonally because of

the seasonal nature of rainfall and stormwater runoff. Water volume and TP concentration also vary annually because of variation in rainfall and st ormwater runoff across years. For example, summary data provided by South Fl orida Water Management District (SFWMD 2010a) indicate that from 2005-2009 the total volum e of water treated ea ch year by the six STAs ranged from about 774,000 acre-feet in water year 2008 to 1,556,000 acre-feet in 2005. Outflow FWM TP for individual STAs ranged from 13 ppb (STA 3/4 2009) to 193 ppb (STA5 2007).

Expressing the WQBEL as a FWM TP concentr ation includes consid eration of not only concentration but load as well, and theref ore protects the downstream Everglades from phosphorus loads. Loading rate (mass per time) is calculated as flow rate (volume per time) multiplied by concentration (mass per volume). For each STA, TP is sampled weekly via grab samples taken at the downstream side of each discharge structure. Flow-proportional composite samples are also taken weekly and analyzed for TP at these same locations to better account for the variation in discharge volu me within the week. Weeks with high TP concentration and high discharge rate are of c oncern because of their potential to impact the Everglades. During the week of February 16, 2006 (week 1), STA1W discharged 127 ppb of

5 Excess phosphorus causes systemic ecological responses in the Everglades such as changed algal (periphyton) communities, loss of water column dissolved oxygen, changes to invertebrate communities and the food web, and expansion of cattail with a decline in native sawgrass, sloughs and wet prairies (SFWMD 1992b; McCormick et al. 1999, 2002; FDEP 2000, 2001a, 2001b).10 TP at a flow rate of 61 cubic feet per s econd (cfs) (weekly STA data from FDEP 2010). During the week of September 28, 2004 (week 2), this STA also discharged at 127 ppb, but at a much higher flow rate of 3115 cfs. Th e phosphorus load discharged during week two was about 50 times higher than during week one due to the much higher discharge rate, although the TP concentrations were identic al. During the week of December 10, 2002 (week 3) STA1W discharged 63.5 ppb at a flow rate of 1240 cfs. Although the concentration discharged during week one was two times the concentration discharged during week three, the TP load discharged into the Everglades during week three was over ten times higher due to the much higher discharge rate. Only e xpressing the WQBEL as the geometric mean of

TP at STA outflows does not consider the flow volume from the STA and, therefore, overlooks the discharge of high phosphorus loads when flows are high.

2) The relationship between the GM and FWM at STA discharges.

For each STA, the annual GM and FWM TP con centrations were calculated for each STA using the procedure described above. Figur e 2 shows the correlation between the flowweighted means and geometric means on a yearly basis, as well as for the total period of record by STA. The FWMs are approximately 20% higher than the GMs, both on an annual and long-term basis (LTFWM = 1.23 x LTGM, R 2 = 0.92). These results indicate that based on the same data, at the STA discharge the long-term TP geometric mean of 10 ppb (the criterion) is equiva lent to a long-term TP flow-w eighted mean of 12 ppb. The high percentage of explained variance (R 2 = 0.92) indicates a very str ong relationship, one that can be reliably employed in this WQBEL derivation. Previous investigator s also independently concluded that a long-term geometric mean of 10 ppb is equivalent to 12 ppb flow-weighted for STA discharges (FDEP 2010b).11 Figure 2. Relationship between Flow-Weighted Mean (FWM) and Geometric Mean (GM) Total Phosphorus Concentrations in ST A Discharges. Data are not rescaled.

Historical monitoring data from each ST A (not rescaled). Blue diamonds ( ♦ ) are the results for each STA-year; red squares ( ■ ) are the period of record result for each STA. The dotted line depicts the average ratio of the FWM to th e GM across STAs and years (y = 1.23x). The FWMs of STA discharges typically exceed GM s by 23% on both an annual basis and a longterm basis. Long-term is the period of record for each STA, the longest of which is 12 years for STA6 (Appendix 1). This relationship between flow-weighted means and geometric means reflects the flow and concentration dynami cs associated with STA discharges. The relationship is observed over a wide range of discharges and concentrations. 

### STA6 STA5

STA34 STA2

STA1E STA1W

ENRP



### 10 100

10 100

Geometric Mean ppbFlow‐WeightedMeanppb y = 1.23 x, R 2 = 0.9212 3) Data rescaling

Deriving the annual maximum WQ BEL requires consideration of the variability of TP concentration at the STA discharge. Since none of the STAs are curre ntly discharging at a long-term geometric mean of 10 ppb, the existin g data could not be directly used to understand and address year-to-year variability. Theref ore the historical data from each STA have been statistically adjusted or rescaled to simulate a STA discharge at the criterion (a long-term geometric mean of 10 ppb). The rescaling factor for each STA is computed as the ratio of the 10 ppb criterion divi ded by the arithmetic mean of the annual geometric mean TP concentrations at the point of discharge. This calculation procedure is consistent with the procedure used in the phosphorus water quality standards for computing long-term geometric

mean concentrations at marsh sites under th e four-part test compliance methodology (FDEP 2006). The summary of results by STA is pr ovided in Appendix 3. The original and rescaled annual average STA discharge TP data are shown in Figure 3 (geometric means) and Figure 4 (flow-weighted means). Similar to re ference sites in the Everglades marsh (Figure 1), annual average TP at STA discharges ma y vary while still attaining the long-term

criterion.13 Figure 3. Period of record annual geometric mean TP concentration for each STA discharge.

