r
EPA 904/9-76-016
ENVIRONMENTAL AND RECOVERY
STUDIES OF ESCAMB
AND THE
;NSACOLA-BAY s
LORIDA
ENVIRONMENTAL PPOTEGTION AGENCY
1421 PEACHTREE ST., ATLANTA, GEORGIA 30309
'I JULY 1975
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ENVIRONMENTAL AND RECOVERY
STUDIES OF ESCAMBIA BAY
AND THE PENSACOLA BAY SYSTEM,
FLORIDA
LAWRENCE W. OLINGER
Technical Director
Environmental Engineer
REGINALD G. ROGERS
Aquatic Biologist
PAUL L. FORE
Fisheries Biologist
RUSSELL L. TODD
Microbiologist
BALLARD L. MULLINS
Chemist
F= THEODORE BISTERFELD
Aquatic Biologist
LLOYD A. WISE, II
Engineering Technician
UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
Region IV
Surveillance and Analysis Division
Escambia Bay Recovery Study
July 1975
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REVIEW NOTICE
This report has boon reviewed by the Environmental
Protection Agency, Royion IV, and approved for publication,
Mention of trade names or commercial products does not
constitute endorsement or reconnenclation for use.
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Foreward
The studies represented in this report indicate that an
environmentally damaged estuary can improve rapidly when
wastewater discharges are reduced* The effort expended to abate
pollution appears worthwhile! and the additional pollution
abatement efforts recommended in the report are necessary for
continued recovery of the system*
The Escambia Bay Recovery Study was initiated as a result of
concern over the degraded condition of Escambia Bay* The success
of the Study was due to the cooperation of conservation and
sportsmens groups• academic institutionsv industries( government
agencies* and concerned citizens* The studies indicated that
environmental protection is not an impossible goal*
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TABLE OF CONTENTS
Page
1. INTRODUCTION. 1-1
GENERAL 1-1
BACKGROUND 1-1
ACKNOWLEDGMENTS 1-3
2. SUMMARY 2-1
AREA DESCRIPTION 2-1
POLLUTION SOURCES 2-1
HYDRODYNAMICS 2-2
BAY SEDIMENTS 2-4
WATER QUALITY 2-6
PLANKTON 2-9
FISHES 2-9
BENTHIC MACROINVERTBERATES 2-11
BENTHIC MACROFLORA 2-12
3. CONCLUSIONS AND RECOMMENDATIONS 3-1
CONCLUSIONS 3-1
Environmental Quality 3-1
Causes of Environmental Problems 3-2
Restoration 3-1
RECOMMENDATIONS . 3-5
4. AREA DESCRIPTION 4-1
CLIMATOLOGY 4-1
Wind 4-1
Precipitation 4-4
Air Temperature 4-8
POPULATION 4-8
ECONOMY 4-8
RECREATION 4-9
SPORT AND COMMERCIAL FISHERIES 4-10
5. POLLUTION SOURCES 5-1
POINT SOURCE DISCHARGES 5-1
Introduction 5-1
Methods 5-1
Results 5-1
General 5-1
Principal Industrial Point Sources . 5-3
Principal Municipal-Private Domestic
Point Sources. 5-12
Discussion 5-16
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Page
WON-POINT SOURCES 5-18
6. HYDRODYNAMICS 6-1
BATHYMETRY 6-1
FRESHWATER HYDROLOGY ." 6-1
Introduction 6-1
Methods 6-1
Results 6-5
FLOWS IN THE ESCAMBIA RIVER DELTA TRIBUTARIES. 6-8
Introduction 6-8
, Methods 6-9
Results 6-9
TIDES. 6-12
Introduction. .............. 6-12
Methods 6-12
Results 6-13
Discussion 6-13
SALINITY 6-16
Introduction -'. . . 6-16
Methods 6-17
Results and Discussion 6-19
Salinity Variation 6-19
Inflow and outflow Based on Salinity 6-26
WATER TEMPERATURE 6-28
Introduction 6-28
Methods 6-28
Results and Discussion 6-28
CIRCULATION IN ESCAMBIA BAY. 6-31
Introduction 6-31
Methods . 6-31
Environmental Conditions 6-34
Results and Discussion 6-34
DISTRIBUTION OF INDUSTRIAL DISCHARGES IN
ESCAMBIA BAY 6-37
Introduction 6-37
Methods 6-37
Environmental Conditions 6-40
Tracer Release 6-40
Background Concentration 6-43
Steady State Tracer Distributions . . . . „ 6-43
CIRCULATION IN PENSACOLA BAY SYSTEM 6-50
CIRCULATION IN MULATTO BAYOU . 6-50
Introduction. 6-50
Methods ...... 6-52
Environmental Conditions 6-52
Results and .Discussion. . . .... . . . 6-52
7. BAY SEDIMENTS :..... 7-1
SEDIMENTATION . . 7-1
Introduction 7-1
Sampling Stations 7-2
11
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Pag;e
Methods 7-2
Results 7-5
Bay Bottom Profiles 7-5
Sediment Particle Size
Characterizations 7-5
Sediment Chemistry 7-12
SEDIMENT NUTRIENT RELEASE. .......... 7-32
Introduction. . ...... 7-32
Methods 7-33
Results and Discussion.. ., .'. ..... .s . . . 7-33
MICROBIAL ACTIVITY ... . ". . ........ 7-41
Introduction. . .... . . . . 7-41
Methods . ....:. . . 7-42
Results ........ 7-45
Discussion. . . . . . . ...... ... 7-47
WATER QUALITY ......... 8-1
INTRODUCTION 8-1
METHODS. 8-1
Water Quality Studies ..... 8-1
Analytical Methods 8-2
ENVIRONMENTAL CONDITIONS ...... 8-2
WATER QUALITY STANDARDS. 8-2
PRINCIPAL NUTRIENTS 8-5
Carbon. . . . . . . ., 8-5
Introduction ...... 8-5
Results and Discussion 8-5
Nitrogen •...-..' 8-11
Introduction ............ 8-11
Results and Discussion . ... • • . 8-12
Phosphorus. ... . . . ... . . . . . . 8-22
Introduction . . . ... . . .' . . . 8-22
Results and Discussion .. ..... 8-26
Principal Nutrient Index. ........ 8-32
Introduction 8-32
Method 8-36
Results and Discussion ....... 8-39
OXYGEN RESOURCES ....... 8-48
Dissolved Oxygen. 8-48
Introduction 8-48
Results. . .... . ... . ... . . . 8-49
Discussion . . ... . 8-60
Biochemical Oxygen Demand . . 8-62
Introduction ............ 8-62
Results and Discussion . ...... 6-63
TOTAL AND FECAL COLIFORMS. ....."'.' 8-72
Introduction. ..... . . 8-72
Results .... . .' . .... . . . . . . 8-72
Discussion 8-80
PARTICULATE MATTER . . "8-83
Introduction. . 8-83
Results and Discussion 8-83
111
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Page
NUTRIENT LOADINGS INTO THE PENSACOLA BAY
SYSTEM 8-89
9. PLANKTON 9-1
PHYTOPLANKTON PRODUCTIVITY 9-1
PHYTOPLANTON CROP 9-1
Cell Counts ........ °. ...... 9-1
ZOOPLANKTON CROP ..... 9-2
CHLOROPHYLL. ............ 9-2
Introduction 9-2
Methods ................. 9-2
Results ........... 9-4
Discussion 9-1
10. FISHES AND PENAEIDS OF ESCAMBIA BAY ........ 10-1
SURVEY AND STATUS OF THE FISHES, SHRIMPS, AND
FISHES 10-1
Introduction 10-1
Material and Methods 10-2
Sampling Stations, Procedures, and
Gear 10-2
Community Structure. ... 10-4
Fish Kills 10-5
Commercial Landings. . 10-5
Results , 10-5
Relative Abundance . 10-5
Distribution of Area 10-8
Seasonality 10-10
Distribution Records 10-11
Community Structure i 10-11
Environmental Relationships 10-15
Shrimp Distribution 10-18
Fish Kills . . 10-20
Freshwater.Sport Fishery 10-25
Biology of Major Species 10-27
Discussion 10-35
FISH COMMUNITIES OF OYSTER-SHELL AND MUD
BOTTOMS IN A POLLUTED ESTUARY WITH COMMENTS ON
SUBSTRATE ALTERATION 10-41
Introduction 10-41
Methods 10-41
Description of Area 10-41
Sediment Analysis. . 10-43
Sampling Procedure 10-43
Results 10-44
Sediments 10-44
Fish Collections 10-44
Distribution of Shrimps. ...... 10-47
Discussion 10-49
11. BENTHIC MACROINVERTEBRATES. 11-1
INTRODUCTION . 11-1
IV
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METHODS 11-1
RESULTS 11-8
Sand Shelf Assemblage 11-8
Transition Zone Assemblage 11-13
Mud Plain 11-14
Oyster Bed Assemblage 11-15
Grass Bed Assemblage 11-16
. Sewage Treatment Plant Discharge
Assemblage. . . ...... 11-17
Industrial Discharge Assemblage 11-18
Deep Water Mud Station Assemblage .... 11-20
High Salinity Area Assemblage ...... 11-21
Comparison of Diversity Indices in the
Pensacola Bay System . 11-22
Comparison of Diversity Indices in Gulf
of Mexico Coastal Systems 11-25
12. BENTHIC MACROFLORA 12-1
SEAGRASS DISTRIBUTIONS .... 12-1
Introduction 12-1
Methods 12-3
Results and Discussion 12-3
SEAGRASS REVEGETATION 12-7
Introduction , . . 12-7
Methods 12-10
Results 12-11
Discussion. ...... 12-11
13. LITERATURE CITED 13-1
14. APPENDICES 14-1
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LIST OF APPENDICES
Appendix ' Page
1-1. Steering Committee . . „ . . . : . . . . . . . 14-1
1-2. Recommendations of the 1972 Enforcement
Conference ............ 1U-2
5-1. NPDES effluent limitations for principal
source discharges into Pensacola Bay and its
tributaries. . «, ........'........ 14-5
5-2. Point source industrial discharges and plant
descriptions . . 14-5
5-3. Point source industrial discharges (loadings
in kg/day) 14-6
5-4. Point source domestic municipal treatment
facilities . . . ... . . . . . 14-7
6-1. Summary of salinity (ppt) data for the
Pensacola Bay system during January through
September 1974 (Pensacola Bay data from the
University of West Florida) 14-8
6-2. Variables used in calculating the flushing
times of Escambia Bay during 1973 14-9
6-2 (cont.) Variables used in calculating the flush-
ing times of East Bay and Blackwater Bay
during 1973. . 14-9
6-2 (cont.) Variables used in calculating the
flushing times of Pensacola Bay during 1973. . 14-10
6-3. Summary of temperature (°C) data for the
Pensacola Bay system during January through
September 1974 (Pensacola Bay'data from the
University of West Florida). . . 14-11
6-4. Tide and wind conditions during the August
1973 dye study 14-12
6-5. Tide and wind- conditions during the Air
Products and American Cyanamid Dye Studies . . 14-13
6-6. Effluent dye concentrations during Air
Products Dye Study . . . . .. , . . . •,.-•"-• • • • 14-14
6-7. Effluent dye concentrations during the
American Cyanamid Dye Study 14-14
VI
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Appendix Page
7-1. Location of sediment sampling stations in the
Pensacola Bay system during 1973-1974 14-15
7-2. Sediment sampling stations and their habitat
type in the Pensacola Bay system 14-17
7-3. Physical and chemical data from core sampling
stations in the Pensacola Bay system,
Choctawhatchee Bay, and Panama City bays ... 14-18
7-4. Pesticides concentrations in the sediments of
the Pensacola Bay system during 1973 through
1971 , . 14-21
7-5. Nutrients (mg) present in the reactor water
by day number during the sediment nutrient
release study 14-21
8-1. Tide levels at U.S. Highway 90 bridge,
sampling periods, and wind vectors at
Pensacola Regional Airport during all studies
performed by US-EPA in the Pensacola Bay
system 14-23
8-2. Location, STORET retrieval information, and
parameters sampled for all sampling stations
occupied by US-EPA and University of West
Florida during the Escambia Bay Recovery
Study 14-27
8-3. Summary of bottom sampling depths (meters)
for Study I (April 13-15, 1973) and Study II
(April 19-21, 1973) 14-29
8-3 (cont.) Summary of bottom sampling depths
(meters) Study III (August 16-17, 1973) and
Study IV (August 23-25, 1973) 14-29
8-4. Summary of depth (meters) for the Pensacola
Bay system during January through September
1974 14-30
8-5. Water quality methods 14-31
8-6. Florida Standards for Class II and Class III
waters 14-35
8-7. Summary of total organic carbon (mg/1) data
for the Pensacola Bay system during January
through September 1974 (Pensacola Bay data
from University of West Florida) 14-38
vii
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Appendix Page
\
8-8. Summary of ammonia (mg/1) data for the
Pensacola Bay system during January through
September 1974 (Pensacola Bay data from the
University of West Florida) . . . 14-39
8-9. Summary of nitrate nitrite nitrogen (mg/1)
data for the Pensacola Bay system during
January through September 1974 (Pensacola
Bay data from the University of West
Florida) 14-40
8-10. Summary of organic nitrogen (mg/1) data for
the Pensacola Bay system during January
through September 1974 (Pensacola Bay data
from the University of West Florida) 14-41
8-11. Summary of total nitrogen (mg/1) data for the
Pensacola Bay system during January through
September 1974 (Pensacola Bay data from the
University of West Florida) 14-42
8-12. Summary of total phosphorus (mg/1) data for
the Pensacola Bay system during January
through September 1974 (Pensacola Bay data
from the Univeristy of West Florida) 14-43
8-13. Summary of dissolved orthophosphorus (mg/1)
data for the Pensacola Bay system during
January through September 1974 (Pensacola
Bay data from the University of West
Florida) 14-44
8-14. Summary of orthophosphorus (mg/1) data for
the Pensacola Bay system during January
through September 19.74 (Pensacola Bay data
from the University of West Florida) 14-45
8-15. Data base for calculation of initial PNI
values 14-46
8-16. Summary of dissolved oxygen data (mg/1) for
the Pensacola Bay system during January
through September 1974 14-47
8-17. Summary of dissolved oxygen percent saturation
data (%) for the Pensacola Bay system during
January through September 1974 14-48
8-18. Mean dissolved oxygen concentrations and
percent dissolved oxygen saturation during
the 1973 diel water quality surveys. . . . . . 14-49
Vlll
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Appendix Page
8-19. Ultimate biochemical oxygen demand data for
Station ER10 surface and bottom by date. . . . 11-53
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station EGLY surface and bottom by date. . 14-53
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station EKMP surface and bottom by date. . 14-54
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station ENNB surface and bottom by date. . 14-51
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station AGJI surface and bottom by date. . 14-55
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station EPRB surface and bottom by date. . 14-55
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station PEUE surface and bottom by date. . 14-56
8-19 (cont.) Ultimate biochemical oxygen demand data
for Station BFEI surface and bottom by date. . 14-56
8-20. Summary of turbidity (JTU) data for the
Pensacola Bay system during January through
September 1974 14-57
8-21. Locations of sampling stations during August
15 and November 20, 1974 turbidity studies . . 14-57
8-22. Turbidities in the Escambia, Blackwater and
Yellow Rivers during August 15 and November
20, 1974 14-58
9-1. Summary of chlorophyll a (mg/1) data for the
Pensacola Bay system during January through
September 1974 taken one foot below the
surface (Pensacola Bay data from the
University of West Florida). 14-59
10-1. Bimonthly distribution of otter trawl samples
by area and by station 14-60
10-2. Spatial distribution of fishes collected by
otter trawl in Escambia Bay, 1973-1974 .... 14-61
10-3. Bimonthly distribution of fishes collected by
otter trawl in Escambia Bay, 1973-1974 .... 14-62
10-:4. Bimonthly distribution of fishes collected by
seine in Escambia Bay, 1973-1974 14-63
IX
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Appendix Page
10-5. Spatial distribution of fishes collected by
seine in Escambia Bay, 1973-1974 . 14-64
10-6. Spatial distribution of shrimp (Penaeus spp.)
collected by otter trawl in Escambia Bay,
1973-1974. 14-65
10-7. Bimonthly distribution of shrimp (Penaeus
spp.) collected by otter trawl in Escambia
Bay, .1973-1974 14-65
10-8. Commercial landings of shrimp (Panaeus spp.)
from Escambia Bay, 1964-1973 14-65
10-9. Commercial landings of shrimp (Panaeus spp.)
from East Bay, 1964-1973 14-66
10-10. Commercial landings of shrimp (Panaeus spp.)
from Pensacola Bay, 1964-1973 14-66
10-11. Commercial landings of shrimp (Panaeus spp.)
from Choctawhatchee Bay, 1964-1973 14-67
10-12. Monthly distribution of fish kills in the
Pensacola Bay system, 1970-1974 14-68
10-13. Listing of the time, place and estimated size
of fish kills in the Pensacola Bay system,
1970 14-69
10-14. Total-length frequency of Gulf menhaden,
Brevoortia patronus, from Escambia Bay,
1973-1974 14-71
10-15. Total-length frequency of Atlantic bumper,
Chloroscombrus chysurus from Escambia Bay,
1973-1974 14-71
10-16. Total length frequency of sand seatrout,
Cynosian arenarius, from Escambia Bay,
1973-1974 14-72
10-17. Total-length frequency of spot, Leiostomus
xanthurus, from Escambia Bay, 1973-1974. . . . 14-73
10-18. Total-length frequency of Atlantic croaker,
Micropogon undulatus, from Escambia Bay,
1973-1974 14-74
11-1. Benthic macroinvertebrate sampling dates and
stations in the Pensacola Bay system 14-76
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Appendix . Page
11-2. Benthic macrofauna from ,the Pensacola Bay
system (E = Escambia Bay, A = East and
Blackwater Bay, and S = Santa Rosa Sound). . . 14-77
11-3. Shannon-Weaver (H1) diversity index values
for all benthic macro-fauna stations in the
Pensacola Bay system 14-82
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LIST OF TABLES
summary or inrormation acout major streamriow
gaging stations in the Escambia, Blackwater,
and Yellow River drainage basins, Florida. . .
Frequency distribution of wind direction and
velocity at Pensacola Regional Airport .... 4-3
4-2. Mean monthly wind velocities at Pensacola
Regional Airport 4-6
4-3. Total commercial landings of finfish and
shellfish in Escambia county, FL during
1964-1973 4-14
5-1. Effluent loadings from Container Corporation
of America, Brewton, AL 5-4
5-2. Summary of data collected at Monsanto
Chemical Co., American Cyanamid Co., and Air
Products and Chemicals Inc. by the U.S.
Environmental Protection Agency and its
predecessor agencies 5-7
5-3. Major industry discharges to the Main Street
Wastewater Treatment Plant 5-14
5-4. Summary of industrial and domestic-municipal
private point' sources of discharge into the
Pensacola Bay system by drainage area. .... 5-17
5-5. Average annual quantities of storm water
runoff expressed as unit values. . 5-20
5-6. Average non-point source pollutant discharges
into the esturarine reaches of the Pensacola
Bay system 5-20
6-1. Summary of the bathymetry of the Pensacola
Bay system ..... 6-3
6-2. Summary of information about major streamflow
aaaino stations in the Kscamhia. Rlarkwa-hpr.
6-3
6-3. Mean annual discharge of the Escambia River at
Century, Florida for water years 1935 through
1974 6-7
6-4. Total flows into the Pensacola Bay system. . . 6-8
6-5. Estimates of flows in the Escambia River
xii
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Table Page
delta tributaries from 1973 to 1974. 6-11
6-6. Flushing characteristics of the Pensacola Bay
system during high (Studies I and II) and low
(Studies III and IV) river inflow periods in
April and August 1 973, respectively 6-29
6-7. Reduction in flushing time (days) due to tidal
mixing in the Pensacola Bay system during
1973 6-29
6-8. Water temperature date (°C) for 1973
intensive water quality studies 6-33
6-9. Summary of wind conditions during Air
Products and American Cyanamid dye studies . . 6-41
6-10. Environmental conditions during tracer dye
studies in Mulatto Bayou performed on June
24-25, 1974 and July 1-2, 1974. Weather data
collected at Pensacola Regional Airport (U.S.
