LTC 027-2023 Park View Island Water Quality Community WorkshopOFFICE OF THE CITY MANAGER
NO. LTC# 027-2023 LE TTER TO COMMISSION
TO: Honorable Mayor Dan Gelb~embers of the City Commission
FROM: Alina T. Hudak, City Manag tr'v '
DATE: January 23, 2023
SUBJECT: Park View Island Water Quality Community Workshop
The City of Miami Beach is committed to protecting and enhancing our environmental resources.
The Environment and Sustainability and Public Works Departments will be hosting an interactive
community workshop at the North Shore Park and Youth Center to review the findings and
recommendations of the water quality assessment conducted by the University of Miami within
the vicinity of Park View Canal.
Tuesday, January 24, 2023 at 6:15pm
501 72 Street, Miami Beach, Florida 33141
During the workshop , University of Miam i water quality experts and City staff w ill present the
resu lts of the study, work conducted to date , and recommendat ions to reduce the levels of fecal
indicator bacteria in the Park V iew Island Canal. Participants will be enco u raged to share their
perspectives and ideas to address the sources· of pollution . In addition , a draft of the final report
will be provided for public comment (see Attachment A). The commun ity feedback at the meeting
and regarding the study will be gathe red as additional components to be considered for the action
plan .
If you have any questions related to the workshop please contact Amy Knowles, Chief Resilience
Officer/ Director of the Environment & Susta inability Department, at
AmyKnowles@miamibeachfl .gov or Lindsey Precht, Assistant Director of the Environment &
Sustainability Department, at LindseyPrecht@miamibeachfl.gov.
f /k{f
Attachment A: University of M iami Draft Final Report for Public Comment
Attachment A
Assessment of Water Quality
at the Miami Beach Park View Canal
to Identify Sources of the Fecal Indicator Bacteria,
Enterococci
DRAFT REPORT
Submitted on January 20, 2023
Authors
Larissa Montas, Ph.D.
Afeefa Abdool-Ghany, M.S.
Yutao Chen, M.S.
Erik Lamm
Ashley Quijada
Rivka Reiner
Hekai Zhang, M.S.
Helena Solo-Gabriele, Ph.D., P.E.
University of Miami, Coral Gables, FL
Department of Chemical, Environmental, and Materials Engineering
Submitted to:
City of Miami Beach ( c/o Lindsey Precht)
1700 Convention Center Drive
Miami Beach, FL 33139
This page left intentionally blank
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TABLE OF CONTENTS
EXECUTIVE SUMMARY
LIST OF ACRONYMS
TABLE OF CONTENTS
CHAPTER I, MOTIVATION, OBJECTIVES, & BACKGROUND
3
5
8
I.l Motivation and Objectives 10
1.2 Target Levels for Enterococci 14
1.3 General Categories of Enterococci Sources 16
1.4 General Conditions of the PVC 17
CHAPTER II, ANALYSIS OF HISTORICAL DAT A
II. I Enterococci Levels at the PVC 20
II.2 Rainfall, Groundwater and Tidal Fluctuations 21
11.3 Relationship Between Historic Enterococci Levels , Rainfall , Tides, and Physicochemical 25
Parameters
CHAPTER III, ANALYSIS OF STORMW ATER AND WASTEWATER CONVEYANCE
INFRASTRUCTURE
III. I Stormwater Conveyance System
III.2 Sanitary Sewer System
111.3 Evaluation of Both Systems
CHAPTER IV, OBSERVATIONS DURING VISUAL INSPECTIONS
CHAPTER V, SAMPLING EFFORTS
V.1 Intense Spatial Sampling
V.2 Sediment and Catch Basin Sampling
V.3 Intense Temporal Sampling Using an Autosampler
V.4 Depth Sampling Within the Waterway, Catch Basins, and Wells
3
36
38
40
45
48
57
62
67
TABLE OF CONTENTS (Continued)
CHAPTER VI, OVERALL ASSESSMENT AND RECOMMENDATIONS
Vl.1 Summary
Vl.2 Detailed Recommendations
Vl.3 Summary and Recommendations
ACKNOWLEDGMENTS
REFERENCES AND PERTINENT LITERATURE
APPENDIX A, Initial Review of Prior Data
APPENDIX B, Historical Data
APPENDIX C, Sample Collection Timeline and Data Tables
APPENDIX D, Details of Visual Inspections
Figures throughout the document depicting sanitary sewer structures owned or operated
by the City are exempt from public disclosure per 119.071(3)(b)l Florida Statute. The
figures depicted in black have been redacted per the Statute.
4
77
80
87
88
89
93
102
111
128
EXECUTIVE SUMMARY
The Park View Canal (PVC) is a secondary canal with limited flow located within Biscayne Bay,
an area of known degraded water quality . Within this context, the water quality at the PVC is
also degraded as documented by elevated levels of the fecal indicator bacteria (FIB), enterococci.
Monitoring of the waterway by the City of Miami Beach (CMB) was initiated April 2019 as part
of a stormwater management program designed to inform decision-making. Although the site is
not part of the Florida Department of Health (FDOH) Healthy Beaches Program, its levels are
compared to recreational beach levels to provide a basis for comparison.
Since the initiation of sample collection by the CMB, levels of enterococci have exceeded the
FDOH recommended 70 most probable number (MPN) per 100 mL recreational swimming
threshold 90% of the time, with occasional values (9.5%) exceeding 10 ,000 MPN/100 mL.
Given these elevated enterococci levels, the PVC was closed to the public for safety concerns
and several studies were initiated by the CMB to evaluate sources of enterococci to the PVC.
Testing by CMB during 2020 and 2021 showed that the FIB could be attributed to dog and bird
waste. Since prior studies had not identified one source or solution, the CMB contracted with the
the Uni versity of Miami to conduct an evaluation of historical data provided by the CMB and
implement a sample collection program aimed at identifying the geographic location of the
source and to better understand the conditions by which enterococci enter the waterway . The
sample collection program included intense spatial sampling (many samples collected around
Parkview Island within a short period oftime), intense temporal sampling (hourly sample
collection at the PVC for 48 hours), sample collection within the stormwater conveyance system
catch basins and wells, and sample collection to evaluate distributions of enterococci with
increasing water depth at the PVC.
Results show that antecedent rainfall was the main predictor of poor water quality within the
PVC. Approximately 329 ,000 m 2 of catchment area contributes rainwater runoff to nine outfalls
that discharge directly to the PVC. The sample collection program showed dramatic increases in
enterococci levels during and after a storm event. Sediments collected from the banks of the
waterway and from the surface and bottom of catch basins were characterized by levels of
enterococci up to several hundreds of thousands per gram. Water collected from catch basins
and drainage wells frequently exceeded 10,000 MPN/100 mL with some samples testing above
the 241 ,960 MPN/100 mL detection limits. However, samples collected from the CMB
groundwater monitoring wells screened at a depth of 35 feet were characterized by low levels of
enterococci suggesting that deeper groundwater does not contribute to the elevated levels of
enterococci. In addition , the ambient water in the PVC is more saline than rainfall resulting in a
surface layer ( or freshwater lens) that floats on top of the saltier water. This freshwater that is
found at the top surface of the water at the PVC frequently exceeds detection limits for
enterococci. Therefore, levels measured are highly sensitive to the method of sample collection.
The distribution in enterococci with depth (with very high levels at the upper surface) likely has
confounded the interpretation of earlier data given potential differences in how (and at what
depth) samples may have been collected .
Given these results , the primary source of enterococci to the PVC was identified as waste
deposited on surfaces that drain towards the PVC. When it rains , the stormwater washes
5
surfaces (streets, roof tops, gutters) and in the process picks up FIB that are on these surfaces.
This runoff containing the FIB from the stormwater catchment area (from Parkview Island
extending east to Collins Avenue) is then carried to the PVC through the stormwater conveyance
system creating the freshwater lens described above that contains very high levels of enterococci
that floats on the surface of the PVC. Specific sources of FIB to freshwater runoff have been
identified from visual observations as fecal matter from animals inclusive of dogs, iguanas,
racoons, and feral birds. Sources also include waste from homeless populations that live within
the stormwater catchment area and who do not have access to sanitation facilities. Trash and
seepage from garbage containers and commercial bins are also sources of FIB that contribute
towards the contamination of surface runoff as well as contaminated sediments found on the
streets and along the waterway banks. Although a specific leaking sanitary sewer was not
identified, the results of this study do not exclude the possibility of sanitary sewage from
contributing to the elevated levels of FIB. The sanitary sewer system is aging and needs upgrades
as recognized by the CMB and for which funding is needed. This aging sanitary sewer system
along with the storm water conveyance system are located just above the groundwater or within
the top few feet of the groundwater and there is a possibility of leakage from the aging sanitary
sewer system impacting shallow groundwater which in tum can be picked up by the stormwater
conveyance system and carried towards the PVC.
In efforts to address the elevated FIB levels at the PVC, we recommend that CMB develop a
comprehensive management plan to reduce the fecal loads to the waterway. This plan (portions
of which have been implemented throughout the course of this study) includes provision of
extensive outreach services to the homeless in the area, continuing with aggressive education
programs to minimize dog fecal waste throughout the stormwater catchment, and management of
non-native feral animals. Trash on streets should continue to be minimized through street
sweeping, code enforcement, educational outreach, and clean up. Leakage from trash bins
should continue to be minimized by maintaining covers and frequent trash pickup. Efforts
should continue to assess the possibility of leaks from aging sewer pipes. In the longer term,
plans are recommended for upgrading the storm and sanitary infrastructure. For stormwater,
efforts should focus on developing conveyance systems to treat the first flush and the possibility
of providing a treatment system for trash and sediment removal. Plans underway should be
implemented that upgrade the sanitary sewer system as soon as possible given the age of the
system and the possibility of leaks. The physical constraints to flow within the PVC also
contributes to the elevated levels, and efforts should also focus on improving water flow through
the removal of debris/trash and possible dredging.
As described in further detail in the last chapter of this report (see page 77), the CMB has
initiated many actions to address FIB contamination. In brief these actions have included a
public education program to encourage dog owners to pick up waste and provision of outreach
services for homeless populations. Actions have also included increased sweeping (by hand and
mechanically) of the streets, more frequent cleaning of the stormwater conveyance system to
remove trash, and more frequent trash pickup. The CMB has existing programs in place to
inspect gravity mains to identify potential leaks on Parkview Island and the CMB is committed
to fixing leaks as they are found. The CMB has applied for $ l l .5M in funding from the NOAA
Transformational Habitat Restoration and Coastal Resilience Grant to provide funding for
shoreline improvements in the PVC and other shoreline areas in Miami Beach. Most
6
significantly the CMB has received a $1 OM Florida Resilient grant to develop design alternatives
for a North Shore D and Towncenter Neighborhood Improvement Project which includes a
proposed stormwater conveyance system that will replace the existing stormwater pipe network
from between 69th and 73rd streets and from the PVC to Collins A venue to the east. The new
stormwater conveyance system is currently projected to include new catch basin structures,
manhole structures, conveyance piping, injection wells (to treat the first flush), and up to two
stormwater pump stations. The City procured Hazen and Sawyer to complete Water and Sewer
Master Plans (2019) that have identified and prioritized critical projects that must be completed
in a timely manner. The water and sewer capital improvements received $122M in funding to
implement the prioritized critical projects. Although the CMB recognizes that a lot of work is to
be done in long-term planning, it has initiated work through its Stormwater Master Plan Update
and Capital Improvement Plan that will identify critical needs to be addressed by the City over
the next 10 years. The plan will take several criteria into consideration including stormwater
flooding, tidal flooding, water quality issues, and resident complaints. The Stormwater Master
Plan Update will be completed and presented to City Commission in November of 2023.
Overall, the intent of this report is to consolidate available data, report on sampling aimed at
identifying enterococci sources, and summarize the initiatives taken by CMB. Our hope is that
this document will assist in further establishing communications with the community in efforts to
best address water quality issues associated with the PVC. A CMB community meeting
scheduled for late January 2023, aims to initiate discussions given the results from this report,
and request feedback and support from community members in establishing action plans.
7
LIST OF ACRONYMS
CFU: Colony Forming Units
CMB: City of Miami Beach
FDEP: Florida Department of Environmental Protection
FDOH: Florida Department of Health
FIB: Fecal Indicator Bacteria
GIS: Geographic Information System
KL: Kayak Launch
KLW: Kayak Launch Waterway (used interchangeably with PVC)
MF: Membrane Filtration
MPN: Most Probable Number
PVC: Park View Canal
PVI: Park View Island
TPTV: Ten Percent Threshold Value
UM: University of Miami
8
CHAPTER I
MOTIVATION, OBJECTIVES, AND BACKGROUND
9
CHAPTER I
MOTIVATION, OBJECTIVES, AND BACKGROUND
This chapter focuses on describing the motivation and objectives (Section 1.1) and the project
background for this study, including target levels for enterococci and fecal coliform (Section 1.2),
general categories of enterococci sources (Section 1.3), and general conditions of the Park View
Canal (Section 1.4)
1.1 MOTIVATION AND OBJECTIVES
The Park View Canal (PVC) at the City of Miami Beach (CMB) (GPS: 25 ° 51' 31.20" N. 80 ° 07'
33.00" W for the Launch) located near 73 Street and Dickens Avenue (Figure 1.1) has a history
of elevated levels of fecal indicator bacteria FIB).
Figure I. I: The PVC emphasizing the location of the Kayak Launch (25" 51' 31.20" N. 80 " 07' 33.00 "
W), near 73 Street and Dickens A venue Miami Beach , FL. Basemap from Google Earth .
10
In recent years several sewage leaks, at various locations in the CMB (see Figure 111.3 in Chapter
III), have resulted in sewage impacting the bay and connected waterways. In October 2018, city
inspectors discovered cracks in a wastewater pipe under the bridge to La Goree Island, located
1.3 km to the south of the PVC study area (MNT 2018). The leak lasted approximately 16 hours
during which 800 gallons of raw sewage discharged into the bay. On July 31, 2019, a wastewater
pipe at 5th Street and Michigan Avenue was accidentally drilled by a contractor causing a leak of
780,000 gallons of untreated sewage over two days, of which an estimated 390,000 gallons
discharged into the bay (MNT 2020). That following year, on March 4 and 5, 2020, the City
experienced back-to-back major sewer main breaks, one of which impacted the immediate
vicinity of the Kayak Launch within the PVC. The first occurred on March 4 near Lincoln Road
(located about 5 miles south from the PVC) when a drilling company accidentally drilled into a
42-inch sanitary sewer main (PV ISA 2021 ). The flow from this main was diverted to other pipes
in the system causing pressure shifts which then caused two additional breaks on March 5, 2020
(WLRN 2020). These additional two breaks emphasize the weakness of the existing aging
infrastructure and the need for its upgrade. One of the two breaks occurring on March 5, was
located at 28 Street and Pine Tree Drive and the second of the two breaks was located at 72nd
Street and Harding Avenue, which is located 1500 feet east of the PVC. This pipe break at
Harding Avenue spilled an estimated 665,000 gallons of untreated sewage towards the PVC.
Overall, an estimated total of 1.4 million gallons of raw sewage spilled into various waterways as
a result of these three breaks.
As part of cleanup efforts, the water quality of waterways receiving wastewater from the
aforementioned breaks was tested for FIB. On March 6, 2020 water quality measurements at the
PVC indicated that enterococci concentrations were 345 times the acceptable State and Federal
value for safe swimming. Although, within days after the spill most waterways tested below the
FDOH advisory levels (including the sites of the original March 4 break plus the other site at
Pine Tree Drive), the PVC has not tested consistently within regulatory levels.
Although the March 2020 spill focused attention on the water quality of the PVC, this site was
being monitoring prior to the spill, since April 17, 2019. This earlier monitoring was part of a
stormwater management program designed to inform decision-making. At the time during 2019,
CMB was in the process of identifying priority areas within Miami Beach for possible
installation of storm water pump and treatment stations. The CMB has installed at other locations
stormwater pump stations fitted with treatment systems designed to remove trash and grit (via
vortexer).
The March 2020 sewage leak set forth discussions by city officials, residents, and other
stakeholders on the time for onset of water quality deterioration and enterococci contamination at
the PVC (PY ISA 2021 ). Considerations put forward by residents emphasized a slow
degradation in water quality over several years with the water slowly changing color, occasional
odors, algae blooms, and a fish kill during April 2020, about a month after the sewage leaks.
Monitoring data collected at the PVC prior to the March 2020 sewage break are of particular
interest as they can provide some insight on whether deterioration of the waterway coincided
with the March 2020 sewer break.
11
Discussions by residents, CMB officials, and other stakeholders also centered on whether the
enterococci in the PVC were generated by human or animal sources, in particular dogs. The
presence of dog feces adjacent to stormwater inlets, and at the Park View Island Park, was
proposed as one possible source for the elevated enterococci levels. Opposing views pointed at
the CMB 's sewage infrastructure as the possible source, citing that the 50-to 70-year-old
sanitary sewer infrastructure was failing, possibly leaking sewage that ended up in the bay and
waterways (MNT 2020).
When the FIB at the PVC did not decrease to below regulatory levels (following the March 2020
sewage leaks) the CMB contracted to have samples analyzed for Microbial Source Tracking
(MST) markers. MST microbial markers are specialized molecular analyses that further identify
which species (humans, dogs and/or birds) are contributing fecal waste to the waterway. Thus,
MST can be used to link the elevated enterococci levels with an animal species. Five sets of
samples were collected (October 13, 2020; November 5, 2020; June 15 , 2021; September 2,
2021; September 24, 2021). Three first three sets (collected on October 13 , 2020, November 5,
2020 , and June 15, 2021) indicated a dominance of dog markers. The set collected on June 15 ,
2021 , although dominated by dog marker, showed some evidence of human marker. The set
collected subsequently on September 2, 2021 showed no significant contributions from animals.
The last set collected on September 24, 2021 showed a dominance of bird markers with some
contributions from dogs. As a result of these MST sampling efforts, the CMB developed an
educational campaign to encourage dog owners to properly dispose dog waste. The CMB
constructed facilities with doggie bags and garbage bins with signage at the park area that leads
to the PVC (Parkview Island Park) to encourage proper disposal of dog waste and thus reduce
contamination of runoff by dog fecal matter.
Despite the implementation of these measures focused on dog waste removal , the levels of FIB at
the PVC remained elevated. Given these continued elevated levels of FIB, Surfrider Foundation
initiated its own MST study (JV 2022). Three samples were collected in the PVC on July 14,
2022, one at the Kayak Launch, one to the north , and one to the south (Figure 1.2). Results from
the Surfrider Foundation study suggest that the fecal indicator bacteria levels in the waterway
come from human and dog sources. The human marker was found in 2 out of 3 replicates at the
south end , and in one replicate at the Kayak Launch. However, human was not detected at the
North end. The average number of copies detected for the Human0 1 assay were almost double at
the south (477 per 100 mL) end than at the Kayak launch (257 per 100 mL). This southern area
also coincides with the storm sewer conveyance line along 72 Street which is in-line with the
location of the March 5, 2020 , line break at Harding Avenue and 72 Street. Given these data, the
sample collection plan developed for this current study takes this information into account by
first establishing a spatially intense sampling effort to confirm the geographic location of
enterococci sources along the entire perimeter of Parkview Island to identify the location of hot
spots in the area.
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Figure 1.2: Location of Surfrider Foundation Study Sampling Sites Shown in Blue Dots Relative
to Storm and Sanitary Infrastructure at Parkview Island.
Concurrent with the water quality monitoring programs describe above, the CMB has conducted
a comprehensive set of studies of the area in attempts to isolate potential sources of FIB. In
addition to the efforts at reducing the impacts from dog waste, CMB has conducted extensive
studies evaluating the sanitary sewer system, inclusive of smoke testing, camera inspections, and
acoustic testing to identify potential leaks. With the exception of the large sewer main break of
March 5, 2020, it is our understanding that leaks identified were minor. For cases where leaks
have been identified the City has taken corrective action where possible. Corrective actions can
be taken by CMB in the public right-of-way but not on private properties. The CMB continues to
evaluate the area for potential sources of FIB inclusive of sanitary sewage but has yet to identify
a source that explains the persistent elevated levels of enterococci in the PVC.
The objective of this project was to identify the source of the elevated levels of enterococci to
the PVC. Source in the context of this study focused on understanding, "From where the
enterococci are coming from?"
We used targeted sampling and measurements to identify the type of water (fresh versus marine)
and geographic location of the source. For example, by collecting many samples along the entire
extent of the PVC in a short period of time (intense spatial sampling) we identified hot spots in
the waterway and used this information to identify infrastructure that could be conveying
enterococci towards these hotspots. Likewise, by collecting many samples at a single location
over 48 hours, we identified environmental and hydrometeorological parameters associated with
high enterococci levels.
13
We did not use Microbial Source Tracking (MST) as part of the current study. Prior MST
studies by the CMB and the Surfrider Foundation have documented that the source comes from
humans, dogs, and birds. The next step was to understand, "How enterococci from humans,
dogs, and birds enter the waterway?"
Therefore, we designed the study to better isolate potential sources to specific geographic areas
and types of water (fresh water coming from the land vs. marine water). To identify the source
and potential transport pathways to the PVC, we have categorized our analysis into four subtasks
as follows. Two subtasks focus on evaluating existing information and two focus on efforts
associated with the team's visit and sampling of the sites.
(1) Evaluate Existing Historical Water Quality Data Available through the City of Miami
Beach (Chapter II)
(2) Evaluate Existing Stormwater Conveyance Infrastructure in the Vicinity of the PVC
(Chapter III)
(3) Provide Qualitative Assessment from Visual Inspections at the Site (Chapter IV)
(4) Conduct Targeted Sample Collection Efforts to Identify Sources (Chapter V). These
efforts included:
o Intense Spatial Sampling at the PVC
o Sediment and Stormwater System Catch Basin Sampling
o Intense Temporal Sampling (Autosampler) at the PVC
o Depth Sampling Within Waterway, Catch Basins and Wells
We used the information provided by (1) to (4) above, to propose recommendations for
approaches to reduce enterococci contributions to the PVC as described in Chapter VI.
1.2 TARGET LEVELS FOR ENTEROCOCCI
Fecal indicator bacteria, enterococci and fecal coliform, are frequently used to establish safety
guidelines for use of a water body. Over the years guidelines have transitioned away from fecal
coliform to other FIB such as enterococci (used predominantly for marine waters) or E. coli
(used predominantly for freshwater). The PVC is a marine water and therefore the enterococci
guidelines would be the most applicable. Since CMB historical data are available for both fecal
coliform and enterococci, this section will describe the guideline levels for both FIB.
In Florida, two agencies set guidelines for FIB in recreational waters, the Florida Department of
Health (FDOH) and the Florida Department of Environmental Protection (FDEP). The FDOH,
through the Florida Healthy Beaches Program, provides guidelines for recreational bathing
beaches and has a centralized reporting website that lists a recreational water as good, moderate,
or poor quality (See:
https://www.floridahealth.gov/environmental-health/beach-water-quality/index.html). The
FDOH lists a water as good quality when enterococci levels are less than 36 enterococci per 100
mL, moderate quality when levels are between 36 and 70 enterococci per 100 mL, and poor
quality when enterococci levels exceed 70 per 100 mL. Beach "advisories" are issued when two
consecutive samples exceed 70 per 100 mL. The FDOH guideline is based upon the U .S.
14
Environmental Protection Agency (U.S. EPA) guidelines (U.S. EPA 2012).
Historically the FDOH had used fecal coliform for establishing beach closures. Fecal coliforms
were recommended earlier by the U.S. EPA for both freshwater and marine water (U.S. EPA,
2017). From August 2000 through June 2002 , FDOH would issue closures when fecal coliform
exceeded 800 CFU/ 100 mL. This was ad justed to 400 per 100 mL , which was in effect from July
2002 until June 2011. After June 2011, fecal coliform was dropped from FDOH sampling (Kelly
et al. 2018).
Similarly, the FDEP also has guidelines established for enterococci. The FDEP regulates surface
waters of the state according to their designated uses and thus the surface waters of the state are
separated into one of six classes. The classes that most closely align to the current uses of the
PVC are Class III and Class III -Limited (See , https://floridadep.gov/dear/water-quality-
standard s/content/surface-water-qua!ity -standards-classes -u ses -criteria). These are defined as:
• Class III: Fish Consumption, Recreation , Propagation and Maintenance of a Healthy,
Well-Balanced Population of Fish and Wildlife
• Class III -Limited: Fish Consumption, Recreation or Limited Recreation , and/or
Propagation and Maintenance of a limited population of fish and wildlife.
The bacteriological criteria for both classes as documented in the Florida Administrative Code
(F.A.C . 2016) is the same and listed as: Most Probable Number (MPN) or Membrane Filtration
(MF) counts shall not exceed a monthly geometric mean of 35 nor exceed the Ten Percent
Threshold Value (TPTV) of 130 in 10% or more of the samples during any 30-day period.
Monthly geometric means shall be based on a minimum of 10 samples taken over a 30-day
period.
Historically, prior to 2016 (F.A.C. 2013) the FDEP had recommended fecal coliform for Class
III and Class III-limited designated waters. The fecal coliform standards for both classes were
listed as: MPN or MF counts shall not exceed a monthly average of 200, nor exceed 400 in 10%
of the samples, nor exceed 800 on any one day. Monthly averages shall be expressed as
geometric means based on a minimum of 10 samples taken over a 30-day period .
A summary of the threshold values as established by the FDOH and FDEP is given by the
following table. When evaluating enterococci levels based upon single sample analyses the
general practice has been to use a threshold value of 70 per l 00 mL to designate the quality of a
beach site. For subsequent discussion purposes the value of 70 will be used as the target
threshold for assessing the microbial quality of the PVC.
15
Table: 1.1: Target Guideline Levels for Fecal Indicator Bacteria as Listed by the FDOH and
FDEP
Fecal Indicator Bacteria FDOH FDEP
Beach Recreational Standards Class III standards
Enterococci (current) • Good quality< 36 per 100 mL • Geometric mean < 36 per 100
• Moderate quality between 36 mL ,
and 70 per 100 mL • 10% of samples within a 30-day
• Poor quality> 70 per 100 mL period < 130 per 100 mL
Fecal coliform (historical , • Beach closures issued > 400
2003 to 2011) per 100 mL
Fecal coliform • Beach closures issued > 800
(historical, before 2002) per 100 mL
Fecal coliform (historical, • Monthly average < 201 per 100
before 2016) mL , 10% samples < 401 per 100
mL , Single day sample < 801 per
100 mL
1.3 GENERAL CATEGORIES OF ENTEROCOCCI SOURCES
Many beach and other marine bathing sites periodically exceed FIB guideline levels , and the
cause of exceedances is difficult to identify. Pollutants including pathogenic and non -pathogenic
microbial organisms such as FIB , nutrients and chemical compounds originate from a single
place or from many places all at once. In the context of marine recreational water quality, single
or point sources are normally related to individual discharges to a marine water body at spatially
discrete locations, for example a leaking wastewater tank in a boat or a building discharging
polluted waters directly through a pipe. Multiple sources or non-point sources are normally
associated with areas of greater spatial scale and thus the contribution of each discrete location ,
to the total amount of pollutants discharged is more difficult to calculate. For example, urban
street sediments contain trace amounts of toxic chemicals from vehicular engine exhaust
emissions, different compounds which end up on the streets and other urban areas through
atmospheric deposition (a process whereby minute particles in the atmosphere free fall to the
ground and deposit on surfaces), and microorganisms from trash, human waste and dog feces
among others. For example, rainwater runoff washes away street sediments, flows downhill and
streams to a marine waterbody along various stretches of shoreline.
Identifying the source of elevated enterococci bacteria in a marine water body is especially
difficult for areas impacted by non-point sources of enterococci and other fecal indicator
bacteria. The first step in the process is to identify the source of the bacteria (in terms of
geography or location) and to then evaluate the transport processes into the water column. Non-
point sources of enterococci to the marine environment can include shoreline sediments and
stormwater run-off through shoreline banks. Particularly, in South Florida, shoreline sediments
have been associated with microbe sources to the water column (Solo-Gabriele et al. 2000,
Desmarais et al. 2002 , Enns et al. 2012). Sources of microbes to sediments include direct input
16
from humans, animals including mammals, birds and reptiles (Wright et al. 2009). Point sources
of microbes to the marine environment include storm water outfalls, roof drains and other drains
connected to private property and accidental direct discharge from marine vessels.
The process of source identification is confounded by microbial persistence and multiplication in
the marine environment. South Florida local environmental factors are exceptionally suited for
microbe persistence over moderate to long periods of time, and microbe regrowth and
multiplication (depending on site-specific conditions). Of note, microbe multiplication is
different for different types of indicator bacteria. For example, bacteria can be split into two
primary groups (Gram-positive or Gram-negative) based upon the structure of their cellular
membranes. Studies have shown Gram-positive microorganisms such as enterococci may
survive in water with higher salinity concentrations than groups of bacteria which are Gram-
negative such as fecal coliforms.