10 100 1000ENRP_1996ENRP_1997ENRP_1998ENRP_1999ENRP_2000STA1W_2001STA1W_2002STA1W_2003STA1W_2004STA1W_2005STA1W_2006STA1W_2007STA1W_2008STA1W_2009STA1W_2010STA1E_2008STA1E_2009STA1E_2010STA2_2002STA2_2003STA2_2004STA2_2005STA2_2006STA2_2007STA2_2008STA2_2009STA2_2010STA34_2006STA34_2007STA34_2008STA34_2009STA34_2010STA5_2001STA5_2002STA5_2003STA5_2004STA5_2005STA5_2006STA5_2007STA5_2008STA5_2009STA5_2010STA6_1999STA6_2000STA6_2001STA6_2002STA6_2003STA6_2004STA6_2005STA6_2006STA6_2007STA6_2008STA6_2009STA6_2010HistoricalGMppb

0 5 10 15 20 25 30 35ENRP_1996ENRP_1997ENRP_1998ENRP_1999ENRP_2000STA1W_2001STA1W_2002STA1W_2003STA1W_2004STA1W_2005STA1W_2006STA1W_2007STA1W_2008STA1W_2009STA1W_2010STA1E_2008STA1E_2009STA1E_2010STA2_2002STA2_2003STA2_2004STA2_2005STA2_2006STA2_2007STA2_2008STA2_2009STA2_2010STA34_2006STA34_2007STA34_2008STA34_2009STA34_2010STA5_2001STA5_2002STA5_2003STA5_2004STA5_2005STA5_2006STA5_2007STA5_2008STA5_2009STA5_2010STA6_1999STA6_2000STA6_2001STA6_2002STA6_2003STA6_2004STA6_2005STA6_2006STA6_2007STA6_2008STA6_2009STA6_2010RescaledGMppb Data

15 ppb = 4PT Marsh Limit

10 ppp = Criterion

Top: Annual geometric means. Red bars are the long-term geometric mean for each STA.

Bottom: Annual geometric means rescaled so th at each STA discharge has a discharge at the long-term geometric mean criterion of 10 ppb. Data outliers that were excluded from the WQBEL derivation because they do not represen t STAs in stable operation include STA-1W in WY 2005-2007 (overloading, hurricane damage , and repair) and STA-1E in WY 2010 (vegetation loss and deteriorati on in performance due to cons truction problems resulting in excessive water depths).14 Figure 4. Period of record annual flow-weighted mean TP concentration for each STA.

10 100 1000ENRP_1996ENRP_1997ENRP_1998ENRP_1999ENRP_2000STA1W_2001STA1W_2002STA1W_2003STA1W_2004STA1W_2005STA1W_2006STA1W_2007STA1W_2008STA1W_2009STA1W_2010STA1E_2008STA1E_2009STA1E_2010STA2_2002STA2_2003STA2_2004STA2_2005STA2_2006STA2_2007STA2_2008STA2_2009STA2_2010STA34_2006STA34_2007STA34_2008STA34_2009STA34_2010STA5_2001STA5_2002STA5_2003STA5_2004STA5_2005STA5_2006STA5_2007STA5_2008STA5_2009STA5_2010STA6_1999STA6_2000STA6_2001STA6_2002STA6_2003STA6_2004STA6_2005STA6_2006STA6_2007STA6_2008STA6_2009STA6_2010HistoricalFWMppb

0

10 20 30 40 50 60ENRP_1996ENRP_1997ENRP_1998ENRP_1999ENRP_2000STA1W_2001STA1W_2002STA1W_2003STA1W_2004STA1W_2005STA1W_2006STA1W_2007STA1W_2008STA1W_2009STA1W_2010STA1E_2008STA1E_2009STA1E_2010STA2_2002STA2_2003STA2_2004STA2_2005STA2_2006STA2_2007STA2_2008STA2_2009STA2_2010STA34_2006STA34_2007STA34_2008STA34_2009STA34_2010STA5_2001STA5_2002STA5_2003STA5_2004STA5_2005STA5_2006STA5_2007STA5_2008STA5_2009STA5_2010STA6_1999STA6_2000STA6_2001STA6_2002STA6_2003STA6_2004STA6_2005STA6_2006STA6_2007STA6_2008STA6_2009STA6_2010RescaledFWMppb Data QBEL = 18.1

LTFWM = 12.0

Top: Annual flow-weighted means. Red bars are the long-term FWM mean for each STA.

Bottom: Annual FWMs rescaled so that each STA discharge has a long-term flow-weighted mean of 12 ppb, which is equivalent to a geomet ric mean of 10 ppb. Data outliers that were excluded from the WQBEL derivation because they do not represent STAs in stable operation include STA-1W in WY 2005-2007 (ove rloading, hurricane damage, and repair) and STA-1E in WY 2010 (vegetation loss a nd deterioration in performance due to construction problems resulting in excessive water depths).15 4) Derivation of the Annual Maximum Discharge Limit

A maximum discharge limit is needed to assess compliance annually and to assure that STA discharges do not cause exceedances of the TP criterion in the EPA. The methodology used to derive the annual maximum discharge limit is similar to that used in previous derivations of the interim STA limit of 50 ppb (Walker 199 6; Nearhoof et al., 2005 ) and in previous WQBEL derivations (FDEP 2005b; 2008; 2010b; Walker 2005b). In translating the 10 ppb long-term geometric mean (LTGM) criterion into the annual FWM discharge limit, USEPA considered the expected year-to- year variability in TP concen trations, as observed both at marsh monitoring sites and in the STA discha rges, and differences between the geometric and flow-weighted annual mean va lues observed at STA discharges.