Department of Commerce, 1972-1974) 6-53
7-1. Percent of mud in sediments (top 15 cm) from
central basins of six northwest Florida bays . 7-9
7-2. Percent volatile organics in surface sediments
in northeast Gulf of Mexico bays and sounds. . 7-13
7-3. Total phosphorus, organic nitrogen, and
organic carbon in mud sediments from
northwest Florida bays 7-17
7-4. Lead concentrations in surface sediments of
selected bays 7-23
7-5. Zinc concentrations in surface sediments of
selected bays 7-23
7-6. Chromium concentrations in surface sediments
of selected bays 7-23
7-7. Cadmium concentrations in surface sediments
of selected bays 7-23
7-8. Copper concentrations in surface sediments of
selected bays 7-25
o
7-9. Manganese concentrations in surface sediments
of selected bays 7-25
7-10. Nickel concentrations in surface sediments of
XI 0.1
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Table Page
selected bays 7-25
7-11. Aluminum concentrations in surface sediments
of selected bays 7-25
7-12. Iron concentrations in surface sediments of
selected bays 7-28
7-13. Cobalt concentrations in surface sediments of
selected bays 7-28
7-14. Vanadium concentrations in surface sediments
of selected bays 7-28
7-15. Titanium concentrations in surface sediments
of selected bays 7-28
7-16. Barge channel sediments, Escambia Bay, Florida
from Highway 90 bridge to channel entrance . . 7-29
7-17. Heavy metal concentrations near and in the
channel at two adjacent stations in Escambia
Bay, 1971. 7-32
7-18. Maximum amount (mg) and rates of release
(mg/m2/day) found in the nutrient release
study. . 7-36
7-19. Comparison of sediment nitrogen release data
with microbial activity data . . . . 7-39
7-20. Comparison of percent organic and nitrogen
content of sediment with rates of release and
total release of total nitrogen 7-39
7-21. Summary of sediment microbial activity ..... 7-46
8-1. Environmental conditions during water quality
studies. . . . 8-3
8-2. Mean total organic carbon concentrations in
the Pensacola Eay system during each date
sampled in 1974 (Pensacola Bay data from the
University of West Florida) 8-6
8-3. Statistical comparison of mean total organic
carbon concentrations in Escambia Bay with
those in other components of the Pensacola Bay
system during January through September 1974
(Pensacola Bay data from the University of
West Florida) 8-8
xiv
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Table Page
8-4. Mean total organic carbon concentrations in
the Pensacola Bay system during 1973 diel
water quality surveys. . . . . . . . . . . . . 8-9
8-5. Comparison of mean total organic carbon con-
centrations in upper Escambia Bay between
September, 1969 water quality surveys and the
surveys in 1973 and 1974 ..„„.. 8-11
8-6. Mean nitrogen concentrations in the Pensacola
Bay system during each date sampled in 1974
(Pensacola Bay data from University of West
Florida) 8-14
8-7. Mean nitrogen concentrations in the Pensacola
Bay system during January through September
1974 (Pensacola Bay data from University of
West Florida) 8-18
8-8. Predicted percent of actual surface total
nitrogen concentrations due to Air Products
and Chemicals, Inc., and American Cyanamid
Co 8-19
8-9. Mean nitrogen concentrations in the Pensacola
Bay system during the 1973 diel water quality
surveys 8-23
8-10. Comparison of mean nitrogen concentrations in
upper Escambia Bay between the September
1969 water quality survey and the studies in
1973 and 1974 8-23
8-11. Mean total and orthophosphorus concentrations
in the Pensacola Bay system during January
through September 1974 (Pensacola Bay data
from the University of West Florida) 8-29
8-12. Mean total phosphorus (T-P) and ortho-
phosphorus (O-P) concentrations (mg/1) in the
Pensacola Bay system during January through
September 1974 (Pensacola Bay data from the
University of West Florida) 8-29
8-13. Mean total and orthophosphorus concentrations
in the Pensacola Bay system during the 1973
diel water quality surveys 8-33
8-14. Comparison of mean total and orthophosphorus
concentrations (mg/1) in upper Escambia Bay
between the September 1969 water quality
surveys and the studies in 1973 and 1974 . . . 8-35
xv
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Page
Mean PNI values for pooled data for the
Pensacola Bay system during studies in April
(I and II) and August (III and IV) 1973. The
number of observations are in parenthesis. . . 8-41
8-16. Percent of PNI values greater than or equal
to 9.0 for the Pensacola Bay system and
Choctawhatchee Bay (Pensacola Bay data from
the University of West Florida). . . . . „ . . 8-46
8-17. Statistical comparison of mean PNI values in
the Pensacola Bay system during September 1969
and the given dates in 1973 and 1974 . . . . . 8-a6
8-18. Statistical comparison of mean PNI values in
upper Escambia Bay during September 1969 and
the given dates in 1973 and 1974 ....... 8-47
8-19. Statistical comparison of mean PNI values in
Escambia Bay with other Gulf Coast estuaries . 8-47
8-20. Frequency distribution of dissolved oxygen
concentrations in Escambia and East Bays
during January through September 1974 8-52
8-21. Dates of, and environmental conditions during,
the 1973 diel water quality surveys. . . . , . 8-55
8-22. Frequency of dissolved oxygen concentrations
less than 4.0 mg/1 during Studies III and IV
(August 1973) . . . 8-55
8-23. Mean ultimate biochemical oxygen demand data
for Escambia Bay stations during January
through September 1974 ........ „ - = . 8-65
8-24. Mean ultimate biochemical oxygen demand data
at Escambia Bay stations for each date
sampled during January through September 1974= 8-66
8-25. Ultimate biochemical oxygen demand data for
Choctawhatchee Bay on September 12, 1974 . . . 8-69
\,
8-26. Ultimate biochemical oxygen demand data for
Escambia Bay stations during the April 1973
diel water quality surveys „ . . . 8-70
8-27. Ultimate biochemical oxygen demand data for
Escambia Bay stations during the August 1973
water quality surveys 0... 8-70
8-28. Total and fecal coliform data (densities per
xvi
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Table Page
100 ml) for oyster harvesting Area 32 during
the 1970-1971 season 8-73
8-29. Total and fecal coliform data (densities per
100 ml) for oyster harvesting Area 32 during
the 1971-1972 season 8-73
8-30. Summary of total and fecal coliform data
(densities per 100 ml) for the Pensacola Bay
system during 1973 8-76
8-31. Summary of total and fecal coliform data
(densities per 100 ml) for the Pensacola Bay
system during 1974 8-78
8-32. Summary of total and fecal coliform data
(densities per 100 ml) for Pensacola Bay
during 1974 (Pensacola Bay data from
University of West Florida) 8-80
8-33. Percent of the samples in turbidity ranges
during the 1974 water quality studies 8-85
8-34. Effective weir discharges for the Escambia,
Yellow, and Blackwater Rivers 8-87
8-35. Comparison of water quality data for the
Escambia River at Century, Florida, and the
Yellow River at Milligan, Florida (data from
U.S. Geological Survey) 8-90
8-36. Nutrient values in the Escambia River
(Station ER10) by date during January through
September 1974 8-90
8-37. Summary of nutrient values in the Escambia
River (Station ER10) during January through
September, 1974 and estimated nutrient loads
entering the Pensacola Bay system from the
Escambia River and from all rivers 8-92
8-38. Summary of nutrient contributions to the
Pensacola Bay tributary rivers, point sources,
and non-point sources 8-92
10-1. Summary of the number of fishes captured with
otter trawl and seine during the bimonthly
survey in Escambia Bay, 1973-1974 10-6
«
10-2. Seasonal means and significance of species
diversity indices as determined by Student-
Newman-Keuls multiple range test. Means not
-------
Table Page
underlined are significantly different from
each other at the 95% level of confidence. . . 10-12
10-3. Temporal and spatial distribution of fish
kills in the Pensacola Bay system, 1970-74 . . 10-21
10-4. Summary of two creel surveys of freshwater
sports fishery on the lower Escambia River,
April 25 to May 30, 1970 and May 4 to June 2,
1974 10-28
10-5. Summary of commercial landing of spotted
seatrout, Cynoscion nebulosus, along the west
coast of Florida and Escambia County, 1964-73. 10-31
10-6. Comparison of the average bimonthly trawl
catches of spot from three estuaries in the
northern Gulf of Mexico 10-31
10-7. Summary of commercial landings of spot,
Leiostomus xanthurus, along the west coast
of Florida and Escambia County, 1964-73. ... 10-32
10-8. Comparison of the average bimonthly trawl
catches of Atlantic croaker from three
estuaries in the northern Gulf of Mexico . . . 10-32
10-9. Summary of commercial landing of Atlantic
croaker, Micropogon undulatus, along the west
coast of Florida and Escambia County, 1964-73. 10-34
10-10. Summary of commercial landings of striped
mullet, Mugil cephalus, along the west coast
of Florida and Escambia County, 1964-73. . . . 10-34
10-11. Summary of commercial landings of Spanish
mackerel, Scomberomorus maculatus, along the
west coast of Florida and Escambia County,
1964-75. 10-36
10-12. Sediment composition at the mud, sand, and
shell stations 10-44
10-13. Comparison of the number of fishes caught by
otter trawl over oyster-shell and mud bottoms
in Escambia Bay, 1973-74 10-45
. .•, (.
10-14. Comparison of the number of penaeid shrimp
caught by otter trawl over oyster-shell and
mud bottoms in Escambia Bay, 1973-74 10-48
11-1. Habitats and related macroinvertebrate data
XVlll
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Table" Page
in Escambia. Bay .for the sununers pf 1973 and
1971 . . 11-11
11-2. Seasonal comparison of benthic macroinverte-
brates at stations located on G and O
transects in Escambia Bay during 1973 to
1974 . . . 11-11
11-3. Comparison of biomass, species, and number of
individuals in upper and lower Escambia Bay. . 11-12
11-U. Comparison of biomass, species, and number
of individuals near the east shore and west
shore of Escambia Bay 11-12
11-5. Macroinvertebrate data for sand stations
sampled in the Pensacola Bay system during
the winter of 1974 11-22
xix
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LIST OF FIGURES
Figure Page
4-1. Map of drainage area 4-2
4-2. Wind roses at Regional Airport, Pensacola,
Florida for October 1972 to September 1973,
and October 1973 to September 1974 4-5
4-3. Total monthly precipitation records at
Pensacola, Florida and Andalusia, Alabama
for October 1972 - September 1974 4-7
4-4. Mean monthly air temperature at Regional
Airport, Pensacola, Florida for October 1972
through September 1974 4-7
4-5. Trends in the commercial landings of finfish
and shellfish in Escambia County, Florida,
1964-1973. . 4-13
5-1. Map of location of point sources 5-2
5-2. Monsanto Chemical Company net chemical oxygen
demand waste load discharged into the
Escambia River 5-6
5-3. Average monthly BODS effluent loads (based on
company self-monitoring data) 5-8
5-4. Average monthly total nitrogen effluent loads
(based on company self-monitoring data).... 5-8
5-5. Average monthly total phosphorus effluent
loads (from company self-monitoring data)... 5-10
5-6. Average monthly cyanide effluent loading from
American Cyanamid Co 5-10
6-1. Map of the Pensacola Bay system 6-2
6-2. Mean, high monthly mean, and low monthly mean
discharges for the Escambia River at Century,
Florida for water years 1960 through 1974. . . 6-6
6-3. Mean monthly, maximum daily, and minimum
daily discharge for the Escambia River at
Century, Florida during water years 1970
through 1974 6-6
xx
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Figure Page
6-4. Map of the Escambia River delta showing
location of discharge measurement stations . . 6-10
6-5a. Tides at U.S. 90 bridge during January 13-28>
1974 6-14
6-5b. Tides at U.S. 90 bridge during September 1-18,
1974 6-14
6-6a. Mean tide levels during January through
September 1974 at U.S. 90 bridge 6-15
6-6b. Mean tide ranges during January through
September 1974 at U.S. 90 bridge 6-15
6-7. Mean surface and bottom salinities in the
Pensacola Bay system during January through
September 1974 (Pensacola Bay data from the
University of West Florida) 6-20
6-8. Mean salinities of the components of the
Pensacola Bay system during January through
September 1974 and the total effective
discharge of the Escambia Piver and all
tributaries to the Pensacola Bay system
(Pensacola Bay data from the University of
West Florida) 6-22
6-9. Salinity and tide variation at Stations ENNBr
AJFD, and POOH during the August 1973 water
quality studies 6-23
6-10. Salinities (ppt) in Choctawhatchee Bay on
September 12, 1974 6-25
6-11. Salinity-depth profiles at Stations P05, ENNB,
and AGJI during water quality studies
performed in January through September 1974. . 6-27
6-12. Mean salinity-depth profiles over a tidal
cycle at stations near the center of the
mouths of bays in the Pensacola Bay system
during 1973 6-30
6-13. Mean temperature in Escambia Bay and Pensacola
Bay for each study performed in 1974
(Pensacola Bay data from the University of
West Florida) 6-32
a
6-14. Mean surface and bottom temperatures (°C) for
stations sampled during January through
September 1974 (Pensacola Bay data from the
xxi
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Figure Page
University of West Florida) 6-32
6-15. Isopeths of the run on which major surface
dye peaks arrived at the given location.
Sampling depth 0.3 m . . . . . . . . . . . . . 6-35
6-16. Locations of stations sampled during the Air
Products and American Cyanamid Dye Studies . . 6-38
6-17a. Salinity^profile during Air Products Dye Study
at 1820 to 2000 hrs on August 26, 1974 .... 6-42
6-17b. Salinity profile during American Cyanamid Dye
Study at 0900 to 1030 hrs on September 18,
1974 6-42
6-18a. Steady state concentration (pg/1) at a depth
of 0.3 m during the Air Products Dye Study
for a discharge of 1,000 kg/day 6-45
6-18b. Steady state concentrations (pg/l) at a depth
of 0.9 m during the Air Products Dye Study
for a discharge of 1,000 kg/day 6-45
6-19. Instantaneous surface dye concentrations
(pg/1) in Escambia Bay per 1,000 kg/day
discharged by the Air Products plant 6-46
6-20a. Steady state concentrations (pg/1) at a depth
of 0.3 m during the American Cyanamid Dye
Study for a discharge of 1,000 kg/day 6-47
6-20b. Steady state concentrations (pg/1) at a depth
of 1.2 m (4 ft) during the American Cyanamid
Dye Study for a discharge of 1,000 kg/day. . . 6-47
6-21a. Percent of steady state dye mass in segments
of Escambia Bay during the Air Products Dye
Study. .- 6-49
6-21b. Percent of steady state dye mass in segments
of Escambia Bay during the American Cyanamid
Dye Study v 6-49
6-22 Mean water transport over a tidal cycle for
the upper layer of the Pensacola Bay system. . 6-51
6-23. Current speed on June 12-13, 1974 in
Pensacola Bay. ....... '•'."' . . 6-51
6-24. Circulation patterns in Mulatto Bayou
derived from tracer dye studies performed
xxn
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Figure . Page
during June and July, 1974 6-53
7-1. Sediment core sample locations in the
Pensacola Bay system . . 7-3
7-2. Sediment core sample locations in
Choctawhatchee Bay, Florida, 1974 7-3
7-3. Sediment core stations in Panama City bays . . 7-4
7-4. Bottom profiles and station location along
benthic transects in Escambia Bay 7-6
7-5. Classification of surface sediments (top 15
cm) in Escambia Bay during 1973 7-8
7-6. Grain size distribution of the sand fraction
in Escambia Bay during 1973 7-8
7-7. Sand-silt-clay sediment distribution in three
northern Gulf Bay systems 7-10
7-8. Distribution of surface sediment (top 15 cm)
volatile organics in Escambia Bay during
1973 7-11
7-9. Biological oxygen demand (BOD5) in surface
sediments (top 15 cm) in Escambia Bay during
1973-1974 7-15
7-10. Phosphorus concentrations (mg/g) in surface
sediments (top 15 cm) in Escambia Bay during
19 73-1974. 7-16
7-11. Total organic nitrogen (mg/g) in surface
sediments (top 15 cm) in Escambia Bay during
1973-1974 7-19
7-12. Organic carbon (mg/g) distribution in surface
sediments (top 15 cm) in Escambia Bay during
1973 7-19
7-13. Organic carbon (mg/g) distribution in surface
sediments (top 15 cm) in the Pensacola Bay
system during 1974 7-20
7-14. Polychlorinated biphenyls (Aroclor 1254,
pg/kg). distribution in surface sediments (top
15 cm) in the Pensacola Bay system during
1974 7-20
7-15. Barge channel sediment station locations in
XXlll
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Figure Page
Escambia Bay 7-30
7-16. Nutrient release study station locations in
Escambia Bay 7-34
7-17. Sediment nutrient release study apparatus. . . 7-34
7-18. Plots of total milligrams of total nitrogen
against day number for each station (total
nitrogen = TKN + NO3NO2) 7-35
7-19. Plots of rates of release and total milligrams
released of total nitrogen against sediment
TKN concentrations 7-40
7-20. Microbial activity (by TPF reduced per gram
of dry sediment) in the Pensacola Bay system
during 1974. . 7-43
8-1. Classification of the Pensacola Bay system
under the Florida Water Quality Standards. . . 8-4
8-2. Mean total organic carbon (mg/l-C) in the
Pensacola Bay system during January through
September 1974. (Pensacola Bay data from the
University of West Florida) 8-7
8-3. Total organic carbon (mg/l-C) in
Choctawhatchee Bay on September 12, 1974 . . . 8-10
8-4. Mean total organic carbon (mg/l-C) in
Escambia Bay during September 23 to September
25, 1969 8-10
8-5. Mean nitrate-nitrite nitrogen (mg/l-N) in the
Pensacola Bay system during January through
September 1974. (Pensacola Bay data from the
University of West Florida). . . . 8-15
\
8-6. Mean ammonia (mg/l-N) in the Pensacola Bay
system during January through September 1974
(Pensacola Bay data from the University of
West Florida) 8-15
8-7. Mean organic nitrogen (mg/l-N) in the
Pensacola Bay system during January to
September 1974 (Pensacola Bay data from the
University of West Florida) 8-16
8-8. Predicted steady state total nitrogen con-
centrations in pg/1 per 953 kg/day (2100 ppd)
and 1314 kg/day (2897 ppd) discharged by
XXIV
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Figure Page
American Cyanamid Co. and Air Products and
Chemicals, Inc., respectively. 8-17
8-9. Ammonia (mg/l-N) in Choctawhatchee Bay on
September 12, 1974 8-20
8-10. Nitrate-nitrite (mg/l-N) in Choctawhatchee
Bay on September 12, 1974 8-20
8-11. Organic nitrogen (mg/l-N) in Choctawhatchee
Bay on September 12, 1974. . . 8-21
8-12. Total nitrogen (mg/l-N) in Choctawhatchee Bay
on September 12, 1974 8-21
8-13. Mean ammonia in Escambia Bay during September
23 to September 25, 1969 8-24
8-14. Mean nitrate-nitrite (mg/l-N) in Escambia Bay
during September 23 to September 25, 1969. . . 8-24
8-15. Mean organic nitrogen (mg/l-N) in Escambia
Bay during September 23 to September 25, 1969. 8-25
8-16. Mean dissolved orthophosphorus (mg/l-P) in
the Pensacola Bay system during January
through September 1974 (Pensacola Bay data
from the University of West Florida) 8-27
8-17o Mean orthophosphorus (mg/l-P) in the
Pensacola Bay system during January through
8-27
O*" 1 O o
8-19.
8-20.
8-21.
8-22.
8-23.
Mean total phosphorus (mg/l-P) in the
Pensacola Bay system during January through
September 1974 (Pensacola Bay data from the
Dissolved orthophosphorus (mg/l-P) in
Choctawhatchee Bay on September 12, 1974 . . .
Total phosphorus (mg/l-P) in Choctawhatchee
Bay on September 12, 1974
Orthophosphorus (mg/l-P) in Choctawhatchee
Bay on September 12, 1974
Mean total phosphorus (mg/l-P) in Escambia
Bay during September 23 to September 25, 1969.
Mean orthophosphorus, (mg/l-P) in Escambia Bay
during September 23 to September 25, 1969. . .