The elevated levels of fecal indicator bacteria (FIB) at the PVC are observed for both enterococci
and fecal coliform, although enterococci are more elevated. In sanitary sewage, the opposite
holds true, where fecal coliform is typically at levels of 106 MPN per 100 mL whereas
enterococci is typically at levels of 10 5 per 100 mL (Roca et al. 2019). So, the fact that
enterococci at the PVC is higher than fecal coliform suggests that there may be differential die-
off or regrowth of enterococci in the environment. Regrowth has been documented to occur in
shallow sediment side slopes of water bodies in areas characterized by high organic matter and
shade (Solo-Gabriele et al. 2000, Desmarais et al. 2002), in stormwater drain biofilm (Skinner et
al. 2010), and high bacterial densities have been detected in algae, vegetation, including
submerged vegetation and marine wrack (Abdool-Ghany et al. 2022, Whitman et al. 2003, Grant
et al. 2001, Badgley et al. 2010). Thus, understanding microbial persistence and regrowth in the
marine environment, particularly how and where they can survive in the water column, is not
only important in the interpretation of measured bacterial levels, but also in conceiving a
sampling plan designed to answer the questions of where the bacteria are coming from and how
they enter the water column.
1.4 GENERAL CONDITIONS OF THE PVC
Several conditions have been identified that are particular to the study area and that provide
insights into the possible transport mechanisms of the bacteria into the PVC as well as
environmental conditions that might favor the regrowth and accumulation of FIB in the
waterway. The PVC is located within Biscayne Bay. It is well documented that water quality in
Biscayne Bay has been degrading (BBTF 2020), especially in the northern regions of the bay
where the PVC is found. Degradation of Biscayne Bay has been attributed to concentrated
freshwater inputs at canal inlets to the bay which erode sediments and carry pulses of nutrients
that encourage algal blooms and resultant seagrass die offs. The PVC resides within the
degraded northern Biscayne Bay. In addition to lying within a degraded Bay area, it is a
waterway within a waterway, with significant restrictions to natural water flows. The PVC
branches off from the main waterway located east of Normandy Shores Island and west of Park
View Island. The PVC is connected to a network of waterways that run north to south (Tatum,
Biscayne Point and Normandy Waterway N-S) and east to west (Normandy Waterway E-W)
17
(Figure 1.3). Most of the waterways in this network have direct access to Biscayne Bay , however
the PVC does not. It is important to note that the waterway has bends in the longitudinal
direction (Northeast and Southeast banks of Park View Island) that impede the natural
circulation of the water which is mainly driven by tides. Studies have shown that the degree of
water circulation impacts the levels of FIB within waterways . Other studies have shown that
ocean facing beaches in the State of Florida have better water quality than bay facing beaches
(Kelly et al. 2018). The PVC is on the bay side of Miami Beach on a narrow waterway within
another narrow waterway, thereby greatly limiting tidal flushing of the waterway and allowing
for the accumulation of FIB. Other waterway characteristics include its relatively shallow depth ,
its numerous bends , and the mangroves and shallow banks along its edge which have been
shown to allow for FIB persistence and growth (Desmarais et al. 2002). Additionally, the area is
very highly urbanized with significant sanitary and storm sewer systems. The following sections
of this report provide details on measured PVC depth in the longitudinal direction and also
observed shoreline types (mangroves, retention walls , exposed sediments, and others).
Figure 1.3: Map showing locations of I) Park View Canal , 2) Biscayne Point Waterway , 3)
Tatum Waterways, 4) Normandy Waterway N-S , and 5) Normandy Waterway E-W.
18
CHAPTER II
ANALYSIS OF HISTORICAL DATA
19
CHAPTER II
ANALYSIS OF HISTORICAL DATA
This analysis is based upon the considerable amount of data collected and shared through the
CMB. The focus of this initial analysis is to evaluate trends of enterococci data to date (Section
I. I), evaluate hydrometeorological data and predict tidally driven water level changes at the PVC
(Section 11.2), and use the information derived to evaluate correlations between environmental
factors and enterococci and fecal coliform levels (Section 11.3).
1.1 ENTEROCOCCI LEVELS AT THE PVC
The PVC has been monitored monthly for FIB since April 17, 2019. Monitoring consists of
collecting a water sample, at approximately the same location in the vicinity of the Kayak Launch
Pad within the PVC, followed by laboratory analysis to measure the Most probable Number of
enterococci per 100 mL (MPN/100 mL). We compiled sampling data, corresponding to the time
period from April 2019 to October 2022 , and found that enterococci levels for samples collected
in the vicinity of the Kayak Launch pad have exceeded the 70 MPN/100 mL FDOH regulatory
threshold, by factors of 10, and 100. Some samples had enterococci concentrations above the
detection limit of 24,196 MPN/100 mL (Figure II. I). This analysis suggests that enterococci levels
have continued to remain elevated following the March 4 and 5, 2020 sewer leaks. There is no
discemable difference in water quality before or after the March 2020 sewage spill. Levels of
enterococci at the PVC were consistently elevated prior to this spill.
tove detection limit
/
Sampling Program Starts in
Below Threshold Response to March 2020 Spill 70 MPN/100 ml
------:;7 -
i '""'"" i60 >
24
,~
6
.~ .... 17,300
'z 10,000 6,590
~ 6-0 934 I 1,010 1•560959 l,090
Z 285 359
67
~331 283 437
1,510
487
~ 169 108 I 142
u 100 63 731
u m
~ I
"' I
323
161 173
2,140 1,660 1,310
521
211 187
909
504 399
173
30 41
i I I
1 ~....,,._..,.....,.......,.....~~~~~
Figure II. I: Results from Monthly Enterococci Measurements at PVC from 4/2019 to 10/2022.
Green bars correspond to data points within the 70 MPN/100 mL recommended recreational
level whereas red bars correspond to data points which exceed this level. Note the data are
plotted on a logarithmic scale due to the wide range of measurements.
20
To further describe the exceedances at the PVC, enterococci levels from the CMB record were
converted to exceedances above the 70 MPN/100 mL advisory threshold for each year.
Table 11 .1: Percent of Exceedances of 70 MPN/100 mL Threshold per Year
Year Number of Number of % Exceed
Exceedances Measurements
2022 8 10 80%
2021 11 11 100%
2020 11 12 92%
2019 8 9 89%
Since the monitoring program started in 2019, the fraction of the time the PVC waterway has
exceeded the 70 MPN/1 00 mL threshold has been at or above 80%, with the hi g hest number of
exceedances observed for year 2021 when all samples collected exceeded the regulatory
threshold 70 MPN/100 mL. For the entire period of record evaluated (April 2019 to October
2022) the PVC exceeded the 70 MPN/100 mL threshold 90% of the time.
11.2 RAINFALL, GROUNDWATER, AND TIDAL FLUCTUATIONS
The first step of preliminary historic data analysis involved compiling available environmental
data including hydrometeorological data of rainfall, tides, and groundwater. The objective of the
analysis was to document the locations of available data. These data were used in the subsequent
section to determine possible associations between hydrometeorological data and enterococci.
Rainfall data were compiled from several sites located north, south, and east of the PVC , for the
period 2019 to date (Figure 11.2). A total of 8 rainfall stations were identified (Table 11.2). Tidal
data were compiled from the National Oceanographic and Atmospheric Administration 's
(NOAA) Tides and Currents repository. NOAA does not have a tidal station located on Parkview
Island. Five NOAA stations located north and south of the study area (Figure 11.2 , Table 11.3)
were used in the preliminary analysis. The team examined data from multiple tide stations
surrounding Parkview Island which included:
• Indian Creek Golf Club station, the closest station, located north of Parkview.
• Haulover Pier station , oceanside and located northeast of Parkview.
• Miami Beach station, oceanside and located south of Parkview.
• San Marino Island, south of Parkview, but northwest of the Miami Beach station.
• Virginia Key station . Has hourly tidal prediction and measurement data which is not
available at the other sites that are closer.
NOAA provides tidal predictions for four of these five stations. The NOAA data consists of only
four data points available per day corresponding to low and high tides. The team obtained the
tidal data ranging from May 2020 to September 2020 from each station to explore any
discernible patterns that could correlated with the high enterococci and coliform levels.
21
In addition to the first four stations listed above, the team also utilized data from the Virginia
Key tidal station, which has available information for both the hourly predicted and verified
(measured) tidal heights (See Figure B.4, Appendix B for a comparison). This station is the
furthest south from Parkview Island, but the data is useful in providing tides at shorter time
scales (hourly) and understanding how the verified tides can often deviate from the predicted
heights.
Table 11.2: Rainfall gauging stations in vicinity of the PVC
Rain Station Period Measure-GPS Coordinates URL for Station and/or Stations Description
Name of ment N w
Record Frequency
F arrbetter -2019-15 mins 25 .864 -80.129 Weather Underground
KFLMIAMl60 Present httns://www.wundenrround .com/dashboard
/ows/KFLM IAMI60 (KFLMIAMI60)
Miami Beach -2019-5 mins 25 .835 -80 .129 Weather Underground
KFLMIAMI89 present httQs ://www.wunderground.com/dashboard
/ows/KFLMIAMI89 (KFL MIAMI 89)
Surfside -2019-5 mins 25 .814 -80 .129 Weather Underground
KFLMIAMI58 present httns ://www.wundenrround.com/dashboard
3 /pws/KFLMIAMI583 (KFL MIAMI 583)
Miami Beach Previous Intennittent 25.77157 -80.14556 Loca!Conditions.com
U.S . Coast 30 days readings https://www.localconditions.com/weather-miami-beach-coast-
Guard (5-15) 1e.uard-station-florida/f1300/past.oho (Coast Guard)
WSl 2019-30 mins 25 .792967 -80. I 35582 City of Miami Beach Station 1, City Hall -1700 Convention
present Center Drive, Miami Beach, FL 33139
WS2 2019-30 mins 25.81467 -80 .128312 City of Miami Beach Station 2, 40 W 42 St, Miami Beach, FL
oresent 33140
WS3 2019 30 mins 25 .85753 -80.12296 City of Miami Beach Station 3,501 72nd St, Miami Beach , FL
present 33141
S27 _R 2019 -15 mins 25.85 -80.19 https://apps.sfwrnd.gov/WAB/Environmenta!Monitoring/index
present .html
Table 11.3: NOAA tidal stations in the vicinity of the PVC. Tidal information used in this project
for all stations (except Virginia Key) are predictions.
Tidal Station Period of Measurement GPS Coordinates URL for Station
Name Record Frequency N w
Indian Creek Not 3-4 predictions per 25 .8750 -80.1433 https://tidesandcurrents.noaa.gov/stationhome.html
Golf Club, available day (2 high tide ?i d=8723094
Biscayne Bay and 2 low tide)
Haulover 07 /14/1981 3-4 predictions 25.9033 -80.1200 https ://tidesandcurrents.noaa .gov/stationhome.html
Pier, N . -09/22/1992 per day (2 high tide ?id=8723080
Miami Beach * and 2 low tide)
Miami Beach 06/01/1931 3-4 predictions 25 .7683 -80 .1317 https://t idesandcurrents.noaa.gov/s tationhome .html
-07/25/1981 per day (2 high tide ?id=8723 l 70
* and 2 low tide)
Virginia Key, 01 /28/1994 Hourly 25 .7314 -80.1618 http s://tidesandcurrents .noaa.gov/stationhome.html
Biscayne Bay -Present ?id=87232 I 4
San Marino Not 3-4 predictions 25 .7933 -80.1633 https ://tidesandcurrents.noaa.gov/stationhome .html
Island availab le per day (2 high tide ?id=8723156
and 2 low tide)
*Period of record for verified data
22
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Figure II.2: Map showing locations of the rainfall, groundwater and tidal stations. The green pin shows
the location of the Park View Canal , the blue drops show the locations of the weather stations, the yellow
stars show the location of the NOAA tide stations, and the red crosses show the location of the City of
Miami Beach monitoring wells. Of note , KFLMIAMI60 and KFLMIAMI583 are very close to one
another and only KFLMIAMI60 is shown explicitly above.
The two closest groundwater monitoring stations are called Parkview Park and North Beach
Bandshell (Figure 11.2 , Table II.4). These stations are owned and maintained by the CMB. At
each station there is a cluster of three wells screened at shallow, intermediate, and deep depths.
23
Table II.4: Groundwater monitoring stations closest to the PVC
Groundwater Period of Measurement GPS Coordinates Description of Station
Monitoring Record Frequency N w
Station Name
Parkview 9/2/2019-Hourly 25 .8572428 80.1248966 Shallow well screened at 25-35 feet , intermediate well
Park (PVP) tpresent at 85 to 95 feet, and deep well at 200 to 210 feet
North Beach 9/2/2019-Hourly 25.8583060 80.1198783 Also called North Shore Park. Shallow well screened
Bandshell pres ent at 30-40 feet, intermediate well at 95 to I 05 feet , and
'NSP) deep well at 195 to 205 feet
Preliminary analysis was conducted to assess the relationships between rainfall, tide and
groundwater data and the dates coinciding with the PVC FIB measurements. Of note CM8
provided FIB data from a series of catch basin sampling efforts. The results from these catch
basin sampling efforts were plotted as "heat maps" by CM8. For the data analysis , first , a time
series plot of rainfall events was superimposed with markers corresponding to heat map peaks in
FIB concentrations (Figure 8.1 , Appendix 8). Second, tidal data for each of the five NOAA tide
stations were plotted with the dates corresponding to FIB peaks (Figure 8.2, Appendix 8). Third,
groundwater data for the two monitoring wells were plotted in a similar manner (Figure 8.3 ,
Appendix 8). Finally, a time series plot for the precipitation, tide and groundwater data and FIB
peaks was generated to explore trends across all three environmental parameters (Figure 11.3).
Results for the preliminary analysis show that no obvious relationships were observed between
the environmental parameters and the catch basin water heat map FIB peaks occurring at the
different dates.
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■Precipitation S_27R ■KFLMiami89 KFLMiami583 · Tidal Chart Indian Creek Golf Course -Ground Water Park View (PVP-SMW)
Figure 11.3: Time series plot of rainfall , tides and groundwater superimposed on dates and peak
enterococci levels measured in catch basins .
24
Following the preliminary analysis of historic data, on July 24 , 2022 we visited the study area to
measure the tidally driven changes in water levels over an 8-hour period at the Kayak Launch
Pad within the PVC. We measured the change in water levels during ebb tide (transition from
high to low .t ide). The tidal data from the Kayak Launch, Indian Creek Golf Club station , and
Virginia Key station were plotted in one graph to compare differences in tidal times . Through
this analysis , we determined that the Kayak Launch high and low tides closely match the tides at
Virginia Key. The low tide at the Kayak Launch lagged the Virginia Key low tide by
approximately 17 minutes (Figure 11.4). From this information, we compiled a table of estimated
tidal times for the Kayak Launch for the all the subsequent months of this study . The estimated
low and high tides were then used to determine the dates of the intense sampling activity as
described in the following sections .
-Virginia Key (Pre dicted ) Virginia Key (Actual ) -Ind ian Cree k Golf Club -Ka yak Laun ch
6:36 AM , 2 .23 7:18PM, 1.97
7:24 PM, 2.37
r 7:1 5Aivi, 1.6o 8 :08 PM . 2.01
2.0
'a51 .5 -12:30AM,0.76 LI /
0 .5 J..,,.,n
1 :37 AM, 0.4 9
12:1 8AM. 0.39
Time (LST/LDT )
Figure 11.4: Measured tidal data at the Park View Canal on July 24 , 2022, and tide predictions at
the NOAA tidal stations located at Indian Creek Golf Club and Virginia Key stations. The data
labels represent the high and low tides.
11.3 RELATIONSHIP BETWEEN HISTORIC ENTEROCOCCI LEVELS, RAINFALL,
TIDES, AND PHYSICOCHEMICAL PARAMETERS
Available enterococci data were combined with available rainfall , tidal , and physicochemical
parameters data to evaluate whether environmental conditions could be used to explain the
enterococci levels. In addition to the heat map comparisons described in the prior section , two
additional sets of data were evaluated. These included the monthly enterococci data collected
from the PVC (described in more detail below, section 11.3.a), plus one additional historical data
set focused on catch basin monitoring results (see section 11.3.b). These catch basin
measurements included multiple measurements of FIB daily (3 to 4 measurements per day at a
site) over the course of three days.
25
11.3.a Further evaluation of monthly enterococci data collected from the PVC
Along with the measurement of enterococci, additional parameters were measured monthly
(April 2019 to October 2022) as provided through CMB. These additional parameters included
total nitrogen, total phosphorus, salinity, field specific conductance, field temperature, pH,
dissolved oxygen, and turbidity. Additionally, cumulative precipitation for different time periods
prior to the time of sample collection (6-hours, 12-hours, 24-hour, 48-hours) and tidally driven
water elevations were also compiled. Rainfall corresponded to Miami Beach Station, WS3.
Missing data points were filled in with data from data collected from the South Florida Water
Management District Station S27 _ R. Tidal data corresponded to the NOAA Station located at
Virginia Key. Details about the rainfall and tidal stations are available in section II.2. A listing
of the enterococci and additional water quality data used in this analysis are provided in
Appendix B (See Table B.1).
To evaluate changes between enterococci and the environmental and physicochemical
parameters, exploratory data analysis was conducted by computing Pearson's correlations and
Spearman ' s ranked correlations for all compiled ( 4/17/2019 to 10/17/2022) data to evaluate the
changes between the enterococci and the environmental and physicochemical parameters (Table
II.5). Correlations were considered significant at 95% confidence limits for p-values less than
0.05. Statistically significant Spearman correlations (lrsl>0.3, p<0.05) were found between
enterococci levels and salinity plus 6 hr, 12 hr, 24 hr and 48 hr antecedent rainfall. The strongest
relationship was observed for 24 hr antecedent rainfall (rs= 0.75). Results for Pearson's
correlation show that statistically significant correlations (IRl>0.38, p<0.05) were found between
enterococci levels and salinity, fecal coliforms, pH and 6 hr, 12 hr, 24 hr and 48 hr antecedent
rainfall. The strongest relationship was observed for 24 hr antecedent rainfall (R = 0.53). It is
interesting to note that a negative relationship was observed between enterococci and salinity.
That is the higher the salinity, the lower the concentration of enterococci. Conversely, the lower
the salinity ( or higher freshwater content), the higher the concentration of enterococci.
Results from multiple linear regression (using SPSS software) again confirmed that rainfall, in
particular 24-hour antecedent rainfall, was the primary parameter correlated with enterococci.
Although the model was set up to evaluate multiple parameters, 24-hour rainfall was by far the
parameter that contributed the most towards explaining the variability of the enterococci levels.
The model developed (Equation II. I) relates P (24-hour antecedent rainfall) to enterococci levels
in units of MPN/100 mL as follows:
Enterococci (MPN/100 mL) = 1006 + 3634 x P (Equation II. I)
26
Table 11.5: Correlation between the enterococci in samples collected monthly from Miami Beach from 4/17/2019 to 10/17/2022 with other
physical chemical parameters (water level, tide cycle, total nitrogen, total phosphorus , salinity, fecal co li forms, field specific conductance, field
temperature, pH, dissolved oxygen, turbidity and cumulative precipitation (6-hour, 12-hour, 24-hour, 4 8-hour)) based on both Pearson's and
Spearman's analysis. Yellow indicates a significant correlation("*" indicates a p-value < 0.05 , "**" in dicates a p-value < 0.01).
Total Total Fecal Field Specific Field Disso lve d 6-hou r 12 -hour 24-hour 48-hour Water Nitrogen, Salinity Turbidity
Kjeldahl Phosphorus (ppt) Coliforms Conductance Temperature Field pH Oxygen (NTU) Pre cipitation Precipitation Precipitation Precipitation Level
(mg/L) (mg/L) (C FU/100 ml) (umhos/cm) (OC) (mg/L) (in) (in) (in) (in) (ft)
Pearson Correlation
Correlation : Coefficient -0.088 0.174 -.44 2" 0.183 -.384 ' -0 .070 -0.124 -0.027 0.059 .439 " .688" .750" .578 " 0 .064
Enterococci (R)
(MPN/100
t oo4 ml) p-value 0.606 0.290 0.003 0.251 0.012 0.663 0.434 0.866 0.713 0.000 0.000 0.000 0 .685
Spearman Correlation
correlation : Coefficient -0.059 0.065 -.313' .485" -0 .235 -0.143 -.385' -0.075 -0.049 .381' .421·· _527·· _457 ·· -0 .060
Enterococci (Rs)
(MPN/100
ml) p-value 0.730 0.694 0.044 0.001 0.133 0.372 0.012 0.636 0.760 0.013 0.006 0.000 0.002 0.706
Sample size 37 39 42 41 42 41 42 42 41 42 42 42 42 42
27
11.3.b Catch Basin Measurements During Three Consecutive Days
During April 19, 20, and 21, 2021 , three combinations of outfalls and upstream catch basins
were sampled (Figure 11.5). The three outfalls were labeled as Outfalls OTI , OT4, and OT7.
Catch basins feeding into these outfalls included:
• USIA and USlB feeding OTI,
• US4A, US4B, and US4C feeding OT4, and
• US7 A and US7B feeding OT7
At each of these sites, three samples were collected on April 19, four samples on April 20, and
four samples on April 21. The data were combined with rainfall and tidal data. Rainfall
measurements came from Miami Beach Stations WS3 (see section 11.2 for details about this
station). Tidal data was interpolated from the Virginia Key NOAA tide station.
Time series plots of the data show that the enterococci concentrations in the waterway were low
during April 19. It rained overnight from April 19 to the 20 th • On the following day , the
enterococci levels were very high throughout, exceeding detection limits (Figure II.6).
Interesting patterns in the enterococci variation were observed at 12 noon on April 20 which was
observed for both the OTI and OT4 system. These patterns were observed at extreme low tide
(Figure II. 7) where oscillations appear to have occurred in the relative levels of enterococci
between the outfalls and the catch basins. The coincidence of these oscillations is striking and
suggests shifting of water sources possibly between the outfalls and the catch basins at these
times.
Spearman and Pearson 's correlation analysis (Table 11.6), identified prior rainfall, specifically 48
hour antecedent rainfall , as the most strongly correlated rainfall parameter. Pearson correlation
coefficients between enterococci and 48-hour rainfall were as high as 0.92 to 0.98 for catch
basins USIA, USlB, US4C, and US7B (Figure 11.8).
28
Figure 11.5: Sampling locations of the upstream (US) and outfall (OT) shown in the blue and red circles within the map.
29
O Oo 0.1
8~8~-0E>E>E>8~888~ 0
12:00 18:00 0:00 6:00 12:00 18:00 0:00 6:00 12:00 18:00
4/19/2021 4/20/2021 4/21/2021
(b) JO ~------O_T_4 __ ><_-_U_S_4_A ___ U_S_4B __ ><_U_S_4_C __ o_l h_r_P_r_e_ci_p_it_at_io_n __ ~
:3' I
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4/19/2021 4/20/2021 4/21/2021
(c)
30
~-------__ O_T_7_-_,._-_U_S_7_A ______ U_S_7_B __ o_l_h_r_P_r_ec_i_pi_ta_t_io_n ____ ~
:3' I
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8 ~8~-0E>E>~E>E>E>~OOOO<>O<:K><>-00-0
18:00 0:00 6:00 12:00 18:00 0:00 6:00 12:00 18:00
4/19/2021 4/20/2021 4/21/2021
Figure II.6: Concentration of enterococci in the outfall (OT) and upstream (US) and hourly
rainfall based on the time series. Panel (a) includes outfall and upstream for the first location;
Panel (b) includes outfall and upstream for the fourth location; Panel (c) includes outfall and
upstream for the seventh location.
30
--on >< USIA -k-USIB -o -Tide
4 /19 /2021 4/20/2021 4/21/2021
--oT4 >< US4A US4B " US4C -o -Tide
4/19/2021 4/21 /2021
4/19 /2021 4/20 /2021 4/21/2021
Figure II.7: Concentration of enterococci in the outfall (OT) and upstream (US) and height of
sea tide based on the time series. Panel (a) includes outfall and upstream for the first location;
Panel (b) includes outfall and upstream for the fourth location; Panel (c) includes outfall and
upstream for the seventh location.
31
o USIA ll USIB x US4C o US78
USIA ---USIB US4C ---US78
R2 =038 R'=032 R'=032 R'=038
;3' 25 ~-------------------■--,-,~,~,-,.~
5
g 20
,,,/ ,,,,
X
/l
:1""" o --------r---------r---------r-----------,
0.0 0.5 1.0 1.5 2.0
48-hour Rainfall (in)
Figure 11.8: Linear correlation between enterococci in the upstream samples (US 1 A, US I B,
US4C, and US7B) and 48-hour cumulative precipitation prior to the sampling time based on
the Pearson's analysis (R2).
32
Table Il.6: Correlation between the enterococci in the samples of outfall (OT) and upstream (US)
and height of sea tide or cumulative precipitation based on both Pearson's and Spearman's
analysis. Yellow indicates the significant correlation (p-value < 0.05). Red indicates the strong
linear correlation (Pearson's R2 > 0.9).
Sample Correlation w/ Tide Height lh Rainfall 6h Rainfall 12h Rainfall 24h Rainfall 48h Rainfall ID Enterococci
Pearson's R 0 .139 0.548 0.536 0 .549 0.356 0.630
(p-value) (0.684) (0 .081) (0 .089) (0 .080) (0.283) (0.038)
OTI Pearson's R2 0.019 0.300 0.287 0.302 0.127 0.397
Spearman 's rank 0.137 0.451 0.633 0.816 0.579 0.695
(p-value) (0.689) (0 .164) (0.037) (0.002) (0 .062) (0.0 18 )
Pearson's R 0.526 NA 0.634 0.478 0 .427 0.824
(p-va lue) {[\ (\07\ (.Q..Q _ __§_) -(0 .137) (0 .190 ) {0.002) \ V ,'v / I /
OT4 Pearson 's R2 0 .276 NA 0.402 0.228 0.182 0.679
Spearman 's rank 0.426 NA 0.800 0.811 0 .640 0.640
(p-value) (0.192) (0.003) (0.002) (0.034) (0 .034)
Pear son 's R 0 .220 NA 0 .2 64 0.145 0.095 0 .775
(p-value) (0.516) (0.434) (0.671) (0.780) (0.005)
OT7 Pearson's R2 0 .048 NA 0.069 0.021 0.009 0 .601
Spearman's rank 0 .270 NA 0 .146 0 .606 0.485 0 .795
(p-value) (0.422) (0.669) (0.048) (0 .131) (0 .0 03)
Pearson's R 0 .260 NA 0.281 0.452 0 .602 0 .987
(p-value) (0.440) (0.403) (0 .163) (0 .050) (< 0.001)
USIA Pearson's R2 0 .068 NA 0.079 0 .204 0.362
Spearman's rank 0.326 NA 0 .6 12 0.839 0.825 0.647
(p-value) (0.327) (0 .046) (0 .00 I) (0 .002) (0.031)
Pearson's R 0 .325 NA 0.236 0 .364 0.439 0 .961
(p-v alu e) (0.329) (0.485) (0 .271) (0 .176) (< 0.001)
USIB Pearson's R 2 0.106 NA 0.056 0.133 0 .193
Spearman's rank 0 .233 NA 0.350 0.493 0.525 0.861
(p-value) (0.491) (0.291) (0.123) (0.097) (0 .00 1)
Pearson's R 0.326 NA 0 .397 0.198 0 .259 0 .737
(p-value) (0 .328) (0.227) (0.559) (0.442) (0.010)
US4A Pearson's R2 0.106 NA 0 .158 0 .039 0 .067 0 .543
Spearman's rank 0 .284 NA 0.356 0 .651 0 .525 0 .758
(p-value) (0.397) (0 .283) (0 .030) (0 .097) (0 .007)
Pearson's R 0.372 NA 0 .340 0.428 0.451 0 .942
(p value) (0.260) (0 .307) (0.189) (0 .164) (<0.001)
US4B Pearson's R 2 0 .138 NA 0.115 0 .183 0 .204 0 .887
Spearman's rank 0 .284 NA 0 .537 0.645 0.647 0.825
(p-value) (0.397) (0.089) (0 .032) (0.03 1) (0 .002)
33
Table 11.6: (Continued). Correlation between the enterococci in the samples of outfall (OT) and
upstream (US) and height of sea tide or cumulative precipitation based on both Pearson's and
Spearman's analysis. Yellow indicates the significant correlation (p-value < 0.05). Red indicates
the strong linear correlation (Pearson's R2 > 0.9).
Sample Correlation w/ Tide Height lh Rainfall 6h Rainfall 12h Rainfall 24h Rainfall 48h Rainfall ID Enterococci
Pearson's R 0 .212 NA 0.310 0.504 0 .648 0.958
(p-value) (0.531) (0.354) (0.114) (0.03 1) (< 0 .00 1)
US4C Pearson's R2 0.045 NA 0.096 0.254 0.420
Spearman's rank -0.010 NA 0.201 0.581 0.729 0.608
(p-value) (0 .978) (0 .554) (0.061) (0.0 1 I ) (0 .0 47)
Pearson's R 0.068 NA -0.101 0 .168 0.407 0.9 12
(p-value) (0.844) (0.767) (0 .621) (0.214) (< 0 .00 1)
US7A Pearson's R2 0 .005 NA 0 .010 0.028 0.166 0 .832
Spearman's rank 0 .105 NA 0.195 0 .581 0.647 0 .825
(p-value) (0.758) (0.565) (0 .061) (0.03 1) (0.002)
Pearson's R 0.277 NA 0 .294 0.460 0.602 0.988
(p-value) (0.409) (0 .380 ) (0.154) (0.050) (<0.00 1)
US78 Pearson's R2 0 .077 NA 0.087 0 .212 0 .362
Spearman's rank 0.475 NA 0.269 0.561 0 .828
(p-value) (0.140) (0.424) (0.073) (0 .002)
34
CHAPTER III
ANALYSIS OF EXISTING WATER CONVEYANCE
INFRASTRUCTURE
35
CHAPTER III
ANALYSIS OF STORMWATERAND WASTEWATER
CONVEYANCE INFRASTRUCTURE
The CMB provided access to images of the stormwater and sanitary sewer infrastructure. Key
elements of this infrastructure as they may relate to PVC water quality are provided below.