The statistical derivation (Appe ndix 2) involves fitting a log-nor mal distribution to the annual data, adjusted to reflect the expected variab ility in an STA FWM discharge that is in compliance with the 10 ppb long-term geometric m ean criterion. Given that some individual STAs have only three or five years of data, da ta for all STAs were pooled. The data from

each STA have been rescaled as described abov e to a long-term geometric mean of 10 ppb. Figure 5 presents frequency distributions of annual geometric and flow-weighted means for STA discharges in compliance with the phosphorus criterion. The annual maximum WQBEL is set at the 90 th percentile of the frequency distri bution of annual FWM values. An annual FWM above the 90th percentile would ha ve only a 10% chance of occurring within the expected range of annual values from a long-term reference distribution of phosphorus discharge data which is center ed at the TP criterion. The statistical resu lt (18.2 +/- 0.5 ppb) is rounded to the nearest ppb to derive the 18 ppb FWM limit. This 18 ppb result is identical to the annual limit derived by FDEP (2010b) us ing STA data collected through April 2009.

A second method confirms the annual maximum WQBEL. The TP criterion four-part test limit that must be met every year at each mars h station is 15 ppb as a geometric mean. This is the marsh counterpart to the annual limit that must be met every year at each STA. As indicated above, annual FWMs in STA discharges average 23% hi gher than GMs (Figure 2). Simply translating the 15 ppb GM marsh limit directly into a FWM limit (FWM = 1.23 x GM) yields a WQBEL estimate of 18.45 ppb, whic h when rounded to 18 ppb is identical with the result obtained from the frequency dist ribution of the rescaled STA data. Together

these results indicate that the available data and methodologies provide a WQBEL annual maximum limit that is consistent with the marsh maximum limit, and is consistent with achieving compliance with the TP criteri on throughout the downstream marsh. A comparison of equivalent long-term and a nnual geometric and flow-weighted means is provided in Table 1.

Table 1. Comparison of Equivalent Annual and Long-Term Geometric Mean and Flow Weighted Mean TP Concentration Valu es. WQBEL requirements are in bold.

Geometric Mean Flow-weighted Mean Long-term Limit 10 ppb 12 ppb Annual Limit 15 ppb 18 ppb16 Figure 5. Frequency Distributions of Annual Geometric and Flow-Weighted Means for STA Discharges in Compliance with the P Criterion.

Variations in annual FWMs (red) and GMs (blue) expected if the discharge had a long-term GM of 10 ppb or the equivalent long-term FWM of 12 ppb (12.0, Standard Error = 0.5 ppb).

The difference between the distri butions reflects the fact that at STA discharges FWMs are on average 23% higher than the GMs of STA Discharges (Figure 2). The solid line represents the statistical fit of rescaled STA data (log-normal distribution).

The 18 ppb WQBEL to be met each year is found at the intersection of the FWM distribution

with the 90 th percentile (18.2 with an estimated uncertainty of +/- 0.5 ppb).

The distribution of geometric means is similar to the distribution at marsh sites used to derive the phosphorus criterion. The vert ical blue line indicates the 90th percentile of the GM, which is the 15 ppb annual limit for compliance with the phosphorus criterion at marsh sites.

SE = Standard Error, approximate uncerta inty in the LTFWM and WQBEL estimates. 0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0

4 6 8 10 12 14 16 18 20 22 24

Yearly TP ppbFrequency

Flow

‐ Weighted

Geometric TP Criterion = 10 ppb WQBEL = 18 pp b

4PT Marsh Limit = 15 ppb17 The concept of higher permit limits for shorte r compliance periods is scientifically sound provided that the resulting WQBEL attains the water quali ty criterion (USEPA 1991). Shorter term compliance periods are also consiste nt with the four-part assessment test for the criterion, which includes a short-term requirement that the annual geometric mean of 15 ppb

not be exceeded at each individual station. The corresponding STA effluent short-term annual limit is 18 ppb (FWM).

Requiring a one-part WQBEL with only the requirement not to exceed 18 ppb (FWM) as an annual maximum limit is inadequate for assuring th at the criterion is met at the STA effluent over the long-term. If the future variability in TP at the discharges is less than the variability assumed in the derivation, and the discharges ar e near 18 ppb, it is possible that STAs could discharge in a range that does not achieve compliance with th e TP criterion (i.e. exceed a LTGM of 10 ppb or the equivalent LTFWM of 12 ppb) and still be in compliance with the annual FWM discharge limit of 18 ppb. The facil ity could be found to be “in compliance” while the long-term concentra tion at the effluent could be as high as 18.4 ppb (18 ppb after rounding), well above the LTFWM of 12 ppb. Moreover, USEPA (2005) and FDEP (2003) rejected a proposal for a long-term geometric mean TP criterion of 15.6 ppb as not being protective within the Everglades marsh, and concluded that based on nutrient threshold research, at a long-term criterion of 15.6 ppb imbalance has already occurred. FDEP

concluded that “all of the information eval uated by the Department indicates that the proposed phosphorus criterion of 10 ppb would be protective of the natural flora and fauna in the EPA without being overly protective or below natural background values” (FDEP 2002, 2003). USEPA previously reviewed the scient ific basis for the 10 ppb TP criterion and concurred with FDEP’s conclusion during the 20 05 Clean Water Act review of the TP rule (USEPA 2005). Therefore, an STA dischargi ng at 18 ppb over the long- term would not meet the protective criterion.