8-28
8-30
8-30
8-31
8-34
8-34
XXV
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Figure Page
8-24. Cumulative frequency distribution of initial
PNI values and PNI values calculated from
multiple regression model 8-38
8-25. Mean surface and bottom PNI values for samples
collected during September 23 to September 25,
1969 (USDI, 1970).... 8-40
8-26. PNI values at Station ER10 during the 1974
water quality studies 8-43
8-27. Mean PNI values in the components of the
Pensacola Bay system during the 1974 water
quality studies 8-43
8-28. Mean PNI values in the Pensacola Bay system
at stations sampled during the 1974 water
quality studies (Pensacola Bay data from the
University of West Florida) 8-44
8-29. Surface and bottom values of PNI in
Choctawhatchee Bay on September 12, 1974 . . . 8-44
8-30. Mean dissolved oxygen concentrations (mg/1)
in the Pensacola Bay system during January
through September 1974 8-50
8-31. Mean values of percent dissolved oxygen
saturation in the Pensacola Bay system during
January through September 1974 8-50
8-32. Mean dissolved oxygen concentrations in
Escambia and East Bays during each study
performed in January through September 1974. . 8-51
8-33. Mean values of percent dissolved oxygen
saturation in Escambia and East Bays during
each study performed in January through
September 1974 8-51
8-34. Bottom dissolved oxygen and salinity levels
during January through September 1974 at
selected stations in the Pensacola Bay
system. (Pensacola Bay data from the
University of West Florida) 8-53
8-35. Dissolved oxygen concentrations during Studies
III and IV (August 1973) for selected stations
in the Pensacola Bay system (Pensacola Bay
data from the University of West Florida). . . 8r58
8-36. Mean surface and bottom dissolved oxygen
XXVI
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concentrations in Escambia Bay during
September 23 to September 25, 1969 (USDI,
1970) 8-59
8-37. Dissolved oxygen concentrations in
Choctawhatehee Bay on September 12, 1971 . . . 8-61
8-38. Values of percent dissolved oxygen saturation
in Choctawhatchee Bay on September 12, 1974. . 8-61
8-39. Mean ultimate BOD (mg/1) in Escambia, East,
and Blackwater Bays during January through
September 1974 8-64
8-40. Mean bottom ultimate BOD (mg/1) and dissolved
oxygen (mg/1) values in Escambia Bay plotted
against each date sampled in 1974 8-67
8-41. Typical long-term BOD curves from the 1974
water quality studies (• = NLINBOD results). . 8-67
8-42. Ultimate BOD (mg/1) values in Choctawhatchee
Bay on September 12, 1974 8-69
8-43. Mean ultimate BOD (mg/1) in Escambia Bay
during April 1973 8-71
8-44. Mean ultimate BOD (mg/1) in Escambia Bay
during August 1973. . 8-71
8-45. Locations of total and fecal coliform bacteria
sampling stations (four letter stations are
EBRS 1973-74, numerals preceded by P are
University of West Florida, numeral only is
the State of Florida, Shellfish Area #32) . . . 8-75
8-46. Mean turbidity in Escambia, East and
Blackwater Bays during each study performed
during January through September 1974, and
total effective flow into the Pensacola Bay
system during each study 8-84
8-47. Mean turbidity in Escambia, East and
Blackwater Bays during January through
September 1974 8-84
8-48. Turbidity values in Choctawhatchee Bay on
September 12, 1974 8-86
8-49. Mean turbidity values in the Pensacola Bay
system drainage basin during August 15, 1974
and November 20, 1974 8-88
xxvn
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Figure Page
9-1. Pensacola Bay system stations and chlorophyll
a averages (pg/1) from January to September
1974 (Pensacola Bay data from University of
West Florida) 9-3
9-2. Chlorophyll a seasonal concentrations in
Escambia, East and Blackwater Bays 9-5
9-3. Chlorophyll a (»jg/l) averages from January to
September 1974 at stations in Choctawhatchee
Bay 9-5
10-1. Study area in Escambia Bay and adjacent
waters 10-3
10-2. Annual mean catch of fishes per trawl sample
by number and by percent for each study area,
1973-1974 10-9
10-3. Temporal distribution of species diversity
index (H1) in three esturine areas, 1973-1974. 10-13
10-4. Relationship between species diveristy (H1)
and distance of three stations (1.6 km = 1
mile) from major point sources of pollution
in Escambia Bay 10-14
10-5. Temporal distribution of species diversity
index (D) in three estuarine areas,
1973-1974 10-14
10-6. Temporal distribution of species diversity
index (J) in three estuarine areas,
1973-1974 10-16
10-7. Water temperature and salinity readings on
the bottom for Trawl Stations III, VI, and
VIII in the open waters of Escambia Bay and
Station IX in Mulatto Bayou, 1973-1974 .... 10-17
10-8. Average catch of penaeid shrimp per trawl
sample (catch-per-unit-effort) for the
various estuarine areas in Escambia Bay,
1973-1974 10-19
10-9. Average catch of penaeid shrimp per commercial
fishing trip in the Pensacola Bay system
and Choctawhatchee Bay (control), 1964-1973. . 10-19
10-10. Location of fish kill sites in the Pensacola
Bay system, 1970-1974. . 10-22
xxviii
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Figure Page
10-11. Annual distribution of fish kills in
Escambia Bay sub-system arid total Pensacola
Bay system, 1970-1974. ............ 10-26
10-12. Study area and sampling sites in Escambia Bay. 10-42
10-13. The average monthly catch of pelagic and
benthic fishes over mud and shell bottoms. . . 10-46
11-1. Fathometer tracing of transect 'S« showing
the three sampling zones 11-2
11-2. Benthic macr©invertebrate station locations
in Escambia Bay 11-3
11-3. Benthic macroinvertebrate station locations
in the Pensacola Bay system 11-4
11-4. Cumulative curves of species taken per grab
at sand shelf stations with the Ponar dredge
during winter of 1974 in the Pensacola Bay
system ......... 11-9
12-1. The Pensacola Bay system and revegetation
sites in Escambia Bay. 12-2
12-2. Escambia Bay grass beds, 1949-1974 ...... 12-4
12-3. The north shore of Pensacola Bay with ship
terminal and the Pensacola Bay bridge,
1951-1974 12-6
12-4. The south shore of East Bay from the
Pensacola Bay bridge to Tom King Bayou,
1949-1974 12-8
12-5. The northeast shore of East Bay from Tom King
Bayou to Escribano Point, 1949-1974 12-9
XXIX
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1 - INTRODUCTION
GENERAL
The Escambia Bay Recovery Study (EBRS) was established when
public concern over the degradation of the waters of Escambia
Bay, Florida - exemplified by massive fish kills, abrupt declines
in commercial and sports fisheries, and waters closed to body
contact sports - was translated into action by Federal and State
governments. ERBS consisted of a multidisciplinary team of
Federal scientists, located at the U.S. Environmental Protection
Agency (USEPA), Gulf Breeze Environmental Research Laboratory,
Gulf Breeze, Florida, who were under the direction of the USEPA,
Region IV, Surveillance and Analysis Division, Athens, Georgia.
A steering committee made up of groups concerned with problems in
Escambia Bay assisted (Appendix 1-1) .
The major goal of the study was to determine methods of
accelerating the recovery of Escambia Bay over and above reducing
waste discharges into the bay. The specific objectives of the
Escambia Bay Recovery Study were to:
• Document conditions in the Pensacola Bay system under
various environmental situations,
• Determine the significant mechanisms causing degradation
to the ecosystem of Escambia Bay,
• Determine the feasibility of restoration schemes such as
diverting a portion of the Escambia River into northeast
Escambia Bay, removing sediments from Escambia Bay,
revegetating the bay, and altering portions of the
sediments.
BACKGROUND
General
Within the past 25 years aquatic conditions in the Escambia
River have changed from healthy to stressed, and have
subsequently improved. Before major industrial plants located in
the area, the lower Escambia River exhabited a healthy aquatic
condition, free from the effects of pollution (Academy of Natural
Sciences of Philadelphia, 1953). By 1962, after the
establishment of major industrial waste discharges, fish kills
and Sphaerotilus growths near the Florida State line were related
to industrial waste discharges (Wastler and Kittrell, 1962).
Between 1960 and 1968, stressed aquatic conditions, as indicated
by declining fisheries and altered macroinvertebrate communities
1-1
-------
in the Escambia River, continued to exist (Schneider,
Florida State Board of Health, 1963, 1966, 1968; Blanchard,
1968). Signs of improvement were noted in 1972 when the water
quality of the Escambia River was found comparable to unpolluted
northwest Florida streams (USEPA, 1972) .
Stressed aquatic conditions in Escambia Bay have been of
considerable concern during the past few years. In 1958,
bioassays indicated industrial waste discharges in northeast
Escambia Bay adversely affected aquatic organisms (Florida State
Board of Health, 1958). Hopkins (1969, 1973) concluded the
assimilative and exchange capacities of Escambia Bay have been
exceeded, causing excessive phytoplankton organisms and diurnal
depletion of dissolved oxygen which have led to fish kills. Weak
circulation in the bay and waste discharges were found to have
contributed to stressed aquatic conditions by USDI (1970) ; USEPA
(1971d); and Florida State Board of Health (1969). High
concentrations of PCB were found in bay oysters during April 1969
(Duke et al., 1970; Nimmo et al. 1971a, 1971b) and, consequently,
stresses due to toxic materials also contribute to problems in
the bay. A systems model of Escambia Bay developed by Schomer
(1975), which required many assumptions, indicated that man-
induced inputs to the system are likely to remain for a long
time.
Weak circulation occurs throughout the entire Pensacola Bay
system due to low tidal energy (E11J.S, 1969) . Strong vertical
stratification was found to contribute to weak circulation and
low dissolved oxygen concentrations in bottom waters of the
Pensacola Bay system during a study by Gallagher (1971). Aquatic
conditions in most of Pensacola Bay were acceptable, but degraded
conditions were found near the Pensacola waterfront (Florida
State Board of Health, 1969, and Baseline Incorporated, 1973) « A
study of near-shore waters of the Gulf of Mexico, including
limited work in the Pensacola Bay system, indicated better
flushing in Pensacola Bay than in other components of the bay
system (Escarosa I, 1973).
The most massive fish kills have occurred in Mulatto Bayou
and Bayou Texar. In Mulatto Bayou, low dissolved oxygen and
possible algal toxicity, resulting from disturbances such as
dredging and filling and artifically enriched waters,, were
considered major factors in the fish kills (USDI, 1969; USDI,
1970, and Livingston et al., 1972). Bayou Texar receives silt,
overflow from sewage lift stations, and runoff from fertilized
lawns and is rapidly becoming a shallow system unfit for
recreational and aesthetic purposes (Moshiri et al., 1972; and
Hannah et al., 1973).
Federal Involvement
The historical responsibility of the Federal Government in
dealing with environmental problems in Escambia Bay led to the
establishment of EBRS within USEPA. Federal involvement first
1-2
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occurred in 1962 when the Conference on Interstate Foliation of
the Conecuh-Escambia River was convened by the U.S. Public Health
Service (USPHS, presently USEPA) at the request of the State of
Florida (USPHS, 1962). The major conclusion of the conference
was that the pollution of interstate waters, as subject to
abatement under the Federal Water Pollution Control Act, was not
occurring in the Conecuh-Escambia River system at the time of the
conference. Solutions to the problems were indicated to be the
responsibility of official State water pollution control
agencies, and assistance from the USPHS was offered.
The Federal Water Pollution Control Administration (FWPCA
presently USEPA) was again involved with Escambia Bay when in
August 1969 the Southeast Region's technical assistance was
requested in evaluating interstate and intrastate pollution from
waste sources entering the Conecuh-Escambia River downstream from
Brewton, Alabama, and Escambia Bay near Pensacola, Florida. An
investigation of waste sources in Florida and Alabama, and a
detailed study of the receiving waters, were conducted during the
period of September 23 - 25, 1969 and October 22 - 30, 1969.
Based on the results of these studies, a conference in the matter
of pollution of the interstate waters of the Escambia River Basin
(Alabama - Florida) and the intrastate portions of the Escambia
Basin within the State of Florida, was convened under the
provisions of Section 10 of the Federal Water Pollution Control
Act, as amended (33 USC 466 et seq) . Three sessions of the
conference were held in January 1970 (USDI, 1970a), February 1971
(USEPA, 1971c), and January 1972 (USEPA, 1972e). The
recommendations of the conference are presented in Appendix 1-2.
ACKNOWLEDGMENTS
We thank
agencies:
the following individuals, institutions, and
Surveillance and Analysis Division, EPA, Region IV, for their
assistance in planning the study, analyzing samples, and for
reviewing the report. The Enforcement and Water Divisions, EPA,
Region IVg for providing field personnel during studies.
Dr. Tom Duke, Director, Gulf Breeze Environmental Research
Laboratory and Staff for the infinite amount of assistance
provided during our stay at their facility.
Dr. Tom Hopkins, Chairman, Faculty of Biology, University of
West Florida, Messrs. Ken Adams and Mike Ziegler, Ms. Debby Reik
and other Sea Grant Staff members who assisted us in the field
studies and in the laboratory.
Mr. Bob Dillard, Region Administrator, Mr. Phil Doherty,
Regional Engineer, and Mr. Walt Flanigan, Florida Department of
Environmental Regulation and the Staff for cooperation and
assistance in field studies and laboratory assistance.
1-3
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The Bream Fisherman Association of Pensacola for their
assistance in the revegetation studies and the stocking of
striped bass fry in the Escambia River.
Mr. Bill Young, Florida Department of Environmental
Regulation, for supplying us with historical records of fish
kills in the Pensacola Bay system.
The South Carolina Wildlife and Marine Resources Department
for providing the Striped Bass fry that were stocked in the
Escambia River.
The U.S. Geological Survey, Tallahassee, Florida for
providing provisional streamflow data and water quality data.
Dr. Marian H. Pettibone, U. S. National Museum; Dr. E. L.
Bousfield, National Museum of Canada; Dr. Henry Kritzer, FSU
Marine Laboratory, Dr. W. H. Heard, FSU Biological Science
Department; and Mr. John R. Hall, NMFS, Panama City, Florida for
assistance in the confirmation and identification of certain
macroinvertebrate species.
Monsanto Chemical Corporation, Air Products and Chemicals,
Inc., and American Cyanamid Co. for providing their water quality
data.
Dr. Ralph D. Harkins, Environmental Protection Agency, Robert
S. Kerr Environmental Research Laboratory, Ada, Oklahoma for
providing the basic computer program used in the calaculation of
PNI values.
Mr. Don Lawhorn, EBRS, for assisting in field studies and for
maintaining field equipment in excellent condition.
Mrs. Cathrine Willard, EBRS, for typing this report and
performing secretarial duties for the project. Mrs. Veronica
O'Hearn, EBRS, for performing secretarial duties. Mrs. Elizabeth
Korhonen, SAD, and Mrs. Elizabeth Dempsey, Water Division, for
assisting in typing this report.
Mr. Roy Weimert (SAD) for preparing drawings for the report.
The following part time employees of EBRS:
John C. Wright Cynthia Nametz
Mahlon Doug Sellers Marvin Kaplan
Diane C. Ricksecker James A. Harper
Paul G. Johnson William L. Howell
Steven B. Dubose Rodney A. Smith
James E. Pritchett William T. Dungan
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2 - SUMMARY
The major goal of this study was to determine methods of
accelerating the recovery of Escambia Bay over and above reducing
waste discharges into the bay. To accomplish this, studies were
performed in the entire Pensacola Bay system. The study period
was October 1972 through September 1974.
AREA DESCRIPTION
Escambia Bay is part of the Pensacola Bay system which also
includes East, Blackwater, and Pensacola Bays (Figure 4-1). The
total surface area of the bay system is 373 km* (144 mi2) . The
drainage area of the bay system consists of 17,550 km2 (6,778
mi2) in Alabama and Florida. Major tributaries to the system are
ths Escambia, Blackwater, and Yellow Rivers.
Seasonal variation of wind, air temperature, and
precipitation have a significant effect on the bay system.
Prevailing winds during the study period were from the northeast
with velocities between 8.4 and 17.6 km/hr (4.5 to 9.5 k).
Annual precipitation was above normal during the first year of
the study period and about normal during the second year of the
study period. Mean monthly temperatures were slightly higher
than normal during the study period.
POLLUTION SOURCES
Pollution discharges are classified as point and non-point
sources. Point sources include effluents from municipal-private
domestic wastewater treatment plants and from industrial plants.
Non-point sources include urban stormwater runoff, agricultural
runoff, forest and swamp drainage, and runoff and groundwater
seepage into surface waters.
The massive quantities of point source waste previously
discharged into the Pensacola Bay system between 1955 and 1964
have been significantly reduced. Based on surveys by USEPA and
its predecessor agencies, the combined quantity of waste
discharged by the four major dischargers into the Escambia Bay
drainage area—Container Corporation of America, Monsanto
Chemical Co., American Cyanamid Co., and Air Products and
Chemicals plants—has been reduced between September 1969 and
January 1975 by 40 percent for BODS, 71 percent for total
nitrogen, and 96 percent for total phosphorus. Based on
discharge limitations in NPDES permits (as of January 1975),
Escambia Bay received the largest portion of the BODS (34
percent) and total nitrogen (43 percent) loads discharged by
point sources. The largest portion of the total phosphorus load
(44 percent) entered Pensacola Bay.
Q
Pensacola Bay received the greatest quantity of BODS and
significant amounts of total nitrogen and phosphorus from non-
point sources entering the estuarine reaches of the Pensacola Bay
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system. Escambia Bay received the lowest quantities of BODS,
total nitrogen, and total phosphorus because the bluff on the
western shore causes most urban stormwater runoff to enter Bayou
Texar instead of Escambia Bay. .
HYDRODYNAMICS
Circulation in an estuary depends on many factors including
river inflow, tides, and wind. The relationships among these
factors are extremely variable and complex. The estimated mean
annual discharge into the Pensacola Bay system is 311 m3/sec
(11,000 cfs), and the estimated seven-day low flow that occurs
once every ten years (seven-day, 10-year low flow), which is
usually used to describe critical streamflow conditions, is 61
m3/sec (2160 cfs). This is about 20 percent of the mean annual
flow.
Higher than normal river discharges occurred during the
periods when EBRS performed field studies. The mean annual
discharge of the Escambia River at Century, Florida from 1935 to
1974 was 170 m3/sec (6016 cfs) and the mean annual discharges at
this location for water years 1973 and 1974 were 293 and 190
m3/sec (10,350 and 6,708 cfs), respectively.
Extremely low flows occurred in the Escambia River during
1967, 1968 and 1969, when the mean annual flows at Century,
Florida were 120, 100 and 82 m3/sec (4,240, 3,530 and 2,895 cfs),
respectively. Circulation in the Pensacola Bay system should
have been considerably weaker during these years than was
observed during the study period by EBRS because water year 1973
was an extremely high flow year and water year 1974 was an above
average flow year.
Tidal energy in the Pensacola Bay system is relatively weak
because of the low mean tidal range of 0.5 m (1.5 ft). In
addition, there is rarely more than one tidal cycle per day. The
tidal range also cycles approximately every two weeks from 0.8 m
(2.5 ft) during tropic tides, to 0.2 m (0.5 ft), during
equatorial tides. Circulation is extremely weak when equatorial
tides occur.
Circulation in the Pensacola Bay system varied between two-
layer flow with entrainment and two-layer flow with vertical
mixing. Mean water transport over a tidal cycle was normally
seaward in the upper layer of the Pensacola Bay system and
riverward in the lower layer. Consequently, the system was
usually vertically stratified and there was little exchange
between the outflowing upper layer and inflowing lower layer. An
analysis using the Two Layer Model, described by Bowden (1967),
indicated that under slightly less than average flow (148 m3/sec)
and average tide conditions, the flushing time for the Pensacola
Bay system was about 34 days. The model indicated a 60 day
reduction in flushing time was caused by tidal mixing. If it is
assumed that tidal mixing would also cause a 60-day reduction in
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flushing time during low flow conditions, the flushing time would
be about 200 days when river inflow is equal to the seven-day,
ten-year low flow of 61 mVsec.
Under certain meteorological conditions, current reversals
occur in the bay; hence, inflow takes place in the upper layer
and outflow occurs in the lower layer. This means that waste
discharges into the bay are sometimes transported riverward and
remain in the system for a longer period than the flushing time
suggests. Wind is probably the most influential factor in
causing these current reversals.
Salinity data and the August 1973 dye study indicated that
more freshwater flows down the western sides of Escambia and East
Bays than the eastern sides. This appeared to be due to the
Coriolis force which is caused by the earth's rotation.
Based on the August 1973 dye study, the L and N Railroad
bridge pilings did not appear to significantly hinder circulation
in upper Escambia Bay after excess pilings had been removed. The
dye study also indicated that the time of travel of the major dye
peak was 2.3 days from the mouth of the Escambia River to the
mouth of Escambia Bay when Escambia River inflow was about
average annual flow (190 m^/sec).
Based on field flow estimations, about 25 percent of the
total flow of the Escambia River basin entered the northwestern
section of upper Escambia Bay through the Little White and
Simpson Rivers. This freshwater inflow traveled seaward along
the Escambia River delta„ not throughout the entire northeast
section of the upper bay.
Discharges from American Cyanamid Co. and Air Products and
Chemicals, Inc. plants tended to accumulate in the vicinity of
the Air Products outfall (based on dye study results). The
effluent from Air Products and Chemicals, Inc. stayed close to
the shore north and south of the outfall.