111.1 STORMW ATER CONVEYANCE SYSTEM
An analysis of Geographic Information System (GIS) data for the stormwater infrastructure
shows that 9 outfalls discharge stormwater directly to the PVC whereas over 45 stormwater
outfalls discharge to waterways that are connected to the PVC on the north, south, and east
(Figure III. I). The six outfalls located on the east banks of the waterway, discharge stormwater
from their corresponding catchment areas located on the main island of Miami Beach. The three
outfalls located on the west bank of the waterway, discharge storm water from the catchment
areas located in Park View Island. The catchment area to the east includes 1 through 5 and partial
areas for 9 through 12. These areas combined consist of approximately 253,443 m2 of mixed-use
urban area (commercial and residential) whereas catchment areas 6 to 8 are comprised of 75,650
m2 residential areas (Table Ill. I). It is important to note, that all three of the Park View Island
outfalls discharge to the PVC and no outfalls are observed on the west part of the island. Thus, a
total of 329,093 m2 of catchment area discharges stormwater to the PVC. Contaminants on
surfaces that may be washed away by stormwater run-off, such as roofs, street sediments, soot
from vehicles, litter, and animal feces may eventually end up in the waterway.
In summary, the PVC is also directly impacted by stormwater run-off along the shoreline,
stormwater discharge through outfalls connected to the conveyance system that transports run-
off from several catchment areas, and indirectly by storm water discharges to surrounding areas
(through connecting waterways to the north and west) (Figure 111.1).
36
Figure III. I: Stormwater catchment area for PVC shown by heavy blue lines on right panel.
Locations of stormwater outfalls are shown by red ovals. This map does not show private
outfalls. Total catchment area (catchments 1 to 8 and partial areas for 9 to 12) that discharges
stormwater to the PVC is approximately 329,000 m2 •
Table III. I : Catchment areas in CMB connected to stormwater conveyance system with
discharge locations in PVC
Proportion
of Basin in
ID Location Basin ID Project Name Catchment Area (m2)
I CMB HU-72ST-DICK North Shores 100% 25,973
2 CMB HU-74ST-DICK North Shores 100% 45 ,651
3 CMB HU-73ST-DICK North Shores 100% 62 ,464
4 CMB HU-75ST-DICK North Shores 100% 33 ,753
5 CMB HU-75ST-OUTF North Shores 100% 10 ,632
6 PVI HU-75ST-GARY NA 100% 47,368
7 PVI HU-73ST-WAYN NA 100% 1,5491
8 PVI HU-74ST-GARY NA 100% 1,2791
9 CMB HU-75ST-HARD North Shores 25% 10 ,650
10 CMB HU-74ST-HARD North Shores 50% 18 ,000
I I CMB HU-73ST-HARD North Shores 50% 30 ,943
12 CMB HU-71 ST-AB BT North Shores 25% 15,377
37
111.2 SANITARY SEWER SYSTEM
Likewise, an analysis of the GIS data for the sanitary sewer infrastructure shows sewer force
mains (sanitary sewers under pressure) along the south leg of the PVC and 72nd street, as well as
along the northeast perimeter of the PVC and along Dickens Avenue. A siphon is located on the
Northeast bend of the canal (Figure 111.3). A high density of sanitary sewer force mains was
observed under the Miami Beach Parking lot located between 72nd and 73rd street. Lateral
connections from residential properties to gravity pipes are also observed throughout the area.
The location of the March 5, 2020, sewage main break is shown by the yellow star (Figure III.3).
As noted prior, the location of sewer leak at 72 nd street and Harding Ave. is approximately 1,500
feet away from the PVC. It is estimated that following the March 5, 2020, sewer leaks , about
665,000 gallons of untreated sewage streamed to the PVC.
The analysis of existing infrastructure suggests that the PVC may potentially be impacted by ,
• Sewage overflow at times of flooding due to heavy rainfall or King Tides
• Non-point discharge through leaking or failing wastewater sewer infrastructure
In the event of failing wastewater pipes, wastewater may impact the PVC through the stormwater
conveyance systems via tidally driven groundwater fluxes to the PVC. Further details are
provided in the following section.
38
Figure lll.3: Locations of sanitary sewer force mains are shown by the dark brown lines . Locations of sewer gravity mains are shown by the beige
lines . The siphon on the northeast bend of the KYW is indicated by the orange-brown line.
39
111.3 EVALUATION OF BOTH SYSTEMS
The tidal and groundwater level variations at the PVC are particularly important, given the
multitude of sanitary sewer system infrastructure in the area, the elevated FIB levels measured in
both the stormwater system and in the waterway, and the potential for cross contamination from
the sanitary to the groundwater and stormwater conveyance system. There are significant
locations where the sanitary and the storm water conveyance system overlap ( e.g., see Figure
IIl.4) thereby emphasizing the possibility of water exchange between the two systems. To assess
how the groundwater levels in the vicinity of the PVC are influenced by tides, plots of
groundwater levels at the nearby Parkview Park monitoring well and tidal predictions at the PVC
were generated (Figure 111.5). Results show a clear relationship whereby, the groundwater levels
are tidally influenced.
Figure III.4: Locations of areas where the storm conveyance system and sanitary sewer system
overlap along 73 rd Street.
40
1
"'--'
0
0 .5
C: -0 E 0 C: ·z <il Q) ...
<il I.. V)
> Q) >-,
Q) ... V)
2 0 '-'
§;
~ z
a:; -0.5
> Cl>
v <il c
C: ~ <il E ....,
QJ I.. ·a b.O 0 <il C: ...
V) V)
<il
0::
...J ....
Cl> ..... ns -1 3:
-1.5
-2 Groundwater contributin to PVC
0 0 0 0 0 0 0 0 0
'?. '?.
0 M
0 0 0 '?. 0 0 '?.
'° 0\ N I.I) co .-i 0
N N N N .-i .-i .-i N N
N N N N N N N N N ----0\ 0\ ----N N N N --0\ 0\ --------0 --------0\ 0\ 0\ 0\ .-i co co co co -----------Ground water'° -nctf co co co
Figure IIl.5 : Estimated tidally driven water levels at PVC and measured groundwater elevation at
Parkview Island Park monitoring well.
41
During high tide, the elevation of the marine water at the PVC is higher than the groundwater
elevation . Since water flows from high elevation to low elevation, during high tide water
generally flows from the PVC towards the groundwater. This flow into the groundwater system
can be facilitated by the stormwater conveyance system acting as a perforated pipes that permits
unrestrained flow from the PVC to the shallow groundwater. However, during low tide, the
elevation of the groundwater is higher than the marine water at the PVC. Again, water flows
downhill. At times oflow tide, groundwater flows into the PVC, from the landside to the
waterway . (Figure III.5). This flow direction is again facilitated by the stormwater conveyance
system where the perforated pipes serve as unrestrained conduits linking the groundwater to the
PVC.
Inlets and
catch basins
upstream
Stormwater
drainage pipe
Groundwater surface
at high tide
Water level high tide -p~~-r
tidally driven fluxes. At the land-marine water interface, one potentially important pathway for
non-point pollution from land to the sea is groundwater (Burnett et al. 2006). Submarine
groundwater discharge is an ubiquitous coastal process. It involves the flow of fresh
groundwater, re-circulated marine water, or a composite of both (Swarzenski et al. 2004). In
some urban locations it has been shown to be an important source of nutrients and has been
indirectly linked to high concentrations of FIB (Boehm et al. 2003, Boehm et al. 2004, Izbicki et
al. 2012 , Russell et al. 2013). In the event of a leaking sewer gravity main, sewer force main , or
laterals at multiple residential units, the wastewater could potentially contaminate the
groundwater and eventually contaminate the PVC through tidally driven groundwater fluxes. It is
important to note that the hypothesis that the wastewater sewer is not impacting the groundwater
has not been proved . Further details and suggested studies are provided in Section VI of this
report.
42
Figure Ill.7 Flow diagram showing possible water pathways into and out of conveyance system .
a) emphasizes the possibility ofleaks from the sanitary sewer contaminating groundwater and
flowing into the perforated pipes of the storm conveyance system, b) emphasizes the possibility
of leaks from the sanitary sewer contaminating groundwater that flows directly to the waterway .
43
CHAPTER IV
OBSERVATIONS DURING VISUAL INSPECTIONS
44
CHAPTER IV
OBSERVATIONS DURING VISUAL INSPECTIONS
As part of sampling efforts, the research team had the opportunity to visit the catchment area and
conduct qualitative assessments of the study area. These qualitative assessment took place during
site visits aimed at gathering samples and data. They included inspections by foot from the land
side and by water via boat and paddle board inspections of the PVC. Our team was present in
the field during mostly dry conditions but they were also present during rain events. A detailed
summary of these visits along with photographs taken is given in Appendix D. Below is a table
that summarizes the main sources of"visible" contaminants during our sampling efforts.
Table IV. I: Potential Fecal Sources Observable During Field Visits. See Appendix D for details
and photos from field visits .
Categories of Potential Sources Fecal Sources Details of Source
Observable During Field Visits
• Dogs
• Roosters
1. Animals feces • Iguanas
• Racoons
• Rats
• Parkview Island Park Adjacent to the
2. Animal feeding stations Kayak Launch. The feeding station
attracks feral animals that release feces in
the area.
• Bridge from PVI to Elementary School
• Bridge from PVI to Dickens A venue
3. Homeless • Shoreline in vicinity of Parkview Island
Park (hammock and mosquito net in
mangrove area)
• West of community garden
45
Table IV. I (continued): Potential Fecal Sources Observable During Field Visits. See Appendix
D fi d ·1 d h ti fi Id .. or etat s an p otos rom te VlSltS.
Categories of Potential Sources Fecal Sources Details of Source
Observable During Field Visits
Observed on all inspection days (source of
FIB and limits circulation)
• Plastic bags
4. Trash in waterway • Soda cans
• Large plastic items
• Landscaping debris
• Animal feces floating in waterway
• White foam
• Food packages, cans, cigarettes, plastic
5. Trash and debris in curbs bags etc.
• Dirt and leaves
6. Trash bins from commercial establishments • Leaking leachate
7. Very little green space in stormwater • Limits percolation of run-off which limits
catchment areas natural contaminant removal
• High population density suggests more
human associated sources of FIB within a
smaller area. Thus the system will need to
8. High population density rely more on engineered systems to
facilitate contaminant removal as natural
attenuation and dilution is not sufficient to
handle the density.
• Shaded soil embankments are known to
9. Shaded embankments with natural soils harbor high levels of FIB due to shade and
wetting and drying cycles which
encourages FIB persistence and growth
• Sediments from shoreline containing high
10. Eroding channel embankments levels of bacteria can enter waterway as
part of tidal changes in water levels or
through rainfall-runoff
11. Stormwater outfalls • Source during rainfall-runoff and evaluated
through sampling as part of this study
46
CHAPTERV
SAMPLING EFFORTS
47
CHAPTERV
SAMPLING EFFORTS
Sampling efforts included: 1) intense spatial sampling (Section V. l), 2) sediment and catch basin
sampling (Section V.2), 3) intense temporal sampling using an autosampler (Section V.3), and 4)
depth sampling within the waterway, catch basins, and wells (Section V.4). The timeline for
sample collection efforts are illustrated on the following time line superimposed on the rainfall
record (Figure V. la). Of note August through early Septnmber (includes the first three sampling
events) corresponded to a relativley dry sampling period (August and early September). The
sample collection during September 16 th (intense sampling during low tide) corresponded to a
wet period. A small rainfall event was observed during the hourly (over 48 hours) sampling
event.
6
5
9/2/2022,
Catch Basin Sampling
8/9/2022,
High Tide
Spatially Intense Sampling
8/17/2022,
Catch 8as,n Sampling
9/16/2022,
low Tide
Spatially Intense Sampling
10/18/2022 11/14/2022, Depth Sampling at
Begin Temporally Intense sampling, Groundwate r Wells, Vertical Wells,
and Catch Basins
10/19/2022,
Depth Sampling ,n KLW
10/20/2022,
End Temporally Intense Sampling
Dept h Sampling ,n KLW
■ DBHydro ■ KF LM IAMl 60 ■ KFLM IAM l 89
Figure V . la: Sample collection timeline superimposed on daily rainfall record. Of note, low tide spatial
sampling occurred during an antecedent wet period. Period corresponding to the hourly sampling period
(over 48 hours) is highlighted by a red circle.
All of the analyses initiated as part of the current study through the University of Miami were
performed using the Most Probable Number (MPN) method based upon the use of chromogenic
substrates (Enterolert-18, IDEXX Industries), their standardized well system (Quantitray-2000),
and incubation temperatures consistent with enterococci measurements ( 41.5 °C for 24 hours± 2
hours). This method was chosen given the wide range of enterococci measurements documented
historically in the PVC. The MPN approach provides the broadest range of detection (from 1 to
2419.6 counts) for a single analysis, thereby increasing the chances of direct measurements of
concentrations . In this study, dilutions of 10 : 1 were preferentially used thereby providing
analytical ranges between 10 and 24 , 196 MPN per I 00 mL.
48
All PVC samples were collected in pre-sterilized Whirlpak bags by collecting samples from the
water's surface with the exception of: a) depth samples from the PVC which were collected with
sterile pipettes (new each time) attached to tubing and a hand pump, and b) 48 hour samples
were collected using a pump set with a purge cycle and collection into sterile bags (new each
time). For catch basin , vertical wells, and groundwater monitoring wells samples were collected
in sterilized 500 mL bottles by either pumping water using a peristaltic pump (new tubing used
each time) or by attaching bottles to a weighted bottle holder on the end of a rope. Early catch
basin sampling (August and September) was conducted using the weighted rope method. Later
sampling documented the sampling depth more precisely through pumping water from a
specified depth.
V.1 INTENSE SPATIAL SAMPLING
Th e next ste p following our preliminary data anal y sis and visual inspections was to identify the
location of the enterococci hot spots in the Kayak Launch area within the PVC. To this end , a
spatially intense sample collection program was conducted. The program included a series of
transects that cut across the canal at locations of interest to the north and south of the Kayak
Launch area. The spatially intense sampling was conducted at extreme high tide and at extreme
low tide, with all samples collected as quickly as possible to get a snapshot of the enterococci
distribution across the entire length of the waterway surrounding Park View Island (Figure V .1 ).
We conducted our first spatially intense sampling effort on August 9 very early in the morning,
targeting high tide. We systematically collected 50 water samples along the transects, which are
ordered locations along the waterways around Park View Island. A greater number of samples
were collected on the east side of the PVC . Transects L through R show the location of28
sample collection points, that is 4 samples per transect. Of note , transects M to O show sample
collection points in the vicinity , to the north and south of the Kayak Launch location (Figure
V. lb). We also collected one sample per transect along the Normandy Waterway N-S (Transects
A to F), at the intersection of the PVC with Biscayne Point Waterway (Transect G), Tatum
Waterway (Transect H). One sample was also collected near the outfall located in the Tatum
Waterway (Transect I). In addition to collecting water samples for analysis of enterococci
concentrations, at each point along transects, we also measured the waterway depth , and a suite
of physical chemical parameters including dissolved oxygen, pH , temperature and salinity.
The second spatially intense sampling was conducted on September 16 very early in the morning
targeting low tide. We collected 50 water samples along the same transects as on August 9, 2022 .
Two additional samples were also collected: a sample was collected from an unidentified outfall
that was discharging water a few meters east of transect K4 , and a duplicate sample was
collected at transect N2 which is closest to the Kayak Launch pad. During the September 16
sampling effort, we also measured physical chemical parameters.
The collection of a high number of samples in a short period of time during high tide and during
low tide , enabled a "snapshot" of the bacteria distribution within the waterways around the
island. Additionally, the results from the intense spatial sampling provided information on the
spatial changes in the enterococci levels in the PVC with respect to the levels in the adjoining
waterways. We also compared differences in environmental parameters measured during high
49
and low tide to gain insights into the tidal and groundwater influences on water quality. These
insights provided a better understanding of the underlying transport and fate mechanisms driving
the different levels of FIB in the waterway and complemented the spatial analysis. Final analysis
of the results for the intense spatial sampling coupled with the analysis of environmental
parameters are provided in the following paragraphs.
On both sampling days , the first sample was collected at Transect A, and the last sample was
collected at Transect S, as the boat transporting our team travelled in a counterclockwise
direction around Parkview Island. Enterococci concentrations measured on August 9, during
high tide , ranged from 52 MPN/100 mL to 4,611 MPN per/100 mL (Figure V.2). Several
samples measured below the 70 MPN/100 mL threshold value, including the sample collected at
Transect A, and several samples collected just before exiting the waterway on the south leg of
the PVC. Sampling results show, a well-defined spatial pattern, of increasing enterococci
concentrations, in the counterclockwise direction starting along the north leg of the PVC , and
through the PVC East and moving south. This trend of increasing concentration, peaked in the
vicinity of the Kayak launch Pad, along transects N through 0. Three hotspots were identified ,
where the highest enterococci concentrations were measured at transect NI (4,611 MPN/100
mL), at transect P3 (2,064 MPN/100 mL) and transect 01 (1,785 MPN/100 mL) (Figure V.4,
panel a).
50
Figure V .1 b: Map showing transects with sampling locations for intense spatial sampling activity
conducted on August 9th and September 16 th • Red points show the location of the stormwater
outfalls, green lines show the location of the storm water mains , orange line on the northeast bend
of the canal shows the location of the siphon, brown lines show the location of the sanitary sewer
system force and gravity mains.
51
~
MPN 100/ml
• 52 -70
0 71 -556
• 557 -1,191 • 1,192 -2,064 • 2,065 -4,611 -Outfall
Figure V .2 : Map showing measured concentrations of enterococci at the PVC during high tide
(August 9, 2022). Hotspots shown by large pink and purple circles.
52
0 9,804
0 9,805 -14,136 • 14,137 -24,195 • >24,195 -Outfall
Figure V .3: Map showing measured concentrations of enterococci at the PVC during low tide
(September 16, 2022).
53
_5000 e 4500 a)
8 4000
~ 3500 -
~ 3000
~2500
'8 2000
8 1500
t 1000
'E 500
w o -i-c=--~+--------+--=------1==--='""""-.
-;::;-
0 .8
0 .6
0.4
~ 0 .2
~
ai 0
> ~ -0.2 ...
Cl) rti -0.4
3 -0.6
-0.8
-1
-1.2
Main KLW North
Waterway
I
I
KLW East
High tide, 7:11 AM
01 FlHl J1
Al' C El!Gl 11
KLW South
L1 Ml
-1.4 +-.--,-........ --.-.......---.-r-r-....-,,....,.......-,-,-"T"""T-r-......-T-,-.,.......--.-
::;: ::;: ::;: ::;: ::;:
<( <( <( <( <(
"' "' ~ ~ "' "' 9 0
io r--r--r--00
32.8
32.6 b)
.;-32.4
a.
..!!:32.2
~ :E 32
iij
"'31.8
31.6
31.4 +---+--------/-------+----~
Main KLW North KLW East KLW South
Waterway
Tl
::;: ::;: ::;:
<( <( <(
"' .-, "' "' .,. 0
00 .;; s
Figure V.4 : Panel a) August 19th (high tide) enterococci levels around the perimeter of Parkview
Island, Panel b) salinity measurements along PVC . Panel c) water levels (NAVO) during
sampling activities.
This trend reverses upon entering the PVC South, where lower enterococci concentrations with
values like those in the main waterway were observed. In general, higher salinity concentrations
were measured along the PVC North and East, than along the main waterway of Normandy
Waterway N-S and the PVC South. The change in salinity between the main waterway and the
PVC is surprising since both the main (31.8 ppt) and PVC North (32.4-32.6) waterways were
54
measured during extreme high tide. This change in salinity could provide insights into the tidal
flushing mechanisms that affect the PVC.
Enterococci concentrations measured on September 16, during low tide, ranged from 9,804
MPN/100ml to over the 24 ,196 MPN /100 mL detection limit value (Figure V .5). None of the
samples measured below the 70 MPN/100 mL threshold value. Several samples measured at the
lower end of the range for that day (9,804 to 14,136 MPN/100 mL). These samples were located
at transects J and N, and along the PVC South. This lower range is two to seven times higher
than the peaks identified on August 19.
Sampling results from September 16 show, a spatial pattern opposite to that observed during
August 19 , with increasing enterococci concentrations upon exiting the PVC. All samples
collected along the main waterway measured above the detection value of 24,195 MPN/100 mL.
A !I sampl es, except for on e , o ll ected a lo n g the PVC North also measured above the detection
limit. However, samples collected in the PVC East had lower enterococci concentrations with 7
samples measuring within the 9,804-14, 136 MPN/100 mL range, and 15 samples measuring
within the 14 ,137 to 24 ,196 MPN/100 mL range. Only five samples in the PVC East had
concentrations above the detection limit. These five samples were collected at transects M , N and
Q , in the same general area as for the peaks observed on August 19. Similarly, to high tide
sampling on August 19 , during the low tide sampling on September 16, the lowest concentrations
were observed along the PVC South. To emphasize, these "lower concentrations" observed on
September 16 were much higher than the peaks observed during high tide sampling conducted on
August 19 . The source of enterococci was much more pronounced on September 16 than on
August 19 . We believe that the very high levels observed on September 16 th were due to the
antecedent wet period during which the stormwater conveyance system had discharged
stormwater shortly prior to sampling. This is consistent with the hypothesis that the primary
source of enterococci are wastes deposited on surfaces that are washed into the PVC by the
stormwater conveyance system.
A change in salinity levels was observed during low tide sampling, whereby the measured
salinity values (26.8 to 30 .3 ppt) during low tide were lower than values measured during high
tide (31.8 to 32.6 ppt). This observation suggests that the extremely high levels of enterococci
are associated with freshwater. It is possible that during low tide, tidal flushing forced freshwater
from the PVC out to the main waterway, thereby explaining the reversal in observed spatial
concentration trends. The study is located in North Biscayne Bay. Tidal flow between North Bay
and the ocean is through Baker's Haulover Inlet. Our team (Dr. Larissa Montas) observed that
during the ebb tide cycle, currents in the PVC North were moving west. However, during the
flood tide cycle, currents in the PVC were moving east. However, during the ebb tide cycle,
currents in the PVC East were in general moving south and not north. This suggests that greater
tidal flushing occurs through the PVC South than through the PVC North. It is possible that tidal
flushing through the PVC North is limited by the sharp 45 degree angles created by Biscayne
Point Island and flows from the waterways to the north. In contrast, water exiting the PVC
South could flow to the main waterway with less impedances.
55
,...._
..J
E
0
0 ..... --.... z
0..
~
'-' ·o
u
0 u
0
'-2l
C ....
33 .-------;:;)-,-;.:;~;.:;~~~,:;;:;:;;:&--:;:;~.;.;;:~_;;:;;_;;:;;.:;:;~.;:;~~~,;:~~~;;""-.;">---~-;;,;:~:;::;:.:;:;,,_-~~-;:~_;)-,--,"''
32
,...._ 31
§: 30
'-'
_q29
;§ 28
□ .P □□□Don □ b DD □□0 0 □ □ □□
~
□ □
re
(/) 27 0
26
25 +------~--------~----------~----------l
Cl El Gl 11 J2 J4 K2 K4 L2 L M2 M4 NZ N4 02 04 P2 P Q2 Q4 R2 R4 S2 S4
Main Wateiwav KLWNorth KLW~t KLWSouth
100,000 -.------------------------------------~
10,000
1,000
100
10
1+-----~~--------~---------------------l
Cl El Gl 11 J2 J4 K2 K4 L2 L M2 M4 NZ N4 02 04 P2 P Q2 Q4 R2 R4 S2 S4
Main Wateiway KLWNorth KLW~t KLWSouth
~ August 9th B September 16th
Figure V.5: Results from spatially intense sampling around the perimeter of Parkview Island ,
comparing the results from the August 19th sampling event (high tide) and the September 16th
sampling event (low tide). Top panel compares salinity and lower panel compares enterococci.
56
Figure V.6: Schematic of conceptualized tidal flushing during ebb tide, with more tidal flushing
towards the south of Parkview Island. It is possible that tidal flushing through the PVC North is
limited by the sharp 45-degree angles created by Biscayne Point Island and flows from the
waterways to the north. In contrast, water exiting the PVC South could flow to the main
waterway with less impedances.
57
V.2 SEDIMENT AND CATCH BASIN SAMPLING
Following our scouting visits, and the evaluation of sanitary and stormwater infrastructure GIS
data, we decided to evaluate the waterway slope sediments and stormwater and sediments within
the catch basins. Sampling took place on two dates, August 17 and September 2, 2022.
On August 17 we conducted sampling activities targeting the stormwater sewer infrastructure.
We focused our efforts on sampling stormwater inlets and catch basins located along the two
gravity pipes leading to the stormwater outfalls that discharge north and south of the Kayak
Launch Dock. These two gravity pipes run along 73rd street and 74th street. We also sampled
sediments along the waterway banks, right next to the outfall discharge during low tide by
scraping the upper 1 inch of sediments using a sterile spoon and placing the sample into a sterile
Whirlpak bag. Specifically, sediments next to the outfall north of the Kayak Launch dock (NS 1,
Figure 6), sediments next to the outfall south of the Kayak Launch dock (NS3 , Figure 6), and
sediments on the banks in front of the Kayak Launch dock (NS2, Figure 6). We also collected
water samples at locations directly across from the sediment sampling locations to allow for
comparison between the FIB levels measured in the sediments and along the stormwater gravity
pipes discharging to the outfalls. Three water samples were collected north , south and adjacent to
the Kayak Launch pad (NWl, NW2, and NW3, Figure V.7).
Six locations were selected for catch basin sampling . These locations included three along 73rd
Street and three along 74th Street. At each location sampling of the catch basins on August 17th
consisted of:
• Collecting sediment samples (top sediments) near the inlets (STl to ST6, Figure V.7) by
using a sterile scoopula to scrape sediments from the top of the catch basins and place
them within sterile Whirlpak bags ,
• Removing the inlet grate and collecting water samples directly from the catch basin (Wl
to W6, Figure V.7) by attaching pre-sterilized polypropylene bottles to a weighted bottle
holder on the end of a rope and lowering the bottle into the catch basin , and
• Using an Ekman dredge to collect available sediments at the bottom of the catch basin
(SB l to SB6 , Figure V.7) and transferring these sediments using a sterile spoon into
sterile Whirlpak bags. Of note, no sediments were available at WB3 nor at WB4.
For the second sampling of the stormwater catch basins conducted on September 2nd , the
sampling program was expanded. We decided to conduct a catch basin analysis by sampling
locations close to the force mains of the sanitary sewer infrastructure located along Harding and
Collins A venues, plus locations as far away as possible from the force mains and high-density
gravity sanitary sewer infrastructure to evaluate whether proximity to the sanitary sewer
infrastructure was associated with enterococci levels.
Three sites were identified as being as far away as possible from the pressurized sanitary
infrastructure (i.e., "far away" sites). These three sites form a triangle around the main study
area. Specifically, these sites were located at the far upstream end of the sanitary sewer gravity
system on Parkview Island (southwest side of the island , site 7), on 77th Street between Byron
and Abbot (site 8), and on the comer of7lst Street and Byron (site 9). Site 7 is located upstream
58
of the two gravity sewer pipes on Park View Island (Figure V.8). Site 8 is not adjacent to any
gravity sanitary sewer main and in addition is not connected to the stormwater conveyance
system (Figure V.8). Finally, site 9 is also as far away as possible to a sanitary sewer force main
and is connected to the stormwater gravity pipe that discharges directly to the main waterway
away from Park View Island (Figure V.8). Six additional sites were chosen given their close
proximity to the wastewater force mains (i.e., "close" sites) under the Miami Beach Parking Lot
between Collins and Byron and 72 nd and 73 rd Street (Sites 10, and 12 through 16). Of note, the
majority of the catch basins in close proximity to the pressurized sewer infrastructure were
inspected but several (as indicated in Figure V.8 bottom panel) contained no water and therefore
were not sampled. In addition, a sample labeled as site 11 was collected from the PVC waterway
from the Kayak Launch to provide a comparison to the levels observed from the catch basins.
Results from the waterway shoreline sampling show enterococci in the range from 2,000 to
360,000 MPN per g. The site that had the highest levels in the shoreline sediment was the site
located immediately adjacent to the Kayak Launch. As observed from the visual inspection at
this site, this is where the animal feeding station was located and where iguana feces were
commonly found along the banks.