The discharge must meet both requirements to be in compliance with the WQBEL. In essence, neither levels of TP in the discharge that would result in an exceedance of the water quality criterion on a long-term basis (10 ppb as a GM) nor levels that would exceed the single station maximum (15 ppb as an annual geometric mean) are allowed. The annual FWMs will be computed from STA outflow volume and concentration data using the methodology currently used by SFWMD in reporting compliance with the existing STA discharge permits. Compliance is evaluated based upon data collected in each Water Year (May - April). For compliance purposes the WQBEL and annual results will be rounded to

the nearest whole number.18 Figure 6 presents the year to year variability in marsh and STA discharge concentrations. The variability of TP observed at the STA discharg es to date (0.33) is s lightly higher than the variability observed at unimpacted marsh st ations and STA3/4, the best performing STA (0.22). However, the variability observed at the ENRP was less than what occurs at Everglades marsh sites while the variability observed at STA 3/4 was comparable to marsh

sites.

Figure 6. Year-to-Year Vari ability in Marsh and STA Discharge Concentrations

Everglades Marsh Sites, Geometric Means, POR 1995

‐ 2010, >= 10 Years / Site STAs Geo Means, >= 3 Yrs STAs FW Means

0.00 0.05 0.10 0.15 0.20 0.25 0.30 0.35 0.40 0.453ANMESO3ASMESOCA215CA27CA29CA311CA315CA316CA317CA318CA32CA33CA34CA35CA38EPLOX10LOX11LOX12LOX13LOX14LOX15LOX16LOX3LOX4LOX5LOX6LOX7LOX8LOX9NE1NP201P33P34P35P36P37S345B6TSBWCA2F4GeometriENRPSTA1WSTA2STA34STA5STA6AllFlow‐WtdENRPSTA1WSTA2STA34STA5STA6All Pooled Estimate for STA FWMs

Pooled Estimate Marsh

Year-to-year standard deviations in log-transformed TP concen trations. The y-axis is the natural logarithm of the standard deviation. Li ght blue bars represen t marsh sites with at least 10 years of data. Geometric means (dark blue bars) and flow-weighted means (red bars)

are shown at STA outflows with at least three years of data.19 Figure 7 presents the STA data used to deri ve the WQBEL rescaled to the long-term TP criterion (FWMs top, GMs bottom). Annual aver age TP concentration at the STA discharge may vary while still attaining the WQBEL.

Figure 7. The two-part WQBEL. STA data us ed to derive the WQBEL are shown rescaled to the long-term TP criterion.

0 5 10 15 20 25ENRP_1996ENRP_1997ENRP_1998ENRP_1999ENRP_2000STA1W_2001STA1W_2002STA1W_2003STA1W_2004STA1W_2008STA1W_2009STA1W_2010STA1E_2008STA1E_2009STA2_2002STA2_2003STA2_2004STA2_2005STA2_2006STA2_2007STA2_2008STA2_2009STA2_2010STA34_2006STA34_2007STA34_2008STA34_2009STA34_2010STA5_2001STA5_2002STA5_2003STA5_2004STA5_2005STA5_2006STA5_2007STA5_2008STA5_2009STA5_2010STA6_1999STA6_2000STA6_2001STA6_2002STA6_2003STA6_2004STA6_2005STA6_2006STA6_2007STA6_2008STA6_2009STA6_2010RescaledYearlyFWMppb

1

‐ Yr Limit = 18 ppb

Long

‐ Term FWM = 12 ppb

0 5 1 0 1 5 2 0 2 5ENRP_1996ENRP_1997ENRP_1998ENRP_1999ENRP_2000STA1W_2001STA1W_2002STA1W_2003STA1W_2004STA1W_2008STA1W_2009STA1W_2010STA1E_2008STA1E_2009STA2_2002STA2_2003STA2_2004STA2_2005STA2_2006STA2_2007STA2_2008STA2_2009STA2_2010STA34_2006STA34_2007STA34_2008STA34_2009STA34_2010STA5_2001STA5_2002STA5_2003STA5_2004STA5_2005STA5_2006STA5_2007STA5_2008STA5_2009STA5_2010STA6_1999STA6_2000STA6_2001STA6_2002STA6_2003STA6_2004STA6_2005STA6_2006STA6_2007STA6_2008STA6_2009STA6_2010RescaledGMppb Rescale d Da ta

15 ppb = 4PT M ars h Lim it

10 ppp = C riterio n

L T Geo Mean = 1 0 ppb 4PT M arsh

Lim i t = 1 5 ppb20 Figure 8 presents the WQBEL compared to the long-term GM and FWM effluent TP for the seven individual STAs. Data from the periods of record for each of the STAs were rescaled to meet the 12 ppb LTFWM limit (bottom) and the annual 18 ppb maximum limit (top). Although

there is some variation in the effluent concentr ations across STAs due to their performance to date, the confidence limits overlap for all seven STAs and the concentrations are statistically indistinguishable. Therefore, USEPA appropria tely pooled the STA data when deriving the WQBEL.

Figure 8. Long-term FWMs & QBELs estimated fo r individual STAs rescaled to a long-term flow-weighted mean of 12 ppb.

Rescaled Long

‐ Term F low

‐ Weighted Means and 90th Percentiles (WQBELs) for pooled da ta set and each STA.

Red lines a re results for pooled dataset. Error bars are approximate 80% confidence intervals. WQBEL = 18.2 +/- 0.6 ppb

0 5 10 15 20 25ALLENRPSTA1WSTA1ESTA2STA34STA5STA6WQBEL ppb

LTFWM = 12 +/- 0.5 ppb

0 2 4 6 8 10 12 14 16ALLENRPSTA1WSTA1ESTA2STA34STA5STA6Long-Term FWM ppb21 E) Excursion frequencies and type 1 error.

The application of any statis tically derived WQBEL involves an assessment of the risk that a facility will be found to exceed the WQBEL when in fact the facility is actually discharging at or below the l ong-term criterion. This is refe rred to as a false positive rate (in statistical terms, this is a type I error). The false positive rate assumed for the development of the WQBEL is 10%. The oppos ite risk, that a fac ility will not be found to exceed the WQBEL when it is in fact discharging above the long-term criterion, is referred to as a false negative rate (in statistical terms, this is a type II error). The risks of type I and type II e rror cannot be avoided because of the inherent variability in the data.