The existing Main Street Wastewater Treatment Plant outfall
terminates at a location where currents transport the effluent
into Bayous Chico and Grande.
Circulation in the Pensacola Bay system was weak and not
conducive to a high assimilative capacity. Although currents in
some areas were stronger than in others, all currents were
relatively weak. Currents in the lower layer were extremely
weak.
Circulation in the northeast arm and in the dredged finger
canals of .Mulatto Bayou was weak during June and July 1974. Dead
fish caused an algae bloom in the unused finger canals of the
bayou, and, later, the algae were transported to the main area of
the bayou by wind.
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BAY SEDIMENTS
The composition of the sediments in the. Pensacola Bay system
and in northeast Gulf bays (Choctawhatchee Bay and Panama City
bays) was compared during this.study. .
Sediments in Escambia Bay consisted of sandy material near
the shore grading into mud in the central portion of the bay.
The sand shelf ended rather abruptly, with a change in slope into
the transition zone which consisted of a sand mud mixture on a
relatively steep slope down to the mud plain. The mud plain was
almost flat and extended throughout the central bay area.
Particle size classification at stations on the sand shelf was
sand, whereas size classification at transition zone stations
ranged from sand to clayey silt. Mud plain station sediment size
classifications ranged from sand to clay. The sand shelf on the
western shore was narrow and the gradient down to the mad plain
was steep. On the eastern side of the bay, the shelf was wider,
oyster beds were present, and the slope down to the mud plain was
more gradual. Water depth over the mud plain increased seaward.
Mud percentage increased with water depth throughout the
Pensacola Bay system.
Total phosphorus, organic nitrogen, and organic carbon
concentrations in sediments throughout the Pensacola Bay system
increased with water depth, and, therefore, mud content. Total
phosphorus and organic nitrogen concentrations were generally
higher in Escambia Bay sediments when compared to East Bay
sediments. Escambia Bay tended to have slightly lower organic
carbon concentrations than East Bay. Concentrations of total
phosphorus, organic nitrogen, and organic carbon were higher in
Choctawhatchee Bay and Panama City bays than in Escambia Bay.
Volatile organic sediment material in Escambia Bay was
distributed with highest concentrations in deeper waters.
Escambia and East Bays have similar concentrations in like
sediments; however, concentrations were higher in Pensacola Bay
than in East Bay. When compared to several northeast Gulf bays,
volatile organic material in Escambia Bay sediments had a similar
distribution.
The area of higher BOD5 concentrations in Escambia Bay
sediments coincided with the zone of maximum mixing of fresh and
saline waters. Flocculation of dissolved oirganics occurred in
this mixing zone with ultimate deposition in bay sediments.
Concentrations of BOD5 were highest near industrial
discharges. Compared to the other bays studied, BOD5
concentrations in Escambia Bay sediments were not unusually high
except around the industrial waste discharges.
Polychlorinated biphenyl (PCB) leaked into the Pensacola Bay
system from the Monsanto Chemical Co. plant in 1969". Arbclor
1254 (a trade name of a type of PCB) was found in sediments
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throughout the Pensacola Bay system, with higher concentrations
in the finer sized particles. Stations with high PCB
concentrations include those in the channel and near the
industrial waste discharges in the northeast portion of Escambia
Bay. This study, plus previous work (Nimmo, et al., 1975; US-
EPA, unpublished data), indicated that the Aroclor 125U was being
removed from the sediments at a rate of about 90 percent per year
between 1969 and 197U.
Dieldrin was the only pesticide, among the 21 investigated,
that was detected in Escambia Bay. Use of this highly toxic
pesticide will soon be greatly restricted.
Eleven of the twelve metals analyzed in sediments of the
Pensacola Bay system were most concentrated in the finer grained
sediments. There were seven metals that had similar
concentrations in both East Bay and Escambia Bay. These metals
were lead, zinc, chromium, manganese, nickel, aluminum, and iron.
Four metals—cadmium, copper, cobalt, arid vanadium—had greater
concentrations in Escambia Bay than in East Bay. Titanium was
equally distributed throughout all bays of the system regardless
of sediment type.
The dredged channel in Escambia Bay acted as a sink for silt
and clay particles and fine organics. Consequently, mud content
and volatile organic material concentrations were higher at
channel stations within the bay. In the Escambia River portion
of the dredged channel, these two constituents had low values.
Nutrient concentrations were also low in the dredged river
channel and high in the bay channel sediments. Total phosphorus
and organic nitrogen were higher in the bay channel sediments
than in sediments at stations adjacent to the channel on the mud
plain. Metal and PCB concentrations were also higher in channel
sediments than in the adjacent muds.
Microbial activity (as determined anaerobically by the
reduction of triphenyltetrazolium chloride) in the sediments of
Blackwater Bay, East Bay, and Pensacola Bay was similar to that
observed in the sediments of Escambia Bay. Northeast Escambia
Bay sediments near the industrial outfalls had microbial activity
that was similar to sediments at other location in the Pensacola
Bay system. Sediments from the river stations and shallow bay
stations which were high in percent sand and low in percent
volatile organic matter had low values of microbial activity. As
the percent volatile organics increased, a corresponding increase
in microbial activity usually occurred until a plateau near the
one percent level was reached. A concomitant increase in
microbial activity with percent volatile organics was not
observed above a one percent organic content.
Significant amounts of total nitrogen, and negligible amounts
of total phosphorus, were released from Escambia Bay sediments
during a sediment nutrient release study performed under aerobic
conditions. The quantity of nitrogen released was directly
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proportional to volatile organic content of the sediments. A.
larger amount of nitrogen was released from sediments located
near the industrial and sewage outfalls.
WATER QUALITY
Total organic carbon (TOC) concentrations were uniformly
distributed in the waters of the Pensacola Bay system during the
1974 study period and they consistently exceeded 2.0 mg/1 (a
maximum concentration to avoid nutrient enrichment, derived from
Water Quality Criteria, 1972). Based on limited data, total
organic carbon concentrations in Escambia Bay appeared to
decrease by 12 percent between 1969 and 1974. Pensacola and
Choctawhatchee Bay systems had about the same TOC concentrations
under similar hydrological conditions in 1974.
Total nitrogen concentrations in the waters of Escambia Bay
were significantly higher than in the rest of the Pensacola Bay
system during 1974. Escambia Bay had mean total nitrogen
concentrations that exceeded 0.360 mg/1, a recommended maximum
level to avoid nutrient enrichment in marine waters (Water
Quality Criteria, 1972), during 10 of the 12 surveys performed in
1974. The remainder of the Pensacola Bay system had mean
concentrations lower than this value. Total nitrogen
concentrations in the Pensacola Bay system were significantly
higher than those in Choctawhatchee Bay under similar
hydrological conditions in 1974. Total nitrogen concentrations
in upper Escambia Bay appeared to decrease by 50 percent between
1969 and 1974, based on a two-day survey in 1969.
Total phosphorus concentrations were also distributed
uniformly throughout the Pensacola Bay system in 1974, and they
were consistently below the 0.05 mg/1 recommended maximum level
to avoid nutrient enrichment in marine waters (Water Quality
Criteria, 1972). Based on limited data, total phosphorus in
Escambia Bay appeared to decrease by 75 percent between 1969 and
1974. Choctawhatchee and Pensacola Bay systems had about the
same total phosphorus concentrations under 'similar hydrological
conditions in 1974.
A nonparametric statistical classification procedure was used
to combine total organic carbon, total nitrogen, and total
phosphorus data into a single value designated the Principal
Nutrient Index (PNI). A PNI value of 9.0 (based on statistical
manipulation of 2.0 mg/1 - total organic carbon, 0.36 mg/1 -
total nitrogen, and 0.05 mg/1 - total phosphorus) was used to
distinguish between excessive nutrient enrichment and acceptable
aquatic conditions. During the September 1969 survey, 91 percent
of the PNI values in Escambia Bay were greater than 9.0. The
mean PNI value of pooled data for upper Escambia Bay during the
summer of 1974 was 10.6, which was a 41 percent decrease from the
1969 value. Values of PNI near waste discharges and in Bayou
Texar and Mulatto Bayou were higher than those at adjacent
locations.
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Dissolved oxygen concentrations in Escambia Bay appeared to
improve between 1969 and 1973 through 1974. The high diurnal
variation in dissolved oxygen observed in 1969 was not observed
in 1973. During the 1974 study period, there were two periods of
low dissolved oxygen, one in the early spring and another in late
summer. The period in early spring occurred after high river
inflows and the one in summer occurred when salinities in the
system were high and river inflow was low (indicating poor
flushing). During both periods lower bottom dissolved oxygen
concentration occurred near the industrial discharges in
northeast Escambia Bay (Station EGLY) . The available data for
Pensacola Bay during 1974 indicated that low dissolved oxygen
concentrations in Escambia and East Bays during the spring of
1974 were not caused by a water mass from Pensacola Bay entering
these systems. Benthic oxygen demand from the sediments appeared
to be a significant factor in causing low bottom dissolved oxygen
concentrations.
Vertical stratification in the system was observed in the
salinity data and also in the dissolved oxygen data. Bottom
dissolved oxygen concentrations were always lower than surface
concentrations. This occurred because the dissolved oxygen
removed from the lower layer by benthic demand was not
continuously replaced when the system was stratified, since there
was very little exchange between reaerated upper layer water and
lower layer water.
Based on dissolved oxygen concentrations measured in East
Bay, low dissolved oxygen concentrations occur during critical
periods (high temperatures, low river inflow) in bays that do not
receive direct point source waste discharges. Consequently, due
to naturally poor circulation and non-point source discharges in
the Pensacola Bay system, the assimilative capacity of the system
with respect to oxygen resources should be extremely limited.
Ultimate BOD values during the 1974 study period were
approximately the same as 1973 values. Ultimate BOD
concentrations in northeast Escambia Bay near the industrial
outfalls were higher than in the Escambia River.
Total and fecal coliform densities were greatest in the
Escambia River and upper Escambia Bay. These densities decreased
as the river water dispersed into the upper bay and diminished
progressively in a seaward direction. Natural die-off and
increasing salinity also contributed to decreased bacterial
densities. Total and fecal coliform densities were higher
following periods of heavy rainfall and increased river flow,
which indicated that the higher densities observed were due to
runoff and swamp drainage. All of the Class III waters
(recreation - fish and wildlife) in the Pensacola Bay system
except the tributaries, were within the mean total coliform and
fecal coliform limitations specified in the Florida water quality
standards.
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Waters in Escambia Bay and East Bay complied (in most
instances) with the mean coliform shellfish standard in areas
opened to harvesting oysters. Violations of the maximum standard
occurred more than ten percent of the time at most stations in
Class II waters (shellfish harvesting) .
The highest turbidities in Pensacola Bay system waters were
measured during winter and spring when rainfall in the drainage
area was high, and the lowest values were measured in summer
during low river inflow periods. Higher turbidities were
measured in the Conecuh-Escambia River than in the Blackwater and
Yellow Rivers. This occurred because most of the Conecuh-
Escambia River drainage basin is an area with clay soils. Most
of the drainage basins of the Blackwater and Yellow Rivers are
areas with sandy soils. Mean turbidities in Blackwater and East
Bays were considerably lower than those in Escambia Bay. None of
the turbidity values measured in the bays during the 1974 surveys
exceeded the State of Florida water quality standard of 50 jtu
for Class II and III waters.
Point sources of waste contributed the greatest portions of
the BOD5, total nitrogen', and total phosphorus loads to the
Pensacola Bay system (based on allowable discharges in NPDES
permits in effect during January 1975 and critical ( 60-day, 10-
year) low flows in the rivers tributary to the bay system, and
average annual non-point discharges). Tributary rivers and non-
point sources of waste followed point-sources with decreased
pollutant contributions. Low flow conditions were used to
determine the pollutant loading from tributary rivers because low
flow periods generally occur in late summer and early fall when
the water temperature of the bays is highest, the bottom
dissolved oxygen concentrations lowest, the chlorophyll a
concentrations (phytoplankton) highest, and when most of the fish
kills occur. Under allowable discharges in NPDES permits in
effect during January 1975 and low flow conditions, it was
estimated that 38, 41, and 21 percent of the BODS loads
discharged into the Pensacola Bay system were from tributary
rivers, point sources and non-point sources,.respectively. At a
later time, when final NPDES limitations will be in effect,_and
under low flow conditions, it is estimated that 50, 22, and 28
percent of the BOD5 loadings will be from tributary rivers, point
sources, and non-point sources, respectively. Point source
discharges will still be the greatest contributor of total
phosphorus, 45 precent, when final NPDES effluent limitations are
in effect. Accordingly, the theory held by many, that point
source discharges are insignificant compared to contributions
from tributary rivers and non-point sources, is incorrect.
PLANKTON
Plankton studies were performed by the University of West
Florida (UWF) and EBRS in the Pensacola Bay system. The
University1svwork on primary productivity indicated that Escambia
Bay and East Bay had similar production. Comparing Escambia Bay
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with Port Royal Sound, South Carolina", shows that Escambia Bay
was several times less productive. Escambia Bay, when compared
to several systems throughout the Gulf Coast, had a low primary
productivity..- All counts of, and seasonal succession of,
phytoplankton were similar in Escambia Bay and East Bay; however,
because of river inflow, Escambia Bay had a less uniform
distribution of phytoplankton than East Bay.
Seasonal trends and total counts of zooplankton were similar
in Escambia and East Bays. No differences were noted between the
bays within the dominant groups of organisms. Acartia tonsa was
the dominant organism in both bays.
Chlorophyll a concentrations were compared throughout the
Pensacola Bay system. Escambia Bay had higher concentrations
than other bays in the system, with concentrations higher in the
upper estuary and decreasing toward the Gulf inlet. Mulatto
Bayou and Bayou Texar had the highest concentrations of
chlorophyll a in the bay system and most of the time bloom
conditions were present.
FISHES
Investigation of the fish fauna was directed toward
developing a pertinent and reproducible data base for future
assessment and to ascertain the present status of the finfishes
and penaeid shrimps.
During the year, a total of 79,373 fishes, representing 57
species and 32 families, was taken in the otter trawl and seine
collections at 15 stations throughout the estuary. The average
trawl catch was 568 individuals per collection.
The dominant pelagic fishes in both the trawl and seine
collections were the bay anchovy (Anchoa mitchilli) , Gulf
menhaden (Brevoortia patronus), striped anchovy (A. hepsetus),
tidewater silverside (Menidia beryllina), and Atlantic bumper
(Chloroscombrus chrysurus); whereas the most abundant benthic
species were the spot (Leiostomus xanthurus) , Atlantic croaker
(Micropocfon undulatus) , and sand seatrout (Cynoscion arenarius) .
An additional fifty other species were represented in the
catches.
Fish kills are visible indications of conditions of poor
water quality. In the past, pollution-caused kills were linked
with excessive amounts of nutrients, polychlorinated biphenyls,
sewage, oils, phenols, toxic metals, pesticides, and other
industrial by-products. In general, reductions in industrial
waste discharges paralleled similar declines in the number of
fish kills. From 1970 through 197U, the frequency of fish kills
in Escambia Bay and associated bayous dropped by 86 percent; in
the entire Pensacola Bay system, the number of kills was reduced
by 75 percent. In addition, there were no massive kills in the
Pensacola area in 1974.
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Freshwater angling in the lower Escambia River and delta
tributaries is a popular sport. The most sought after and most
frequently caught species were bluegill (Lepomis macrochirus),
redear sunfish (L. microlophus) t and largemouth bass (Micropterus
salmoides). Based on a comparison of the catch rates between the
1970 and 1974 creel surveys (both approximately 1.0 fish per
angling hour), there has been no significant improvement in this
fishery.
An analysis of the diversity of the fish communities provided
a technique for ascertaining the effects of pollution or
environmental stress. In Escambia Bay, species diversity
(Shannon-We aver formula,, H°) was inversely correlated with the
nutrient concentrations (PNI) in the water column. In other
words, higher nutrient concentrations contributed to lower
species diversity, whereas low nutrient levels resulted in higher
species diversity in various areas of the bay and bayous.
Overall, nutrients contributed U2 percent of the variance of
diversity. It is apparent that further reductions in waste
discharges will contribute to the well-being of fish populations.
Both the relative abundance and species diversity of the fish
populations in Escambia Bay were similar to, and in some
instances superior to, many estuaries in the northern Gulf of
Mexico. In general, the finfish populations and the nursery
grounds (for fishes) were judged to be in an intermediate stage
of recovery.
The decline in shrimp fishery was attributed to the
deterioration in the bottom habitat by various pollutants.
However, persistent pollutant residues in the sediments, such as
PCB, and associated materials in the water column continue to
obstruct the development of a viable shrimp fishery. Further
leaching of various foreign substances from the sediments should
lead to improved conditions on the bottom. At present, both the
shrimp fishery and nursery grounds are in the early stages of
recovery.
In some estuaries, the bottom environment might be altered to
improve conditions. In Escambia Bay, an intensive study of
utilization of two major substrates (compact shell and soft mud)
revealed that both bottom areas were quite productive. Large-
scale changes in the existing substrates, at least in the open
bay, would not enhance bottom nursery habitat for young fishes
and penaeid shrimps.
Historically, the anadromous striped bass (Morone saxatilis)
inhabited the waters of Escambia Bay and River. The feasibility
of re-establishing this valuable sport fishery was enhanced due
to the overall improvement in environmental quality. In April
1975, five million fry, descendants of the famed striped bass
population in the tail waters of the Santee-Cooper Reservoir in
South Carolina, were stocked in the tributary streams of the
lower Escambia River.
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BENTHIC MACROINVERTEBRATES
Benthic macroinvertebrates at sand shelf, mud plain, and
transition zone stations were compared for biomass, species
number, and numbers of individuals. All three parameters
increased from mud to transition to sand stations. The same
trend applied for diversity (Shannon - Weiner formula, H1)? that
is, H' increased from mud to transition to sand. There was no
significant difference within sand shelf stations between values
for biomass, species number, number of individuals, and diversity
for the upper bay compared to the lower bay and for the east side
compared to the west side. The same is true for the transition
zone and mud plain stations. In all cases except one, the winter
samples within like sediments had higher biomass, species
numbers, and numbers of individuals than did the summer samples.
Biomass was higher in the summer at sand shelf stations.
Oyster bed stations had the highest number of species,
diversity, and biomass of any other habitat in Escambia Bay.
Grass beds were the second most productive habitat in
Escambia Bay. East Bay grassbed sample data were similar to the
data for an Escambia Bay grassbed.
Near the Northeast Wastewater Treatment Plant discharge, the
assemblage of organisms observed was similar to that found in
other sediments with similar physical characteristics. However,
samples at this station were taken a year later than those at
comparable sediment stations, and the annual variation must be
considered in evaluating the data.
At the industrial discharge stations, there was a shift in
species types from mullusca and Crustacea to polychaete worms.
The species number, biomass, and numbers of individuals of
organisms around the industrial discharges were altered only in a
narrow band nearshore at the discharge from Air Products and
Chemicals, Inc.
Deep water mud sediments in Escambia, East, and Pensacola
Bays generally had similar assemblages, except Pensacola Bay
which had two high salinity species that were not found in the
other two bays.
The high salinity area assemblage sampled in Santa Rosa Sound
produced by far a higher number of species, biomass, diversity,
and number of individuals than found in the Pensacola Bay system.
Escambia Bay had diversity (H') values lower than values from
Hillsborough Bay and Galveston Bay within comparable mud
sediments ° during the summer, indicating stressed
macroinvertebrate populations in Escambia Bay.
In general, Escambia Bay sediments supported a population of
benthic macroinvertebrates similar to that in East Bay.
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BENTHIC MACROFLORA
Seagrasses are an especially important component of an
estuary, since they function as a nursery ground for finfish and
shellfish. There has been extensive vegetation loss throughout
the Pensacola Bay system. All seagrasses (Thalassia and
Halodule) were gone except one bed on the northeast shore of.East
Bay, and this bed has diminished significantly. The shoreline
near this bed is the least altered by man in the system and seems
to have the least beach erosion. A persistent freshwater specie,
Vallisneria americana, is growing well in Blackwater Bay but
declined in upper Escambia Bay prior to 1974. However, in 1974
and 1975, there has been an expansion of Vallisneria in the
Escambia River delta area.