Results from the catch basin sampling show that top sediments and bottom sediments were
characterized by enterococci levels that would exceed 1,000 MPN per gram with values reaching
several hundreds of thousands MPN per gram (800,000 MPN/g). Site 4 which had the highest
levels of enterococci in the catch basin water (>240,960 MPN/100 mL) also had high levels of
enterococci in the top sediments (650,000 MPN/g) suggesting that the top sediments (sediments
from the curbs on the street) serve as a significant source of enterococci. Visual inspection of the
areas contributing runoff towards the curb in this area showed leaking garbage dumpsters and
dumpsters without covers. Bottom sediments in the catch basins were also elevated suggesting
that these also serve as a concentrated source of enterococci. The site with the highest level of
enterococci in the bottom sediment was also the catch basin where considerable trash was visible
within the catch basin.
Overall results from shoreline and catch basin sampling suggest that major sources of
enterococci to the catch basins are runoff and sediments potentially contaminated by animal
feces, trash, and liquids from garbage dumpsters.
59
Figure V.7: Map showing locations for intense catch basin sampling conducted on August 17th •
The August 17th sampling focused on both the water and sediments. Red ovals show the location
of the stormwater outfalls, yellow squares show the location of the stormwater inlets and catch
basins. Dark brown lines and light brown lines show the location of the wastewater force mains
and gravity lines, respectively. Yellow squares, yellow and blue triangles show the locations of
the catch basins, sediment, and waterway water sampled on August 17th.
60
Figure V.8: Panel a) Map showing locations for intense catch basin sampling conducted on
September 2nd. On September 2nd sampling focused on water only. "Far-away" sites from the
pressurized sanitary infrastructure are shown as 7, 8 and 9. "Close" sites are shown as 10, 12 to
16. Panel b) Details of "far-away sites given in middle panel. Panel c) Details of "close" sites
along with location of catch basins with no water are provided in the lower panel
61
Homeless camp Food at Animal Feeding Station
Z'
C .,
3.§
C ""2 g ~
--a --._ OD z--._
0.. z
::;: 0.. ~::;:
'-~
~ !.l
"'" :s:.,
c:: .§ ·--a i~
~ .: ..., "'
"8~ 0., ~::: '-u ., u
-0 ~ ~
~
" tu
100,000
10,000
1,000
100
10
= 8/9TopSediments = 8/17 Top Sediments
13221 9/2 Top Sediments
-8/17 Bottom Sediments
-8/17 Catch Basin Water
••'JI!•• 9/2 Catch Basin Water
,Shoreline
Hotspot
~ :'r;i
SDI SD2 SD3 Sl S2 S3
m,355 2,158. 174.5
10,704 359,8 2,212
Trash in catchbasin
Bottom -/
Sediment ~/
><
·••; , •.
·{II:
·:•:
1 2 3 5
?$
6
Top
Sediment
.. ..
;i
7
¥
8
38 6,709 3,526 526,09 87.023 15.743
654,0
798,01 18,751
12,873 13,053 17,968 241.9
2,718 13,393 18,868 14.923 12,248 241.9 173 19.648
.. . .
ii
9
463
Leaking trash bins
..... x ... ···x·····•X... ..x .. . ··x···
10 12 13 14 15 16
37.135
13,753 16,768 11,730 14,978 6,240 12,528
4R
32,467
Figure V.9: Results from sediment and water sampling of channel banks and catch basins (August 17 and September 2). Sediment
results shown by bar plots and water results shown by lines.
62
V.3 INTENSE TEMPORAL SAMPLING USING AN AUTOSAMPLER
Prior efforts have been completed to collect bacteria data on a daily basis and also several times
per day. The results show that the enterococci levels are highly variable between days and
between fractions of a day. The lack of trends indicates that the temporal time scale of sampling
is too coarse. In other words, sample collection should occur on shorter time scale (such as
hourly) in order to capture trends in enterococci concentrations. Given the need to collect
samples from one location over shorter time scales, an autosampler (ISCO 6712) was installed at
the Kayak Launch (in an enclosure to avoid vandalism) which collected samples every hour over
the course of 48 hours (from October 18 at 7 am to October 20, 2022 , at 6 am). Samples were
retrieved 2 times per day (once every twelve hours) in individual pre-sterilized containers. In
addition, an EXO3 sonde fitted with water temperature, pH, salinity, dissolved oxygen, and
turbidity sensors was also deployed outside of the enclosure and attached to the floating dock in
the waterway suc h that the instrument maintained a constant depth from the water's surface. The
EXO3 sonde (Xylem Inc.) was set to record data every one minute. Similarly, the nozzle used
for the autosampler was also suspended from the floating dock such that it too maintained a
constant depth , screened at a depth from 6 inches to 12 inches below the water 's surface . Upon
processing of the hourly samples, the remaining sample was used for additional water quality
measurements (water temperature , pH , salinity, dissolved oxygen , and turbidity) using an YSI
Pro DSS sonde (YSI Inc).
In addition to direct measurements, additional hydrometerologic data were collected. This
included rainfall , tidal heights, and solar radiation. Rainfall was consolidated from three
stations , Miami Beach, Farrbetter, and Coast Guard Station (more details about these stations is
given in Section 11.2). Tidal heights were interpolated from the NOAA station at Virginia Key.
Solar Radiation was also available at the NOAA station at Virginia Key.
Results show a very strong response of enterococci to rainfall. During the 48-hour sampling
period no rain was detected for the first 31 hours with the exception of 0.01 inch detected at the
Miami Beach rain gauge at 2 pm on October 18 and 0.01 inch detected at the Coast Guard rain
gauge at 2 am on October 19 . Starting at 1 pm on October 19, rainfall was detected across
multiple rain gauging stations, with 0.41 , 0.38, and 0.34 inches recorded at the Farrbetter, Miami
Beach, and Coast Guard stations respectively (see Figure V .10).
Prior to the rainfall period (prior to 1 pm on October 19) the enterococci levels at the PVC were
less than 1800 MPN/100 mL, ranging from 228 to 1,730 MPN/100 mL. Upon the initiation of
rainfall, the enterococci levels increased considerably to values above detection limit (>24 ,200
MPN/100 mL). The response to rainfall was striking. These results confirm earlier analysis of
the historical data which showed strong correlations between enterococci levels and antecedent
rainfall.
A weaker relationship was observed with tidal height. Prior to the rainfall event, in general,
there was a general trend of higher enterococci concentrations during low tide and lower
enterococci concentrations during high tide. During low tide, the primary source of water to the
river would be groundwater (see Section 111.3 for further explanation). At high tide the primary
source would be ocean water pushing water back up into the waterway system. The Pearson
63
correlation (R) between enterococci and tidal height was computed as 0.81 (R2=0.66) (Figure
V.11). These results suggest that shallow groundwater may be a source of enterococci to the
PVC. However, compared to the impacts from rainfall, the impacts from groundwater are more
subtle.
Among the water quality parameters (as measured from the actual sample using a YSI probe), a
significant Pearson correlation was observed between enterococci and salinity (R=0.88, R2=0.78)
(Figure V.12). No significant correlations were observed between water quality measured from
the waterway with the EX03 (Figure V .13). These results suggest that water quality is highly
site specific and thus water quality results from actual samples is more indicative of enterococci
levels compared to ambient water quality in the vicinity of where samples were collected .
64
(a) -><-Eoterncocci ....... Farrbetter ....... Miami Beach o Coast Guai-d D Nighttime D Daytime 30 ~--------------------------::.._ _____ :...__~ 0.4
~
0.2 ·;
0::
>, .:: =
0.1:
0 -H~__.._.:&--<>----.---e4~~~~-4=~i-<,--o-"'i-e--G=~~...;.::;11===¥:...,,;,,.;=~➔-4---+-+-4>--e----o---<o----+--<>--~ 0.0
6:00 12:00 18:00 0:00 6:00 12:00 18 :00 0:00 6:00
10/18/2022 10/19/2022 10/20 /2022
(b) __,._ Enterococci -o-Tide (hr) D Nighttime D Daytime
30 ,-------------------------------------,-1.2
:3'
E 25
0
0 f 1.0
-
:::,
(c)
\ I
\ I J
0 x-><__,._,.-><-.c
6:00 12:00 18:00
10/18/2022
\
0:00
0 \
6:00 12:00 18:00
10/19/2022
-><-Enterococci -e--Solar Radiant D ighttim e D Daytime
0.8 --0.6 ..
~
0.4 ~
.':!'
0.2 .. ::c ..
0.0 -0 ~
-0 .2
-0.4
-0 .6
0:00 6:00
10/20/2022
30 ~----------------------------------~ 700
I
I
600 -500 ~e
~
400 c
"'
300 ~ 0::
200 ~
"'
100
0 ~~--'-'---'-~-===IS=~~_;:~~1!12="'=::!!::;l!.'.'...,._~-JJ...-Q-o-e--o--o--<>-&-e-e-0
6:00 12:00 18:00 0:00 6:00 12:00 18:00 0:00 6:00
I 0/18/2022 I 0/19/2022 I 0/20/2022
Figure V. I 0: Enterococci concentration at the KL W during the 48-hour sampling effort along
with: Panel (a) hourly rainfall from three closest weather stations; Panel (b) tidal height; and
Panel (c) solar radiation. White and grey background indicated daytime and nighttime during
the sampling, respectively.
65
_1.6 -r---------------------------,
,.J ~
E1r = = ... 1.2 z
~ 1.0
g 0.8
= co.6 -~
~ 0.4
(j
0 ~ 0.2
R2 = 0.66
....
C 1;i;J 0.0 +---~--~--~--~---~--~--~-----l
-0.40 -0.20 0.00 0.20 0.40 0.60 0.80 1.00 1.20
Tide Height (feet)
Figure V.11: Linear correlation between the concentration of enterococci and height of tide
(water level) from 7:00 to 19:00 on Oct. 18 , 2022.
25
<>' 00 O<> 0
' R2 = 0.78 ' ' -' ~ 20 ' ', 0 = ' ' ·-= '
Cj = '
Cj .,.... 15 ◊' ' Q ---' ~z ' ' 0 ' '"" Q.. ' ~ ~ 10 ' 0 ' 0 <;'
~ = ',◊ = 0 ' = .... ' ' 5 ' ..... ' '-' 0 ' ' 0
0 0
19 21 22 24 25 27
YSI Salinity (ppt)
Figure V .12: Linear correlation between the concentration of enterococci and YSI salinity from
19:00 on Oct. 18, 2022, to 6:00 on Oct. 20, 2022.
66
(a) ->t-Enterococci o Turbidity (EXO3) A Turbidity (YSI)
30 2
;J
8 2s A A A
0 A A A A ~ A 0 A A A A A A
Z 20 A A A A A A A
\
A A A A
=--1 ~ 0
g IS ~ ~ -2
5-
-3 'E 10
0 ~ oo
-4 "' 0 9 .. 5 ~ 0 I -5 = 0
r.l -)(->C....~,.__ _,._..____
0 x--"-><-....---~ _,._ --6
6:00 9:00 12:00 15:00 18:00 21:00 0:00 3:00 6:00 9:00 12:00 15:00 18 :00 21:00 0:00 3:00 6:00
10/1 8/2022 10/19/2022 10 /20 /2022
(b)
->t-E nterococci o DO (EXO3) o pH (EXO3) A pH (YSI)
30 --,---------------------------------------,-11
0
10
9
8
A A
0 7
0
0 0
o+.-2~...:;.....:.:_-,---=~=:!;1=!~=¥=-C.:,:--~...:;....~~-~-=-~-~)(;._::!:!.0
:::-X:.--,---=--,----,---.----,----,-----,l-6
6:00 9:00 12:00 15:00 18:00 21 :00 0:00 3:00 6:00 9:00 12:00 15:00 18:00 21:00 0:00 3:00 6:00
(c)
;J
10 /18 /2022
-><-Enterococci o Temperature (EXO3)
10 /19 /2022
o Salinity (EXO3)
10 /20 /2022
A Salinity (YSI)
30 --,-----------------------------------,-31.0
0 O
8 2s 0
-0 0
29.0
0
0 o _o O o @-o·9
0 o -o O O
0
0
A
A
A A A
A
A
A
A A 21.0
A
_j___2x--X-C~)(~-~,._,.=--:"-:_:"--><~-*-~-:::1><-~~±-~~~.:._-.:.:>C....::::!~~~~~~~~-~.----,-__::A___:A;:__--,----,------,l. 0 19.0
6:00 9:00 12:00 15:00 18:00 21:00 0:00 3:00 6:00 9:00 12:00 15:00 18:00 21:00 0:00 3:00 6:00
10 /18/2022 10/19 /2022 10/20 /2022
s-z.
"--c· :a
:Ei ... ;: ....
Figure V .13: Enterococci concentration at the KL W during the 48-hour sampling effort with
related physical chemical parameters : Panel (a) includes turbidity ; Panel (b) includes pH and
dissolved oxygen; and Panel (c) includes temperature and salinity.
67
V.4 DEPTH SAMPLING WITHIN THE WATERWAY, CATCH BASINS, AND WELLS
Variations in enterococci levels and water quality with depth were evaluated: a) within the
waterway, b) within catch basins, c) within vertical drainage wells , and d) within groundwater
monitoring wells. In addition to collecting samples for enterococci measurements, a YSI probe
was used in the field to measure temperature, pH, salinity, dissolved oxygen, and turbidity with
depth. After the samples were process for enterococci, the YSI probe was used again in the
laboratory to measure the same parameters from the samples that were collected.
For the waterway, samples were collected on two occasions, October 19 at 7 pm , and October 20
at 6 :30 am. These were collected at depths of 0.5 inch Gust below the water 's surface using a
sterile pipette) and from depths of 1, 2, 3, 4, and 5 feet from the kayak floating dock (GPS 25°
51 ' 31 .19", 80° 07' 32.95 "). Results show a strong gradient in enterococci with depth (Figure
V.14). The highest levels (above 19,000 MPN/100 mL) were observed in the surface samples
with decreases in enterococci concentrations with depth. The enterococci concentration of the
deepest samples collected at 5 foot depth measured at 1200 to 1700 MPN/100 mL. This trend
was observed consistently during both sampling efforts. In terms of water quality, temperature
was observed to increase with depth with temperatures in the 23 to 25 °C range at the surface and
near and above 27 °C at depth . Similarly, salinity was observed to increase from 16 to 20 ppt
near the surface to near 27 ppt at depth . pH also increased with depth from 7.4 to 7.7.
The density of water is dependent upon its temperature and salinity. For example, for the
October 19 sampling date , the density of the very top surface water is estimated at 1,010 kg/m 3
(temperature of 25.10 °C and salinity of 16.82 ppt). The density of the water at depth on that day
was 1017 kg/m 3 (temperature 27.60 °C and salinity of26.91 ppt). Essentially the fresher water
containing the higher levels of enterococci is floating over the saltier water with lower levels of
enterococci. Apparently, there is a density gradient vertically in the waterway that tends to
maintain the waters with the higher enterococci levels near the surface. The fresh water that
tends to float at the surface of the waterway tends to have high enterococci concentrations, lower
salinity, lower temperature, and lower pH.
For the catch basins, sites included:
• Site W4 located at Collins and 73 Street (GPS 25° 51 ' 30 .81 "N, 80° 07' 15.62 "W)
• Site W6 located at Dickens and 73 Street (GPS 25° 51' 29.98"N, 80° 07' 32.30"W)
• Site W8 located at 77 Street between Byron and Abbott (south side of road) (GPS 25° 51 '
43.53 "N , 80° 07' 24.40 "W)
Two samples were collected from each site, one from the surface (top) and one at depth
(bottom). Results for the catch basins (Figure V .15) showed that enterococci was generally
lower at W4 (360 to 1930 MPN/100 mL), which had been a hot spot during earlier sampling
rounds. Levels above detection limits (>24,200 MPN/100 mL) were observed for both samples
collected at W8 and for the top sample collected at W6. W6 was the only site among the three
that had a depth beyond 1.5 feet (7 ft) and the enterococci levels at depth were at 930 MPN/100
mL , lower than at the surface. Water quality at each site was distinct with the shallower sites
(W4 and W8) showing more uniformity. The deepest site (W8) showed distinct trends in the
68
vertical direction. At W8 there was evidence of a fresher water lens within the top foot
characterized by lower salinity, lower pH , and higher temperatures .
. For the vertical drainage wells, sites included:
• Site Vl located near the Kayak Launch (GPS 25° 51 ' 29 .99 "N, 80° 07' 32.23 "W)
• Site V2 located at Ocean Terrace and 73 Street (GPS 25° 51' 31.07"N, 80° 07' 10 .68"W)
• Site V3 located at Harding and 74 Street (GPS 25° 51' 34 .14"N, 80° 07' 20.24"W)
Similar to the catch basins, two samples were collected from each site, one from the surface (top)
and one at depth (bottom). Results for the vertical drainage wells (Figure V.16) indicate that V2
had the highest enterococci levels(> 17 ,000 MPN/100 mL). This site also had very low salinities
even at depth, and the lowest levels of dissolved oxygen and temperatures .
For the gr ou nd vvater monito rin g ,ve ll s, sites inc luded:
• Site G 1 located at North Beach Bandshell (GPS 25.8583060 , -80.1198783)
• Site G2 located at Parkview Park southwest comer (GPS 25.8572133, -80.1249013)
Unlike the other sites evaluated, enterococci levels at the groundwater wells (Figure V.17) were
very low . Three of the four measurements were below the detection limit of 10 MPN/100 mL
whereas one site measured at 20 MPN/100 mL. In general salinity increased with depth at the
groundwater monitoring wells with a freshwater lens observed within the top 10 feet. Turbidity,
dissolved oxygen, and pH decreased with depth. Overall, the enterococci levels at the
groundwater monitoring wells were different than at the catch basins, vertical drainage wells,
and waterway. The low levels of enterococci may be attributed to the deep screening depth of
the wells (about 35 feet) and the fact that they do not receive direct stormwater discharges.
Correlations between enterococci and water quality parameters showed Pearson and Spearman
significant correlations with pH (R>0.56) when the catch basin, vertical drainage wells, and
groundwater monitoring wells were considered (W4, W6 , W8 , Vl , V2 , V3, Gl , G2) (Table V.l).
When only the catch basin and vertical well sites were considered Pearson correlations were
significant for pH (R=0.63) and Pearson correlations were significant for salinity (rs=-0 .60)
(Table V.2).
69
(a) Enterococci (1,000 MPN/ 100 mL) (b) Turbidity (FNU) (c) Temperature (oC)
0 10 20 30 -1.0 0.0 1.0 2 .0 23 25 27 29
0 0 0 19-0ct -><-19-0cl 0 19-0cl 0
-0 -20-Oct A 0 A -20-0ct A 0 ·A 20-0ct o -A A 0
AO A 0
,<> A 0 ,. 0
A 0 • 0
Af o bo °'A
~ 0 ~
2 ? Detection Lim its • 0 A O
A 0 A 0 ' Exceeded z A 0 ti A 0
" ~ ,a! ~ ;3 ? ;3 A 0 :;;' 3 A 0
Q. C. a
~ ~ • 0 ~ AO
4 4 • 0 4 • 0
• 0 A 0
5 5 • 0 5 A 0
0 0
6 6 6
(d) Salinity (ppt) (c) Dissolved Oxygen (mg/L) (0 pH
15 20 25 30 3 .0 3.5 4 .0 4.5 5.0 5.5 7.4 7.5 7.6 7.7 7.8
0 0 0 19-0t:l 0 19-0l·I 0 19-0ct 0
0 • • 20-Qct 0 • A 20-0ct AO • 20-0<t OA 0 • D .. A 0 • 0
OA A 0 • 0
0 • • 0 • 0
00 •• • • 'b • 8 0
0 • .. 0 • 0
0 • 2 • 0 2 • 0
06 • 0 • 0
"' -;;-• 0 ti • 0
" " ~ ~ ~
:;;'3 0, :;3 • 0 :;;-3 A 0
fr C. a 00 " • 0 ~ A 0 0 0
4 ... 4 • 0 4 • 0
• • 0 • 0
5 5 • 0 s • 0
0 0 0
6 -'--------------~ 6 -'--------------~ 6 -'--------------~
Figure V.14: Measurements versus depth at the KLW. Panel (a) enterococci concentrations;
Panel (6) turbidity; Panel (c) temperature ; Panel (d) salinity; Panel (e) dissolved oxygen; and
Panel (f) pH.
70
(a)
3
6
En terococc i (1,000 M P N/ 100 mL)
10 20
(h)
0
t
Detection Limits-3
Exc eeded il ::,
*W4
~W6
♦W 8
-= ~
C.
Q
s
6
7
0.0
Turbidity (FN UJ
2.0 4.0 6.0
B-W4
-&-W6
♦W8
(c)
3
z ~
.c ,
C.
Q s
6
7
Te mperatu re (°CJ
26 27 28 29
B-W4
-&-W6
♦WS
8
8 .,__ ___________ __,
Sal ini ty (p pt) (c)
10 20 30 40
0
J 3
" " ..: ..:
:; 4 :; 4
a;-C.
Q Q
5 s
6 B-W4 6
7 -6-W6 7
♦W 8
8 8
0.0
Di sso lv~d Oxygen (mg/L)
1• LO 1 0 , C.
B-W4
-&-W6
♦WS
(f) pH
6.7 6.8 6.9 7.0 7.1 7.2 7.3 7.4 7.5 7.6 7.7 7.8
4.0 0 +-~--'--,,..--'---'-L.._.L_-'-~--'---4
2
3
" ..:
:; 4
C.
Q
5
6 B-W4
7 -&-W6
♦W8
8
Figure V.15: Catch basin measurements (W4 , W6 and W8) collected on November 14 , 2022 . Panel (a)
enterococci concentration ; Panel (b) turbidity; Panel (c) temperature; Panel (d) salinity ; Panel (e) dissolved
oxygen; and Panel (f) pH.
71
(a) Enterococci (1,000 MPN/ 100 mL) (b) Tu r bidity (FNU) (c) Te mperature ("C)
10 20 0.0 2.0 4.0 6.0 25 26 27 28
0 0
I 5
10
4 4
~15 " " ~ ,;! ,;!
..c ; 6 ;6
fr20 Q. 'c..
Q Q Q
8 8
25 *VI
-0-Vl
~V2 10 10 -0-VI
30 -o-V2 -o-V2
♦VJ ♦VJ ♦VJ
35 12 12
(d) Salinity (ppt) (e) Di ssolved Oxygen (mg/l.) (I) pH
0 10 20 30 40 0.0 1.0 2.0 3.0 4.0 6.9 7.0 7.1 7.2 7.3 7.4 7.5 7.6 7.7
0 0 0
5 2 2
10
4 4
~5 ;; " ~ " ,;!
= ~6 ;6
~o =-~ Q Q
8 6 8
25
-0-VI -0-V I -0-VI
10 10 30 -o-V2 -o-V2 -o-V 2
♦VJ ♦VJ ♦VJ
JS 12 12
Figure V .16: Vertical drainage wells measurements (VI , V2 and V3) collected on November 14 , 2022.
Panel (a) enterococci concentration; Panel (b) turbidity; Panel (c) temperature; Panel (d) salinity ; Panel (e)
dissolved oxygen; and Panel (f) pH.
72
29
7.8
(a) Enterococci ( MPN/ 100 mL) (b)
0 5 15 20 0.0
Turbidity (FNU) (c)
5.0 10.0 15.0 20.0 26
Temperatu re (°Cl
27 28
0 t---..,__-----,1'1'+--~---0 0 +-------,1,r..,.-,,,-------t
5 5
10 10 4
~15 ~6
~ ~
Bel o w Det ect io n
25 Limit
30
i -=
~ ...
0 20 Q 8
25 10
30 B-GI 12 B-GI
-b-G2 -b-G 2
35 14
(d)
0
o an----~----~-,
Sa linity (p pt) (e) Dissolve d Oxygen (mg/L) (f) p H
10 20 0.0 1.0 2.0 3.0 4.0 5.0 6.0 7.0 6.8 6.9 7.0 7.1 7.2 7.J 7.4
0
-6-GI 0
s -6-G2 2
10 4 4
Z6 ~6
~ ~
-= .c
fs C.
Q Q 8
25 10 10
30 12 ( -e-Gt 12 -e-Gt
-e.--G2 -b-G2
35 ~----------~ 14 14
Figure V.17 : Groundwater measurements at stations G 1 (Bandshell) and G2 (Parkview Island) collected
on November 14 , 2022. Panel (a) enterococci concentration; Panel (b) turbidity ; Panel (c) temperature;
Panel (d) salinity ; Panel (e) dissolved oxygen ; and Panel (f) pH .
73
7.5
Table V. l: Correlation between the enterococci in samples collected for Miami beach from November 14, 2022 with other physical chemical
parameters (field temperature (0 C), dissolved oxygen (mg/L), salinity (ppt), field pH and turbidity (NTU)) based on both Pearson's and
Spearman's analysis. Yellow indicates the significant correlation (p-value < 0.05). All sites for Table 4, including all top and bottom samples each
site for groundwater and stormwater (W 4, W6, W8, VI, V2, V3 , GI ,G2,).
Field Temperature Dissolved Oxygen Salinity (ppt) Field pH Turbidity (NTU) (OC) (mg/L)
Pearson Correlation 0.038 -0.184 -0.275 .6 73 " -0.376 Correlation : Coefficient (R)
Enterococci ( 1000
MPN/100 mL)
p-value 0.889 0.496 0.303 0.004 0.151
Spearman Correlation -0 .096 -0.349 -0.378 .569 ' -0.373 correlation: Coefficient (Rs)
Enterococci ( 1000
MPN/100 mL) p-value 0.723 0.185 0 .149 0.021 0 .155
Sample size 16 16 16 16 16
74
Table V.2: Correlation between the enterococci in samples collected for Miami beach from November 14, 2022 with other physical chemical
parameters (field temperature (0 C), dissolved oxygen (mg/L), salinity (ppt), field pH and turbidity (NT U)) based on both Pearson's and
Spearman's analysis . Yellow indicates the significant correlation (p-value < 0.05). All sites for groundw ater and stormwater including all top and
bottom samples each site for stormwater (W4, W6, W8 , VI, V2, V3).
Field Temperature Dissolved Oxygen Salinity (ppt) F ie ld pH Turbidity (NTU) (OC) (mg/L)
Pearson Correlation 0.150 0.031 -0.300 .626 * -0.406 Correlation: Coefficient (R)
Enterococci (1000
MPN/100 mL)
p-value 0.643 0.923 0.343 0 .029 0.190
Spearman Correlation 0.219 -0.142 -.599 ' II 0.249 -0 .402 correlation: Coefficient (Rs)
Enterococci ( 1000
MPN/100 mL) p-value 0.493 0.659 0.040 0.435 0.195
Sample size 12 12 12 12 12
75
CHAPTER VI
OVERALL ASSESSMENT AND RECOMMENDATIONS
76
CHAPTER VI
OVERALL ASSESSMENT AND RECOMMENDATIONS
Vl.1 SUMMARY
Results from this study indicate that the primary source of enterococci to the PVC is waste
deposited on surfaces of the areas draining towards the waterway. When it rains, the rainwater
washes surfaces (streets , roof tops , gutters) and in the process picks up FIB that are on these
surfaces. This runoff containing the FIB is then carried to the PVC through the stormwater
conveyance system . These sources and mode of conveyance to the waterway were identified
through the historical analysis of the data which showed the strongest correlations between
enterococc i and 24-hour antecedent rainfaii. This wa s co nfirme d from the 48 -ho ur sampling
effort at the PVC which showed a striking increase in enterococci within the waterway
immediately after a rainfall event, with sustained high levels of enterococci for many hours after
the rainfall event. Sources of enterococci to runoff include all waste that is found on the streets
within the catchment (Parkview Island plus areas to the east to Collins Avenue) including waste
from domestic (dogs) and feral (iguanas , racoons , and birds) animals plus waste from homeless
populations that live within the catchment and do not have access to sanitation facilities. Trash
was frequently found in the catch basins and flowing during storms from the storm conveyance
system to the waterways. Plus uncovered trash dumpsters and leaking trash bins were observed
to contribute towards the streets and thus ultimately washed into the storm conveyance
infrastructure. Roof drains which flow towards the storm conveyance system can also serve as
sources of enterococci. All these sources of enterococci are absorbed by the sediments which
can be flushed into the storm conveyance system and ultimately impact the PVC.
Although FIB on street surfaces was found to be the primary source of enterococci, this does not
discount the possibility of sanitary sewage leaks from contributing to groundwater
contamination. There is evidence that groundwater is contaminated and that it enters the
waterway during low tide, regardless of storm conditions. The groundwater influence is at a
lower level compared to the extreme impacts observed during storms from surface runoff. The
source of groundwater contamination can be surface runoff (FIB from the street surfaces) or
from sanitary sewer leaks. Samples collected from within catch basins and vertical drainage
wells show that the upper surface of the groundwater in areas that are designed to receive surface
runoff are contaminated with high levels of enterococci , frequently exceeding levels of detection
(>24,200 MPN/100 mL). In contrast groundwater in areas that are not impacted by surface
runoff have low levels of enterococci (<20 MPN/100 mL). The extremely high levels of
enterococci were usually found at the very top water surface of the catch basins , at the top of the
vertical wells , and at the very top of the surface waters of the PVC. These extremely high levels
of enterococci were fresher and thus float at the surface due to its lower density (because of its
lower salinity). Deeper groundwater and water from the ocean that enters the PVC tends to be
saltier and thus denser, denser than the freshwater that contains the extremely high levels of
enterococci. As a result a freshwater lens of lower density water that contains very high levels of
enterococci floats at the surface of the PVC. We believe this floating freshwater lens observed
within the PVC is produced by the waters that are conveyed by the stormwater infrastructure.