The derivation of the marsh TP criterion for the Refuge and WCAs 2 and 3 used a significance level of 5% (FDE P 2003, 2005a). Compared to a 5% significance level, a significance level of 10% has two times the risk that the facility will be found to be out of compliance when it is meeting the long- term criterion. The phosphorus criterion

limits for inflows to the Park used a si gnificance level of 10% (SFWMD 1992a). Previous STA permit effluent limits used a significance level of 10% (Nearhoof et al. 2005; Goforth et al. 2007; FDEP 2010b). The st atistical approaches that were used to develop the BMP program compliance test for the C-139 basin and for the EAA basin also used a significance leve l of 10% (SFWMD 2010b).

Figure 9 shows the expected annual excursion fre quencies for each component of the test for STAs operating with long-term GM values ranging from about 6 to 14 ppb, as compared with the long-term GM of 10 ppb required to achieve compliance with the P criterion. Results are based upon 50,000 years of simulated discharge c oncentrations drawn from the log-normal distribution with the parameters calibrated to th e rescaled historical monitoring data used to derive the annual limit (natural logarithm m ean = 2.47, standard deviation = 0.33, Figure 6). Requiring more than one WQBEL test simultaneous ly results in a highe r type I error rate (excursion frequency) than a single test because each individual test has a type I error. The resulting type I error for the two-part WQBEL assuming the current variance at STA discharges is estimated to be about 15% (F igure 9 top, intersection of either excursion frequency with 10 ppb LTGM). This variability in TP at the discharge is expected to

decrease in the future as the STAs are desi gned and operated to achieve compliance with the

criterion. The lower chart shows the excursi on frequencies that would occur if the actual discharge variability were similar to mars h data or to STAs operating in the low concentration range (natural logarithm standard deviation = 0.22, Figure 6). STA 3/4 has operated with a TP variance at the discharge co mparable to the Everglades marsh, while the ENRP had a variance lower than the Everglades marsh (Figure 6). With future operations, as STA discharges operate at a lower concentra tion range with the va riance observed at STA 3/4 and the ENRP, the excursion frequency is pr ojected to decrease to less than 10% (Figure 9 bottom, intersection of either excursion fr equency with 10 ppb LTGM). As noted above, a 10% type I error or excursion frequency is cons istent with previous regulatory requirements in the Everglades. It also provides a le vel of protectiveness for the Everglades.22 Figure 9. Simulated Excursion Freq uencies versus long-term GM.

Top: Variance estimated from all historical STA data:

Bottom: Variance estimated from marsh data and STA’s in low concentration range (STA 3/4):

X Axis: LTFWM of STA discharge. An STA operating with a LTGM < 10 ppb would be in compliance with the phosphorus criterion. Y- Axis: Predicted excursion frequencies for each component of the two-part test. The red li ne depicts the probability that either of the tests will be exceeded in any year. Log StdDev = 0.22 0.0 0.1 0.2 0.3 0.4 0.5

6 7 8 9 10 11 12 13 14

Actual Long

‐ Term Geo Mean ppbExcursionFreq 1 Yr FWM > 18 ppb

> 2 Yrs GM > 10 ppb

Either Log StdDev = 0.33 0.0 0.1 0.2 0.3 0.4 0.5

6 7 8 9 10 11 12 13 14

Actual Long

‐ Term Geo Mean ppbExcursionFreq 1 Yr FWM > 18 ppb

> 2 Yrs GM > 10 ppb

Either23 V. Summary

The WQBEL presented here for the STA discharges is derived from and complies with the 10 ppb geometric mean long-term TP criterion for the Everglades. The WQBEL for STA 1E, 1W, 2, 3/4, 5, and 6 and other future STAs that discharge into the EPA has two parts,

both of which must be met. TP concentra tions in the discharge from each STA may not

exceed either:

Part 1: 10 ppb as an annual geometric mean in more than two consecutive years; or Part 2: 18 ppb as an annual flow-weighted mean

The WQBEL is directly derived from and is equivalent to the 10 ppb geometric mean longterm TP criterion and it is directly applie d to each STA outflow. Compliance with the WQBEL is determined on an annual basis. In the case of multiple discharge structures from a STA, the maximum annual FWM limit (18 ppb) will be applied to the FWM TP concentration across all discharg e points and pump stations sampled as identified in the permit, resulting in one annual FWM reported for the STA. The annual GM limit (10 ppb) will be applied to the GM of grab samples co llected at each outflow structure on days when discharge is occurring, resulting in one annua l GM reported for the STA. For compliance purposes the WQBEL and annual results will be rounded to the nearest whole number.

Requiring both parts of the WQ BEL provides greater certainty that attainment of the WQBEL will result in attainment of the unde rlying 10 ppb long-term geometric mean TP

criterion.

Inherent in this WQBEL derivation are the following conservative assumptions:

- There is no long-term net assimilative capacity in the canal between the STA discharge point and the Ev erglades receiving marsh.

- The criterion applies th roughout the Everglades Pr otection Area, including the Everglades marsh at the edge of the waterbody. It is assumed that there is no long-term net assimilative capacit y within these marshes above the criterion that would not trigger an imbalance.

- A significance level of 10% is used to establish the 18 ppb annual limit.

- The 18 ppb annual limit to be met every ye ar is expressed as a flow-weighted mean, providing a limit that addresses TP loads.