Major causes of this vegetation loss were sewage and
industrial waste discharges, dredging and filling, beachfront
alteration, and changing watershed characteristics. In the
Pensacola Bay system many factors have synergistically affected
the entire system with certain factors having an increased local
effect. For instance, the loss of vegetation around the
Northeast STP was caused first by laying the discharge pipe
directly through the bed and later by sewage effluents. Along
the southern shore of East Bay, bulkheads -and groins likely
caused changes in nearshore water movements and, therefore,
erosion of seagrass beds. Industrial discharges, no doubt,
caused the loss of vegetation in the northeast section of
Escambia Bay since these effluents remain near shore in that
area. Dredging and filling of the Port of Pensacola caused
turbidities which affected the vegetation in addition to the
actual removal of the grassbeds in some instances.
In neighboring Santa Rosa Sound, seagrasses have remained
relatively stable. This area should be considered as endangered,
however, and every effort should be made to preserve the
integrity of these seagrass beds.
Transplants of Halodule wrightii were taken from East Bay and
introduced into Escambia Bay during July and September 1974.
One-hundred plugs of H. wrightii were placed at each of four
sites in depths from 0.3 to 1.0 m.
Observation of the plants in May 1975, after overwintering,
revealed green leaves on 37 percent at one site, 10 percent at
another site, and two sites were covered with 12 cm of sand.
Additional leaves may have developed later in the spring as water
temperature increased. In June 1975, additional transplanting
was performed at two new sites and near two old sites. One month
after transplanting, green leaves were observed on 23, 43, 61,
and 78 percent of the plugs. Continued evaluation of the
revegetation program will be performed ; by. the . Bream Fisherman
Association of Pensacola and a UWF student as a.special course
project.
2-12
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3 - CONCLUSIONS AND RECOMMENDATIONS
CONCLUSIONS
As evidenced by an improved dissolved oxygen regime, a
reduction in frequency and intensity of fish kills, and
attritional losses of toxic materials from the sediments, aquatic
conditions in Escambia Bay were considerably improved during 1973
and 1974. These improvements resulted from a combination of
higher than normal annual river inflows and accelerated pollution
abatement efforts. Conditions will continue to fluctuate as a
function of freshwater inflow, but overall quality can be
expected to improve further as point source waste inputs are
reduced. In addition to waste reduction, restoration techniques
such as revegetation of marine grasses, relocation of waste
discharge sites, stocking of striped bass, and implementation of
an areawide water quality management plan will protect gains made
in improved aquatic conditions. The following conclusions
elaborate further (including reasons for rejecting certain types
of restoration techniques such as selective dredging and
tributary flow pattern alteration).
Environmental Quality
• Physical and chemical characteristics of sediments from
Escambia Bay are similar to sediments from other Florida
bays. Finer grained sediments with the highest
concentrations of organic material, nitrogen, and
phosphorus occurred at mud plain locations in each bay
at deep water depths. Most of the particulate material
entering the Pensacola Bay system from point and non-
point waste sources and tributary rivers are retained in
the system. However, this material is distributed
throughout the bays before sedimentation occurs. Thus,
the effects of the waste discharges are bay-wide.
• Based on all water quality data collected, aquatic
conditions are worse in Escambia Bay than in the other
bays of the Pensacola Bay system and Choctawhatchee Bay.
Conditions appear to have improved in upper Escambia Bay
based on decreased nutrient concentration between a two-
day study in 1969 and studies performed in 1973 and 1974
under similar hydrological conditions.
• Nutrient enrichment was greatest in Mulatto Bayou and
Bayou Texar, and algal blooms occurred there during the
summer months.
• Ba°sed on rates of primary production, phytoplankton cell
counts, and zooplankton counts, during 1973 and 1974,
Escambia Bay and East Bay were similar to other northern
Florida bays.
3-1
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• Estuarine waters were functioning as productive
nurseries for young fishes. The most productive nursery
grounds for finfishes were in the semi-protected bayous
and not in the open bays. The dominant fishes in
Escambia Bay were anchovies, clupeids, and scianids.
Similar faunal assemblages are found in other nearby
estuaries of the northern Gulf of Mexico., Annual shifts
in the number of species of fishes were related to
seasonal changes.
• Overall, the condition of the fish populations and
fishery was judged to be in an intermediate recovery
stage, whereas, the penaeid shrimp nursery and fishery
showed indications of an early stage of recovery. No
improvement was noted in the freshwater sport fisheries
on the lower Escambia River between 1970 and 1974.
• Based on limited sampling in East Bay, macroinvertebrate
species found in a given type of sediment are similar in
both Escambia Bay and East Bay.
• Escambia Bay sediments support stressed populations of
benthic macroinvertebrates.
• Algal blooms in the partially constructed finger canals
of Mulatto Bayou are intensified by weak circulation.
Causes of Environmental Problems
• Because of poor circulation and flushing charac-
teristics, the assimilative capacity of the Pensacola
Bay system is extremely limited and the bay is barely
able to assimilate natural inputs of nutrients and
oxidizing materials.
• Circulation caused most of the discharge from the
American Cyanamid plant to be transported north toward
Floridatown instead of seaward during the September 1974
survey. Effluent from the Air Products and Chemicals
Inc. plant remained concentrated in the nearShore zone
north and south of the discharge point during the August
1974 survey. Both effluents entered Mulatto Bayou.
• Critical aquatic conditions in the Pensacola Bay system
occur in late summer-when:
1) The system is vertically stratified and oxygen is
not transported from the upper layer, which
undergoes reaeration, to the lower layer which must
satisfy the benthic oxygen demand„
2) Water temperature is highest which increases the
rates of biological growth processes.
3-2
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3) Low river inflows occur which reduce flushing and
weaken circulation.
4) Low turbidities promote phytoplankton growth.
• Point source wastewater discharges are the major cause
of poor aquatic quality conditions during late summer.
Non-point sources and tributary river inflow also
contribute to poor aquatic quality conditions.
•• Although nutrient levels decreased between 1969 and
1973-1974, nutrient enrichment still exists in Escambia
Bay. Nutrient concentrations during 1973-1974 usually
exceeded the levels recommended in Water Quality
Criteria (1972) for marine waters.
• In the past, nutrient enrichment in the Pensacola Bay
system caused high phytoplankton concentration during
summer months and contributed to benthic oxygen demand.
Phytoplankton were a food source and attracted numerous
fish (Menhaden) into areas where phytoplankton
concentrations were high. Phytoplankton respiration and
benthic oxygen demand depressed dissolved oxygen
concentrations and caused fish kills.
« Tributaries were the major source of total and fecal
coliform bacteria to the Pensacola Bay system. Wastes
discharged from the Pensacola sewage treatment plants
did not contribute significantly to coliform densities
observed in Escambia Bay or Pensacola Bay except in the
vicinity of the outfalls. The potential for the
presence of pathogens based on coliform densities was
greatest in the tributaries, bayous, northern Escambia
Bay, and Blackwater Bay.
• Under aerobic conditions, significant amounts of total
nitrogen, and negligible amounts of total phosphorus,
were released from Escambia Bay sediments. The highest
amounts of nitrogen were released from sediments located
near American Cyanamid and Air Products and Chemicals
Inc. plants and Northeast Wastewater Treatment Plant
outfalls.
• Diversity of the fish communities was inversely related
to nutrient content in the water column. That is,
species diversity was depressed in areas with high
nutrient concentrations, whereas diversity was improved
in waters with low nutrient levels. The numerical
distribution of the fishes and penaeids was not related
to the major point sources of pollution in the upper
bay,,
3-3
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• The decline in the shrimp fishery, since 1970, in the
Pensacola Bay system is attributed to persistent
pollutant residues in the sediments.
• Man's influence (dredge and fill activities, waterfront
alterations, and waste discharges) appears to be the
cause for the reduction of seagrasses.
Restoration
The circulation of upper Escambia Bay improved after the
excess pilings under the L and N Railroad bridge were
removed in 1970.
There is no evidence that diverting freshwater into the
Little White and Simpson Rivers would change the flow
pattern in the vicinity of Floridatown and improve water
quality. The possibility exists that such changes could
damage a productive fishery.
The soft mud and compact shell bottoms are nursery
grounds for young fishes. Major changes in either
substrate would not speed up the recovery processes.
Techniques for transplanting Halodule wriqhtii (shoal
grass) have been developed. The best period for
transplanting Halodule wriqhtii is late May or early
June; however, transplants can live through the winter
when planted as late as September. The plug method of
transplanting (as used in this study) cannot be
evaluated in less than two to three years since the
plant will be living on the original soil during the
first one or two years.
It was not possible to evaluate the success of the
initial stocking of striped bass in the lower Escambia
River because of the projects termination.
3-U
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RECOMMENDATIONS •
1. An areawide pollution abatement and management plan
should continue to be developed for the Pensacola Bay
system and should be adopted. The planning process
should:
• Prohibit municipal-private domestic wastewater
discharges into Escambia and Pensacola Bays, their
tributary bayous, and the lower Escambia River
v .. other than the discharge from the Main Street
Plant, which shall receive advanced waste treatment
and not exceed 77,500 m^/day (20 mgd) .
• Allow only existing municipal-private domestic
wastewater discharges into East and Blackwater
Bays, their tributary bayous, and the lower Yellow
and Blackwater Rivers after advanced waste
treatment has been provided.
• Not modify the final effluent limitations of
currently issued NPDES permits to reflect less
stringent effluent limits.
• Prohibit new industries from discharging
wastewaters into the Pensacola Bay system and the
lower reaches of tributary rivers.
• Provide for the use of alternate methods of
wastewater disposal, such as land application,
where practical and where potable groundwater
supplies are not endangered.
• Formulate comprehensive land use management
practices (stressing preservation of environmental
quality) for Escambia and Santa Rosa Counties in
order to address the control of non-point sources.
• Develop and design an integrated physical,
chemical, and biological ambient and waste source
monitoring program.
2. The Main Street Outfall should be extended to discharge
about 1830 m from shore to improve dispersion of the
waste.
3. Effluents from American Cyanamid Company and Air
Products and Chemicals, Inc., should be discharged
through outfalls extended to the vicinity of the barge
channel in Escambia Bay. The American Cyanamid plant
outfall would have to be extended about 1920 m.
U. A detailed evaluation of the effects of open water
disposal of dredged material on the environment, which
3-5
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includes a cost-benefit analysis containing the cost of
environmental damage, should be performed before open
water spoil disposal is allowed in Pensacola, East, and
Blackwater Bays.
5. No open water disposal of dredged material should be
allowed in Escambia Bay. No dredging should be
performed in Escambia Bay during June through October.
6. Contained spoil areas with discharges into the Pensacola
Bay system should be designed to minimize the discharge
of fine sediment materials into the receiving waters.
7. A striped bass fishery should be established in the
Escambia River under the auspices of a government agency
to augment the sport fishery and to better utilize the
abundant forage base.
8. Research grants, from the Environmental Protection
Agency and others, should be be awarded for revegetation
of seagrasses in Escambia Bay in May-June, 1976.
9. The productive nature of the bayous, as a habitat for
young fishes, should be recognized, enhanced, and
protected in the Pensacola Bay system.
10. Partially constructed finger canals in Mulatto Bayou
should be sealed off from the remainder of the bayou.
11. The deep borrow pits in Mulatto Bayou should be
eliminated if fish kills occur in the Bayou in the
future.
12. Every effort should be made to preserve the integrity of
the seagrass beds in East Bay and Santa Rosa Sound.
3-6
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- AREA DESCRIPTION
The Pensacola Bay system is located in Escambia and Santa
Rosa Counties in the extreme northwestern portion of the State of
Florida (Figure U-1). The river systems that feed the bay have
extensive drainage areas totaling 17,550 km2 (6,778 mi2). The
Escambia, Yellow, and Blackwater Rivers, which are the major
tributary rivers, extend to the northeast into Alabama. Most of
the Escambia River drainage basin is in Alabama, and only the
.upper reaches of the Yellow and Blackwater River basins are in
Alabama.
The area adjacent to the Pensacola Bay system that drains
directly into it is 828 km2 (320 mi2), and the land use of this
area are about 7, 7U, and 19 percent agricultural, forest, and
urban-residential, respectively. The rest of the drainage area
has agricultural and forest land use.
The rivers draining into the Pensacola Bay system have been
considered point sources discharging into the estuarine reaches
of the system. Thus, the study area of this report is the
Pensacola Bay system.
CLIMATOLOGY
Climatic conditions have a significant effect on aquatic
systems. Winds, air temperature, and precipitation are generally
seasonal with short-term variation due to local disturbances.
Wind
Wind velocity and direction can affect a body of water like
the Pensacola Bay system in a number of ways. Winds can cause
water to "pile up" on one side of the system and in this way
reverse normal circulation patterns. Wind velocity is an
important factor with respect to reoxygenation; high velocity
wind transfers dissolved oxygen into the water at a rapid rate.
Conversely, high wind velocity may resuspend sediments which can
exert a considerable oxygen demand on the water column.
Prevailing winds were from the north at Pensacola Regional
Airport (Table U-1). The data were obtained from U.S. Department
of Commerce (1972 to 1974, a). During October 1972 through
September 1973 the prevailing winds were from the north (3U
percent of the time). Winds were from the south and east about
22 percent of the time. West winds occurred only 16 percent of
the time dnd were the least frequent. Calm conditions occurred
5.2 percent of the time. During October 1973 through September
1974, winds from the north and south occurred about 29 percent of
the time. Winds from the east and west occurred 21 and 12
-------
Gulf
of "e*ic°
Scan IIJOO.OOO
JO 40 H
10 O 10 20 30 «0 50 >
Figure 4-1. Map of drainage area.
14-2
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lablw 4 - 1. Frequency distributions OL wind direction and velocity at
L'onsacoia iiegional Airport.
Direction Oct. 197
N (315 to 450)
E ( 40 to 135)
S (1Jb to 225)
h (226 t'j 315)
CALM
Velocity
(kra/hr) (knots)
CALK
1. 2 to a. 3 I .5 to 4.5
B.4 to 17.6 4.o to '^.5
17.7 to 26. 8 J.6 to 14.5
> 2 b . S > 1 4 . t
Date
2 to Sep. 1-J73
34.2
22.6
21.7
1h. 1
'3.2
5.2
1 : . a
54.5
2J.7
:i . 'J
Oct. V?73 to Sao. 1974
oC Tino
25.2
21.2
29. i>
7.S
7.5
7.5
12.2
52.3
' U 1
3.*
a-3
-------
percent of the time, respectively. Calm conditions existed 7.5
percent of the time. Data were not available to determine if the
above conditions were normal.
The frequencies of wind velocities were similar during both
periods, and velocities between 8.4 and 17.6 km/hr occurred
slightly more than 50 percent of the time (Table 1-1).
Wind roses for conditions at Pensacola Regional Airport
(Figure 4-2) indicate that winds with velocities between 8.4 and
17.6 km/hr occurred with the highest frequency in every
direction, and that north and south winds generally have higher
velocities than east and west winds. Winds from the northeast
with velocities between 8.a and 17.6 km/hr were the most frequent
during both periods.
Mean wind velocities were about normal during the period when
studies were performed by the Escambia Bay Recovery Study (Table
4-2). Lowest wind velocities (about 11 km/hr) normally occurred
in July and August. During both years of the study period, mean
wind velocities were slightly above normal in July and slightly
below normal in August. Thus, the energy contributed by wind for
circulation and reoxygenation was lowest during the summer months
when critical conditions, with respect to dissolved oxygen,
normally occur.
Precipitation
Surface water and groundwater discharges into rivers and
estuaries are controlled by precipitation. The precipitation at
Pensacola, Florida, and Andalusia, Alabama, (U.S. Department of
Commerce, 1972 to 1974, b) is presented in Figure 4-3. Normal
annual rainfall for Pensacola and Andalusia was 152 cm (60 in)
and 145 cm (57 in), respectively. At Pensacola, Florida, during
the period October 1972 to September 1973, the total annual
rainfall was above normal at 188 cm (74 in), and during October
1973 to September 1974, the total annual rainfall was lower than
normal at 140 cm (55 in). At Andalusia, Alabama, during October
1972 through September 1973, total annual precipitation was
greater than normal at 196 cm (77 in), and during October 1973
through September 1974, total precipitation was 152 cm (60 in)
which is greater than normal. Thus, the total annual rainfall
during the first year of the study period was significantly above
normal and during the second year about normal.
Air Temperature
Air temperature controls water temperature, which has a
profound effect on the aquatic systems in an area. The
saturation concentrations of dissolved gases in the water and the
rates of respiration of organisms in the ecosystem are also
affected by temperature. Mean monthly air temperature data for
the Pensacola Regional Airport are presented in Figure 4-4 (U.S.
Department of Commerce, 1972 to 1974, b). Normal mean monthly
4-4
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October 1972 - September 1973
153 observations of Calm
October 1973 - September 1974
1-4 10-14
3-9 15-24
Wind Speed (mph)
(Observations every three hours)
221 observations of Calm
Figure 4-2. Wind roses at Regional Airport, Pensacola, Florida
for October 1972 to September 1973, and October 1973 to
September 197U.
U-5
-------
•Table u - 2. i-joan iiiont.'iiy wind velocities (km/ur) ** at Pensacola
I'.cj ion.11 A i rpor t.
Month
Cctooar
Nov '.eiflher
Eecemher
January
February
March
April
Hay
June-
July
August
Septoitiuer
Year
Dat
197^ to 1973 1973 to
13.2 12.
Tj.o 13.
1 j . •:• 17.
15.6 13.
1 ^ . U 15.
17.2 15.
17.9 15.
16. 1 14.
12.2 12.
11.1 11.
9.5 9 .
13.2 13.
14.3 13.
e
1974
1
2
2
3
y
3
*
2
7
1
a
5
7
1941 to
12.
12.
14.
14.
15.
15.
15.
13.
12.
10.
10.
12.
13.
1970*
9
9
5
3
1
3
1
a
i
<*
5
4
4
* No t'ou Is
* * K in/ h r X C . 6 2 2 = m u h
4-6
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30
25
20
15
10
5
KEY
Pensocolo
Pensocolo Normal (1934-1973)
I I I I I I I I I I I I I I I I I
33
30
25
20
15
10
5
KEY
Andalusia
Andalusia Normal (1934-1973)
i i i i i I I I I
\lllllllllll
ONOJ FMAMJ JAS ONDJ FMAMJ JAS
1972
1973
MONTHS
1974
Figure 4-3. Total monthly precipitation records at Pensacola,
Florida and Andalusia, Alabama for October 1972 - September
1974.
30
Q:
LU
Q.
Pensacola Mean
( 1934- 1974)
0 NDJ FMAMJ JASONDJ FMAMJ
10
Figure 4-U. Mean monthly air temperature at Regional Airport,
Pensacola Florida for October 1972 through September 1974.
4-7
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temperature data for the period of 1934 through 1973 are also
presented in the figure. Normally, January is the coldest month,
with a mean temperature of about 12°Cf and the highest mean
temperature of about 27°C occurs in July and August. Mean
monthly temperatures during October 1972 through September 1974
followed the same trend as the normal mean temperature, but were
usually slightly .higher.
POPULATION
The population of Escambia and Santa Rosa Counties is
expected to more than double between 1970 and 2010. Population
trends for this area between 1900 and 2010 are shown below:
Thousand persons (from Henningson, et al., 1975)
1940 1950 1960 1970 1980 1990 2010
91 131 203 244 327 427 570
ECONOMY
Pensacola Bay is an excellent, easily defended harbor and due
to this, a military base and the City of Pensacola developed on
its shores. In the late ISOO^, Pensacola was a world timber
center. Unfortunately, due to poor reforestation practices, this
industry diminished in importance. Reforestation of the land led
to the development of the paper industry in the area.
Historically, agriculture and commercial fishing were extremely
important to the economy of the area, but, at the present time
manufacturing has surpassed them in importance. The Naval Air
Station at Pensacola has been and is an important part of
regional economy.
The proximity of Pensacola to the Gulf of Mexico and the
abundance of.historical landmarks has made this area a tourist
attraction. The beautiful beaches and water resources of the
area have contributed to the development of motels, restaurants,
recreational related and travel oriented businesses.
Unfortunately, Pensacola fell from the fifth to the thirteenth
most visited city in Florida between 1961 and 1970. This adverse
effect on tourism is believed to have been caused by a decline in
water quality (Henningson, et al., 1975).
The economy of the area is characterized by a lack of
industrial diversification, because there are only four major
classifications of industries in the area: chemicals, lumber and
wood products, food products, and stone, clay, and glass. These
industries employ about 7,200, 2,400, 1,000 and 800 persons,
respectively, (1967 census of manufacturing, p. 10-15, cited by
Henningson, et al., 1975). The Pensacola Naval Air Station and
outlying bases employ about 19,000 military and civilian
personnel. Thus, of the 65,500 persons from this area that had
4-8
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non-agricultural employment in 1969 (Henningson, et al., 1975),
22 percent or 14,300 were employed in manufacturing and 29
percent were employed by the military. Other employers besides
industry and the military include retail stores, construction,
and tourist-oriented trades and services.