77
However, both surface runoff and sanitary sewage are freshwaters. Because of the timing of the
extreme enterococci levels, runoff contaminated by FIB found on surfaces within the catchment
is considered to be the major source at this time. However, we cannot discount the possibility of
wastewater contributions where leaks in the sanitary sewer system result in wastewater floating
at the surface of the groundwater which can then enter the PVC through the storm water
conveyance system (See Figure VI. I for conceptual diagram).
78
esher
(high bact
Saltier water .,,.,/'
(lower bac eria )
Salty
San itary Sewer ?
(fresh water)
Not proven but possible
.. o}
it 0
ater Inlet
(fre ater) ../
Figure VI.1: Conceptual illustration of stormwater conveyance system carrying freshwater with
high levels of enterococci towards the PVC. High levels of enterococci were found in the catch
basin waters and catch basin sediments. The stormwater conveyance system is designed to carry
surface runoff from storm events towards the PVC. Although no sanitary sewage leaks were
found as part of this study , the study cannot discount the possibility of sanitary sewage impacting
the upper layers of the groundwater which are connected to the storm conveyance system.
79
Vl.2 DETAILED RECOMMENDATIONS
The prior sections have identified the stormwater conveyance infrastructure as the conduit by
which high enterococci levels enter the PVC. The stormwater conveyance infrastructure that
discharges at the PVC , collects runoff from a large area (329 ,000 m2) comprising a wide range of
contributing factors (street sediments, roof run-off, animal feces, trash) which originate in the
vicinity of the PVC, Park View Island , and Park View Island Park and in areas farther away.
Other factors detailed in Chapter IV, such as animals and human settlements, potentially
contribute to the elevated levels as well. Finally, tidally driven groundwater fluxes could
potentially contribute to the high concentrations of enterococci.
Inputs of FIB in the stormwater conveyance system were identified in prior sections of this study
which detail elevated FIB concentrations in top sediments, bottom sediments and in the catch
basin water. Likewise, prior sections detail elevated FIB concentrations in shoreline sediments.
These inputs are visible and the following sub-sections set forth recommendations aimed at
reducing the impact from these inputs .
Other processes which may play a role in the elevated enterococci levels are not visible and are
more difficult to address. We observed evidence of elevated FIB , in the hundreds to thousands
MPN/100 mL , in the waterway during low tide not impacted by storm water flows. This suggests
that groundwater may be contaminated with FIB even during times between storm events. This
could potentially explain why enterococci levels , remain elevated during the dry season, and on
days with no antecedent rainfall. More work is needed to evaluate if tidally driven groundwater
fluxes to the waterway are contributing (to a lesser degree than the outfalls) to the elevated
enterococci levels. A confounding factor encouraging the accumulation of FIB is limited tidal
flushing coupled with persistence and multiplication of enterococci in the PVC and surrounding
sediment banks.
VI.2.a Reduce Inputs of FIB to Stormwater Conveyance System
The catchment contributing towards the PVC is highly urbanized with a significant amount of
impervious area with disproportionately small areas available for natural treatment or attenuation
of contaminants carried by runoff. Due to this situation, the catchment is unable to naturally
cleanse itself and will rely on human intervention or actions to reduce levels of FIB in runoff that
is carried towards the PVC. Below are recommendations for actions that can be taken to reduce
FIB inputs to the waterway.
• Within the catchment, excessive sediments and debris were observed in the curbs and
gutters that lead towards the underground stormwater conveyance system. These
sediments and debris have very high levels of enterococci and should be removed .
Studies should be conducted to benchmark street-sweeping frequency against other
nearby communities and any increases in sweeping frequency should be tied to a budget
requests and action to assure longer term sustainability. In response to this observation ,
the CMB has taken a two-pronged approach as a short-term solution. The CMB
sanitation team has since increased the frequency of hand crew cleanings from once a
week to twice a week. These crews clean debris from sidewalks, gutters, and the right of
80
way. In addition to hand crew cleaning, the CMB has increased the frequency of
mechanical street sweeping on Parkview Island, with considerations given to increase the
frequency of street sweeping for catchment areas to the east.
• Trash was frequently found within the stormwater conveyance system. Trash is a source
of FIB as it contains feces plus it contains nutrients needed for FIB to grow . Efforts
should focus on increasing trash pickup and minimizing the amount of trash that enters
the stormwater infrastructure. In response the CMB sanitation team has increased the
cleaning of public litter cans to twice day from once a day (7 days a week).
• To further address trash, trash filters should be explored at curb and gutter inlets. If this
is not feasible , trash racks with the stormwater system can also be considered . With the
inclusion of filters and rack comes the possibility of increased flooding if the racks and
filters become blocked. The feasibility of the installation of filters and racks should
consider their potential contributions towards flooding. It is our understanding that the
CMB has explored filters at catchbasins and their initial assessment ind icate that such
filters contribute towards flooding. A better alternative identified by the CMB is the
inclusion of trash racks at pump stations since they can be more easily maintained to
prevent blockage by debris. Another alternative is to install bar racks upstream of the
outfalls, which would require further exploration.
• Leakage from trash bins should be eliminated by enforcing that trash dumpsters be
covered and liquid leakage from the dumpsters be redirected away from storm drains .
Redirection towards grassy areas that provide some treatment is one possibility. In
addition, considerations should be given towards minimizing leaks from trash dumpsters
by lining the trash bins. In high volume locations, additional trash receptacles may need
to be added to handle the amount of trash generated. In response, the CMB has increased
the frequency of cleaning public litter cans and has added rain domes to the public trash
bins to minimize leakage from trash cans.
• Reduce animal sources by eliminating animal feeding stations and improving
management of invasive wild animals such as iguanas, racoons, and non-native birds
(e .g., roosters). In response to this observation, the animal feeding station at Parkview
Park was removed (but it then returned). The CMB is committed to addressing this
situation through increased vigilance of the area and by enforcing park hours of
operation. The CMB is in the process of developing signs to discourage feeding wild
animals.
• CMB has initiated a strong campaign to encourage dog owners to remove pet waste. The
signage and availability of doggie bags and waste bins is prevalent at Parkview Island
Park. Extending this signage throughout the catchment area including areas extending
east through to Collins Avenue and Ocean Terrace would be beneficial.
• CMB public education efforts are commendable as evidenced by its easy-to-use web site
(https://www.miamibeachfl.gov/engagementtoolbox/) and mobile apps used for
communications purposes. Such efforts should continue and expand to further emphasize
proper disposal and covering of trash and proper disposal of yard debris away from the
waterway. Fertilizer use , especially in areas that drain towards the waterway, should be
discouraged as these fertilizers provide nutrients which may allow bacteria to proliferate.
Businesses in the area should continue to be informed of ways to reduce their potential to
81
pollute stormwater. In response , the CMB has initiated efforts to add signage about
fertilizer use within the catchment including within the community garden area.
• Encourage further public participation in identifying and reporting potential sources of
contamination to the waterway. During a sampling event, a community member informed
the team of live-aboard boats in the area which could potentially serve as a source of
bacteria if the waste from the boats is not disposed via pump out stations . Assuming that
this is in fact the case within the PVC , a public education campaign for live aboard boat
owners of the availability of pump out stations could help encourage proper disposal of
waste. In response to this recommendation, the CMB is developing a public education
campaign to engage the community champions and building managers in efforts to
minimize sources of contamination to the waterway.
• Evaluate improve sanitation opportunities for homeless through either rehabilitation of
the homeless (e .g., Lazarus project), relocation to places that have proper sanitation, or
provision of sanitation facilities . The CMB should continue with its strong homeless
outreach services. Outreach occurs two to three times per week at Parkview Park to offer
services to homeless populations.
• Evaluate the stormwater conveyance system for its ability to treat the first flush of
rainfall-runoff. Modern stormwater conveyance systems are required to treat the first
inch or so of stormwater prior to discharge to a receiving water body. The stormwater
conveyance system should be comprehensively evaluated for its ability to treat the first
flush of contaminants. Common ways to treat the first flush involve letting the first
portion of the rainfall-runoff enter a detention area where particulates settle. Other
designs are based upon the use of grassy swales to retain the first flush. Given the lack of
space for stormwater retention, consideration should be provided towards replacing
impervious areas with pervious systems that allow for some runoff treatment.
Along these lines , the CMB was awarded a $1 OM Florida Resilient Grant for the
design of a Neighborhood Improvement Project (North Shore D and Towncenter
Neighborhood Improvement Project) which includes a proposed stormwater conveyance
system that will replace the existing stormwater pipe network from 69th street to the
south to 73rd street to the north and from the PVC to the west to Collins Avenue to the
east. The stormwater conveyance system is currently projected to include new catch basin
structures, manhole structures, conveyance piping, injection wells (to treat the first flush),
and up to two stormwater pump stations. The stormwater pump stations will be
configured to include upstream water quality filtration and treatment to treat the first
flush of contaminants in the form of bar racks and vortex water quality structures.
Additionally, energy dissipation structures will be constructed downstream of the pump
stations prior to discharge into adjacent canals to prevent damage to the existing plant life
and canal bottom. The stormwater system will also be fitted with back flow prevention
devices where needed to prevent backflow of tidal waters into the storm water system.
The scope of this project also includes the replacement of adjacent potable water and
sanitary sewer conveyance, distribution, and transmission systems. The aerial potable
water and sanitary sewer pipe crossings at the 71st street bridge over the PVC will be
replaced with subaqueous crossings under the scope of this project. This project is
currently in negotiation and is projected to start design early 2023.
• Additionally, the City has a Blue-Green Infrastructure Concept Plan that was adopted by
City Commission. All Neighborhood Improvement Projects must consider proposing
82
blue-green storrnwater infrastructure such as swales, bioswales, injection wells,
permeable pavement, rainwater harvesting, tree canopy, etc. The North Shore D and
Towncenter Neighborhood Improvement Project will incorporate blue-green
infrastructure where feasible. Given the limited space for storrnwater retention facilities
to treat the first flush , more highly engineered systems should be considered inclusive of
bar racks (for trash removal) and vortexers (for coarse sediment removal). If elevated
levels of enterococci persist even with these measures, alternative methods to treat the
runoff can include active disinfection process through UV disinfection. However, UV
disinfection systems are expensive, require considerable maintenance, and are effective
only for low turbidity waters. It is unclear whether the rainfall-runoff from the catchment
area would be suitable for UV disinfection , but the possibility should be explored. In
addition to the approaches described in the above bullet, one alternative that has been
imp lem ented by C MB is the inclusion of a vortexer called the Hydrodefender. This
device adds 1 foot of head (causes water to back up by 1 foot) which may be excessive in
areas prone to flooding. This can be addressed by placing the Hydrodefender
downstream of pumps. This way the pumps can provide the 1 foot of pressure needed to
minimize impacts on flooding.
• Focus on illicit connections and their removal. Illicit connections are those that are not
composed of storrnwater. They flow during dry weather due to connections with other
sources of water and examples can include water from car washing, clothes washing , and
inadvertent cross connections with sanitary sewage. The CMB is currently working with
the legal authority (County ID ERM) on illicit discharges from outfalls. A list of illicit
connections is provided biannually to DERM and CMB continues to actively notify the
environmental regulatory authorities. Connections prior to 1984 (when DERM
established) have been grandfathered. It is our understanding that these grandfathered
connections can only be legally addressed when the facility with the connection goes
through its 40-year recertification. In the meantime, the CMB will continue to refer these
connections to DERM, and will press the county for a resolution.
VI.2.b Reduce Impacts of Stormwater Discharge in the PVC
•
•
The hydrology of the PVC should be explored further to better understand its water
circulation during and after storms and during the cyclical ebb and flow of the tides. The
waterways on the north end of the PVC (Biscayne Point) are anecdotally believed to limit
flushing of water from the PVC to the north. The hydrodynamics of the area should be
explored to better assess areas with restricted circulation.
One option to improve circulation is dredging of the PVC , particularly at the north and
south intersections with the Biscayne Point Waterway and the Main Waterway
(Normandy N-S). Additionally, circulation along the northeast and southeast bends could
be improved by dredging at depth angles that limit the deposition of sediments. The CMB
is currently exploring potential dredging to improve water circulation . The CMB has
identified funding ($500 ,000) for bathymetric and geotechnical surveys of the PVC .
• Removal of trash from the PVC waterway. If dredging is not an option , at least the
removal of trash from the bottom and along the banks of the PVC should be explored . At
83
low tide, near the banks of the PVC trash was observable from the water 's surface and
the trash should be removed as it serves as a source of resistance to water flow.
• To limit the erosion of sediments and transport of trash by runoff along the shoreline we
recommend that the shoreline be protected by increasing vegetation cover, inclusive of
mangroves and other plant species which act as deterrents to the public accessing the
PVC through any point other than the Kayak Launch pad. CMB is developing plans for
an improved living shoreline that can provide additional treatment of direct runoff to the
waterway while improving the area 's ability to maintain a healthy ecosystem.
To address this issue , the CMB acquired Cummins Cederberg to conduct a Nature
Based Shoreline Assessment (CCI 2021) that selected the most viable locations for living
shorelines within the sites of CMB-owned seawalls. Ten locations where identified, two
of which are directly adjacent to the the PVC. Given the recommendations from the
Cummins Cederberg report, the CMB has applied for $ l 1.5M (with $1.5M match) in
funding from the NOAA Transformational Habitat Restoration and Coastal Resilience
Grant. The Cummins Cederberg study showed that the 2,460-foot shoreline along the
PVC is densely packed with mangroves. The living shoreline project will remove
invasive vegetation, repair and rehabilitate damaged seawalls, and mitigate coastline
erosion. Awards for this grant should be announced early 2023 and the design would
commence shortly thereafter.
VI.2.c Continue Searching for Sanitary Sewer Leaks
• The CMB has conducted considerable work towards identifying potential sources of FIB
to the stormwater system impacting the PVC and issues have been corrected when found.
Efforts include water sampling, sanitary sewer inspections, stormwater conveyance
system inspections. Sampling has been conducted to evaluate source tracking markers
(through Source Molecular) and via a contract to ESciences which included an evaluation
of the catch basins. Work has also been extensive in evaluating potential cross
connections between the sanitary sewer and storm conveyance system. Techniques used
include evaluation of the proximity of the systems through GIS and evaluation of
construction drawings, dye testing , camera testing, acoustical testing , and smoke testing .
For example, the CMB has been conducting work towards reducing infiltration and
inflow into the sanitary sewer system (Hazen 2022a). The focus has been on
rehabilitating manholes, gravity mains , and laterals. Techniques utilized include night
flow isolation , camera inspections, manhole inspections, and smoke testing. A study
specific to Parkview island (Hazen 2022b) found multiple gravity sewer pipes in need of
cleaning and repair . These pipes have been repaired by lining the sewers to reduce leaks.
This study focused on gravity sewers within the public right-of-way and did not evaluate
the integrity of sewer laterals on private property. Although the work has been extensive
through CMB, additional efforts are recommended below.
• Focus on rehabilitating areas with excessive infiltration and inflow as identified through
Hazen 2022a. The area south of 72 Street has been identified as one such area. Continue
with plans to line sanitary sewer pipes known to have excessive infiltration. To address
this, as mentioned above , the CMB was awarded a $1 OM Florida Resilient Grant for the
84
design of a Neighborhood Improvement Project (North Shore D and Towncenter
Neighborhood Improvement Project). The scope of this project also includes the
replacement of potable water and sanitary sewer conveyance, distribution , and
transmission systems from 69th street to the south to 73rd street to the north and from the
PVC to the west to Collins Avenue to the east. The aerial potable water and sanitary
sewer pipe crossings at the 71st street bridge over the PVC will be replaced with
subaqueous crossings under the scope of this project. The infrastructure identified as
critical due to age , infiltration , or other criteria will be addressed within this project
scope . This project is currently in negotiation and is projected to start design early 2023 .
• Evaluate new technologies to identify potential sanitary sewer leaks. It is our
understanding that CMB is currently working with companies who can provide
innovative leak detection services (e.g ., Asterra which is currently in procurement).
e Characterize the groundwater to surface water pathway . Additional sampling of the
upper surface of the groundwater is recommended to evaluate the extent of enterococci
contamination. The direct push technology currently being implemented at other
locations in Miami Beach should be explored for gathering shallow groundwater samples
within the top centimeters of water table at various locations close to and away from the
sanitary sewer system. Assessment of groundwater sample data should take into account
the direction of groundwater flow.
VI.2.d Quantify Tidally Driven Groundwater Discharge
• In order to understand the interaction of tidal fluctuations in the PVC and nearshore
groundwater zones we recommend activities to assess the groundwater flow direction and
vertical and horizontal hydraulic gradients in order to develop a robust conceptual site
model. Such information can be integrated into a model that would allow for a better
assessment of contaminant (microbe) fate and transport.
• More accurately document the hydraulic gradient between the adjacent groundwater and
surface water.
• To better characterize the hydrology , set up a surveying benchmark to provide a reference
for water elevations at the Kayak Launch pad . An ideal benchmark can be a marker of
known elevation on the piling that supports the Kayak Launch.
• Recommend groundwater sampling to evaluate potential sanitary sewer contamination.
Direct push technology (Res 2022) can be potentially used to obtain samples which can
be then analyzed for indicators of sanitary sewage. Indicators of sanitary sewage, in
addition to the FIB (e.g ., enterococci) can include chemical indicators of human waste
such as caffeine, sucralose, and acetaminophen.
Vl.2.e Develop a Long-Term Comprehensive Plan for Stormwater (and Sanitary) System
Improvements
• It is our understanding that the CMB has initiated work with consultants for a design to
improve stormwater management in the area by re-routing stormwater towards a
centralized treatment system that would be designed to remove trash and coarse
85
particulates using vortex separators. The plan, as described above (through the $1 OM
Florida Resilient Grant), includes the integration of injection wells that would provide
additional treatment for the first flush of stormwater. Such a system would be similar to
the one designed for first street which receives stormwater from Alton Road and
Washington Avenue. The treatment system elements include water quality wells, bar
screens, vortex separator, and an energy dissipator structure. Assuming that this system
is effective (by measuring water quality in and out of the system), this process should be
considered for treating PVC stormwater.
• Benchmark plan against those developed for other communities. The Florida Keys have
been successful at improving coastal water quality through a comprehensive 20-year plan
which aimed at improving both sanitary and stormwater infrastructure. For example, the
main goal of the 2001 stormwater master plan (COM 2001) for Monroe County was
water quality protection and improvement. This report provides an excellent summary of
stormwater best management practices listing both structural (JEA 2020) and
nonstructural stormwater controls. A hierarchy is provided in terms of actions that can be
taken from low cost to higher cost.
Although the CMB recognizes that a lot of work is to be done on long-term
planning, it has initiated some work through its Stormwater Master Plan Update and
Capital Improvement Plan that will identify critical needs to be addressed by the City
over 10 years. The plan will take several criteria into consideration including storm water
flooding, tidal flooding, water quality issues, and resident complaints. The Stormwater
Master Plan Update will be completed and presented to City Commission in November
of 2023.
The City acquired Hazen and Sawyer to complete Water and Sewer Master Plans
(2019a,b) that have identified and prioritized critical projects that must be completed in a
timely manner. Projects for the capital improvement plans were based on specific criteria:
the sanitary sewer system was evaluated based on capacity, probability of failure (useful
life), and consequence of failure (cost of repair, social/health impacts, and environmental
impacts). The water and sewer capital improvements received $122M in funding to
implement.
VI.3 SUMMARY OF RECOMMENDATIONS
Overall, a comprehensive plan should be developed for the PVC that address both short term and
long term improvements in water quality. In the short term, efforts should focus on management
of feral animals within the catchment, continued aggressive education programs to minimize dog
fecal waste and other waste sources throughout the stormwater catchment, and facilitating
improved sanitary conditions for the homeless. Minimizing trash on the streets, capturing trash
prior to entering the waterway, reduction of seepage from trash bins, and increased street
sweeping should also be considered. Efforts should be continuous for assessing the possibility of
sewer leaks. Of interest would be to explore the extent of enterococci contamination at the
surface of the groundwater by documenting groundwater gradients in the area coupled with
86
sampling of the shallow groundwater. Such an approach may help to pinpoint areas with possible
sanitary sewage leaks.
In the longer term, plans are recommended for upgrading the storm and sanitary infrastructure .
For stormwater, efforts should focus on developing conveyance systems to treat the first flush
and the possibility of providing a treatment system for trash removal, sediment reduction, and
possibly disinfection . Plans should also be put into place to upgrade the sanitary sewer system
given the age of the system and the possibility of leaks. The lack of circulation within the PVC
also contributes to the elevated levels , and efforts should also focus on better understanding the
hydrology of the PVC and improving water flow through the removal of debris/trash and
possible dredging.
87
ACKNOWLEDGMENTS
This project was funded by the City of Miami Beach . We thank the City of Miami Beach Public
Works teams who provided available data and logistical support during sampling efforts . We
also thank the many interested parties who have shared their insights with us in efforts to better
understand the cause of the elevated enterococci levels.
88
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COVID-19 shutdown period and associations with decomposing seaweed and human presence.
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Badgley, B.D., Thomas, F.I.M., Harwood. V.J., 2010. The effects of submerged aquatic
vegetation on the persistence of environmental populations of Enterococcus spp. Environ.
Microbiol. 42: 1271-1281
Biscayne Bay Task Force (BBTF), 2020. A Unified Approach to Recovery for a Healthy &
Res ili ent B iscayne Bay, B iscayne Ba y Task Force Repo rt and R ecomme datio ns , June 202 0 .
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association with fecal indicator bacteria in the surf zone. Environmental Science & Technology,
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Boehm, A .B., Fuhrman, J.A., Mrse, R.D ., Grant, S .B., 2003 . Tiered approach for identification
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Indicator Organisms in a Tidally Influenced Subtropical Environment. Applied and
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l 172.2002
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Phillips, M.C., Klaus, J.S., Piggot, A.M., Feng, Z., Reniers, A.J.H.M., Haus, B.K., Elmir, S.M.,
Zhang, Y., Jimenez, N .H., Abdel-Mottaleb, N., Schoor, M.E., Brown, A., Khan , S.Q ., Dameron,
A.S., Salazar, N .C., and Fleming, L.E., 2012. Spatial and Temporal Variation in Indicator
Microbe Sampling is Influential in Beach Management Decisions, Water Research, 46: 2237-
2246. http://dx.doi.org/10.1016/j.watres.2012.0l .040 PMID: 22365370
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Grant, S. B; Sanders, B. F; Boehm, A . B; Redman, J. A; Kim, J. H; Mrse, R. D; Chu, A. K;
Gauldin, M; McGee, C. D; Gardiner, N. A; Jones, B. H; Svejkovsky, J; Leipzig, G. V; Brown,
A. Generation of enterococci bacteria in a costal saltwater marsh and its impact on surf zone
water quality. Environ. Sci . Technol. 35: 2407-2416
Hazen and Sawyer (Hazen), 2019a. City of Miami Beach Sewer System Master Plan.
Hazen and Sawyer (Hazen), 2019b. City of Miami Beach Water System Master Plan.
Hazen and Sawyer (Hazen), 2022a. City of Miami Beach Sanitary Sewer Evaluation Survey,
Phase I, preliminary sewer system survey, sewer system analysis, and corrective action plan,
Hazen and Sawyer (Hazen), 2022b. Parkview island Gravity Sewer Video Review -Part 1,
Technical Memorandum .
Izbicki, J.A., Swarzenski, P.W., Burton, C.A., Van De Werfhorst, L.C., Holden, P.A ., Dubinsky,
E.A., 2012. Source of fecal indicator bacteria to groundwater, Malibu Lagoon, and the nearshore
ocean, Malibu, California, USA. Annals of Environmental Science, 6, 35-86.
Jonah Ventures (JV), 2022. Report prepared for bwtf@miami.surfrider.org, BatchID =
JVB 1755. info@jonahventures.com.
Jones Edmunds & Associates (JEA), 2020 . Updated Manual of Storm water Management
Practices, Prepared for Monroe County Department of Planning & Environmental Resources,
Key Largo, FL
Kelly, E. A., Feng, Z., Gidley, M. L., Sinigalliano, C. D., Kumar, N., Donahue, A.G., Reniers,
A. J. H. M., and Solo-Gabriele, H. M., 2018. Effect of Beach Management Policies on
Recreational Water Quality. Journal of Environmental Management, 212 : 266-277.
doi: 10.1016/j.jenvman.2018.02.012 PMID: 29448181
Miami New Times (MNT), 2018. Horrible Biscayne Bay Pollution Worsened by 800-Gallon
Sewage Leak. Story written by Jessica Lipscomb and published on November 27, 2018.
https://www.miaminewtimes.com/news/biscayne-bay-polluted-by-800-gallons-of-poop-from-
miami-beach-city-says-l 0926772
Pace Analytical, 2020. Report of Laboratory Analysis, Pace Project Number: 35593582.
Submitted by Brad Smith to Elizabeth Wheaton on December 7, 2020.
Pace Analytical, 2021. Report of Laboratory Analysis, Pace Project Number: 35600623.
Submitted by Brad Smith to Elizabeth Wheaton on January 11, 2021.
Park View Island Sustainable Association (PV ISA), 2021. Miami Beach's Dirty Little Secret -
The Park View Island Canal. Story written by Valentina Palm and published on March 17, 2021 ,
credit: FIU/South Florida Media Network.
https ://www.parkviewisland.com/miamibeachsdirtylittlesecret
90
RES Florida Consulting (RES), 2022. Proposal for Sewer and Groundwater Sampling for the
West Avenue Sewer Extension Permit Miami Beach, Miami Dade County, Florida. E Science
Roca, M.A., Brown, R., Solo-Gabriele, H. M . 2019. Fecal indicator bacteria levels at beaches in
the Florida Keys after Hurricane Irma. Marine Pollution Bulletin , 138, 266-273 .
http://doi.org/10.1 0l 6/j.marpolbul.2018.09.036
Russell, T. L., Sassoubre, L. M., Wang, D., Masuda, S., Chen, H., Soetjipto, C., Hassaballah, A .,
Boehm, A. B., 2013 . A coupled modeling and molecular biology approach to microbial source
tracking at Cowell Beach, Santa Cruz, CA, USA. Environmental Science & Technology, 47,
10231-10239.
Skinner, J .F ., Kappe ler, J.; Gu zman , .J. 2010. Regrowth of Enterococci & Fecal Coliform in
Biofilm . Stormwater. Published on July 1, 2010. Available at:
https://www.stormh2o.com/bmps/article/l 3005530/regrowth-of-enterococci-fecal-coliform-in-
biofilm
Solo-Gabriele, l--:1-, Wolfert, M , Desmarais, T., and Palmer, C., 2000. Sources of E.coli to a Sub-
Tropical Coastal Environment. Applied and Environmental Microbiology, 66(1): 230-237.
http://dx.doi.org/10.1128/AEM.66 . l.230-237.2000
Swarzenski , P.W., Burnett, B ., Reich, C., Dulaiova, H., Peterson, R., Meunier, J., 2004, Novel
geophysical and geochemical techniques used to study submarine groundwater discharge in
Biscayne Bay, Florida: U.S. Geological Survey Fact Sheet 2004-3117, 4.,
https://doi.org/10.3133/fs20043117.
Whitman, R.L., Shively, D.A., Pawlik, H, Nevers, M.B., Byappanahalli, M.N. 2003. Occurrence
of Escherichia coli and enterococci in Cladophora (Chlorophyta) in nearshore water and beach
sand of Lake Michigan. Appl. Environ. Microbial. 69: 4714-4719
WLRN Miami, South Florida 91.3 FM , 2020. Miami Beach Lost Half Its Sewage Capacity. Age
Was Partly to Blame. Story written by Jenny Staletovich and published on March 10, 2020.
https ://www.wlrn.org/environment/2020-03-10/miam i-beach-Iost-half-its-sewage-capacity-age-
was-partly-to-blame
Wright, M.E., Solo-Gabriele, H.M., Elmir, S., Fleming, L.E. 2009. Microbial load from animal
feces at a recreational beach, Marine Pollution Bulletin, 58(11 ): 1649-1656.
http://dx.doi.org/10.1016/j.marpolbul.2009.07.003 PMID:19664785
91
APPENDICES
92
APPENDIX A
INITIAL REVIEW OF PRIOR DATA
93
APPENDIX A
INITIAL REVIEW OF PRIOR DATA
Review of Data Provided during April 2022
Access to a shared drive was facilitated through the City of Miami Beach (Mariana Evora). This
drive included a set of folders. A brief assessment of what was observed in each folder ( each
subheading is a folder name) is provided below. Recommendations for additional information is
provided.
Groundwater Wells
A map of groundwater wells is provided in the folder called, "Groundwater Wells." The nearest
groundwater well is "Parkview Park (PVP)". Physical Chemical data is provided for this site
(GPS 25.85723264751922 -80.12488156557083, located on Google Earth to be on the southwest
comer of the baseball fields, See Figure Al below). Results show salinities in the 25 to 29 psu
range. Recommendation: As part of a preliminary reconnaissance -collect a sample of this
groundwater to determine whether it is impacted fecal indicator bacteria.
Figure A.1: Location of groundwater well for which data were included in the shared folder.
Background image from Google Earth.