- A two-part WQBEL is established, pr oviding assurance that the long-term

criterion with be attained at each STA. The requirement that the 10 ppb (GM) long-term criterion is not exceeded more than two consecutive years provides a statistical component that is robust to the inter-annual variability in TP at the STA discharge.

These factors together provide a margin of safety that will assure that compliance with the WQBEL will result in attainment of the TP criterion within the EPA.24 VI. References

Florida Department of Environmental Protec tion. 2000. Everglades Phosphorus Criterion Technical Support Document. Staff Draft Part I: Water Conservati on Area 2. Florida Department of Environmental Protection, Ever glades Technical Support Section. Grover Payne, Temperince Bennett, Kenneth Weaver and Frank Nearhoof. Revised November 2000. Tallahassee, Florida.

Florida Department of Environmental Protecti on. 2001a. Everglades phosphorus criterion technical support document. Staff Draft Part II: Water Conservati on Area 1. Florida Department of Environmental Protection, Ever glades Technical Support Section, Bureau of Water Resource Management. Grover Payne , Temperince Bennett, Kenneth Weaver and Frank Nearhoof. Revised January 2001. Tallahassee, Florida.

Florida Department of Environmental Protec tion. 2001b. Everglades Phosphorus Criterion Technical Support Document. Staff Draft Part III: Water Conservation Area 3 and Everglades National Park. Florida Departme nt of Environmental Protection, Everglades Technical Support Section. Grover Payne, Temp erince Bennett, Kenneth Weaver and Frank

Nearhoof. October 2001. Ta llahassee, Florida.

Florida Department of Environmental Prot ection. 2003. Development of a numeric phosphorus criterion for the Ever glades Protection Area. Pa yne, Grover, Kenneth Weaver and Temperince Bennett. Chapter 5 in 2003 Everglades Consolidated Report . South Florida Water Management Dist rict and Florida Department of Environmental Protection. West Palm Beach, Florida.

Florida Department of Environmental Prot ection. 2005a. Technical and regulatory information in support of the State of Florid a’s adopted phosphorus criterion contained in

Rule 62-302.540 Florida Administrative Code. Submitted to USEPA January 12, 2005.

Florida Department of Environmental Protec tion. 2005b. Derivation of the water quality based effluent limit (WQBEL) for phosphorus in discharges to the Everglades Protection Area. Payne, Garry, Kenneth Weaver and Fr ank Nearhoof. Florida Department of

Environmental Protection. Tallahassee, Florida.

Florida Department of Environmental Protecti on. 2006. Calculation of annual and 5-year geometric mean total phosphorus concentratio ns to assess achievement of the phosphorus criteria for the Everglades Protection Area. July 2006. Tallahassee, Florida.

Florida Department of Environmental Pr otection. 2008. Technical support document: derivation of the water quality based effluent limit (WQBEL) for phosphorus in discharges to the Everglades Protection Area. Payne, Ga rry, Kenneth Weaver and Frank Nearhoof. October 15, 2008. Florida Department of Enviro nmental Protection. Ta llahassee, Florida.25 Florida Department of Environmental Protec tion. 2010a. Annual Total Phosphorus Criteria Compliance Assessment for Water Year 2005 through Water Year 2009. Appendix 3A-6 in

S outh Florida Environmental Report – Volume I.

Florida Department of Environmental Prot ection. 2010b. Technical support document: derivation of the water quality based effluent limit for total ph osphorus in discharges to the Everglades Protection Area. May 3, 2010. Pa yne, Garry, Kenneth Weaver, Frank Nearhoof and Katie Hallas. Florida Department of E nvironmental Protection. Tallahassee, Florida.

Florida Department of Environmental Pr otection. 2010. FDEP WQBEL calculation spreadsheet. STA data used to derive WQBEL. Posted on th e Technical Oversight Committee web site May 5, 2010. File name : fdep_wqbel_calc_95-09_ggp_04-11-10.xlsx

Goforth, Gary, Nenad Iricanin, Steve Hill, Shi Kui Xue, Tracey Piccone, Frank Nearhoof and Ken Weaver. 2007. Technical support document for the STA-1W TBEL. October 12, 2007.

McCormick, Paul, Susan Newman, Shili Miao, Ramesh Reddy, Dale Gawlik, Carl Fitz, Tom Fontaine and Darlene Marley. 1999. Ecologi cal needs of the Everglades. Chapter 3 in Everglades Interim Report . South Florida Water Management District. West Palm Beach,

Florida.

McCormick, Paul V., Susan Newman, ShiLi Mi ao, Dale E. Gawlik, Darlene Marley, K. Ramesh Reddy and Tom D. Fontaine. 2002. E ffects of anthropogenic phosphorus inputs on the Everglades. Chapter 3 (pages 123-146) in The Everglades, Florida Bay and Coral Reefs of the Florida Keys: An Ecosystem Sourcebook. James W. Porter and Karen G. Porter, editors. CRC Press. Boca Raton, Florida.

Nearhoof, F., K. Weaver, G. Goforth and S. Xu e. 2005. Test for determining achievement of 50 part per billion phosphorus initial TBEL for Everglades st ormwater treatment areas. August 2005. Florida Department of Environm ental Protection and South Florida Water Management District. Tallahassee, Florida.

Pietro, K., G. Germain, R. Bearzotti and N. Iricanin. 2010. Performance and optimization of stormwater treatment areas. Chapter 5 in S outh Florida Environmental Report – Volume

I . South Florida Water Management District, West Palm Beach, FL.

South Florida Water Management District . 1992a. Surface Water Improvement and Management Plan for the Everglades. Appe ndix E. Derivation of phosphorus limits for Everglades National Park. West Palm Beach, Florida.