RECREATION
Outdoor recreational opportunities in the Pensacola area are
centered around water-borne and water-related activities. Water
bodies available for recreation include large portions of the
estuarine zone and the coastal waters of the Gulf of Mexico.
These waters have become increasingly important as recreational
resources because of the nearness of the major population center
in northwest Florida. Popular features that attract people, both
residents and»visitors, include renowned, white-sand beaches,
sparkling blue waters, picturesque bays, and mild climate.
Outdoor activities, enjoyed by all age groups, are generally
similar in type, but often not in degree, to those in other
sundrenched estuarine and coastal waters of Florida. Specific
usage includes:
Boating (sail, motor, canoe)
Swimming and wading
Fishing (boat, pier, beach, and jetty)
Water skiing and surfing
Scuba diving and snorkeling
Picnicking and camping
Other shoreline activities (sunbathing, shelling, hiking,
bird watching)
Waterfowl hunting
Aesthetic enjoyment.
The four most popular activities enjoyed by all age groups
are • swimming, sunbathing, boating, and fishing. Sailing has
become increasingly popular, and a number of sailboat regattas,
both local and regional in scope, are held in Pensacola Bay and
offshore waters during the warmer months. In Florida, fishing
was recently cited as the main reason that tourists return, but
precise information is lacking on the monies generated by sport
fishing activities in this area. During the warm summer months,
crowds of people participate in swimming, sunbathing, and related
shoreline activities.
-------
In Escambia Bay, outdoor activities largely center around
boating and fishing. Beach activities are limited, partly due to
the lack of access points and to the less attractive brownish-
sand shoreline that must compete with the famous Gulf beaches.
Saltwater sport fishery in the bay and bayous and the popular
freshwater fishery on the lower Escambia River and delta streams
are major recreational outlets. In the fall, duck hunting is
actively pursued along the shores and backwaters of the river.
Numerous water-oriented services and industries in the
Pensacola area are dependent on the tourist industry,
particularly those near the beaches. Included in this category
are .numerous motels, restaurants, boat agencies, marinas, tackle
shops, charter boats, gasoline stations, and other related
services. In turn, outdoor activities that attract people are
interwoven and dependent on maintaining .-conditions of good water
quality.
SPORT AND COMMERCIAL FISHERIES
Sportfishing in the Pensacola area may be divided; for
discussion purposes, into three contiguous aquatic zones: Sulf
waters, estuarine waters, and fresh waters. Fishermen must
travel offshore, well beyond the sight of land to reach the more
successful red snapper, grouper, and billfishing grounds.
,Biilfishing is becoming increasingly popular and the established
Pensacola International Billfishing Tournament is held each
summer. In the inshore or coastal waters, those with smaller
boats actively pursue the king mackerel, an extremely popular
game and foodfish, from late spring until fall. Trolling with
feather jigs and cigar minnows is a favorite and successful
method for catching kings. In April, the fishing season is in
full swing by the time the cobia (known locally as the ling) pass
the area on their annual westward migration to Mississippi
waters. Other species that are taken while trolling or casting
include ladyfish, Spanish mackerel, and occasionally, dolphin,
wahoo, and sailfish. .Some spearfishing for groupers, flounders,
and sharks occur around reefs and wrecks such as the U.S.S.
Massachusetts which was sunk outside Pensacola entrance in 1922
during a demonstration of railroad artillery. Surf and pier
fishermen take whiting .(Menticirrus spp.) , pompano, red drum,
bluefish, and black drum; in addition to these species, king and
Spanish mackerel and cobia are caught near the end of the beach
pier.
In the estuarine waters of the bays, sounds, and bayous, the
most sought after species is the speckled seatrout (or speck) .
Numerous fishermen will usually be found spin casting with jigs
or lures or fishing.'with live-.shrimp over the grass beds for this
popular fish. The best fishing period is late spring to early
summer. In Escambia Bay, the L and N Railroad trestle, which
spans the bay, is a favorite fishing site for specks in the fall
and winter. :
4-10
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During the warmer months, schools of Spanish mackerel,
crevalle jack, ladyfish, and Atlantic bonita, are found in the
open waters of the estuary. Spin casting and trolling are the
most used fishing methods for these pelagic fishes. Other sport
fishes, that mainly frequent the more saline portions of the bays
and bayous, include flounders, red drum, striped mullet, king
mackerel, spot, spadefish, sheepshead, and pompano. The mullet
is a fine food fish that is rarely taken by hook-and-line, but
when schooling, they are readily caught with snag hooks or cast
nets.
In Florida, when replacement bridges are built, the old
structures are usually converted to stationary fishing platforms,
such as the Pensacola Bay (three-mile bay bridge) and Santa Rosa
Sound bridges. Maintaining old bridges for fishing purposes is
not the case in some coastal states. Many avid bridge fishermen,
often in family groups, travel long distances in order to bottom
fish for white trout, Atlantic croaker, sheepshead, speckled
seatrout, and flounder. Bridge fishing is such a popular and
enjoyable pastime that many individuals camp and fish all night
from these structures.
Lower reaches of the rivers, such as Escambia, Blackwater,
Yellow, and East Bay Rivers; are frequented by freshwater fishing
enthusiasts. The largemouth bass, warmouth, channel catfish, red
ear, and spotted sunfish form the bulk of the catches. The last
two species are more readily known in this region by their
colorful vernacular names, which are "shell cracker" and "stump
knocker," respectively. Results of two recent creel surveys on
the lower Escambia River are analyzed in Chapter 10.
Although there are no statistics on the marine sport
fisheries of the Pensacola area, the value and magnitude of this
resource can be inferred from regional figures for the eastern
Gulf of Mexico (Deuel, 1973). In the 1970 saltwater angling
survey, the eastern Gulf was defined as the area along the Gulf
Coast from the Florida Keys to the Mississippi River Delta.
The estimated number of saltwater fishermen and their catches
were:
Fishing area
Ocean Estuary Total
Thousands
Number of fishermen 633 915
Number of fishes caught 42,352 146,336 188,888
Total weight of fishes 111,177 222,943 334,120
There was no firm total for the number of fishermen, because some
anglers fished in both areas. However, approximately 1.5 million
individuals participated in saltwater sport fishing in the
eastern Gulf in 1970 and caught an estimated total of 189 million
4-11
-------
fishes; the average catch rate was 122 fishes (or 216 Ibs) per
angler per year. Of the total saltwater catch, 78 percent of the
fishes were caught in various bays, sounds, and tidal rivers of
the estuarine zone. A recent survey revealed that a total of
349,000 private recreational boats were used in saltwater fishing
in the Gulf of Mexico from November 1972 through October 1973
(Ridgely, 1975).
From different regions of the country, it has been estimated
that 65 to 90 percent of the species in the commercial landings
are estuarine-dependent (Sykes, 1968). Estuaries provide an
essential and irreplacable habitat for finfish and shellfish
species at various phases of their life cycle.
The importance of commercial fisheries to the economy of the
Pensacola area can be judged from records of commercial landings
in Escambia County during the past ten years (Florida Department
of Natural Resources, 1964-72 and U.S. National Marine Fisheries
Service, 1974). Annual landings are comparable in terms of
either dollars or weights, or both (Figure 4-5) . However,
weights are generally preferred for evaluating fluctuations and
trends because poundage is less influenced by inflationary
increases than are dollars.
Not all of the finfishes in the landings by county were
caught in nearby estuarine and coastal waters. Some may have
been taken in distant waters, such as off Louisiana and Campeche,
Mexico. However, more precise yields by area are kept for
selected valuable species, such as shrimp and oysters.
Annual poundage of finfish and shellfish in the commercial
landings of Escambia County steadily increased from a low of 3.2
million pounds in 1966 to a 10-year high of 5.6 million pounds in
1973. The five-year annual catch in the 1969-73 period
represented a 21 percent increase over the previous 1961-68
period (Table 4-3) .
The composition of the commercial landings in Escambia County
in 1973 was:
Species Pounds
Fishes 4,649,294
Blue Crab 69,451
Spanish lobster 62
Oysters 7,287
Shrimps (heads-on) 906,133
Squid 12,516
4-12
-------
6.0 -i
4.0 -
- 2.0 -
0.0
3.0 -i
2 2.0-
± 1.0-
0.0
n
64 65 66
67 68 69
YEAR
70 71 72 73
Figure 4-5. Trends in the commercial landing of finfish and
shellfish in Escambia County, Florida, 1964-1973.
4-13
-------
An additional 25,659 Ibs of oysters were harvested from the
beds in East Bay and landed in Santa Rosa County. Although the
political boundary of Santa Rosa County encompasses the eastern
half of Escambia Bay, all of East Bay, and portions of Pensacola
Bay, 95 percent of the total catch from the Pensacola Bay system
and adjacent offshore waters were landed in Escambia County.
Therefore, the values presented in Figure 4-5 and Table 4-3 for
the Pensacola area were depressed by roughly five percent.
During the past 10 years, the dollar value:of the landings,
which represented monies paid to the fishermen or wholesale
value, increased from 643 thousand dollars in 1964 to 2.1 million
dollars in 1973. This was more than a three-fold increase.
However, no adjustments were made for inflationary increases
since 1964. Processing, distribution and retailing create a two-
fold increase in the retail price over the wholesale or dockside
value. Thus, the commercial fishing industry generated over four
million dollars in the local economy in 1973.
Table 4-3. Total commercial landings of finfish and shellfish in
Escarcbia County, Florida from 1964 through 1973.
Year
1964
1965
1966
1967
1968
1969
1970
1971
1972
1973
Annual average
Landings
Pounds
3,367,085
3,480,821
3,170,075
3,291,330
U, 119,232
3,626,583
3,915,520
3,916,007
U, 968, 873
5,644,743
3,950,028
Dollars
643,874
772,322
883,475
923,668
1,191,738
1,039,101
1,039,607
1,395,483
1,757,793
2,115,015
1,176,258
Five-year average
(1964-1968)
Five-year average
(1969-1973)
3,485,709
4,414,347
883,258
1 ,469,400
4-14
-------
5 - POLLUTION SOURCES
POINT SOURCE DISCHARGES :
Introduction •. . '..• • •' "
: An aquatic estuarine ecosystem must 'have external- energy
sources to function at a productive level. For each estuary
there is an optimum productivity level based on the bathymetry,
hydrodynamics and climatology of the .system. At this level,
energy sources are utilized without causing • water * quality
problems such as depressed dissolved oxygen. In some cases,
waste discharges may provide energy sources that increase the
productivity of a system to its optimum level; unfortunately, in
the majority of cases, waste discharges cause over-production
that results in water quality problems. Thus, a knowledge of
waste discharges into the Pensacola Bay system is extremely
important in evaluating the condition of the system.
Although the study area is the estuarine reaches of the
Pensacola Bay system, information on waste discharges for the
entire drainage area of Escambia Bay will be provided in this
chapter.
Methods
Specific surveys of point source discharges were not
performed by the Escambia Bay Recovery Study. The data discussed
in this section were plant self monitoring reports obtained from
the Florida Department of Environmental Regulation (FDER),
Regional Office, Gulf Breeze, Florida; compliance monitoring
conducted by the U.S. Environmental Protection Agency (USEPA) and
its predecessor agency, the United States Department of Interior,
Federal Water Pollution Control Administration (USDI, FWPCA).
Results
General
There are a total of 23 significant (wastewater flow greater
than 378 m3/day or 0.1 mgd) municipal-private domestic point
sources and 10 significant industrial point sources discharging
into the Pensacola Bay system and its tributaries, the Escambia,
Blackwater, and Yellow Rivers. The locations of these point
sources are shown in Figure 5-1.
To control point source discharges, the National Pollutant
Discharge Elimination System (NPDES) was established by Public
Law 92-500 (92nd Congress 5.2770r October 18, 1972, Federal Water
Pollution Control Act Amendments of 1972, Section 402). Under
this system, permits are issued to each point source specifying
the quantities of pollutants that may be discharged into surface
5-1
-------
©
©
©
©
©
©
©
®
©'
©
MUNICIPAL POINT SOURCE FACILITIES
Andalusia
North Side disposal plant
West Side treatment plant
South Side disposal plant
Brant ley UTP
Brewcon WTP
Ease Brewcon UTP
Evergreen
Plane #1
Plant 02
Fort Deposit UTP
Greenville UTP
Luverne UTP
Troy
East Side WTP
West Side WTP
Century WTP
University of West Florida
Ponsacola, Northeast WTP
Pensecola, Main St. WTP
Warrington WTP
Penn Haven WTP
Gulf Breoze WTP
Pensacola Beach WTP
Milton WTP
Crcetvlew WTP
©
®
©
©
©
©
©
©
INDUSTRIAL POINT SOURCE FACILITIES
Container Corporation of Acer ICQ
T. R. Miller
Exxon Corporation
Alger - Sullivan Lueber Co.
Gulf Power
Monsanto Chemical Co.
Air Products and Chemical Co.
American Cyanatald Co.
NAS Whiting Field
NAS Pensacola
GQEENVILLE I
©
IO O ' 10 2O 50 40 W KilomtUr
Figure 5-1. Map of location of point sources.
5-2
-------
waters. Most of the permits issued contain interim and final
effluent limits. The interim limits usually reflect the amount
of waste water discharged when the permit was issued. The final
limits are designed to reduce plant discharges to an amount that
can be obtained after best practical treatment for a given
industrial wastewater or to a lower amount in areas where water
quality problems exist. Final effluent limits become effective
after the discharger has had adequate time to construct
facilities to meet the limits. The period of time required to
meet the final limits is determined when the permit is issued.
Information concerning NPDES permits for principal point sources
discharging into the Pensacola Bay system and its tributary
rivers is presented in Appendix 5-1.
Information on all significant point sources of waste in the
tributary area to the Pensacola Bay system is provided in
Appendices 5-2 and 5-3 for industrial discharges, and Appendix 5-
U for municipal-private domestic discharges into all rivers and
bays.
Principal Industrial Point Sources
Container Corporation of America
The Container Corporation of America, Brewton, Alabama,
integrated kraft mill began operation in December 1957 with an
average daily production of 272 MT/day (300 tons/day) (Alabama
Water Improvement Commission 1962), and production increased to
1043 MT/day (1150 tons/day) of paperboard in 1975, of which
approximately 50 percent is bleached (USEPA compliance monitoring
report for January 1975 study).
Wastewaters from this facility are from the unbleached pulp
process, bleach plant, and wood yard. Unbleached pulp process
wastewaters are treated in a clarifier, liquid oxygen applicator,
aeration basin, and oxidation pond; and then they flow through a
creek, swamp, and six natural lakes before discharging into the
Conecuh River, about 80 km (50 mi) upstream of Escambia Bay.
Bleach plant and woodyard effluents go directly to the creek,
swamp, and lake system. Sanitary wastewaters are discharged into
the clarifier to provide nutrients for treatment of unbleached
pulp process wastewaters.
Effluent loadings from the Container Corporation of America
Mill have decreased between 1969 and 1975 (Table 5-1). Using
196^9 as a base, the BODS effluent load discharged into the
Conecuh River decreased between 1962 and 1969. The BOD5 loading
was 30 percent less than the 1969 base during the January 1975
survey.
5-3
-------
Tahiti '3 - 1. Effluent loadiaqs from Container Corporation of America, brew ton, (. /ila.
en
Eato
Flow
(1)
tcrnd (niy)
+ 36."
-
-
+ 1 a . 6 4 4 '4 4
(9870)
-70.1 22 :a
(4<360)
-IB. 4 2221
(UU97)
-29.6 1 b J 0
(373-)
'4 charge
ii astl
1962
J S(D I ,
JSF.PA
-50.1+ JS2PA
-50.0 NPDiS
-52.:- JSSPA
er,;T. A. 'ani Sitt rall,F. H.
1970
, 1971a
, 1971b .
perrait application
compliance monitoring
report
(1) Pcjrcant cnange from Sept 1969
(2) Percant chanje from Auy 1970
(3) Unusually hij.i rlow due to rainfall during th^ study
(4) thousand cubic maters per day
-------
Monsanto Chemical Company
The Monsanto Chemical Company Pensacola Plant began
manufacturing nylon in December 1953 (USEPA, 1972a) . Nylon
production increased by 300 percent during the period 1953
through 1962 and by an additional 400 percent during 1963 to
1972. The principal products of the plant include nylon
intermediates and finished nylon.
Concentrated wastes generated at the plant are collected in a
separate system and disposed of by deep well injection. Other
waste streams, reported by the company to contain cooling water
and materials from spills, are discharged through two outfalls
into the Escambia River. The north outfall receives effluents
from the yarn manufacturing area and the research and development
building. The main outfall receives effluents from the remainder
of the plant. Sanitary wastes are treated by a primary treatment
plant and then discharged into a lagoon, which supplies makeup
water for cooling towers.
In the past, Monsanto Chemical Company Pensacola Plant
discharged a large quantity of waste into the Escambia River.
The chemical oxygen demand load discharged by the Pensacola Plant
from 1954 to 1972 is presented in Figure 5-2 (Monsanto Chemical
Corporation self monitoring data) . An extremely high average
annual load of 61,200 kg/day (135,000 Ibs/day) was discharged
into the Escambia River in 1955. The waste load decreased until
1959, and then increased until 1963, when a peak average annual
load of 33,100 kg/day (73,000 Ibs/day) was discharged. Waste
injection wells were installed after 1963 and the discharge to
the Escambia River decreased steadily after that time.
The five-day biochemical oxygen demand (BOD5) load discharged
by the Pensacola Plant has decreased by 92.6 percent between
September 1969 and January 1975 based on USEPA monitoring studies
(Table 5-2). Mean monthly BODS waste loadings (self-monitoring
data) indicate discharges vary considerably, but a general
downward trend is evident (Figure 5-3). The exception to this is
relatively large discharges in May and July 1972, and small
discharges in September and November 1972, and January 1973.
Total nitrogen and phosphorus discharges have decreased by
93.8 and 96.5 percent, respectively, between September 1969 and
January 1975, based on USEPA monitoring data (Table 5-2). Mean
monthly self-monitoring data (Figure 5-4) indicated the quantity
of total nitrogen discharged was relatively constant during 1971
through 1974. During the same period, the mean monthly total
phosphorus effluent load was extremely variable and no trends
were obvious.
5-5
-------
140
120
tn
I
I
o
o
o
o
1 80
z
UJ
o
X
60
UJ
40
20
, MONSANTO CHEMICAL COMPANY
NET CHEMICAL OXYGEN DEMAND WASTE LOAD
DISCHARGED INTO THE ESCAMBIA RIVER
( FROM USEPA, 1972 a )
Monsanto Data
EPA Result* March 7-14,1972
O
-------
Table 5-2. Summary of data collected at Monsanto Chemical Co., Amsrican Cyanamid CD., ini Air Products and Chamicals, Inc.
by the 0. 5. Environmental Protection Agency and its predecessor agencies.
Date
MONSANTO CHEMICAL
Sep. 1959
Mar. 1972
Feb. 1974
Jan. 1975
AMERICAN CYANAH1D
Sep. 1969
Mar. 1572
Feb. 1974
Jan. 1975
AIE PnOCUCTS AND
Sep. 1969
Mar. 1972
Jan. 1975
Flow
tcrad (1)
(mgd)
CO.
198.7
(52.5)
127.2
(33.6)
112.4
(29.7)
75.5
(21.0)
CO.
17.0
(4.5)
20.4
(5.4)
16. 3
(4.3)
16.4
(4.33)
CHEMICALS
19.7
(5.2)
6 .8
(1.8)
3.8
(1.C)
BOD5
kg/day % change
4580
(1010C)
526 -88.5
(1160)
943 -79.4
(2080)
339 -92.6
(746)
2020
(4450)
2900 +44.0
(6390)
1520 -25.0
(3350)
3230- +62.0
(7240)
130
(290)
84 -35.0
(105)
29 -78.0
(64)
TSS
kg/day X change
(PPd)
-
603
(1330)
1925
(4246)
— ~
460
(1020)
366
(806)
329
(725)
-
120
(26C)
26
(58)
Total-Nitrogen
kg/day £ change
1452
(32 CO)
303 -79.1
(668)
263 -81.9
(5801
90 -93.8
(198|
22CC
(4850)
1750 -20.0
(3850)
1270 -42.0
(2800)
1480 -33.0
(3260)
2560
(5650)
145; -43.0
(3190)
554 -78.0
(1220)
Total- Phosphor us
kg/lay 8 change
191
(421|
27 -85.7
(60)
20 -
-------
- 2000
*
i I
j i
f !