Heat Maps ( data not verified)
The heat maps clearly indicate that the storm drain system has extremely high levels of fecal
indicator bacteria on frequent occasions. Results between enterococci and fecal coliform are
consistent with one another. Below in Table A 1 is a very quick review of the data.
Recommendation: As part of a preliminary reconnaissance -in addition to collecting a sample
from the Kayak Launch, collect a sample of surface water at the outlet of each of the outfalls at
low tide, at the point where it enters the canal with the Kayak Launch. Record date and time and
tie back to tidal stage.
94
Table A . I: High level summary of heat maps of storm drainage system.
Sampling Date Enterococci
(estimated units of counts per 100 mL)
June 9, 2020 hundreds
June 18, 2020 hundreds to tens of thousands
June 30, 2020 double digits to hundreds
July 7, 2020 hundreds to above detection limits*
July 31, 2020 hundreds to thousands
August 26, 2020 above detection limits
August 27 , 2020 hundreds to above detection limits
September 3, 2020 hundreds to above detection limits
*Detection limits > 24196 counts per 100 mL.
Photos
Fecal coliform
(estimated units of counts per 100 mL)
double digits to hundreds
double digits to hundreds
double digits to hundreds
hundreds
above detection limits
hundreds to above detection limits
hundreds to above detection limits
The photos include views of the canal and sewage pipe that runs under the bridge at 857 Michael
Street (Figure A2). Recommendation: As part of a preliminary reconnaissance -collect a
sample from the sediments under the mangroves (at low tide) to determine whether it is impacted
fecal indicator bacteria.
Figure A.2: Photo of canal where kayak launch is located and photo of pipe under bridge at 857
Michael Street.
Sanitary and Storm Sewer Maps in the Area
The maps emphasize that there is a very intricate network of storm and sanitary sewers with the
possibility of cross-over between the two. In another folder the locations of the cross-overs have
been identified. There is a very large sewer main connection from the mainland passing at 72 nd
Street equivalent (Figure A .3). To complement the comprehensive map in the file called "North
Beach Sewer Overview,pdf', images "4A", "4B", and "5" provide additional details. These
detailed maps provide locations of storm drain outfalls at the canal where the Kayak Launch is
located. Recommendation: Add sample collection IDs to these maps. In the folder called
"Water Quality Results" there are data corresponding to locations called OT-2 , OT-4 , OT-7, US-
IA, US-1 B, etc ... which do not have GPS coordinates nor location descriptions. The results at
these locations show very high (enterococci >24 ,196 MPN/100 mL). Efforts are needed to
determine when these sites are contributing to the Kayak Launch location. But first we need to
know where these sites are located relative to the storm drain system.
95
Figure A.3: Storm and sanitary sewer network emphasizing the location oflarge sewer main that
crosses the Parkview Canal at 72nd Street. Image from file "North Beach Sewer Overview.pdf',
City of Miami Beach.
Siphon Inspection
The siphon is located at Park View Island and 75th Street and is defined by manhole A and B.
On June 9th, 2020 the Public Works Operations Division conducted a dye test on a siphon that
crosses the canal. From this test there were no visible traces of dye in the waterway and the dye
was seen coming out the siphon's downstream manhole . On July 20, 2020 the siphon was
inspected by camera with no visible signs of leakage. Recommendation: Location of siphon
needs to be clearly identified on the maps. GPS coordinates for manhole A and B are needed.
Smoke Testing
Many recommendations were made by the consultant to minimize leaks from a December 2020
inspection of the sanitary sewer system. Recommendation: Document whether these
recommendations have been addressed and conduct another smoke test to follow up.
Test Results
This folder includes results from two sets of studies: one from Microbial Source Tracking and
another from a bay-wide water quality study.
Microbial Source Tracking
Microbial Source Tracking found evidence of dog inputs in a groundwater well and at the Kayak
Launch on October 13, 2020, and again at the Kayak Launch on November 5, 2020. There was
96
no strong evidence of human sources. These results are very interesting in that it would point the
source away from sanitary (human) sewage towards runoff. Of interest would be to test the
water in the storm drains for human and dog markers, especially when values are above detection
limits for fecal indicators.
Bay Wide Water Quality Results
The "Test Results" folder also contains physical chemical, nutrient, and fecal indicator bacteria
data for the sites shown in the following map (Figure A.4) (Pace Analytical 2020, 2021) for the
months of November 2020 and December 2020. The site within the PVC is site 69. The next
two closest sites are sites 70 and 79. When reviewing the data in these reports only data for site
79 was available. This site is located to the southwest of the PVC within a larger more open
section of the bay (Figure A.4). From the summary of results (Table A.2) the fecal indicator
bacteria levels were high on November 2020 which is surprising given that this area is much
more highly flushed. Of particular interest is that for this site the dissolved oxygen level was
very low (0.96 mg/L) and the ammonia was high (1.3 mg/L) which suggests a source of
biochemical oxygen demand (possibly wastewater).
Of note is that since the provision of the November and December 2020 reports, the consolidated
data was provided by the CMB for the PVC (site 69). This consolidated data for the entire
period ofrecord (monthly from April 2019 to October 2022, summarized in Table B. l in the
appendix) was evaluated for correlations in Section 11.3.a of the report (page 26). Results
showed in section 11.2.a that antecedent rainfall was the primary predictor of enterococci levels
(more rain more higher enterococci). Salinity and specific conductivity also contributed towards
correlations with enterococci (higher salinity or specific conductivity corresponded to lower
enterococci). No significant correlations were observed with nutrients, nitrogen and phosphorus.
Table A.2: Summary of water quality results from site 79, site closest to the PVC.
Site 79 Water Quality Parameter November 2020 Decem her 2020
(page 25 of report) (page 27 of
report)
Enterococci, MPN/100 mL 490 10
Fecal Coliform, CFU/100 mL 1750 175
Salinity, ppt 7 7
Dissolved Oxygen, mg/L 0.96 0.24
Nitrogen as Ammonia, mg/L 1.3 1.3
Nitrogen as Total Kjeldahl Nitrogen, 1.5 1.5
mg/L
Nitrogen as NO2 plus NO3, mg/L 0.033 U 0.033 U
Phosphorous as P total, mg/L 0.19 0.099
In addition, when evaluating data at other sites farther to the south, results show that dissolved
oxygen levels are more in line with what would be expected from waters not impacted by
wastewater (>5 mg/L). Of note errors were found in the dissolved oxygen levels in the
November 2020 report for site 38 (p. 14, quoted at 640 mg/L) and for site 80 (p. 21, quoted at
599 mg/L). It is possible that a decimal place was missed. Recommendation: Go back to
97
consultant to get dissolved oxygen levels corrected. In future measurements, include measures
of physical chemical parameters including dissolved oxygen. Dissolved oxygen can be analyzed
almost instantly in the field and can be used to track back towards a source of biochemical
oxygen demand. There is the possibility that it can be used to guide where to collect samples for
fecal indicator bacteria.
Water Quality Results
The folder called water quality results contains many files. The files include comparative fecal
indicator bacteria results between two laboratories (Pace Analytical and Florida Spectrum). The
results between the laboratories are consistent. The data in the file called "2021 Kayak Launch
Results.xlsx" shows that enterococci values tend to be higher than the fecal coliform values
(whereas in sewage the opposite is observed). The results also show that levels of fecal indicator
bacteria are chronically elevated. The folder also has several files that have results for
enterococci and fecal coliform at sites called "OT-1, OT-4 , OT-7, US-lA, US-18 , US-4A , etc .. "
showing that the fecal indicator bacteria at these sites are chronically elevated with days showing
extraordinarily high values above 24, 196 MPN/100 mL. Recommendations: The locations of
these sites (OT-1, etc .. ) need to be provided and mapped relative to the Kayak Launch. The
sources of fecal indicator bacteria to these sites need to be evaluated further. Also, the impact of
discharges from these sites should also be evaluated further.
Additional files in this folder are data analysis files. For example, "Copy of WQ Sampling
Results ... " is the data used to plot the heat maps in the "heat maps folder ". The folder contains a
file called "Kayak Launch Water Quality Evaluation" that evaluates multiple samples collected
during the same day but spread out in intervals of three hours. These results are interesting but
do not show a distinct trend except that some sites have higher levels than others.
Recommendation: Plot the data in "Copy of WQ Sampling Results ... " in time series and using
box and whisker plots. In the time series include measures of tide to see ifthere is a pattern in
time . The box and whisker plots can be used to evaluate whether the values at one location are
different than at another location .
Interestingly this folder also has results from Microbial Source Tracking and in the file called
'Source & FIB.xlsx." From this file there is also evidence , especially for the data in column AF
corresponding to September 24 , 2021 , that birds may be contributing towards the elevated fecal
indicator bacteria levels.
98
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Figure A.4: Map showing locations of sampling sites for Bay-Wide Water Quality Study. From
City of Miami Beach in folder called "Test Results" and file called "Current WQ Sampling
Locations.pdf'.
99
Main Folder
In the main folder there were two files , one called "Timeline" and another called "Water Quality
Evaluation_Project Status .... pdf'. The timeline was very helpful. Of particular attention was
the summary of the fecal indicator data collected during March 2020 (Table A .3). These results
show that the fecal indicator bacteria are highly variable. The extremely elevated levels were
observed March 6, and then 6 days later on March 12, then another 5 days later on March 17.
Tides shift over time and perhaps this periodicity may be associated with a tidal height
coinciding with a specific tide level. Recommendation: Plot bacteria data super-imposed on a
plot that illustrates tidal height. Start with a time series plot and proceed to X-Y plots .
Table A.3: Fecal indicator bacteria results from daily sampling at the Kayak Launch. Data from
"Timeline.docx" file located in the main folder.
Collection location Collection Date Parameter Results
Kaya k La unch March 6t h, 2020 Feca l Coliform MPN TNTC
Kayak Launch March 6th, 2020 Enterocoa:i MPN >24196
Kayak La unch Ma rch 7t h, 2020 Feca l Col iform MP N 2COO
Kayak Launch March 7th, 2020 Enterocoa:i MPN 146
Kayak Launch March 8th, 2020 Feca l Col iform MPN 818
Kayak Launch March 8th, 2020 Enterocoa:i MPN 355
Kayak La unch Ma rch 9th, 2020 Fe ca l Col ifo rm MP N 280
Kayak Launch March 9th, 2020 Enterococ:ci MPN 98
Kaya k Launch Ma rch 10th, 2020 Feca l Col iform MP N 32
Kayak Launch March 10th, 2020 Enterocoa:i MPN 146
Kayak Launch March 11th, 2020 Feca l Coliform MPN 53
Kayak Launch March 11th, 2020 Enterocoa:i MPN 134
Kavak La unch March 12th, 2020 Feca l Coliform MP N TNTC
Kayak Launch March 12th, 2020 Enterocoa:i MPN 1500
Kaya k Launch March 13th, 2020 Feca l Coliform MPN 320
Kayak Launch March 13th, 2020 Enterococ:ci MPN 408
Kayak La unch March 16th, 2020 Feca l Coliform MPN 120
Kayak Launch March 16th, 2020 Enterocoa:i MPN 279
Kayak La unch Ma rch 17t h, 20 20 Feca l Coliform MP N TNTC
Kayak Launch March 17th, 2020 Enterocoa:i MPN 624
Kayak La unch March 18th, 2020 Feca l Coliform MP N 204
Kayak Launch March 18th, 2020 Enterococci MPN 275
Kayak Launch March 19th, 2020 Fe ca l Coliform MPN 106
Kayak Launch March 19th, 2020 Enterocoa:i MPN 272
100
In addition to evaluating the data in the shared folders, Google Earth maps were reviewed over
time.
Visual Inspection of Google Earth Maps
Review of Google Earth maps of the Kayak Launch area shows that the launch is first seen in
May of 2017. Images since 2013 show a consistent darker colored water to the west of the
launch, north of 73 street. The clearest recent image is dated January 2021 (Figure A5).
Recommendation: Conduct a detailed sampling program collecting samples along perpendicular
transects. See Phase le and Figure 2 in the main report.
APPENDIXB
HISTORICAL DAT A
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Figure B .3: Time series plot of groundwater data from the Parkview Park and North Beach Bandshell groundwater monitoring well. Dates of heat
maps are highlighted for the months June , July and August 2020 . The horizontal straight lines corresp ond to missing data.
105
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Table B.1: Concentration of enterococci in samples collected monthly from Miami Beach from 4/17 /20 19 to 10 /17/2022 with other physical
chemical parameters record including water level, tide cycle, total nitrogen, total phosphorus, salinity , fe cal coliforms , field specific conductance,
field temperature , pH , dissolved oxygen, turbidity and cumulative precipitation (6-hour, 12-hour, 24-ho ur, 48-hour)
Total Fecal Field Specific Field Di ssolved 6-ho ur 12-hour 24-hour 48-hour Enterococci Total Salinity Coliforms Tu r bidity Tide Date Time (MPN/100 Nitrogen, Phosphorus Conductance Temp Field pH Oxygen Precipi t ati Precipitati Precipitati Precipitati Water
ml) Kjeldahl (mg/L) (ppt) (CFU/100 (umhos/cm) (OC) (mg/L) (NTU) on (i n ) on (in) on (in) on (in) Level (ft) Cycle '
(mg/L) ml)
4/17/201 11:10AM 640 0.09 0 .04 28.2 125 51835 27 .7 7 .95 5.20 7 .50 0 .00 0.00 0 .00 0 .01 -0.95 ebb
5/20/201 11 :03AM 63 0 .21 0 .04 27.4 25 57304 29 .9 8 .02 5.36 N/A 0 .00 0.00 0 .00 0.00 0 .38 ebb (high
6/27/201 10 :56AM 169 0 .34 0 .04 20.8 400 42 30.8 8 .03 6.95 1.28 0 .00 0 .00 0 .00 0 .00 -1.45 ebb (low
7/29/201 11 :51AM 1660 0 .27 0 .03 15 .8 402 39339 30.9 8.04 7.05 2.66 0 .00 0 .00 0 .00 0 .01 -1.09 ebb (low
8/13/201 11 :58AM 934 0 .09 0 .04 15 .8 92 39940 32.8 7 .99 5.21 3 .29 0 .01 0 .01 1.27 2.12 -0.49 ebb
9/25/201 11:10AM 285 0.31 0 .04 25 .2 157 48284 29.4 7 .85 4 .63 2.92 0 .00 0 .00 0.00 0 .00 -0 .7 ebb (low
10/16/20 9:26AM 359 0.33 0 .06 20 .1 430 40327 28 .0 8.10 4 .60 3.60 0 .00 0.00 0 .00 0.00 1.19 flow (high
11/19/20 11 :10AM 108 0 .18 0 .032 15.8 20 32796 23.7 7.72 7.32 3.78 0 .00 0 .00 0.00 0 .00 1.02 flow
12/23/20 10:19AM 24196 0 .23 0 .059 10 .8 600 15542 22.3 7.89 5.79 9.43 0 .0 1 6.01 6.01 6.01 -0 .55 ebb
1/15/202 11:15 AM 73 0 .290 0 .040 17 .9 270 27936 24 .9 7.84 5.10 6.24 0 .00 0 .00 0 .00 0 .03 -0.080 flow (high
2/3/2020 11:22 AM 679 0.350 0 .042 22 .6 112 44060 21.9 7.77 6.19 2.53 0.00 0.00 0.00 0 .37 -0 .960 flow
3/17/202 10:36AM 331 0 .330 0 .055 36 260 54600 25 .0 8.11 4 .87 16.40 0 .00 0 .00 0 .00 0 .00 -1.490 ebb (low
4/14/202 10 :06AM 142 0 .290 0.044 36.3 92 54081 28 .0 8.06 6.67 6.44 0 .00 0 .00 0 .00 0 .00 -1.720 flow (low
5/26/202 10:23 AM 13000 0 .370 0 .040 14.4 so 2 1901 26 .1 7.78 5.85 4 .36 0 .03 0 .18 3.88 6 .30 0.320 flow (high
6/23/202 10 :38AM 20 0.290 0 .027 27.2 so 39714 30 .2 8.25 6.63 1.92 0.00 0 .00 0.01 0.04 0 .380 flow (high
7/29/202 10:40 AM 283 0 .270 0 .034 28 340 43117 31.2 8.30 5 .26 4 .66 0 .00 0 .00 0 .00 0 .00 -1.850 ebb (low
8/14/202 11 :15 AM 437 0 .254 0.056 29.3 570 47804 31.9 7 .95 3.88 4 .46 0 .00 0 .01 0 .02 0 .04 -1.270 ebb (low
9/22/202 10:55 AM 1010 0 .390 0 .034 30.2 1320 45718 29 .9 7.98 4.23 8.14 0.00 0.00 0 .78 1.07 1.030 flow
10/13/20 10 :47 AM 19900 0 .280 0 .028 23.7 600 38537 29 .5 7 .88 4 .30 1 .33 0 .00 0 .00 0.40 0 .44 -0 .650 ebb
11/18/20 10 :37 AM 1560 0 .290 0 .033 26 142 38528 26 .3 8.02 5 .74 2 .80 0 .00 0 .00 0 .00 0 .00 1.250 flow (high
12/21/20 11 :15AM 959 0.310 0 .055 31.8 96 44107 23 .1 8 .15 5.69 1.60 0.0 0 0 .00 0 .00 0 .00 -0 .220 flow
1/28/202 10 :48AM 1090 0.370 0 .041 32.9 110 49340 23.6 7 .87 5.97 2 .07 0 .00 0 .00 0.00 0.00 -0.460 Ebb
3/29/202 11:05AM 161 0 .360 0 .031 36.8 145 51203 27.4 8 .21 4 .30 9 .58 0 .00 0.00 0 .00 0 .00 0.510 Ebb (high
4/30/202 11:02AM 173 0 .310 0 .023 36.2 20 50654 28.1 8 .29 5.72 3 .18 0 .00 0.00 0 .00 0 .00 0.080 flow (high
5/25/202 10:55AM 323 0 .170 0 .029 36.3 114 55252 N/A 8 .15 6.81 6 .38 0 .00 0 .00 0 .00 0 .00 -0 .590 ebb
6/16/202 10:41AM 6590 N/A N/A 28.5 600 40968 28 .0 7.97 3.45 3.80 0 .00 0.07 1.27 1.54 -0.840 flow
7/14/202 11:00AM 487 0.320 0 .030 28 .8 300 40390 26 .3 7 .97 3.71 6.00 0 .00 0 .06 0 .73 5.46 -0 .380 flow (high
8/16/202 10 :47AM 1510 N/A N/A 26 .3 2100 45122 29 .6 8.02 4.48 5.49 0 .00 0.00 0 .04 0.41 -1.570 flow(low
9/22/202 11 :50AM 17300 0.270 0 .022 26.2 N/A 43811 30.2 7 .93 5.55 8 .56 0 .9 1 0 .91 1.14 1.14 0.750 Ebb (high
10/28/20 10:29AM 521 0 .340 0 .007 29 .6 670 44383 27 .9 7.81 3.80 2.09 0 .00 0 .00 0 .00 0 .00 -0 .670 flow(low
11/15/20 10:45AM 2140 0.460 0.011 29.4 770 45049 24.2 7.05 7 .10 4 .11 0.00 0 .00 0.00 0 .00 -0.670 ebb (low
12/22/20 10:26AM 1660 0 .300 0 .011 33 .1 440 48650 21.4 7.72 5 .01 7 .80 0.00 0 .00 0 .09 0 .13 0 .750 flow (high
1 Verified water levels and tide cycle, from NOAA Virginia Key station, at the same date and time the enterococci samples were col lected .
Table B. l (Continued): Concentration of enterococci in samples collected monthly from Miami Beach from 4/17/2019 to 10/17/2022 with other
physical chemical parameters record including water level, tide cycle, total nitrogen, total phosphorus, salinity, fecal coliforms, field specific
conductance, field temperature, pH , dissolved oxygen , turbidity and cumulative precipitation (6-hour, I 2-hour, 24-hour, 48-hour)
107
Enterococc1 Total Total Fecal Field Specific Field Dissolved 6-hour 12-hour 24-hour 48 -hour Water Nitrogen, Salinity Coliforms Field Turbidity Tide Date Time (MPN/100 Kjeldahl Pho s phorus (ppt) (CFU/100 Conducta nce Temperat u re pH Oxygen (NTU) Precipitation Precipitat ion Precipita tion Precipit ation Level Cycle ' ml) (mg/L) (mg/L) ml) (u m ho s/cm) (OC) (mg/L) (in) (i n ) (in) (in) (ft)
1/18/2022 11 :30AM 211 N/A 0 .010 32 .4 58 48410 20 .6 8 .06 6.33 2.07 0 .00 0.00 0 .00 0 .24 -0 .2 70 e bb
flow
2/25/2022 10:2 8AM 1310 0 .250 0 .010 34 38 51157 25.5 7.92 3 .25 4.49 0 .00 0 .00 0 .00 0 .00 -1.410 (low
tid e )
3/28/2022 10:48AM 187 N/A N/A 35 .4 92 29107 23.5 7 .8 7 5 .54 2.24 0 .00 0 .00 0 .00 0 .00 -1 .010 e bb
ebb
4/25/2022 10:17AM 504 N/A 0 .009 38 .1 114 53469 26.5 8 .14 6 .54 5 .76 0 .00 0 .00 0 .00 0 .00 -1 .170 (low
tide)
flow
5/19/2022 10 :37AM 173 0 .300 0 .007 37.2 147 55355 29 .4 8 .14 4.5 9 5.37 0 .00 0 .00 0 .00 0 .00 0.400 (high
ti de )
e bb
6/14/2022 10:38AM 399 0.280 0 .008 25 430 35575 30.8 8.05 2.71 0 .21 0 .01 0 .01 0 .01 0 .0 1 0 .230 (low
tide)
7/18/2022 10:53AM 30 0 .370 0.013 34.6 20 46892 29.2 10.48 3 .13 8.25 0 .00 0 .00 0 .00 0.10 -0 .400 flow
8/11/2022 10:54AM 4 1 0.410 0.011 35 .5 62 4 8079 27 .9 7 .2 6 5 .38 19.80 0 .00 0 .00 0 .00 0.00 -0 .260 ebb
09/15/2022 11 :09 909 0.410 0 .018 31 .1 28 48077 26 .7 7.59 5 .78 6 .17 0 .00 0 .00 1.67 2.03 0 .580 high
10/17/2022 10 :48 184 47485 28.5 8 .17 7.43 4 .19 0 .00 0 .00 0 .01 0.14 -0 .040 low
AM 278 0.420 0 .011 29 .9 ti de
1 Verified water levels and tide cycle, from NOAA Virg inia Key station, at the same date and time the ent erococci samples were collected .
108
Table B.2: Enterococci, height oftide, and cumulative rainfall of each sampling location based on time series.
Date Time Enterococci Tide (ft) lh Rainfall 6h Rainfall 12h Rainfall 24h Rainfall 48h Rainfall
MPN/l00mL) (in) (in) (in) (in) (in)
OTl
19-Apr 9 :38 1,010 -0.37 0.00 0.00 0.00 0.00 0.00
19-Apr 12:31 627 -0.97 0.00 0 .00 0 .00 0.00 0 .00
19-Apr 15:30 292 -0.61 0.00 0.00 0.00 0 .00 0 .00
20-Apr 7:43 24,196 0.09 0.01 0.60 1.63 1.65 1.65
20-Apr 10:43 8,160 -0.58 0.00 0.02 1.63 1.65 1.65
20-Apr 13:31 14,100 -0.94 0.00 0.00 0 .60 1.65 1.65
20 -Apr 16:31 3,260 -0 .29 0.00 0.00 0 .02 1.65 1.65
21-Apr 8:50 8,660 0.34 0 .00 0.30 0 .30 0 .30 1.95
21-Apr 11:49 24,196 -0.45 0 .00 0.04 0 .30 0 .30 1.95
21-Apr 14:42 15 ,500 -1.09 0 .00 0 .00 0 .30 0.30 1.95
21-Apr 17:46 3,880 -0 .39 0 .00 0.00 0.05 0.30 1.95
OT4
19-Apr 9:32 471 -0.35 0 .00 0.00 0.00 0 .00 0 .00
19-Aor 12 :26 988 -0.96 0.00 0.00 0.00 0 .00 0 .00
19-Apr 15 :25 1,400 -0.63 0 .00 0.00 0.00 0.00 0.00
20-Apr 7:38 24,200 0 .10 0 .00 0.59 1.63 1.65 1.65
20-Apr 10:36 12,000 -0 .55 0 .00 0.02 1.63 1.65 1.65
20-Apr 13 :2 6 17,300 -0.9 5 0 .00 0 .00 0.60 1.65 1.65
20-Apr 16 :25 I 1,200 -0.31 0.00 0.00 0.03 1.65 1.65
21-Apr 8 :45 24,196 0 .35 0 .00 0.30 0.30 0 .30 1.95
21-Apr 11 :44 24,196 -0.42 0 .00 0.06 0.30 0.30 1.95
21-Apr 14 :37 11 ,200 -1.09 0 .00 0.00 0.30 0.30 1.95
21-Apr 17 :41 12,000 -0.41 0 .00 0.00 0 .07 0 .30 1.95
OT7
19-Apr 12 :4 9 31 -1 .00 0 .00 0 .00 0 .00 0 .00 0.00
19-Apr 13:55 262 -0 .99 0 .00 0 .00 0 .00 0 .00 0.00
19-Apr 15:43 624 -0 .54 0.00 0.00 0.00 0.00 0.00
20-Apr 7 :59 15,500 0 .08 0 .00 0.56 1.63 1.65 1.65
20-Apr 11:03 5,480 -0.67 0 .00 0.01 1.62 1.65 1.65
20-Apr 13:47 24 ,200 -0 .94 0 .00 0 .00 0.58 1.65 1.65
20-Apr 16:45 2,100 -0.22 0 .00 0 .00 0 .02 1.65 1.65
21-Apr 9 :06 24,196 0.34 0 .00 0 .30 0 .30 0.30 1.95
21-Apr 12:03 15 ,500 -0 .53 0 .00 0 .00 0 .30 0 .30 1.95
21-Apr 14:57 24,196 -1.09 0.00 0 .00 0.30 0 .30 1.95
21-Apr 17:35 24,200 -0.44 0 .00 0 .00 0.09 0.30 1.95
USIA
19-Apr 9:50 41 -0.43 0.00 0.00 0.00 0.00 0 .00
19-Apr 12:41 84 -0.98 0.00 0.00 0.00 0.00 0 .00
19-Apr 15:37 63 -0.57 0.00 0.00 0.00 0.00 0.00
20-Apr 7 :52 24,200 0 .09 0.00 0.57 1.63 1.65 1.65
20-Apr 10 :54 24,196 -0 .63 0.00 0 .01 1.63 1.65 1.65
20-Apr 13 :42 24 ,196 -0.94 0 .00 0.00 0.58 1.65 1.65
20 -Apr 16 :39 24,196 -0.25 0.00 0 .00 0.02 1.65 1.65
21-Apr 8:59 24,196 0.34 0 .00 0.30 0.30 0 .30 1.95
21 -Apr I 1:57 24,196 -0.49 0.00 0.01 0.30 0.30 1.95
21-Apr 14 :51 24,196 -1.09 0.00 0.00 0.30 0.30 1.95
21-Apr 17 :53 24,196 -0 .35 0.00 0.00 0.03 0.30 1.95
109
Table B.2 (Continued): Enterococci, height of tide, and cumulative rainfall of each sampling location based on
time series.