South Florida Water Management District . 1992b. Surface Water Improvement and Management Plan for the Everglades. Suppor ting Information Document. Derivation of phosphorus limits for Everglades National Park. West Palm Beach, Florida.

South Florida Water Management District. 2010a. STA period of record data. Excel file provided to USEPA via e-mail June 17, 2010. File name: STA-POR-WY2010.xlsx.26 South Florida Water Management District. 2010b. Phosphorus source controls for the south Florida environment. Chapter 4 in “South Fl orida Environmental Report – Volume I”. Edited by S. Van Horn and P. Wade. South Fl orida Water Management District, West Palm Beach, FL.

United States District Court. 2001. United States vs. Sout h Florida Water Management District et al, Case no. 88-1886- Civ-Hoeveler (2001 S.D. FL). Settlement Agreement. Appendix B.

United States Environmental Protection Ag ency. 1991. Technical support document for water quality-based toxics control. March 1991. Second printing. EPA/505/2-90-001. Office of Water. Washington, D. C.

United States Environmental Protection Agency. 1996. NPDES Permit Writers' Manual.

December 1996. EPA-833-B-96-003. Offi ce of Water. Washington, D. C.

United States Environmental Protection Agenc y. 1999. Approval of water quality standards

for surface waters of the Miccosukee Tribe of In dians of Florida. May 23, 1999. Letter from John H. Hankinson, Jr., Regional Administrato r, Region 4, USEPA to Billy Cypress, Chairman, Miccosukee Tribe of Indians of Florida.

United States Environmental Protection Agency, 2004. Annual Permit Limits for Nitrogen and Phosphorus for Permits Designed to Protect Chesapeake Bay and its tidal tributaries from Excess Nutrient Loading under the Nationa l Pollutant Discharge Elimination System. Memorandum from James A. Hanlon, Director, Office of Wastewater Management, to Jon Capacasa, Director, Water Permits Division, EPA Region 3 and Rebecca Hammer, Director, Chesapeake Bay Program Office. May 3, 2004.

United States Environmental Protection Agenc y, 2005. Approval of water quality standards for phosphorus within the Everglad es Protection Area. Letter fr om J. I. Palmer, Jr., Regional Administrator, Region 4, USEP A to Mimi Drew, Director, Division of Water Resource Management, Florida Department of Envi ronmental Protection. January 24, 2005.

Walker, William W., Jr. 1996. Test for evalua ting performance of Stormwater Treatment Areas. Draft. Prepared for U. S. Depa rtment of Interior. January 3, 1996.

Walker, William W., Jr. 1999. Long-term water quality trends in the Everglades. Pp. 447-

466 in Phosphorus biogeochemistry of subtropical ecosystems . K. R. Reddy, G. A. OConner and C. L. Schelske, editors. CRC Press, Inc. Boca Raton, Florida.

Walker, William W. Jr. 2000. Interim phosphorus standards for the Everglades. Pages B-34

to B-46 in Nutrient Criteria Technical Gui dance Manual. Lakes and Reservoirs. First

Edition. United States Environmental Protec tion Agency. Office of Water, Office of Science and Technology. EPA 822-B00-001. April 2000. Washington, D. C.27 Walker, William W. 2004. Evaluation of 1-year 15 part per billion limit.

Walker, William. 2005a. Evaluation of a 4-part test for TP compliance: ENP and LNWR.

Walker, William. 2005b. Estimation of water quality based effluent limits for measuring compliance with the Everglades phosphorus crite rion. Draft for discussion purposes. For the U. S. Department of Interior. November 8, 2005.28 Appendix 1. Historical STA Outflow Data Used for WQBEL Derivation

Flows, FWMs, Status from SFWMD (2010); GM = geometric means of grab samples from outlet structures on days with flow; data are from SFWMD DBHYDRO database. STA Water Yr FWM ppb Flow kac

‐ ft Grab Samples Geo Mean ppb Status (SFWMD)

ENRP 1996 24 172.4 47 24

1997 19 119 43 20

1998 21 81 48 21

1999 19 86 51 19

2000 25 121 83 19

STA1W 2001 39 91 40 25

2002 37 268 36 27

2003 53 596 78 46

2004 47 298 48 39 Cell 2 o ff

‐ line for tus suck removal and Cell 4 off

‐ line for ve g etation rehabilitation (4 months)

2005 98 383 60 68 Western Flowway off

‐ line fo r LTP enhanc, Northern flowway off

‐ line for rehab/hu rricane repairs (variable times)

2006 113 138 49 84 ""

2007 119 126 52 76 Northern, Western and Eastern Flowways off

‐ line fo r LTP Enhancements (variable times)

2008 53 117 24 42 Eastern Flowway off

‐ line for LTP Enhancements and Western Flowway off

‐ line for Rehabilitation (4 months)

2009 36 187 31 27

2010 40 221 40 36

STA1E 2008 20 125 38 18 Eastern Flowway passed startup Sept 200 7 and on

‐ line but with flow restrictions due to PSTA project

2009 21 149 26 19 Eastern Flowway on

‐ line but with flow restrictions due to PSTA projec t

2010 94 89 31 55 Western Flowwa y out of commis sion

STA2 2002 16 241 29 17

2003 18 308 39 15

2004 14 285 51 11

2005 20 371 51 15
2006 21 322 51 18 Begin load diversion from S5A Basin (G341 Clo sure)

2007 41 218 27 23

2008 22 227 30 18 Cell 4 pas sed startup 9/21/07

2009 18 291 22 17

2010 37 371 36 20

STA34 2006 23 736 252 18 Western Flowway off

‐ line fo r LTP Enhancements (6 months)