'• \ A • ! «
! * 1 '. * ! '. \
! • > • \ i i i i .
•. .- • / \ ;•!.••..!
•. ft ;«
i\; ^ mi i en
•.: •CUIIIID
UIIMTO
III PIOOOCTi
Figure 5-3. Average monthly BODS effluent loads (based on
company self-monitoring data).
jnnfl .
IIEIICII
ennui o
111 raoBocit
•OIIIITO
Figure 5-U. Average monthly total nitrogen effluent loads (based
on company self-monitoring data).
5-8
-------
American Cyanamid Company
The American Cyanamid Company, Santa Rosa Plant, has produced
acrylic polymer from acrylonitrile and methyl-methacrylate
monomers since 1958. The monomers are reacted, washed, stored,
and, when needed, dissolved in sodium thiocyanate solvent. The
dissolved polymer is passed through spinnerettes which produce
continuous fibers. The solvent is separated from the fiber by
countercurrent washing with water. Solvent recovery is built
into the manufacturing process, and more than 99 percent of the
solvent is recovered and reused. The fiber is then subjected to
further mechanical processes of crimping, cutting, and bailing.
Fiber production in September 1969 was about 103 MT/day (111
tons/day) (USEPA 1972b). Fiber production was about 107 MT/day
(118 tons/day) in March 1972 and increased to 122 MT/day (135
tons/day) in 1974 and early 1975.
/•
Treatment facilities at the plant consist of two 1.6 ha (4.0
acre) baffled lagoons. The influent to the lagoons is composed
of process and primary treated sanitary wastewaters. Sanitary
wastes receive preliminary treatment through a_ manual bar screen
and two Spirahoff units. The effluent is discharged into
Escambia Bay through a 1524 m (5000 ft) submerged outfall with
three diffusers spaced at intervals of 183 m (600 ft) . Under the
terms of the American Cyanamid Company NPDES permit (No.
FL0002593), their facility shall commence discharging into a deep
well disposal system by May 31, 1975. This deep well will be an
interim method of waste disposal. This company is required to
perform treatability and pilot plant studies for surface
treatment of the total plant waste by March 31, 1978.
Four studies of the American Cyanamid Plant were performed by
USEPA and its predecessor agencies (Table 5-2). The BOD5
discharge loading from the Santa Rosa Plant increased by 62
percent between the September 1969 and January 1975 surveys. The
total nitrogen load discharged by the plant decreased by 33.0
percent between the same surveys.
Monthly average effluent data from 1971 through 1974 for
BOD5, total nitrogen, and total phosphorus and cyanide indicated
the discharge varies considerably.
The monthly average BODS waste loading from the plant was
very erratic and there was a decrease in the discharge in late
1974 (Figure 5-3).
Total nitrogen discharges by the plant were relatively
constant between October 1971 and September 1974 (Figure 5-4),
with the exception of an extremely high mean monthly discharge in
October 1973. The quantity of phosphorus discharged by this
plant was extremely small (Figure 5-5). The quantity of cyanide
discharged by the plant decreased drastically between late 1971
and early 1972 (Figure 5-6), and remained relatively low
thereafter.
5-9
-------
o
10 -
Q O AIR PRODUCTS
A---4 MONSANTO
' • AMERICAN CYANAMIO
I9TI
1972
1973
1974
Figure 5-5. Average monthly total phosphorus effluent loads
(from company self-monitoring data) .
Figure 5-6. Average monthly cyanide effluent loading from
American Cyanamid Co.
5-10
-------
Air Products and Chemicals, Incorporated
The Escambia Plant was constructed in 1955, and it produces
ammonium nitrate, ammonia, nitric acid, amines, urea,
dinitrotoluene, and polyvinyl chloride. In 1970, methanol and
mixed fertilizer (NPK) plants at this facility were closed.
The wastewater treatment system at the plant consists of a
3.2 ha (8.0 acre) anaerobic lagoon, followed by four aerobic
lagoons with a total area of 29.4 ha (72.5 acres) , and finally
discharges into Escambia Bay. The plant has a serious problem
with contaminated groundwater, which accounted for 50 percent of
the total nitrogen in the plant effluent (USEPA, 1972c) . The
plant has reduced this problem by improved housekeeping and by
intercepting contaminated groundwater before it enters the lagoon
system.
Based on U.S. Environmental Protection Agency studies, BOD5,
total nitrogen, and total phosphorus have been reduced by 78, 78,
and 95 percent, respectively, between September 1969 and January
1975 (See Table 5-2).
Company self-monitoring data again indicated the effluent
loads from this plant were variable. Mean monthly BODS effluent
loads discharged in 1973 and 1974 were much lower than the 1971
effluent loading (Figure 5-3) .
The mean monthly total nitrogen loads discharged were
extremely high during the last half of 1970 and 1971 (Figure 5-1)
and decreased steadily after April 1974.
Monthly average total phosphorus discharges by the plant were
extremely erratic between June 1970 and September 1974 (Figure 5-
5).
Gulf Power Corporation
The Gulf Power Corporation steam plant is located 5.3 km (3.3
mi) upstream of the mouth of the Escambia River. This fossil
fuel electric generating plant produces 10,791 MWH of electricity
(application for Corps of Engineers Discharge Permit - EPA, NPDES
permit - dated July 13, 1971). The effluent consists of 1.09 x
10* m^/day (288 mgd) of cooling water, 16.3 x 10^ m'/day (U.3
mgd) of ash sluice water, and 21.9 x 103 m3/day (5.8 mgd) of
cooling tower blowdown. Under the conditions of the NPDES permit
(No. F10002275) issued to this plant, off-stream cooling
facilities for the entire discharge are to be operational by
February 26, 1976.
5-11
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U.S. Naval Air Station, Pensacola
A primary mission of the Naval Air Station (NAS) at Pensacola
is to overhaul and rework aircraft, including air frames and
aircraft engines (USEPA, 1972d). The base population of
approximately 16,755 people includes naval personnel, • dependents,
and civilians.
The wastewater treatment plant provides the equivalent,of
secondary treatment for all domestic and industrial wastes from
the station (USEPA, 1972d). This system includes an old primary
plant, which treated the domestic wastes prior to construction of
the present 3.0 mgd combined treatment plant. The wastewater
flow is about two-thirds domestic and one-third industrial. The
Navy plans to increase the old primary portion of the wastewater
treatment plant to 9.5 x 103 m3/day (2.5 mgd). Before the
existing waste treatment plant began .operation, several waste
streams (with and without treatment) discharged into Pensacola
Bay from various locations around the station. At the present
time, the effluent is discharged into Pensacola Bay through a
submerged outfall line, 61 cm (24 in) in diameter and 732 m
(2,400 ft) in length.
In March 1972, the USEPA (1972d) collected a single 24-hour
composite sample at the polishing pond discharge (prior to
chlorination) of this facility. The organic load discharged from
this facility was 42 Ibs/day of BOD5, 988 Ibs/day of COD, 382
Ibs/day of organic carbon and 146 Ibs/day of oil and grease.
Metal analyses showed that the discharge into Pensacola Bay also
contained 1.3 Ibs/day of total chromium, 0.7 Ibs/day of
manganese, and 0.7 Ibs/day of zinc. The daily discharges also
contained 0.2 Ibs of phenols and 0.3 Ibs of cyanide. The metal,
phenol, and cyanide loadings are relatively small and should not
significantly contribute to the concentration of these substances
in Pensacola Bay.
U.S. Naval Air Station, Whiting Field
The treatment facility at the Naval Air Station, Whiting
Field, Milton, Florida, was constructed in the 1940's. Treatment
consists of grit removal, primary clarification, standard rate
trickling filter, secondary clarification, chlorination, and
aerobic sludge digestion. The effluent is discharged into Clear
Creek, a tributary of the Blackwater River.
Principal Municipal-Private Domestic Point Sources
City of Pensacola, Main Street Plant
The Main Street Wastewater Treatment Plant serves a majority
of the population in the Pensacola metropolitan area. This
activated sludge secondary treatment plant was designed for a
sewage flow of 34.0 x 103 m3/day (9.0 mgd) ,;and presently serves
a population of 55,000 and numerous industries ;(Table 5-3) .
5-12
-------
Treatment provided at the plant consists of screening,
preaeration, grit removal, primary settling, activated sludge
aeration, secondary settling, chlorination, anaerobic digestion,
vacuum filtration of sludge, and sludge disposal in a landfill.
The effluent is discharged through a 121 cm (48 in) diameter
submerged outfall line which extends 853 m (2,800 ft) into
Pensacola Bay. In addition to receiving domestic waste, the Main
Street Treatment Plant receives between 7.6 x 103 and 11.3 x 103
m3/day (2.0 and 3.0 mgd) of industrial waste (USEPA, I972d).
In March 1972 a survey of the plant by the USEPA (1972d) was
performed. Operating reports indicated that the plant was
providing 80 to 90 percent treatment at that time. Based on one
composite sample, 800 kg/day (1800 Ibs/day) of BODS, 1300 kg/day
(2900 Ibs/day) of total suspended solids, 1100 kg/day (2400
Ibs/day) of total nitrogen, and 290 kg/day (633 Ibs/day) of total
phosphorus were discharged.
The mean monthly BOD5 and TSS waste loads discharged by the
Main Street Wastewater Treatment Plant in 1973 and 1974, based on
self-monitoring data, were extremely variable. The annual
average BODS loads discharged in 1973 and 1974 were 570 kg/day
(1263 Ibs/day) and 870 kg/day (1920 Ibs/day), respectively; and
the ranges of BOD5 discharges were 157 to 1035 kg/day in 1973 and
547 to 1298 kg/day in 1974. Removal levels of BOD5 were 92.9
percent in 1973 and 88.2 percent in 1974. In 1973 the mean
annual suspended solids discharge was 940 kg/day (2080 Ibs/day)
and in 1974 the mean annual load discharged was 1120 kg/day (2460
Ibs/day). Between February and September 1974, an average of 230
kg/day (510 Ibs/day) of nitrate nitrogen and 160 kg/day (350
Ibs/day) of total phosphorus was discharged. The mean flow from
the plant during 1974 was 34.0 x 103 m3/day (9 mgd). The plant
reported exceptionally high flows for June through November 1974
due to high industrial discharges (letter from D. M. Heath,
Department of Public Utilities, City of Pensacola, Florida,
February 12, 1975).
To serve the future population of the Pensacola area, the
City of Pensacola is planning to expand this plant to 75.6 x 103
m3/day (20 mgd) and provide advanced waste treatment. Plans also
include the extension of the outfall line in Pensacola Bay
(letter from D.M. Heath).
City of Pensacola, Northeast Wastewater Treatment Plant
This wastewater treatment plant began operation in 1962, and
serves a population of approximately 11,000. The design flow of
the plant is 3.8 x 103 m3/day (1.0 mgd). The waste undergoes
screening, preaeration, grit removal, primary settling,
biological treatment using trickling filters, chemical treatment,
secondary settling, effluent chlorination, and disposal through a
550 m (1,804 ft) outfall line discharging into Escambia Bay just
south of Devils Point in 1.4 m (4.5 ft) of water (NPDES permit
application).
5-13
-------
Table 5-3. Ma-jor industrial discharges tc the (lain Street wastewat.er treatment
plant.
Industry
P re treatment
Aqrico Chemical Co.
Armstrong Cork Co.
Ashland Chemical Co.
Deasley Packing Co. of Florida, Inc.
Borden Co.
Escambia Treating Co.
Florida Sausage Co., Inc.
Gulf Coast Plating, Inc.
Pepsi-Cola Bottling Co. of Florida, Inc
Tenneco Chemicals, Inc.
Lime treatment - holding pond
Solids Removal - Neutralization
Holding Pond
Holding (Evaporation) Pond
Solids Removal - Neutralization
5-14
-------
The effluent from the Northeast Wastewater Treatment Plant
was sampled by the U.S. Department of Interior (1970) in
September 1969, and 207 kg/day (457 Ibs/day) of BODS, 765 kg/day
(1,688 Ibs/day) of total nitrogen, and 97 kg/day (213 Ibs/day) of
total phosphorus were measured. In the report on the above study
the flow was estimated at 3.8 x 103 m3/day (1.0 mgd) but the City
of Pensacola claimed that the flow was about 1.9 x 103 m3/day
(0.5 mgd) during the study (USDI, 1970). Another survey was
conducted by USEPA (1972d) in March 1972 and indicated the
discharge contained 159 kg/day (351 lbs/day| of BOD5, 60 kg/day
(132 Ibs/day) of total suspended solids (TSS) , 87 kg/day (191
Ibs/day) of total nitrogen, and 25 kg/day (56 Ibs/day) of total
phosphorus. The effluent flow of the plant was 1.9 x 103 m3/day
(0.5 mgd) during this study.
Based on self-monitoring data, the mean annual BOD5 and TSS
levels in the effluent were 82 kg/day (181 Ibs/day) and 101
kg/day (223 Ibs/day), respectively, in 1973; and 154 kg/day (340
Ibs/day) and 161 kg/day (355 Ibs/day), respectively, in 1974.
The average degree of BOD5 removal was 92.5 percent in 1973 and
84.2 percent in 1974
The Northeast Wastewater Treatment Plant is being enlarged to
treat 1.85 mgd. A higher degree of treatment than secondary will
be provided and by June 30, 1975 the plant will only be allowed
to discharge 53 kg/day (116 Ibs/day) of BODS and TSS, 63 kg/day
(139 Ibs/day) of total Kjeldahl nitrogen, and 15 kg/day (32
Ibs/day) of total phosphorus (NPDES permit) . The NPDES permit
for this plant also states that operation of this plant will be
discontinued when the Main Street Sewage Treatment Plant can
serve this area on or before June 30, 1977.
City of Milton Wastewater Treatment Plant
This 6.4 x 103 m3/day (1.7 mgd) secondary wastewater
treatment plant was placed in operation in 1955. Treatment units
consist of grit removal, primary clarification, high-rate
trickling filters, secondary clarification, chlorination and
anaerobic sludge digestion. The plant effluent is discharged
into the Blackwater River.
The USEPA (1972d) collected a 24 hour composite sample from
this plant in March 1972, when the average flow through the plant
was 3.8 x 103 m'/day (0.99 mgd). Analysis of the samples
indicated that the amount of BODS, TSS, total nitrogen, and total
phosphorus loads discharged were 180, 98 103, and 35 kg/day (396,
215, 227, and 78 Ibs/day), respectively.
The quantity of waste discharged by the plant for a portion
of 1974 (January through June, and August) based on self-
monitoring data indicates that the BODS load discharged has
increased considerably since 1972 and the TSS load discharged has
remained the same. The mean effluent flow during this pariod was
1.9 x 103 m3/day (1.3 mgd) which was 76 percent of design flow.
5-15
-------
The mean BOD5 discharge load was 299 kg/day (659 Ibs/day) with a
range of mean monthly values from 200 to 387 kg/day (441 to 851
Ibs/day), and the mean monthly TSS effluent load was 99 kg/day
(218 Ibs/day) with a range from 46 kg/day (101 Ibs/day) to 176
kg/day (387 Ibs/day).
Other Significant Point Sources
The three industrial and twenty municipal-private domestic
point sources not discussed in the previous sections are
described in Appendices 5-2, 5-3, and 5-4.
Discussion
The Pensacola Bay system and its total drainage area receives
a considerable quantity of waste from man-associated point
sources (Table 5-4). The total amounts of waste that can be
discharged, based on present NPDES permit limits (in effect
during Janaury 1975) or estimated permit limits for sources where
permits have not been issued, are 10,198 kg/day (22,480 Ibs/day)
of BODS , 11,796 kg/day (26,000 Ibs/day) of TSS, 5,474 kg/day
(12,070 Ibs/day) of total nitrogen, and 1,368 kg/day (3,016
Ibs/day) of total phosphorus.
Sixty percent, or 6120 kg/day (13,490 Ibs/day), of the total
quantity of BOD5 discharged, entered the estuarine reaches of the
system. The forty percent of the BODS discharge that entered
freshwater reaches, travels at least 50 km (31 mi) before
arriving at the estuarine reaches and should be assimilated in
the river. Escambia Bay received 34 percent of the total
quantity of BOD5 discharged by point sources to the system and
Pensacola Bay received 17 percent.
The estuarine reaches of the Pensacola Bay system received 30
percent, 3,540 kg/day (7,800 Ibs/day), of the total quantity of
TSS discharged by point sources. The Conecuh River received 69
percent of the total TSS discharge by point sources, 8,193 kg/day
(18,062 Ibs/day), and this consisted mainly of the effluent from
the Container corporation of America paper mill which may
discharge 4,490 kg/day (9,900 Ibs/day).
Most (79 percent) of the total nitrogen received by the
Pensacola Bay system is discharged into the estuarine reaches.
Of this, 43 percent is discharged by point sources into Escambia
Bay and 24 percent into Pensacola Bay.
Sixty-four percent of the total phosphorus discharged into
the system is received by estuarine reaches. Pensacola Bay
receives 44 percent of the total discharge, or 602-kg/day (1,330
Ibs/day).
Most of the discharges to the freshwater reaches of the
Pensacola Bay system occur at a distance of at least 50 km (31
mi) upstream of the estuarine reaches of the system. Based on
5-16
-------
Table 5-4. Summary of industrial and domestic - municipal point sources of .discharge into the
Pensasola Bay system by drainaye area.
'• • > Total
Drainage Area 300 5
Load
(kg/day)
Conecuh River 3865
0' Escambia Kiver 511
l
-» Elackwatar River 312
-j
Y.ellofc River 170
Escantbia Bay 3432
Fensacola Bay 1685
Santa Hosa Sound (west end) 223
Total kg/day 10198
(ppd) (22480)
Percent
(X)
38
5
2
2
34
17
2
Suspended
Solids
Load
(kg/day)
8193
113
312
170
1039
1685
284
11796
(26000)
Percent
(*)
59
1
3
1
9
14
2
Total .
Nitrogen
Load
(kg/day)
1019
271
243
132
2351
1308
150
5474
(12070)
Percent
'(»)-
19
5
4
2
.43
. 24
3
Total
Phosphorus
Load
(kg/day)
439
39
104
57
63
602
64
1368
(3016)
Parcent
(»)
32
3
8
4
5
44
5
-------
the low concentrations of pollutants at the upstream end of the
estuarine reach, these discharges appear to be assimilated in.the
rivers before they enter the estuaries. Consequently, water
quality problems in the bays appear to be due to discharges
entering the estuarine areas directly. .
NON-POINT SOURCES , .
Non-point sources of pollution into the Pensacola Bay system
consist of: 1) urban storm water runoff; 2) agricultural runoff;
3) forest and swamp drainage and runoff; and 4) groundwater
seepage^ into surface waters. The first three categories are
slug type discharges that occur during rainstorms. Urban storm
water runoff usually contains substantial quantities of suspended
solids/ oxygen demanding materials, nutrients, bacteria, oil,
grease, and miscellaneous debris such as sticks and paper. The
pollutant load in urban storm water runoff depends on the amount
of the above materials present, the topography and type of ground
cover in the drainage basin, the intensity and duration of the
rain storm, and the period between rain storms. Agricultural
land runoff-pollutant loads depend on the type of soil, the type
of agricultural activity, fertilizer types and application
schedule, and rainfall patterns. Because of the ability of
heavily vegetated forests, marshes, and swamps to hold runoff,
the pollutant loads from this category are lower than the two
categories previously discussed. However, intense rainfall may
flush swamp waters containing low dissolved oxygen concentration,
low pH, and some oxygen demanding potential into the bay system.
In the Water Quality Management Plan for Escambia and Santa
Rosa Counties (Henningson, Durham and Richardson, 1975), unit
values (per km2) of average annual BODS and nutrient loads for
the three categories discussed above were developed from study
area data and a literature review. These unit values are
presented in Table 5-5.
Groundwater discharges into surface waters consist of
material from septic tank drain field leachate, sanitary landfill
leachate, and the pollutants described above that infiltrate into
groundwaters. Pollutant discharges from groundwaters entering
surface waters were not considered in this report. However,
this contribution is significant and should be the subject of
further studies.
The average annual loading due to storm water runoff from
urban, agricultural, and forest-marsh-swamp areas was 3,111, 676,
and 205 kg/day of BODS, total nitrogen and total phosphorus,
respectively. The breakdown of these loadings by system
components are shown in Table 5-6, which only includes non-point
source discharges directly into estuarine areas and the Pond
Creek drainage basin. The breakdown of land use and the
pollutant discharges were obtained from Exhibit 6-2 of the Water
Quality Management Plan (Henningson, Durham and Richardson,
1975). The total land area considered in this analysis was 828.5
5-18
-------
km2 (319.9 mi2). The classification of this area for urban,
forest-marsh-swamp, and agricultural use is 6.7, 7U.3, and 19.0
precent respectively.