Date Time Enterococci Tide (ft) lh Rainfall 6h Rainfall 12h Rainfall 24h Rainfall 48h Rainfall
l(MPN/l00mL) (in) (in) (in) (in) (in)
USlB
19-Apr 9:44 85 -0.40 0.00 0.00 0.00 0 .00 0.00
19-Apr 12:37 292 -0.98 0.00 0.00 0.00 0.00 0.00
19-Apr 15:34 2,060 -0.59 0.00 0.00 0.00 0.00 0.00
20-Apr 7 :48 19,900 0.09 0.00 0.58 1.63 1.65 1.65
20-Apr 10:49 24,196 -0.61 0.00 0.01 1.63 1.65 1.65
20-Apr 13:38 13,000 -0.94 0 .00 0.00 0.59 1.65 1.65
20-Apr 16:35 24,196 -0.27 0.00 0.00 0.02 1.65 1.65
21-Apr 8:55 24,196 0.34 0 .00 0.30 0.30 0.30 1.95
21-Apr 11 :53 24,196 -0.47 0.00 0.03 0.30 0.30 1.95
21-Apr 14:47 24,196 -1 .09 0.00 0 .00 0.30 0.30 1.95
21-Apr 17:50 24,196 -0.37 0.00 0 .00 0.04 0 .30 1.95
US4A
19-Apr 9:30 465 -0.34 0.00 0 .00 0.00 0.00 0.00
19-Apr 12:40 199 -0.98 0.00 0.00 0 .00 0.00 0.00
19-Apr 15:40 583 -0.56 0 .00 0.00 0.00 0.00 0.00
20-Apr 7:56 17,300 0.08 0.00 0 .57 1.63 1.65 1.65
20-Apr 10:53 5,500 -0.63 0.00 0.01 1.63 1.65 1.65
20-Apr 13:43 24,196 -0.94 0.00 0.00 0.58 1.65 1.65
20-Apr 16:44 5,170 -0.23 0 .00 0.00 0.02 1.65 1.65
21 -Apr 9:03 24,196 0 .34 0.00 0.30 0.30 0.30 1.95
21-Apr 12:04 12,000 -0 .53 0.00 0 .00 0.30 0.30 1.95
21 -Apr 14:54 10,500 -1.09 0.00 0.00 0.30 0.30 1.95
21-Aor 17:50 24,196 -0.37 0 .00 0 .00 0.04 0.30 1.95
US4B
19-Apr 9:38 41 -0.37 0.00 0.00 0.00 0.00 0.00
19-Apr 12:36 74 -0 .97 0.00 0.00 0.00 0.00 0.00
19-Apr 15:34 643 -0.59 0.00 0 .00 0.00 0.00 0.00
20-Apr 7:49 24,196 0.09 0.00 0.57 1.63 1.65 1.65
20-Apr 10:47 24,196 -0.60 0.00 0.01 1.63 1.65 1.65
20-Apr 13:36 10,500 -0 .94 0 .00 0.00 0.59 1.65 1.65
20-Apr 16:36 24,196 -0.26 0.00 0.00 0.02 1.65 1.65
21-Apr 8:55 24,196 0.34 0.00 0.30 0.30 0.30 1.95
21-Aor 11 :55 24,196 -0.48 0.00 0.02 0.30 0 .30 1.95
21 -Apr 14:47 24,196 -1 .09 0.00 0.00 0.30 0.30 1.95
21-Apr 17:44 24,196 -0.40 0.00 0 .00 0 .06 0.30 1.95
US4C
19-Apr 9:35 141 -0.36 0.00 0.00 0.00 0.00 0.00
19-Apr 12:33 1,040 -0.97 0.00 0.00 0.00 0.00 0.00
19-Apr 15:37 1,000 -0 .57 0.00 0.00 0.00 0.00 0.00
20-Apr 7 :53 24,196 0.08 0.00 0.57 1.63 1.65 1.65
20-Apr 10:50 24,196 -0 .61 0.00 0.01 1.63 1.65 1.65
20-Apr 13:39 24,196 -0 .94 0.00 0.00 0.59 1.65 1.65
20-Apr 16 :40 24,200 -0.25 0.00 0.00 0.02 1.65 1.65
21-Apr 8:59 24,196 0.34 0.00 0.30 0.30 0.30 1.95
21-Apr 12:00 24,196 -0.51 0.00 0.00 0.30 0.30 1.95
21-Apr 14:50 24,200 -1.09 0.00 0.00 0.30 0.30 1.95
21-Apr 17:47 17,300 -0.38 0 .00 0.00 0.05 0.30 1.95
110
APPENDIXC
SAMPLE COLLECTION TIMELINE AND DATA TABLES
11 1
APPENDIXC
SAMPLE COLLECTION TIMELINE AND DAT A TABLES
Table C I Sample Collection Timeline
Date Location Activities
6/11 /2022 • Parkview Island Park and Scouting visit
adjoining streets
• Kayak Launch Pad
7/24/2022 • Kayak Launch Pad
• Park View Canal banks,
shoreline and surroundings
8/09/2022 • Normandy Shores waterway
(N -S), Park View Canal
north , east and south
• Kayak Launch Pad
• Park View Canal banks,
shoreline sediments and
surroundings
8/17/2022 • Kayak Launch Pad
• Park View Canal banks,
shoreline sediments and
surroundings
• 74th and 75 th streets between
Dickens and A 1 A
Scouting visit,
• Water level elevation measurements at
Kayak Launch Pad
Spatially Intense Sampling:
• high tide sampling by boat
• Measurement of a suite of environmental
parameters with YSI probe
• Water level elevation measurements at
Kayak Launch pad
• Shoreline sediment sampling
Stormwater catch basin sampling:
• Marine water in vicinity of storm water
discharge
• Shoreline sediments in vicinity of
stormwater discharge pipe
• Top sediments adjacent to inlet,
• Basin water, basin bottom sediments
9/2 /2022 Sites in study area: Stormwater catch basin sampling:
• 74th and 75 th streets between • Top sediments adjacent to inlet,
Dickens and A 1 A • Basin water
Background sites:
• Gary Ave & Raymond Street
on Parkview Island
• 77th street between Byron
and Abbott
• 71 rst street and Byron Ave
Sites in the vicinity of
wastewater sewer
infrastructure:
• Miami Beach Parking lot
located between 72nd and
73rd street
• 72nd street and 73rds street
between Dickens and A 1 A
112
Table C. 1 ( continued) : Sample Collection Time line
Date Location Activities
9/16/2022 • Normandy Shores Spatially Intense Sampling:
waterway (N-S), Park View • Low tide sampling by boat
Canal north, east and south • Measurement of a suite of
• Kayak Launch Pad environmental parameters with
• Park View Canal banks, YSI probe
shoreline sediments and
surroundings
10/18/2022 to • Kayak Launch Pad Temporally Intense Sampling:
10/20/2022 -• Hourly sampling of top 10 cm of
Site visits water column adjacent to Kayak
approximately Launch Pad
every 12 hours • Measurement of a suite of
starting at 5: 00 environmental parameters with
amon YSI probe
10/18/2022 and
ending at 7:00
amon
10/20/2022.
10/19/2022 and • Kayak Launch Pad Vertical Measurements of Water
10/20/2022 Column:
• Samples collected at 0.5 inch then
in I-foot intervals
• Measurement of environmental
parameters with YSI probe
11/14/22 • Parkview Park Groundwater sampling
• North Beach Bandshell Vertical well sampling
Catch basin water sampling
113
Table C.2: Environmental parameters, physicochemical parameters, and measured enterococci concentrations for high tide
sampling on August 9, 2022 .
Sample Sample Sample Latitude Longitude Depth (Feet Temp DO Salinity pH Turbidity Enterococci
ID Date Time (N) (W) decimals) (OC) (mg/L) (not) (NTU) MPN/100 mL
Al 8/9/2022 6:49AM 25.8563184 -80.1271770 10.42 31.1 6.19 32.17 7.89 2.3 63
Bl 8/9/2022 6:55 25.8569200 -80 .1276828 12.00 31.2 6.24 32.18 8.04 2.17 85
Cl 8/9/2022 6:59 25.8575344 -80.1281636 14.58 30.9 5.77 31.84 8.09 1.28 228
DI 8/9/2 022 7:03 25.8579687 -80 .1285361 14.17 30.9 5.93 31.88 8.07 0 .83 96
El 8/9/2022 7:09 25.8587981 -80.1289130 14.67 31.1 6.05 31.94 8.14 1.5 439
Fl 8/9/2 022 7:13 25.8598674 -80.1294867 16.00 30.9 6.00 31.86 8.13 1.02 295
GI 8/9/2022 7:18 25.8601156 -80.1286710 12.00 30.8 6.19 32 .20 8.13 0.35 122
Hl 8/9/2 022 7:21 25 .8605303 -80.1281583 13.08 30.9 5.81 32.47 8.11 0.95 327
11 8/9/2022 7:27 25.8609629 -80.1281091 9.67 30 .9 5.74 32.46 8.13 0.79 457
JI 8/9/2022 7:33 25.8604635 -80.1276108 9.92 31.0 5 .2 8 32.45 8.06 1.31 842
J2 8/9/2022 7:50 25.8604312 -80.1276242 10 .25 31.0 5.30 32.46 8 .07 1.29 637
J3 8/9/2 022 7 :53 25.8603817 -80.1276383 4.25 31.1 5.36 32.46 8.09 1.52 689
14 8/9/2 022 7:56 25.8603509 -80 .1276421 4.17 31.0 5.34 32.45 8.08 1.41 767
Kl 8/9/2 022 8:01 25.8605233 -80 .1269827 5.50 31.0 5.31 32.36 8.09 1.11 677
K2 8/9/2022 8:07 25.8604686 -80.1269847 8.00 31.1 5.53 32.57 8.10 1.76 556
K3 8/9/2 022 8:10 25.860391 -80.1270200 5.75 31.1 5.56 32.43 8 .10 1.55 609
K4 8/9/2022 8:13 25.86039 -80.1269700 4.50 31.1 5.52 32.43 8 .10 1.85 644
LI 8/9/2022 8:15 25.8605288 -80.1264439 3.33 31.0 5 .53 32.33 8.11 2.14 884
L2 8/9/2022 8:18 45.8604786 -80.1265244 4 .25 31.1 5.55 32.38 8.11 2.72 784
L3 8/9/2022 8:24 25.8604151 -80.1265903 7.42 31.1 5.60 32.47 8.11 1.77 473
L4 8/9/2022 8:30 25 .8603724 -80.1266 291 5.50 31.1 5.64 32.40 8 .12 1.85 548
Ml 8/9/2022 8:34 25.8594608 -80.1265879 6 .75 31.1 5 .34 32.36 8 .09 1.32 663
M2 8/9/2022 8:37 25.8594626 -80 .1266158 6.83 31.1 5.38 32.36 8.09 1.35 676
M3 8/9/2022 8:42 25.8594753 -80.1266803 6.50 31.1 5.43 32.38 8.10 1.84 933
M4 8/9/2 022 8:44 25.8594712 -80 .1267133 4.42 31.1 5.49 32.39 8.10 1.69 373
Nl 8/9/2022 8:51 25.858924 -80.1261444 7 .75 31.2 5.41 32.39 8.11 1.65 4,611
N2 8/9/2 022 8:53 25.8588905 -80.1261676 7.25 31.1 5.51 32.41 8.11 1.91 1,191
N3 8/9/2022 8:55 25.8588145 -80 .1262487 5.33 3 1.2 5.73 32.42 8.13 2.3 7 203
N4 8/9/2 022 8:57 25.8587618 -80 .1262598 2.58 31.3 5.72 32.47 8.12 2.22 231
114
Table C.2 ( continued): Environmental parameters , physicochemical parameters, and measured enterococci concentrations
for high tide sampling on August 9, 2022 .
Sample Sample Sample Latitude Longitude Depth (Feet Temp DO Salinity pH Turbidity Enterococci
ID Date Time (N) (W) decimals) (OC) (mg/L) foot) (NTU) MPN/100 mL
01 8/9/2022 9:06 25 .8583645 -80.1258331 3.67 31.1 5 .39 32 .41 8.10 1.81 1,785
02 8/9/2022 9:10 25.8583454 -80 .1258505 3.75 31.3 5.50 32.45 8.09 2.99 279
03 8/9/2022 9:14 25 .8583039 -80.1258763 3.58 31.4 5 .51 32.59 8.10 4 .63 496
04 8/9/2022 9:17 25 .8582934 -80.1259095 2.58 31.3 5 .56 32 .55 8.11 2 .75 388
Pl 8/9/2022 9:21 25 .8581557 -80.1258348 18.00 31.2 5 .32 32 .52 8.08 4.45 624
P2 8/9/2022 9:26 25.8581554 -80.1258574 4.75 31.3 5 .37 32.56 8.09 4.01 727
P3 8/9/2022 9:29 25.8581543 -80.1259121 4 .25 31.2 5.35 32.36 8. 10 2.19 2064
P4 8/9/2022 9:32 25 .8581567 -80.1259337 4.50 31.3 5.44 32.56 8.10 4.36 609
QI 8/9/2022 9:42 25 .8576120 -80 .1254248 8.33 31.2 5 .62 32.41 8.11 2.17 173
02 8/9/2022 9:43 25 .8576171 -80.1254713 11.17 31.2 5 .62 32.43 8.11 3.2 142
Q3 8/9/2022 9:50 25 .8576374 -80.1255726 6.83 31.4 5.57 32.53 8.11 4.71 185
04 8/9/2022 9 :53 25 .8576142 -80 .1256349 3.00 31.4 5 .74 32.5 8.12 4 .31 146
RI 8/9/2022 9:58 25.8569812 -80 .1253133 1.25 31.2 5.83 32.31 8.13 1.4 617
R2 8/9/2022 10:00 25.8570254 -80.125364 4.33 31.2 5.56 32.36 8.11 2.26 173
R3 8/9/2022 10:03 25.8570933 -80 .1254534 7.42 31.3 5.76 32.43 8.12 3 .26 201
R4 8/9/2022 10:05 25 .8571271 -80.1254725 3 .58 31.4 5.84 32.4 8.13 3 .27 63
SI 8/9/2022 10:09 25 .8568891 -80.1262559 3.75 31.3 5.9 32.34 8.13 1.66 63
S2 8/9/2022 10:13 25.8570321 -80.1263211 8.00 31.3 5.87 32.39 8.13 2.28 148
S3 8/9/2022 10 :16 25.8569639 -80 .1262934 8.08 31.3 5.97 32.34 8.14 1.38 73
S4 8/9/2022 10 :19 25.8570690 -80.1263333 4 .25 31.3 5.98 32.36 8.13 1.4 52
Tl 8/9/2022 10:23 AM 25 .8569656 -80.1271906 10 .33 31.3 5.98 32.33 8.14 1.47 52
115
Table C.3: Environmental parameters , physicochemical parameters, and measured enterococci concentrations for low tide
sampling on September 16, 2022.
Sample Sample Date Sample Latitude Longitude (W) Temp DO Salinity pH Turbidity Enterococci
ID Time (N) (OC) (mg/L) (ppt) (NTU) MPN/100 mL
Al 9/16/2022 7:36 AM 25 .8563184 -80.1271770 28.9 4.53 26.76 7 .82 0.15 >24,196
Bl 9/16/2022 7:43 AM 25.8569200 -80.1276828 29.7 5.56 28.73 8 .01 -0 .24 >24,196
Cl 9/16/2022 7:52 AM 25.8575344 -80.1281636 30.0 5.38 28.97 8.1 -0 .09 >24,196
DI 9/16 /2022 7:53 AM 25.8579687 -80 .1285361 30.1 5 .27 28.82 8.1 -0.14 >24,196
El 9/16/2022 7:56 AM 25.8587981 -80.1289130 30.3 5.18 29.15 8.08 0 .05 >24,196
Fl 9/16/2022 8:00 AM 25.8598674 -80 .1294867 30.3 5.16 28.87 8.08 0.80 >24,196
GI 9/16/2022 8:04AM 25.8601156 -80.1286710 30.9 4.9 30.13 8.05 0.70 >24,196
HI 9/16/2022 8:06 AM 25.8605303 -80.1281583 30.5 4.77 29.32 8 .05 0.40 >24,196
11 9 /16 /2022 8:09AM 25.8609629 -80.1281091 30.4 5.46 28.99 8.07 0.10 >24,196
JI 9/16/2022 8 :13 AM 25.8604635 -80.1276108 30.9 4.75 29 .91 7.99 1.48 >24,196
J2 9/16/2022 8:15 AM 25.8604312 -80 .1276242 30.5 4.85 28 .98 8.06 1.00 >24,196
13 9 /16 /2022 8:17 AM 25.8603817 -80.1276383 30.6 4.74 28.05 8.00 0 .92 12,997
14 9/16/2022 8:19 AM 25.8603509 -80.1276421 30 .7 4.79 28.61 8.04 14.05 >24,196
Kl 9 /16/2022 8:24AM 25.8605233 -80 .1269827 30.3 4.41 28.56 7.97 0.07 >24,196
K2 9/16/2022 8:26 AM 25.8604686 -80.1269847 30.5 4.68 28.81 8 .03 -0.16 >24,196
K3 9 /16/2022 8:30 AM 25 .8603910 -80 .1270200 30.4 5 .21 29 .1 8 .06 0 .46 >24,196
K4 9/16/2022 8:31 AM 25.860390 -80.1269700 30.5 5.13 28 .87 8.09 1.56 >24,196
LI 9/16/2022 8:37 AM 25 .8605288 -80.1264439 30.4 3 .17 29 .24 7 .63 4.72 >24,196
L2 9 /16 /2022 8:40 AM 25 .8604786 -80.1265244 30.4 3.58 28 .78 7 .86 2.39 >24,196
L3 9/16/2022 8:42AM 25.8604151 -80.1265903 30.3 5.08 28.4 8.03 0 .28 >24,196
L4 9 /16 /2022 8:44AM 25.8603724 -80.1266291 30.1 4.69 28.35 8.01 3.15 >24,196
Ml 9/16/2022 8:48 AM 25 .8594608 -80.1265879 30.5 4.31 29.25 7.99 1.01 15,531
M2 9 /16 /2022 8:50 AM 25.8594626 -80.1266158 30.2 4.92 28.73 8.07 -0 .11 >24,196
M3 9/16/2022 8:53 AM 25.8594753 -80.1266803 30.1 4.89 27.81 8.06 0 .25 24,196
M4 9/16/2022 8:55 AM 25.8594601 -80.1267784 30.2 4.73 28.43 8.03 0.95 24,196
NI 9/16/2022 8 :58 AM 25 .8589240 -80.1261444 30.7 3.44 28.81 7.91 0.28 >24,196
N2 9 /16 /2022 9:03 AM 25.8588905 -80.1261676 31.1 3.64 29.5 7 .94 1.32 15,531
N3 9 /16/2022 9:05 AM 25 .8588145 -80 .1262487 30.7 4.55 29.53 8.02 2.97 9,804
N4 9/16/2022 9 :07 AM 25.8587536 -80.1262658 30.8 4.65 29.08 8.03 8.66 >24,196
01 9 /16 /2022 9 :12 AM 25.8583645 -80.1258331 30.6 4.38 28.8 8.01 2.75 >24,196
02 9/16/2022 9:15 AM 25.8583454 -80 .1258505 30.5 4.31 28 .05 7 .99 1.92 24,196
03 9/16/2022 9 :17 AM 25.8583003 -8 0.1288860 30.8 4.03 27.98 7.96 40.52 14,136
04 9 /16 /2022 9:19 AM 25.8582934 -80.1259095 30.5 4.25 27.51 7 .99 5.07 17 ,329
Pl 9/16/2022 9:23 AM 25.8581557 -80.1258348 30.5 3.95 27.24 7.96 23.54 19,863
P2 9 /16/2022 9:27 AM 25.8581554 -80.1258574 30.6 4.23 28 .88 7 .9 7 9.42 24,196
P3 9/16 /2022 9:29 AM 25.8581543 -80 .1259121 30.6 4.37 28.43 7.99 5.06 17,329
P4 9 /16 /2022 9:31 AM 25.8581567 -80 .1259337 30.6 4.31 28.2 7 .98 4.41 24196
116
Table C.3 (continued): Environmental parameters, physicochemical parameters, and measured enterococci concentrations
for low tide sampling on September 16, 2022.
Sample Sample Date Sample Latitude Longitude (W) Temp DO Salinity pH Turbidity Enterococci
ID Time (N) (DC) (mg/L) (not) (NTU) MPN/100 mL
QI 9/16/2022 9:34AM 25 .8576120 -80.1254248 30.5 4 .15 28.22 7.97 1.69 15 ,531
Q2 9/16/2022 9:35 A M 25 .8576171 -80.1254713 30.6 4 .28 28 .71 7 .99 3.55 24,196
Q3 9/16/2022 9:38 AM 25 .8576374 -80 .1255726 30.7 4.14 28.09 7.98 2.37 24,196
Q4 9/16/2022 9:40 AM 25 .8576142 -80.1256349 31.0 4 .39 28.53 8.00 2.85 >24,196
RI 9/16/2022 9:44 AM 25.8569812 -80 .1253133 30.8 3 .70 28.79 7 .94 4.26 19 ,836
R2 9/16/2022 9:46 AM 25 .8570254 -80.1253640 30.3 4 .08 28.03 7.97 1.94 17,329
R3 9/16/2022 9:48 AM 25 .8570933 -80.1254534 30.8 4 .15 28.4 7 .98 2.18 24,196
R4 9/16/2022 9:50 AM 25 .8571271 -80.1254725 30.7 4 .05 28.32 7 .99 0.45 19,836
SI 9/16/2022 9:53 AM 25 .8568891 -80.1262559 30.8 3.54 28.49 7 .93 1.09 11 ,199
S2 9/16/2022 9:55 AM 25.8570321 -80 .1263211 30.7 3.81 28.71 7 .95 1.18 12 ,997
S3 9/16/2022 9:57 AM 25 .8569639 -80 .1262934 31.3 3 .72 30.28 7 .97 1.4 19,836
S4 9/16/2022 9:59AM 25.8570690 -80.1263333 31.1 3.66 29.32 7.96 1.41 12,033
Tl 9/16/2022 10:02 AM 25 .8569656 -80.1271906 30.6 4.32 28 .9 8.06 0 .25 12,033
117
Table C.4: Measured enterococci concentrations in waterway sediments, catch basin top sediments, catch basin
bottom sediments, catch basin water, and roof drain sediments. Sampling locations are shown in Figure V.8.
Location 8/9 Top 8/19 Top 8/19 Bottom 9 /2 Top Sediments 8/19 Catch 9/2 Catch Basin Water Sediments Sediments Sediments Basin Water
SDI >69,355.7 NM NA NM NA NA
SD2 2,158.3 NM NA NM NA NA
SD3 174.5 NM NA NM NA NA
SI NM 10,704 NA NM NA NA
S2 NM 359,886 NA NM NA NA
S3 NM 2,212 NA NM NA NA
I NM 38 798,013 NM 12,873 2,718
2 NM 6,709 18,751 NM 13,053 13,393
3 NM 3,526 NA NM 17 ,968 18,868
4 NM 526,092 NA 654,063 > 241,960 14,923
5 NM 87,023 12,042 NM 1,327 12,248
6 NM 15,743 5,787 NM 512 > 241,960
7 NM NM NM NM NM 173
8 NM NM NM NM NM 19,648
9 NM NM NM NM NM 463
10 NM NM NM 37,135 NM 13,753
12 NM NM NM NM NM 16,768
13 NM NM NM NM NM 11 ,730
14 NM NM NM NM NM 14,978
15 NM NM NM NM NM 6,240
16 NM NM NM NM NM 12,528
4R NM NM NM 32,467 NM NA
NM -not measured. NA -Not applicable.
118
Table C.5: Enterococci concentration in samples collected from PVC on Oct. 19 and 20, 2022 versus water depth coupled with
measurements of physical chemical parameters including temperature, dissolved oxygen, salinity, pH, and turbidity .
Depth Temperature (0 C) Dissolved Oxygen Salinity (ppt) pH Turbidity (FNU) Enterococci (MPN) (mJ /L)
feet I 0/19 /22 10 /20 /22 I 0/19 /22 10 /20 /22 10/19/22 I 0/20 /22 10 /19 /22 10 /20 /22 10/19/22 10 /20 /22 10/19/22 10 /20 /22
0.04 NA NA NA NA NA NA NA NA NA NA 19 ,863 > 24,196
0.50 25.10 23 .80 4.22 4.60 16.82 19 .28 7.43 7.42 1.29 -0.07 NA NA
0.67 25.70 23.90 4.03 4.18 20.66 21.19 7.44 7.44 -0.33 -0 .06 NA NA
0.83 25.90 24 .30 3.95 3.81 22 .52 22.45 7.48 7.45 -0.16 -0 .25 NA NA
1.00 26.00 25.20 4.21 3 .31 22.90 23 .37 7 .52 7.44 -0 .08 -0.40 > 24,196 7,915
1.17 26.20 25.50 4.22 3.30 23.55 24.70 7 .55 7.46 -0 .06 -0 .37 NA NA
1.33 26.30 26.80 4.30 3.39 24.53 25.83 7.58 7 .52 -0 .15 -0 .30 NA NA
1.42 26.50 27 .00 4.35 3 .71 24.94 26.42 7.61 7.58 0.04 -0.20 NA NA
1.67 26.70 26.80 4 .36 3.59 25 .23 26.26 7.63 7.59 0.26 -0.31 NA NA
1.92 27.10 26.90 4.33 3.79 25.52 26.42 7.65 7 .61 0.60 -0.30 NA NA
2.00 NA NA NA NA NA NA NA NA NA NA 15 ,531 4,198
2.17 27.30 26.80 4 .28 3 .73 26.09 26.47 7.66 7.62 1.13 -0.38 NA NA
2.42 27.50 26 .90 4.14 3.90 26.40 26 .54 7 .66 7 .64 1.07 -0.17 NA NA
2.92 27.50 27.10 4.20 3.75 26.53 26.75 7 .67 7 .63 0.86 0.39 NA NA
3.00 NA NA NA NA NA NA NA NA NA NA 6,910 4,360
3.42 27.40 27.20 4.28 3 .50 26 .56 26.89 7 .68 7.63 0.85 0.35 NA NA
3.92 27.50 27.20 4.28 3.49 26 .62 26 .96 7.69 7.64 0.85 0 .07 NA NA
4.00 NA NA NA NA NA NA NA NA NA NA 2,812 1,211
4.42 27.60 27 .10 4.26 3.70 26.86 26.83 7 .69 7 .66 1.15 -0.01 NA NA
4.92 27.60 27 .10 4.26 3.72 26.91 26 .93 7 .70 7 .66 1.03 0.50 NA NA
5.00 NA NA NA NA NA NA NA NA NA NA 1,594 1,674
5.42 27 .60 NA 4.24 NA 26.95 NA 7.70 NA 1.48 NA NA NA
119
Table C.6 : Enterococci concentration , w ater quality measurements, and amb ie nt conditions during 48 hou rs of hourly consecutiv e
sampling at the PVC. Water qu a li ty pa ram eters measured includ ed temperature, dissolved oxygen, salinity , pH, and turb id ity. Am bi ent
conditions included tida l height and solar radiation ( as measured at the Virginia Key NOAA station . The EX 03 sonde readings occurre d
di rectly fr om th e w aterway and th e YS I sonde readings were taken directly fr om th e sampl e s after the aliquot w as re moved for
enterococci meas urements .
Date Time Enterococci Temperature DO (EX03) Salinity Salinity pH (EXO3) pH (YSI) Turbidity Turbidity Tide (feet) Solar
(EX03) (EXO3) (YSI) (EX03) (YSI) Radiant
MPN/100 ml ·c mg/L ppt ppt FNU FNU feet W/m2
10/18/22 7:00 620 28 .10 7 .70 30 .21 NA 8 .07 NA -5 .12 NA -0 .63 0
10/18/22 8 :00 1,169 27 .99 7 .66 30 .15 NA 7.95 NA -4 .88 NA -0 .88 43
10/18/22 9 :00 958 27 .51 7 .72 29 .31 NA 7 .90 NA -4.97 NA -1.09 148
10/18/22 10:00 1,010 27.43 7 .81 28 .71 NA 7.88 NA -4 .92 NA -1.20 314
10/18/22 11:00 1,354 27.46 7 .71 28.43 NA 7 .86 NA -4 .79 NA -1.18 476
10/18/22 12 :00 1,182 27.52 7 .88 28 .20 NA 7 .87 NA -4 .56 NA -1.00 608
10/18/22 13 :00 1,301 27 .67 8.07 28 .11 NA 7 .86 NA -4 .68 NA -0 .70 410
10/18/22 14:00 676 27.90 8 .23 28 .05 NA 7 .87 NA -4 .77 NA -0.36 273
10/18/22 15 :00 359 28 .01 8.35 28.04 NA 7 .88 NA -4 .86 NA -0.04 184
10/18/22 16 :00 622 28.21 8.33 28 .05 NA 7 .85 NA -4.92 NA 0 .20 87
10/18/22 17 :00 554 28 .30 8.31 28 .00 NA 7 .83 NA -4 .95 NA 0 .27 23
10/18/22 18:00 480 28 .31 8.19 27.90 NA 7 .81 NA -5 .01 NA 0 .16 0
10/18/22 19 :00 620 NA NA NA 25 .56 NA 7 .61 NA -0.45 -0.09 0
10/18/22 20:00 285 NA NA NA 25.99 NA 7.70 NA -0.62 -0.39 0
10/18/22 21:00 228 NA NA NA 25.51 NA 7 .75 NA -0.22 -0.69 0
10/18/22 22:00 428 NA NA NA 25 .24 NA 7 .77 NA 0 .78 -0 .92 0
10/18/22 23:00 457 NA NA NA 25 .24 NA 7 .77 NA 0.18 -1.01 0
10/19/22 0 :00 985 NA NA NA 24 .92 NA 7 .78 NA 0.80 -0 .93 0
10/19/22 1:00 1,320 NA NA NA 24 .71 NA 7 .79 NA -0 .24 -0 .70 0
10/19/22 2 :00 1,374 NA NA NA 24 .66 NA 7.77 NA -0 .32 -0.41 0
10/19/22 3:00 823 NA NA NA 25 .14 NA 7 .79 NA -0.48 -0 .12 0
10/19/22 4:00 1,726 NA NA NA 25.02 NA 7 .80 NA -0 .30 0 .11 0
10/19/22 5 :00 703 NA NA NA 25 .00 NA 7 .78 NA -0 .28 0 .19 0
10/19/22 6:00 768 NA NA NA 25 .27 NA 7 .82 NA 0 .24 0 .10 0
120
Table C.6 (Continued): Enterococci concentration, water quality measurements, and ambient conditions during 48 hours of hourly
consecutive sampling at the PVC. Water quality parameters measured included temperatu re, dissolved oxygen, salinity, pH, and
turbidity. Ambient conditions included tidal height and solar radiation (as measured at the V irginia Key NOAA station. The EX03
sonde readings occurred directly from the waterway and the YSI sonde readings were taken di rectly from the samples after the aliquot
was removed for enterococci measurements.