2007 22 355 83 18 Western Flowway off

‐ line fo r LTP Enhancements (1 month)

2008 20 296 117 19

2009 13 459 143 12

2010 15 637 246 14

STA5 2001 99 40 35 75

2002 83 126 78 65

2003 134 161 102 1 13

2004 97 136 96 90

2005 82 121 77 62 Cell 1B off

‐ line for LTP Enhancemen ts

2006 95 201 92 1 00 Cells 2A and 2B o ff

‐ line for LTP Enhancements

2007 192 54 24 1 31 Cell 2B off

‐ line for LTP Enhancemen ts

2008 96 7 7 76

2009 56 106 57 36 Cell 1A of f

‐ line for Rehabilitation; Sou thern Flowway passed startup 8/28/0 8

2010 51 97 86 41

STA6 1999 22 24 19 14

2000 15 59 30 13

2001 36 26 52 20

2002 16 22 67 13

2003 26 26 77 14

2004 12 29 68 10

2005 19 16 59 14

2006 25 23 47 26

2007 45 12 41 21 Section 1 o ff

‐ line 2 months fo r LTP Enhancements

2008 36 2 8 40 Section 2 pas sed startup 8/14/07

2009 27 7 24 32 Section 1 Data Onl y (Section 2 Not Stabilized, No C139 Annex Pum p )

2010 29 14 56 22 ""29 Appendix 2. Statistical Methodology

The objective is to estimate the two parame ters of the log-normal distribution (mean, standard deviation) of early FWMs for a hypothetical STA in compliance with the phosphorus criterion (Long-Term Geometri c Mean of 10 ppb). Computations are applied to log-transformed tim e series of yearly FWM concentrations for each STA, each rescaled to LTGM = 10 ppb.

y ij = ln ( C ij )

m = 

### N y k

i n

j ij

i 

### /

1 1 

# ∑∑

= =

s y 2 = ) /( ] ) ( [

1 1 2 k N y y k

i n

j i ij i

− − 

## ∑ ∑

= =

df = N - k

L p = exp (m + s y · t p )

where,

C ij = FWM for year j and STA i, rescaled to LTGM = 10 ppb.

y ij = ln [ Cij ]

i 

### y = mean Ln (FWM) for STA i across years

N = total number of STA-years

k = number of STAs

m = Mean of log-normal distribution across STAs and years (rescaled FWM)

s y 2 = pooled year-to-year vari ance across STAs and years

s y = pooled year-to-year standard deviation

df = degrees of freedom in s

L

p = limit FWM concentration with exceedance probability p

t p = 1-tailed t statistic, significance level p and degrees of freedom df

p = 0.10

(adapted from FDEP, 2010b)30 Appendix 3. Summary of Data & Calculations

Flow Historical ppb Historical ppb

ST A Years kac

‐ ft/ y r LTFWM SE GM SE

ENRP 5 116 22.0 1.3 20.4 0.8

STA1W 7 254 45.4 3.5 34.6 3.1

STA1E 2 137 20.7 0.4 18.6 0.5

STA2 9 293 22.9 3.0 17.1 1.1

STA34 5 497 18.8 2.3 16.5 1.4

STA5 10 105 95.5 10.4 78.9 9.5

STA6 12 22 22.2 2.9 19.9 2.6

Rescaled Flow

‐ Weighted Mean ppb (a) Discharge Limits ppb

Dataset LTFWM SE Ln Mean Ln SD Limit SE ( b )

ALL 12.0 0.4 2.470 0.333 18.2 0.5

ENRP 10.8 1.0 2.352 0.130 16.2 1.5

STA1W 13.1 1.0 2.518 0.168 19.1 1.6

STA1E 11.1 1.6 2.409 0.028 17.1 2.5

STA2 13.4 0.9 2.540 0.356 19.5 1.4

STA34 11.4 1.1 2.408 0.259 17.1 1.6

STA5 12.1 0.8 2.457 0.382 18.0 1.2

STA6 11.2 0.7 2.484 0.401 18.5 1.0

Summar y of Rescaled Data Ad j usted Std

Statistic Mean Std Dev Std Dev (b ) Error

ln ( GM ) 2.26 0.302 0.322 0.05

ln (FWM) 2.47 0.312 0.333 0.05

ln ( FWM / GM ) 0.21 0.196 0.209 0.03

LT Flow

‐ Wtd Mean 12.0 0.982 1.048 0.15

LT Geometric Mean 10.0

Parameter Value Formula

Number of STAs 7 NSTAS

Number of STA

‐ Years 50 NYEARS

De g rees of Freedom 43 DOF = NYEARS ‐ NSTAS

LTFWM for LTGM = 10 ppb 12.0 Average of Rescaled FWMs across STAs and Years

Std Error of LTFWM 0.40 Standard Error of Rescaled FWMs across STAs and Years Log Mean FWM 2.47 m = Mean ( Ln Rescaled FWM)

Lo g Std Dev FWM 0.333 s = Standare Deviation ( ln Rescaled FWM )

Assumed Tail Probability 0.1 p

Students

‐ t 1.30 t = F ( p
, DOF )

, 1 Tailed

FWM Limit 18.2 Exp ( m + s t )

Std Error of FWM Limit 0.50 SE of LTFWM x Limit / LTFWM

( a ) Rescaled FWM = Observed FWM x 10 / Avera g e of Yearl y Geometric Means; (b ) LTFWM is flow

‐ weighted mean of rescaled yearly FWMs for each ST A ( c ) SE for individual STAs uses p ooled estimate of y ear

‐ to

‐ y ear standard deviation ( 0.33 ) in Ln FWM (d ) Adjusted Standard Deviation Using DOF instead of NYEARS ‐ 1