Date Time Enterococci Temperature DO (EX03) Salin it y Salinity pH (EX03) pH (YSI) Turbidity Turbidity Tide (feet) Solar
(EX03) (EX03) (YSI) (EX03) (YSI) Radiant
MPN/100 ml ·c mg/L ppt ppt FNU FNU feet W/m2
10/19/22 7 :00 459 28.09 7 .0 4 27 .13 24.99 7.67 7.83 -1.48 -0.08 -0 .15 0
10/19/22 8 :00 743 27 .82 6.81 26.99 25.02 7 .63 7.81 -4.01 -0.42 -0.47 24
10/19/22 9:00 982 28 .01 6.44 27 .37 25.10 7 .62 7 .79 -5.00 -0.38 -0.79 70
10/19/22 10:00 651 28.00 6 .26 27.45 25.16 7.60 7.78 -4.96 -0.27 -1.06 90
10/19/22 11:00 397 27.73 6.19 27 .28 24.74 7.57 7.78 -4 .82 -0.32 -1.22 179
10/19/22 12 :00 1,459 27.62 6.22 27 .1 5 24.43 7 .56 7 .79 -4.79 0 .26 -1.19 152
10/19/22 13:00 2,513 NA NA NA 23.92 NA 7 .78 NA 0 .34 -0 .99 205
10/19/22 14:00 911 NA NA NA 23 .68 NA 7.78 NA -0.12 -0.67 119
10/19/22 15:00 4,160 NA NA NA 23.69 NA 7 .79 NA -0.26 -0 .31 58
10/19/22 16 :00 10,112 NA NA NA 24.17 NA 7.77 NA -0 .10 0 .03 38
10/19/22 17:00 9,606 NA NA NA 22.97 NA 7.78 NA -0.24 0 .25 4
10/19/22 18:00 24,196 NA NA NA 20 .75 NA 7 .74 NA 0 .20 0 .30 0
10/19/22 19:00 7,215 27 .06 6.40 27 .24 22.44 10.64 7 .74 -4.35 0.14 0 .15 0
10/19/22 20:00 12,033 NA NA NA 19.46 NA 7.71 NA 0 .94 -0 .13 0
10/19/22 21:00 24,196 NA NA NA 19.59 NA 7.68 NA 0 .15 -0.46 0
10/19/22 22:00 24,196 NA NA NA 20.39 NA 7.69 NA 0.05 -0.79 0
10/19/22 23:00 24,196 NA NA NA 20.55 NA 7.69 NA 0 .04 -1.02 0
10/20/22 0:00 19,866 NA NA NA 21.07 NA 7.68 NA 0.04 -1.10 0
10/20/22 1:00 15,531 NA NA NA 21.53 NA 7.66 NA 0.15 -0 .98 0
10/20/22 2:00 > 24,196 NA NA NA 20.86 NA 7 .65 NA 0.32 -0.72 0
10/20/22 3:00 24,196 NA NA NA 20.42 NA 7 .66 NA 0 .36 -0.39 0
10/20/22 4:00 10,112 NA NA NA 22.22 NA 7 .67 NA 0 .31 -0 .07 0
10/20/22 5 :00 24,196 NA NA NA 23.57 NA 7 .70 NA 0.09 0 .18 0
10/20/22 6:00 8,704 NA NA NA 23.59 NA 7 .66 NA -0.15 0.27 0
121
Table C.7: Concentration of enterococci in 48 hours sampling from the PVC based on time with
weather and water characteristics including height of tide, solar radiant and hourly rainfall from
three adjacent weather stations (Farrbetter, Miami Beach , and Coast Guard).
Solar Hourly Rainfall (inch)
Date Time Enterococci Tide Radiant Farrbetter Miami Beach Coast Guard
(MPN/100 mL) (feet) (W/m2)
(25 .86 °N , (25.83 °N , (25.77°N ,
80.13°W) 80.13 °W) 80.15°W)
10 /18 /22 7 :00 620 0 .32 0 0 0 0
10 /18 /22 8:00 1,169 0 .04 43 0 0 0
10 /18 /22 9:00 958 -0 .20 148 0 0 0
10 /18 /22 10:00 1,010 -0.31 314 0 0 0
10/18 /22 11 :00 1,354 -0 .25 476 0 0 0
10 /18 /22 12:00 1,182 -0 .04 608 0 0 0
10/18 /22 13:00 1,301 0.29 410 0 0 0
10/18 /22 14:00 676 0.58 273 0 0 0
10/18 /22 15:00 359 0.86 184 0 0.01 0
10/18 /22 16:00 622 1.02 87 0 0 0
10 /18 /22 17:00 554 1.07 23 0 0 0
10/18/22 18 :00 480 0.97 0 0 0 0
10 /18 /22 19:00 620 0.63 0 0 0 0
10 /18 /22 20 :00 285 0 .34 0 0 0 0
10 /18/22 21 :00 228 0.08 0 0 0 0
10 /18 /22 22:00 428 -0.09 0 0 0 0
10/18/22 23:00 457 -0 .16 0 0 0 0
10 /19 /22 0:00 985 -0.01 0 0 0 NA
10 /19 /22 1:00 1,320 0.24 0 0 0 NA
10/19/22 2 :00 1,374 0.55 0 0 0 0
10/19/22 3:00 823 0.75 0 0 0 0.01
10 /19 /22 4 :00 1,726 0.96 0 0 0 0
10/19/22 5:00 703 0.99 0 0 0 0
10/19/22 6:00 768 0.86 0 0 0 0
10 /19 /22 7:00 459 0.58 0 0 0 0
10 /19 /22 8:00 743 0.24 24 0 0 0
10 /19 /22 9:00 982 -0.08 70 0 0 0
10/19/22 10:00 651 -0.32 90 0 0 0
10/19/22 11 :00 397 -0.38 179 0 0 0
10/19/22 12 :00 1,459 -0.35 152 0 0 0
10 /19 /22 13:00 2,513 -0.18 205 0 0 0
10 /19/22 14:00 911 0.10 119 0 .01 0 0.07
10/19/22 15:00 4,160 0.43 58 0 0 0.01
10/19/22 16:00 10 ,112 0.62 38 0.03 0 .01 0.01
10/19/22 17:00 9 ,606 0.86 4 0.1 0.01 0 .24
122
Table C.7 (Continued): Concentration of enterococci in 48 hours sampling from Miami Beach
based on time with weather and water characteristics including height of tide , solar radiant and
hourl y rainfall from three adjacent weather stations (Farrbetter, Miami Beach, and Coast Guard).
Solar Hourly Rainfall (inch)
Date Time Enterococci Tide Radiant Farrbetter Miami Beach Coast Guard
(MPN/100 mL) (feet) (W/m 2) (25 .86 °N , (25 .83 °N, (25 .77 °N,
80.13 °W) 80.13°W) 80.15 °W)
10 /19/22 18:00 24,196 0.96 0 0.27 0.35 0.01
10 /19/22 19:00 7 ,215 0 .79 0 0 0 .1 0
10/19/22 20:00 12,033 0.44 0 0 0 0 .002
10 /19/22 21:00 24,196 0 .13 0 0 0 0
10 /19/22 22 :00 24 ,196 -0.22 0 0 0 0
10/l Q/2 23 :00 24 ,196 -0.45 0 0 0 0
10 /20/22 0 :00 19,866 -0.49 0 0 0 0.001
10/20/22 1:00 15 ,531 -0.37 0 0 0 NA
10/20/22 2:00 > 24,196 -0 .06 0 0 0 NA
10/20/22 3:00 24 ,196 0 .20 0 0 0 NA
10/20/22 4:00 10 ,112 0.48 0 0 0 NA
10/20/22 5:00 24,196 0 .71 0 0 0 NA
10/20/22 6:00 8,704 0.80 0 0 0 NA
123
Table C.8: Water quality parameters including field temperature (°C), dissolved oxygen (mg/L), salinity
(ppt), field pH and turbidity (NTU) for catch basins (W4, W6, and W8) sampled on November 14, 2022.
Field Dissolved Turbidity Sample ID Depth (feet) Temperature Salinity (ppt) Field pH
(OC) Oxygen (mg/L) (NTU)
0.17 28 1.4 1.03 7 1.9
0.33 28.4 1.01 2.2 6.99 1.96
0.50 28.4 0.84 2.21 6.99 2.01
W4 0.67 28.4 0.78 2.21 6.99 1.94
0.83 28.4 0.7 2.21 6.98 1.94
1.00 28 .4 0.67 2.21 6.98 1.88
1.25 28.4 0.65 2.21 6.98 1.95
1.50 28.4 0.63 2.21 6.98 1.91
0.33 26 .8 3.6 24 .5 7 09 1.28
0.50 26 .9 2.9 24 .98 7.12 1.05
0.67 26 .9 2.85 25 .13 7.14 1.04
0.83 26 .9 2.8 25 .18 7.16 1.06
1.00 26 .9 2.77 25.3 7.17 1.12
1.25 26 .8 2.77 25 .59 7.18 0.91
1.50 26.4 2.72 32 7.29 0.67
1.75 26.4 3.18 33.2 7.36 0.94
2.00 26 .1 3.45 33 .66 7.4 1.15
W6 2.50 26 3.39 33.52 7.4 1.48
3.00 25.9 3.58 34 .09 7.43 1.59
3.50 25 .9 3.55 34 .18 7.43 1.85
4.00 25 .9 3.5 34 .25 7.43 1.82
4.50 25 .9 3.47 34 .3 7.43 1.91
5.00 26 3.34 34.49 7.42 2.04
6.00 26 3.33 34 .53 7.42 2.19
7.00 26 3.3 34 .56 7.42 2.05
7.17 26 3.2 34.55 7.42 3 02
7.17 34 .73 7.11 4.3
0.50 25 .1 1.04 0.07 7.73 2.54
0.67 25.2 0.9 0.13 6.97 2.48
W8 0.83 25 .1 0.83 0.13 6.9 2.94
1.00 25 .1 0.78 0.13 6.86 2.26
1.25 25 .1 0.76 0.13 6.82 2.4
124
Table C.9: Water quality parameters including field temperature (0 C), dissolved oxygen (mg/L), salinity
(ppt), field pH and turbidity (NTU) for vertical wells (VI , V2, and V3) sampled on November 14, 2022.
Field Dissolved Turbidity Temperature Salinity (ppt) Field pH
Sample ID Depth (feet) (OC) Oxygen (mg/L) (NTU)
0 .17 28 .1 2.23 5.31 7 .1 0 .99
0.33 28 2 .1 5.31 7 .11 1.13
0 .50 28 1.85 5.31 7 .12 1
0 .67 28 1.78 5.3 I 7 .13 I
0.83 27.9 1.74 5.3 I 7 .14 0 .96
1.00 27 .9 1.71 5.3 I 7 .14 1.01
1.25 27 .9 1.68 5.31 7 .15 1.06
1.50 27 .9 1.66 5.32 7 .14 1.06
1.7 5 27 .9 1.65 5.34 7.14 I
VI 2 .00 27 .9 1.6 5.4 7 .13 1.11
2 .50 27 .9 1.55 5.48 7 .12 1.14
3.00 27 .8 1.68 28.92 7 .17 1.83
3 .50 26.3 3 .14 34.98 7 .26 2 .1
4 .00 26.2 3.24 35 .11 7.3 1.9
4 .50 26.2 3.25 35 .14 7.32 2 .11
5.00 26.2 3 .27 35 .16 7.33 1.92
6 .00 26.2 3.28 35 .17 7 .33 2.22
7 .00 26 .2 3.31 35 . 16 7 .34 2.55
8.00 26.2 3 .35 35 .16 7.34 3 .13
0 .17 26 1.66 0 .15 7 .72 1.92
0.33 26 1.14 0 . 13 7.55 1.71
0.50 25 .9 0 .91 0 .13 7.48 2 .14
0 .67 25 .9 0 .83 0 .12 7.42 1.87
0.83 25 .7 0 .75 0 .12 7.36 1.57
1.00 25 .7 0 .74 0 .12 7 .33 1.47
1.25 25 .7 0 .73 0 .12 7 .31 1.5
1.50 25 .7 0 .7 0 .12 7.28 1.52
1.75 25 .7 0 .67 0 .11 7.26 1.82
2 .00 25 .7 0 .67 0 .11 7 .25 1.5
2 .50 25 .7 0 .66 0 .11 7.23 1.5
V2 3 .00 25 .7 0 .65 0 .11 7 .21 1.46
3 .50 25 .7 0 .65 0 .11 7.19 1.45
4 .00 25 .7 0 .65 0 .11 7 .18 1.55
4.50 25 .7 0 .65 0 .11 7.17 1.57
5 .00 25 .7 0 .63 0 .11 7 .16 1.6
6 .00 25 .7 0.63 0 .12 7 .16 1.5
7 .00 25 .7 0 .63 0 .12 7 .15 1.46
8 .00 25 .7 0 .62 0 .12 7.14 1.44
9.00 25 .7 0 .62 0.12 7 .14 1.31
10 .00 25 .7 0 .62 0 .13 7 .15 1.27
11 .00 25 .7 0 .62 0 .13 7 .16 1.16
11.50 25 .6 0 .61 0 .15 7 .16 I.I I
0.33 28 .5 1.33 4.26 7.13 4 .1
0 .50 28.5 115 4.44 7.11 2.48
0 .67 28.5 1.05 4 .69 7 .1 3.3
0 .83 28.5 1.03 5.07 7 08 2 .13
1.00 28.5 1.01 5.15 7.08 1.77
1.25 28.5 0 .97 5 .25 7 08 1.63
V3 1.50 28 .5 0 .95 5 .35 7 07 1.71
1.75 28 .5 0 .94 5.41 7 .07 1.57
2 .00 28.5 0 .91 5.66 7 .07 1.52
2 .50 28 .5 0 .91 5 .63 7.07 1.52
3 .00 28 .5 0 .93 5.3 7.07 1.48
3.50 28.5 0.88 6 .6 7 04 1.43
4 .00 28.5 0 .76 6 .97 7 .03 1.83
125
Table C.10: Water quality parameters including field temperature (0 C), dissolved oxygen (mg /L ), salinity
(ppt), field pH and turbidity (NTU) for groundwater monitoring wells (GI and G2) sampled on November
14, 2022.
Field Dissolved Turbidity Sample ID Depth (feet) Temperature Salinity (ppt) Field pH
(OC) Oxygen (mg/L) (NTU)
0 .17 27 6.59 0 .04 7 .16 16 .1
0.33 27 .2 5 .76 0 .88 7 .02 14 .64
0 .50 27.2 5 .67 0 .86 6 .99 13 .68
0 .67 27.2 5 .64 0 .85 6 .97 12 .61
0 .83 27 .3 5 .65 0.86 6 .95 13
1.00 27 .3 5 .67 0.86 6 .93 13 .18
1.25 27 .3 5.63 0 .81 6 .92 10 .81
150 27 .3 5.59 0 .79 6 .91 10 .21
1.75 27 .3 5.56 0 .77 6.91 10.24
2 .00 27 .3 5 .55 0 .76 6 .91 8.8
GI 2.50 27 .3 5.51 0 .74 6 .9 7 .8
3 .00 27.4 5.48 0 .74 6 .9 7 .27
3 .50 27.4 5.46 0 .73 6 .9 6 .68
4 .00 27.4 5.4 0 .73 6 .89 6.23
4.50 27.4 5.25 0 .73 6 .89 6 .29
5 .00 27.4 5.18 0 .73 6 .89 8 .11
6 .00 27.4 5 .15 0 .73 6 .89 5 .52
7 .00 27.3 4 .9 0 .73 6 .88 4.32
8.00 27.3 4.47 0 .73 6 .88 6 .04
9 .00 27.2 4.23 0 .73 6 .87 5.4
30.17 NIA NIA 22.48 6 .84 3 .15
0.17 27 5.1 0 .65 7.41 10 .26
0 .33 27 .1 5 .01 0 .61 7 .31 9.41
0.50 27 4 .96 0 .63 7 .35 9.45
0 .67 27 .1 4 .94 0 .61 7 .32 9 .96
0 .83 27 4 .89 0 .59 7.31 8 .55
1.00 27 4 .83 0 .58 7.31 7 .86
1.25 27 .1 4.83 0 .58 7.3 7.4
1.50 27 4 .8 0 .57 7 .3 7 .3
1.75 27 .1 4 .74 0 .56 7.29 7 .77
2 .00 27 .1 4 .73 0 .56 7 .29 8.56
2.50 27 .1 4 .7 0 .55 7 .29 6 .79
3 .00 27 .1 4 .62 0 .54 7.28 7 .25
G2 3.50 27 .1 4 .57 0 .54 7.28 6 .7
4 .00 27 .1 4.56 0 .55 7 .27 5 .8
4.50 27 .2 4 .5 0 .58 7.26 4 .74
5 .00 27 .2 4.47 0 .64 7 .25 4.41
6 .00 27 .3 4.43 0 .86 7.23 3 .73
7 .00 27 .3 4 .28 1.37 7 .18 4 .81
8.00 27 .3 4 .03 2.56 7 .12 4 .95
9 .00 27.3 3.44 4.4 7 .09 4 .55
10 .00 27 .3 2.41 8 .11 6 .99 2 .52
11 .00 27.2 1.57 12 .55 6 .98 2.45
12 .00 27 .1 0 .96 14 .71 6 .98 2.2
13 .00 27 .1 0 .9 14 .86 7 .01 2.4
31 .33 NIA NIA 24 .74 6 .95 6.44
126
Table C .11: Enterococci concentrations for samples collected on November 14th , 2022 based on sample location and depth (Top (T) or bottom
(8)) with other physical chemical parameters including field temperature (°C), dissolve d o x ygen (mg/L ), salinity (ppt), field pH, turbidity (NTU),
enterococci (MPN/100 mL).
Field Dissolved Temperature Oxygen (mg/L) Salinity (ppt) Field pH Turbidity (NTU) Enterococci
Sample ID Date (OC) (MPN/100 mL)
Gl-T 11 /14/2021 20 .1 5 .83 0 .71 6 .82 18 IO
Gl-8 11 /14/2021 20.5 4.05 22.48 6 .84 3.15 10
G2-T 11/14/2021 20.4 5.9 0 .52 7 .25 6 .05 20
G2-B 11 /14/2021 20.4 3 .63 24.74 6 .95 6.44 10
W4-T 11/14/2021 20 .1 1.6 2.26 7 .12 19 .27 364
W4-B 11 /14/2021 20 .3 1.74 2.28 7.1 11 .52 1927
W6-T 11/14/2021 20.4 4 .67 25 .1 7 .03 3.29 24196
W6-B 11/14/2021 20.8 4 .91 34.73 7 .11 4 .3 934
W8-T 11/14/2021 20.4 3 0 .23 7 .53 4.43 24196
W8-B 11 /14/2021 20 3 .1 0 .23 7.31 4.58 24196
VI-T 11 /14/2021 19.6 4.06 5.19 7 .06 3.56 4611
Vl-8 11 /14/2021 19.6 4 .34 34.79 7.13 4 .03 238
V2-T 11/14/2021 20 .3 3.8 0 .19 7.85 3 .9 24196
V2-B 11 /14/2021 20 .3 3 .57 0.81 7 .7 4 .73 17327
V3-T 11/14/2021 20 .2 4.5 4.02 7.22 4.8 1616
V3-B 11/14/2021 20.5 4 6 .83 7.07 5.43 1989
127
APPENDIXD
DETAILS FROM VISUAL INSPECTIONS
128
APPENDIXD
DETAILS OF VISUAL INSPECTIONS
SCOUTING VISITS BY SEQUENCE OF VISIT
Helena Solo-Gabriele, Ph.D., from the University of Miami research team visited the PVC
Kayak Launch site on June 11, 2022. During Dr. Solo-Gabriele 's visit she observed suspected
dog feces near stormwater catch basin inlets on the street and sidewalk that contribute towards
the site (Figure D.1 , a and b). Although the area has dog waste disposal stations with bags
available along with educational signs (Figure D. l , c and d), feces were still observed.
Observations of dog walkers in the area indicate that about half pick up after their dogs. In
addition, in the park area that leads to the kayak launch , animals besides dogs were observed that
co 1ld potentiall y contribute feca l waste . T hese additional animals included iguanas and different
types of birds. She observed a flock of pigeons, a wading bird, and a rooster (Figure D.2). The
number and the diversity of the birds in the area was unusual. The area where the birds
congregated had a stored lawn chair in the tree plus a cup and water tray which appeared to
possibly serve as a possible bird or animal feeding station. During her visit she took photographs
from the base of the kayak launch and observed the riverbanks in the area which had a
considerable amount of rip rap , in addition to uncovered sediment. The mangrove canopy
extended several feet into the water from the banks (Figure D.3). This is of significance as shade
limits sunlight inactivation of microbes that may be in the wateway.
Erik Lamm from the University of M iami research team visited the PVC Kayak Launch site on
July 24, 2022 , to measure the tidally driven changes in water levels over an 8-hour period and
scout for potential sampling locations. Various sampling locations were identified during the
reconnaissance mission on July 24 th . These locations were either exposed during low tide or only
submerged by a few centimeters of water. Easy access was identified from within the canal. The
sample locations varied in vegetation . The majority are in areas with an abundance of
mangroves , which might provide an ideal environment for bacteria growth. Another location is
near a stormwater outfall , which might isolate the stormwater system as a source. Other
locations are on the bends of the canal where natural beaches with shallow water form during
low tide . The southern bend is next to a large building that borders the canal (Figure D.4, a to d).
The northern bend is directly above the sanitary sewer system siphon. The results from this
scouting visit were used to inform the selection of the sampling transects detailed in the
subsequent section of this report.
On August 9, 2022 the University of Miami research team employed a two pronged approach
whereby Larissa Montas, Ph. D., and Rivka Reiner deployed by boat with CMB staff from the
boat ramp located on Purdy Avenue and navigated to the Normandy Isles waterway N-S and the
PVC while Dr. Helena Solo-Gabriele, Ph.D., deployed to the Kayak Launch pad. As the boat
approached the Normandy Isles Waterway and the PVC , Larissa Montas observed trash floating
in both waterways, including plastic trash bags , miscellaneous plastic items of varying size and
dog feces floating on the water surface (Figure D .5, a and b). She also observed trash and leaves
were accumulated against the retaining walls and below the docks connected to several homes
along the PVC North. Where the trash had accumulated a white foam covered the water surface
129
and higher concentration of suspended solids were observed (Figure D.6 , a and b ). Additionally ,
during the visual inspection she observed small to medium size cracks in the retaining wall along
the perimeter of Parkview Island. On the landside of the waterway 's banks shoreline types varied
from sediment shoreline with dense mangrove canopy that extended approximately one to three
meters over the water surface, exposed sediments showing signs of erosion, sediment shoreline
reinforced with human-made walls, and residential units with overhanging docks and a retaining
wall extending to an undetermined depth (Figure D.7 , a toe).
Dr. Montas observed three homeless camps during the marine water sampling and site inspection
by boat. She identified three homeless camps: one in the PVC North under the bridge leading
from PVI to Biscayne Beach Elementary School , a second camp was located under the bridge
leading from PVI to Dickens Ave, and a third camp was located on the shore of PVC East in the
vicinity of Park View Island Park (Figure D.8 , a, band c). During this trip Dr. Solo-Gabriele
who was at the Kayak Launch Pad observed a homeless camp on the west side of the community
garden (see Figure D.8, panel d).
On August 17 , Dr. Helena Solo-Gabriele, Dr. Larissa Montas and Erik Lamm conducted
sampling activities at the PVC, PVI Park and along the stormwater conveyance infrastructure.
Three water samples and three sediment samples were collected at the hot-spot locations
identified during the high tide sampling . Dr. Montas observed what appeared to be animal feces
at one of the shoreline sediments sampling locations . A homeless camp identified prior
(hammock and mosquito net) appeared to have been moved to another sampling location. The
shoreline sediments at the location directly across the PVI park had a foul odor. That same day ,
Dr. Solo-Gabriele led the team efforts on sampling the stormwater conveyance infrastructure
with the support from the Public works Department, CMB. The team sampled stormwater inlets
and catch basins located along the two gravity pipes leading to the stormwater outfalls that
discharge north and south of the Kayak Launch pad. These two gravity pipes run along 73rd
street and 74th street. In general , the manholes and catch basins located closest to the PVI Park
and downflow of the commercial areas along Collins Ave., were full of trash. For these basins
the water color was dark grey to black and a foul odor was noted. In particular, sites WI and W2
had the most trash , with the team noticing an odor similar to sulfur, emanating from W2. Other
basins, like site W5 , were cleaner and the water appeared to have less suspended sediments. In
terms of general observations of the top sediments adjacent to the inlets, there was high
variability in the color, grain size and apparent organic content. For example sediments at
location WI , appeared similar to dry grey ash or very fine sand. Sediments at location W4 had a
similar appearance while sediments at location W5 were full of dry organic matter and the grain
size was larger than for the two other locations (Figure D .9, a , band c).
On September 2, Dr. Larissa Montas and Erik Lamm conducted sampling activities at 16
locations along the stormwater sewer infrastructure. These sampling activities were an effort to
sample stormwater sewer catch basins and wells that were located along the 74 th and 73 rd Street
gravity pipes and very close to the sanitary sewer infrastructure, locations within PVI , and
locations that were far away from the PVC and as far away as possible form the sanitary sewer.
The team observed similar conditions to those recorded on August 17. Several differences were
noted. In particular, the catch basin at locations WI and W2 had been cleaned by city
130
contractors. Please refer to Section V .2 for further details on measured changes in enterococci
concentrations in the catch basin water.
On September 16 , 2022 the University of Miami research team comprised of Dr. Larissa Montas
and Yutao Chen, deployed by boat with CMB staff from the boat ramp located on Purdy Avenue
and navigated to the Normandy Isles waterway N-S and the PVC. A heavy storm impacted the
Co MB the night before. Significant amounts of trash were observed on the water surface in main
waterway and PVC. Discoloration was observed at water surface, as well as areas where a
greenish color was observed at water surface. Large quantities of trash (water bottles, soda cans,
plastic wraps , large plastic items including a dish pan and a bucket) were observed on sediment
banks, covering bottom sediments and on the water surface was well. In particular, along the
shallow banks of the north and south bend, she observed that the waterway 's bottom sediments
were completely covered by trash. Signs of erosion were observed along some of the exposed
sediment shore line , "\Wh ere it was evident that run-off had 'carved" small gullies into the sediment
banks (Figure D . l 0, a, b and c ).
On September 21 , 2022, Helena Solo-Gabriele met with CMB public works staff to discuss the
enclosure location for the autosampler. It was raining very heavily during this visit. Helena
Solo-Gabriele along with CMB staff went out in the rain (with umbrellas) to discuss the location
for the enclosure . They stood over the 73 Street outfall to discuss possible installation there .
During this observation, water from the storm conveyance system wsa carrying trash into the
waterway. The discharge of bags and broken up pieces of plastic were observed coming out of
the storm conveyance system. Also , flows coming from smaller private outfalls were observed
to have been discolored.
Helena Solo-Gabriele collected all samples with the assistance of Hekai Zhang and CMB staff
from the Kayak Launch pad which resulted in five trips to the station during dark hours. During
this time she observed manatees and iguanas swimming in the PVC. It was very lightly raining
during the October 19 evening pick up (about 7 pm). She also interviewed the CMB staff the
day before and after the rain to get their insights on when the rainn started prior (between 2 and 4
pm immediately prior to the October 19 evening pickup) based upon CMB staff near the site at
the time.
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a) Suspected dog
waste
b) Disintegrating c) Dog waste station d) Signage for dog
suspected fecal waste with bags waste cleanup
Figure D. l: Suspected dog feces and doggie disposal stations and educational materials (Photos
taken June 11, 2022)
Rooster Wading Bird
Figure D.2: Birds in park area that leads to the PVC Kayak Launch. Lawn chair, cup and water
tray circled in red. At the time of the visit there was a flock of pigeons observed at the site which
scattered prior to the photo (Photos taken June 11, 2022)
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Figure 0 .3: Mangrove canopy at PVC, extending several feet from the banks providing shade
and potential protection against UV light which is known to inactivate microbes
Photo cndit: Erik Lamm
Figure 0.4: Locations along the PVC with shallow water during low tide which are more highly
influenced by channel bank sediments. Channel bank sediments have been shown to have
elevated levels of enterococci.
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Figure D .5: Animal feces and a doggie bag with feces floating on the water surface
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Figure 0.6: Water showing discoloration and white foam
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Figure 0.7: Shoreline types along PVC varies from sediment shoreline with dense mangrove
canopy, exposed sediments showing signs of erosion, sediment shoreline reinforced with human-
made walls, and a retaining wall extending to an undetermined depth
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Figure D.8: Pictures of homeless encampments that were found immediately adjacent to the
PVC. These encampments were located: a) underneath the bridge from PVI to Biscayne Shores
Elementary School, b) bridge from PVI to Dickens Ave, c) mangroves in the vicinity of the park
adjacent to the PVC Kayak Launch, and d) immediately west of the community garden area
adjacent to Park View Island park.
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Figure 0.9: Trash and debris within stormwater conveyance system. a) Catch basin with trash,
b) Top sediments near inlet, c) Black sediments near curb gutter
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Figure 0.10: Shoreline details. a) and b) Shallow banks exposed during low tide are covered
with trash . c) Shoreline showing signs of erosion. At the shallow banks trash covered the
sediment bottom
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