Pensacola Bay received the greatest quantity of BOD5 and
significant amounts of total nitrogen and phosphorus from non-
point sources. Escambia Bay received the lowest quantities for
each pollutant, because the bluff on the west shore of Escambia
Bay prevents most urban storm water runoff from entering the bay.
This runoff entered the bay system through Bayou Texar which
received 14 percent of the BODS, 10 percent of the total
nitrogen, and 11 percent of the total phosphorus discharge to the
Pensacola Bay system.
In reality, the discharge from storm runoff would occur as
individual slugs and not continuously as inferred in Table 5-6.
The discharge loadings from stormwater runoff are comparable to
the point source pollutant loadings discussed in the previous
section, and, as is becoming evident in other sections of the
country, control of these materials will have to be considered.
5-19
-------
I
to
o
Table 5-5. Average annual quantities of stoca water cunoff ezpressed as
unit values.
Unit values (kg/dav/ko2)
Parameter Urban Agricultural Forest - Snanp
EOD5 12.2 7.7 1.2
• ' lotal Nitrogen 1.8 3.7 0.2
^' lotal Phosphorus C.6 0.6 0.1 ' '
Table 5-6. Average non - point source pollutaut discharges into the
estuacine reaches of the Pensacola 3ay system.
Total Total :
Basin • Area BODs Nitrogen 'Phosphorus
(Km2 ) (kg/day) (kg/day) (kg/day)
Escambia Bay
Eensacola Bay
Elackwatar River
East Bay
Total
126.9
1U8.7
316. 2
236. 7
828.5
U33
1,337
88U
U57
3,11 1
92
202
280
102
676
29
. 69
.. 70
37
205'
-------
6 - HYDRODYNAMICS
BATHYMETRY
The Pensacola Bay system is located in Escambia and Santa
Rosa Counties in the extreme northwest portion of Florida. The
Bay system contains four sub-systems - Pensacola Bay, Escambia
Bay, East Bay, and Blackwater Bay (Figure 6-1) .
The surface area and volume of the system were determined
using coast and Geodetic Survey Chart 1265 (17th Ed., Nov. 6,
1971). The areas of the bays were found using a planimeter. The
volume of the bays were determined by dividing each bay into 0.8
km squares and determining the volume of each square using the
mean chart depth for the particular square. The mean depth of
each bay was obtained by dividing the volume of each bay by its
area. Since the datum of the chart is mean low water, all
dimensions presented in this section are with respect to mean low
water.
The total area of the Pensacola Bay system (Table 6-1) is
372.9 km* (143.8 mi2), and its total volume is 1,348.8 x 10* m3
(47,640 million ft3). With respect to both surface area and
volume, the Pensacola Bay sub-system is the largest, with East,
-Escambia, and Blackwater Bays following in descending order.
FRESHWATER HYDROLOGY
Introduction
The freshwater discharge into an estuary affects the system
in numerous ways. The relationship between river discharges and
tides will dictate circulation patterns in the estuary, i.e.,
whether the type of circulation is two layer flow or homogeneous.
The river discharge controls the salinity of the estuary which in
turn determines the organisms that can live there. Large
quantities of materials are transported into the estuary by river
discharge. Some of these materials are nutrients, which provide
energy for the system, and others like suspended solids disrupt
energy flows by diminishing light penetration into the water.
Since all of these factors are related to, or controlled by,
river discharge, it is necessary to understand variations in
river discharge in order to evaluate a system.
Methods
All surface water records used to describe river discharges
into the Pensacola Bay system were obtained from the United
States Geological Survey, (1934 through 1974), and from
provisional data supplied by the United States Geological Survey,
District Office, Tallahassee, Florida. Information about the
rivers that discharge into the Pensacola Bay system, and the U.S.
Geological Survey streamflow gages located on them, are presented
in Table 6-2.
6-1
-------
I
to
Figure 6-1. Map of the Pensacola Bay system.
-------
Table 6-1. Suiaary of the bathymetry «f the Pcnsacola Day system. (Ml dati uitn
respect to aean low water *-'C 5 3S Chart 12o5, 17th Ei., Nov. 6, 1971.)
Table 6-2.
and yellow
Drainage Basin
JELtOK HIVE3
k»2
PENSSCOU BAH SUBSYSTEM
Pensacola Bay 133.6
Bayou Grande 3.8
Bayou Chico 1. 1
Bayou roiar 1. 5
subtotal 1UO.C
ESCANDIA BAY SUBSYSTEM
Escaibia Bay 92.6
nulatto Bayou 0.9
subtotal 93.5
BLACKHATEB BAY SUBSYSTEH
BlacXwiter Day 21. 6
Catfish Basin 0.9
subtotal 25.5
EAST 3AY SUBSYSTEM
East Bay 109. 1
East Bay Bayou 4.5
subtotal 113.9
Grand Total 372.9
Hi2
51.6
1.5
O.t
0.6
51.1
35.7
3.3
36.0
9.5
0.3
9.8
U2. 2
1.7
D3.9
1U3.3
SUDQary oC inforaation about najor streaaflow gaging
alvor drainage basins.
Gage no. Location of Gage
3680 Yellow River at .lilligan
BLACKHATEH 3IVE6
ESCSHBI* RIVE3
CONE CHEEK
Total Drainage
3705 Big Coldnater aiver
near Hilton
Baker
3755 Escambia Kiver near
Century
3760 Pine Barren Creek near
Barth
3707 Pond Creek near
Hilton
Area
Drainaje
a rea
kmj
(ni )
3380
(1335)
1616
(62I4)
w 1228
<«7U)
2227
(860)
61<*
(237)
531
(2C5)
10,963
(1233)
9836
(3817)
195
(75.3)
152
(58.7)
16,722
(6U57)
volun
lill. n3
793.8
10.3
2.0
2.3
838.9
225.7
1.4
227.1
•*7. 1
1. 1
as. 2
259.3
5.3
260.6
1348.8
stations
Hean
flow
a 3 /sac
(cfs)
J2
(I12U)
3C
(1351)
1U
(515)
9
(305)
170
(6315)
u
(111)
2
(72.9)
e
• ill. ft3
280U3
361
71
99
28570
7972
149
8021
166U
39
1732
9158
187
93«7
476UO
in the Escac
Plow/unit
area
a 3 /sec
per kmj
Ccfi2)
0.02
(1.80)
C.52
(2.22)
0.02
(2.17)
0.02
('."9|
0.02
(1.58)
0.02
(1.87)
C.01
(1.21)
:iean Depth
i ft
5.9 19.5
2.7 9.0
1.3 6.3
1.9 6.1
2.K 8.1
1.5 U.J
1.9 6.3
1. 2 3.9
2. U 7.9
1.2 3.9
nbia, Blackvater
7 day
10 yaar Period
n3 /sec
(cfs)
5.7 July 1938 to 1971
(201)
3.5 July 1938 to 197»
(331)
6. 1 Oct. 1938 to 197H
(215)
1.3 Bar. 1950 to 1974
(6H)
23.3 Oct. 1938 to 197»
(812)
1.7 Oct. 1952 to 19711
(60)
1.1 Jan. 19S8 to 1 97U
(33)
6-3
-------
The estimated discharge for the Escambia River drainage basin
was obtained by adding the flows for the Escambia River at
Century and Pine Barren Creek near Earth to the average of the
unit flows at Pine Barren Creek near Earth, and Pond Creek near
Milton, multiplied by the ungaged drainage area of the Escambia
River Basin as follows:
Q = Q + Q + [
-------
Results
The Escambia River is the fifth largest river in Florida
(Musgrove, et al., 1965). It starts near Union Springs, Alabama,
as the Conecuh River and changes to the Escambia River near the
Florida State Line. The drainage area is 10,963 km2 (4233 mi2)
of which 10 percent is in Florida. The mean Escambia River
discharge at Century, Florida was 170 m3/sec (6,016 cfs) from
1934 to 1974, and using the method described in the previous
section, the mean discharge of the Escambia River drainage basin
for 1935 to 1974 was 189 mVsec (6,687 cfs) . Mean annual flows
in the Escambia River at Century, Florida, ranged from 82 to 293
m3/sec in water years (October through September) 1960 through
1974 (Figure 6-2). The mean annual flow of 293 m3/sec (10,350
cfs) in water year 1973 was the highest annual flow since 1960
and the maximum monthly mean of 890 m3/sec (31,410 cfs) was also
the highest since 1960. Water year 1974 was also a high flow
year. Water years 1967, 1968, and 1969 had extremely low mean
annual discharges. In fact, the lowest mean annual flow for the
period of record, 82 m3/sec (2895 cfs), occurred in water year
1968.
The mean monthly discharges, along with the minimum and
maximum daily discharges for the Escambia River at ,Century,
Florida, during water years 1970 through 1974, were variable as
shown in Figure 6-3,, This figure shows the pattern of high flows
in March, and April and low flows in September, October, and
November described by Musgrove, et al. Water year 1973 began in
October 1972 with an extremely low mean monthly flow of 25 m3/sec
(868 cfs). From December through June, river discharges were
extremely high with a maximum mean monthly value of 890 m3/sec
(31,410 cfs) in April 1973. River discharges decreased to a mean
monthly value of 54 m3/sec (1917 cfs) in October 1973. During
water year 1974 high flows occurred in January, February, and
April. Low flows occurred in July, and an unusually high mean
monthly flow of 235 m3/sec (8,305 cfs) was measured in September
1973. This high discharge was due to rains from Hurricane
Carmen.
The mean annual discharges of the Escambia River at Century,
Florida, for water years 1935 to 1974 ranged from 82 to -296
m3/sec (Table 6-3). Water years 1967, 1968, and 1969 were
extreme low flow years and only eight, none and three years,
respectively, had lower mean annual flows. Water year 1972 was
also an extremely low flow year and only nine years had lower
mean annual flows. The mean annual discharge of 293 m3/sec
(10,350 cfs) in water year 1973 was only exceeded once during the
period of record. The mean annual discharge for water year 1974
was 190 m3/sec (6,708 cfs) and was exceeded by 12 years during
the period of record.
The Escambia River flooded in April 1973 and a maximum daily
flow of 2,097 m3/sec (74,100 cfs) having a return period of seven
years, was measured at Century, Florida. A maximum daily flood
flow of 1,221 m3/sec (43,100 cfs) occurred in September 1974,
6-5
-------
HIGH MONTHLY
MEAN
LOW MONTHLY
MEAN
ami Y[««S
Figure 6-2. Mean, high monthly mean, and low monthly mean
discharges for the Escambia River at Century, Florida for
water years 1960 through 197U.
141* r
in* •
it** •
... •
u.
4*.
i*.
•
y
i
:
t
t
('
\
•|
II
4
1
|
1
1
1
t
1
i
10
,
V
, j. /
/
i
,
•
i
<
\
\
i
<
*
\
V
•u
i
*
1
'«!
1
1
V
I
1
I
^
1
1
;
1
1
I
4
1
1
f
1
00
s
i
%-
i
•
i
•
i
•
i
i
i
<>
i
i
i
i
•-
i
•
t
<
•
i
i
i
\
w
Figure 6-3. Mean monthly, maximum daily, and minimum daily
discharge for the Escambia River at Century, Florida during
water years 1970 through 197U.
6-6
-------
Table 6-3. Mean annual discharge of the Escarabia River
at Century, Florida for water years 1935 through 1974.
Bank
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
Year
Mean Annual
Flow Bank
m
/sec
Mean Annual
year Flow
m 3 /sec
1968
1956
1951
1969
1963
1950
1955
1941
1967
1972
1953
1952
1945
1958
1957
1954
1935
1959
1937
1966
82
87
93
100
101
103
108
112
120
127
128
132
139
142
142
148
148
157
169
173
21
22
23
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
40
1940
1962
1933
1942
1970
1964
1939
1974
1965
1936
1943
1971
1943
1961
1960
1947
1949
1946
1973
1944
173
174
181
133
183
187
189
190
191
198
203
210
212
224
239
243
278
234
293
296
having a return period of three years. The return periods are
based on an analysis of annual maximum daily flows for the
Escambia River at Century, Florida, 1929 - 1971, performed by
Rumenik (letter dated April 17, 1973 from Roger P. Rumenik, U.S.
Geological Survey, Tallahassee, Florida). The maximum discharge
for the Escambia River was estimated to be 8,921 m^/sec (315,000
cfs) in March 1929 by the U.S. Geological Survey based on
information from local residents.
The seven-day, 10-year low flow, which is usually used to
describe critical low flow conditions, was 23 m^/sec (812 cfs)
for the Escambia River at Century, Florida, during the period of
record (Stone, 1974). The seven-day low flows for 1973 and 1974
were 17 m3/sec (605 cfs) and 38 m3/sec (1350 cfs), respectively.
The seven-day low flow in water year 1973 had a recurrence
interval of greater than 30. years. In water year 1974, the
recurrence interval was about two years (Stone, 1974). Thus,
extremely high and extremely low flows occurred in 1973.
6-7
-------
The total annual gaged river discharge into the Pensacola Bay
system from the three major river systems for the period of
record was 259 mVsec (9,150 cfs) as shown in Table 6-4. The
estimated total mean discharge from these river basins was 311
m3/sec (11,000 cfs), and the total mean gaged discharge was 83
percent of the estimated total mean discharge. The estimated
seven-day, 10-year .low flow, from the entire basin was 61 m3/sec
(2160 cfs).
FLOWS IN THE ESCAMBIA .RIVER , DELTA TRIBUTARIES
Introduction
Circulation in the northeastern section of upper Escambia Bay
was found to be poor during past studies (USDI, 1970). A lack of
freshwater discharge into this area, because it is farther from
the Gulf than the mouth of the Escambia River, was considered the
cause of this poor circulation. In the recommendations of the
Escambia Bay Conference that established the Escambia Bay
Recovery Study (USEPA, 1972e) it was suggested that the
feasibility of diverting freshwater from the Escambia River into
the northeast section of upper Escambia Bay be investigated.
Escambia River delta tributaries, such as the Little White and
Table 6 - 4. Total flows into the Pansacola Pay system.
River 5asin
Mean Annual Flow
lotal Gayed Total Estimated
in 3 /sec m 3 /sec
(cfs) (cfs)
7-day
10-year
LD* Flow
m 3 /sac
(cfs)
Zscambia
Elackwater
Yellow
Total
174
(6157)
23
(82C)
62
(2175)
259
(9150)
189
(669?)
44
(1570)
78
(2750)
' 311
(11000)
28
(1000)
18
(620)
15
(540)
61
(2160)
6-8
-------
Simpson Rivers, would have to be modified to accomplish the
diversion.
Methods
Discharge estimates in the Escambia, Little White, and
Simpson Rivers were performed on October 26, 1973, February 15,
1974, March 6, 1974, and April 16, 1974, during flood tides, and
river discharge was considered to be the seaward flow. Current
speed and direction in each river were measured using an
Oceanographic Engineering Corporation (Hydroproducts) Model 451
Savonius rotor current meter and Model 452 current direction
meter. The current meter was calibrated against a Marine
Advisor's Model S-6a ducted current meter with internal
calibration during each field study. Current speed and direction
and salinity were measured at approximately third points of a
lateral transect of the river during the October 26, 1973 study
and at quarter points during the other studies. At each current
measurement point, current and salinity measurements were made at
a depth of 0.2 m (0.5 ft) and then every 0.6 m (2.0 ft) . Four
current speed and direction measurements were made at each depth
and the averages were used in calculations. The cross-section
area of each river was measured using a Raytheon DE-719 Survey
Fathometer.
Discharge was calculated by drawing isopleths of constant
current speed on a drawing of the cross-section area and then
measuring the areas of constant current speed with a planimeter.
The total discharge of each river was estimated by summing the
products of cross-section area and current speed for all constant
current speed areas.
Salinity was measured using a Beckman RS5-3 induction
salinometer.
Results
Exploration of the tributaries in the Escambia River delta
indicated that Saltzmans Bayou, Little White River, and Simpson
River connect the Escambia Bay upstream of the U.S. Highway 90
Bridge with Escambia Bay (Figure 6-4). To determine the flow of
these rivers relative to the Escamtia River, flow was measured in
the Escambia, Little White, and Simpson Rivers on four occasions
at the locations shown on Figure 6-4. Flow was not measured in
Saltzmans Bayou because of its relatively small cross-section
area.
The measured total flow ranged from 80 to 87 percent of the
estimated total flow for the entire Escambia River basin (Table
6-5). An average of 75 percent of the total measured flow
entered Escambia Bay through the Escambia River, during the
studies; and averages of 16.5 and 8.5 percent of the total
measured flow entered the northeastern section of upper Escambia
Bay through the Simpson and Little White Rivers, respectively.
6-9
-------
Figure 6-U. Map of the Escambia River delta showing location of
discharge measurement stations.
6-10
-------
Table 6-5. Estimates ox flows in the Escarabia Hiver delta tributaries, 1973 - 1974.
Parameter
Measured total flow
Estimated total flow
Percent of estimated tota
ESCAMLJIA EIVER
Measured flow
Percent of measured total
Center channel Sdlinity -
Center channel salinity -
SIMPSON 3IVFR
Measured flow
Percent of measured total
Center channel salinity -
Center channel salinity -
LITTLE WHITE HIVER
Measured flow
Percent of measured total
Center channel salinity -
Center channel salinity -
1 flow
flow
surface
bottom
flow
surface
bottom
flow
surface
bottom
Change in tide level during study
Average wind speed
Units
in 3 /sec
m 3 /sec
percent
m /sec
percent
\jyt
p p t
m3 /sec
percent
opt
ppt
a
a /sec
percent
PPt
ppt
meters
km/hr
Date
October
48
55
•37
33
69
—
— —
B
17
4
23
7
14
6
21
+ C.23
12
February March
477
600
80
364
76
D
3
7 3
16
:
^
35
7
.^
'••-
+ 0. 29
9
155
191
81
119
77
0
0
28
13
0
A
J
3
5
o
0
• *0.20
19
April
410
497
82
320
78
3
o
60
15
0
•?
31
7
•}
0
O. 11
10
-------
Consequently, about 25 percent of the total flow of the Escambia
Fiver basin flows directly into the northeastern section of upper
Escambia Bay. However, most of this water does not alleviate
circulation problems in the vicinity of Floridatown and the
industrial discharges since it flows seaward in a southerly
direction along the Escambia River Delta. Thus, there appears to
be no justification for diverting additional water from the
Escambia River into the northeastern section of upper Escambia
Bay.
Although no flow measurements were made in Escambia River
delta tributaries downstream of the U.S. Highway 90 bridge, it is
believed that most of the discharge from the Escambia River
drainage area enters the Escambia Bay through the dredged channel
of the Escambia River. Other tributaries entering the bay in
this area are East River, Sullivans Ditch, and Gum River, and all
are relatively shallow, especially at their mouths.
TIDES
Introduction
Tidal energy is a major driving force of estuarine
circulation or water transport. The tides of the Gulf of Mexico
are relatively weak compared to those in the Atlantic Ocean;
nevertheless, they are considerably more complex. Marmer (1954)
in his excellent discussion of the tides in the Gulf of Mexico
separates tides into three major types. The first type is
semidiurnal where most of the time two tidal cycles of
approximately equal range occur each day. The second type is
mixed tides where either one or two tidal cycles with unequal
ranges can occur during a day. The third type is diurnal, with
one tidal cycle per day occurring most of the time.
At all locations in the Gulf of Mexico, tides are generally
mixed or diurnal, and because tide producing forces are
profoundly modified by hydrographic features, the type of tide
found from location to location varies significantly." Marmer1 s
(1954) explanation of the relatively large diurnal component in
Gulf tides is that due to the bathymetry of its basin its free
period of oscillation is about 24 hrs which approximates the
period of diurnal tide producing forces, and thus, it responds
better to the diurnal forces than to the semidiurnal forces. The
section of the coast of the Gulf of Mexico near Pensacola has
diurnal tides.
Methods
In 1973, two tide gages were installed in Escambia Bay by the
Escambia Bay Recovery Study. One was attached to the Interstate
10 bridge, west of the barge channel, and the other to the U.S.
Highway 90 bridge at the mouth of the Little White River. The
Interstate 10 tide gage proved unreliable and only the data
6-12
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collected by the U.S. Highway 90 tide gage will be discussed in
this section.
A Stevens Type-A71 water level recorder was used to measure
tide level. Recorder charts were changed monthly and the
recorder was calibrated against a known datum on the U.S. Highway
90 bridge. Mean sea level (MSL) as referred to in this report is
0.0 elevation 1929 datum.
Results
Typical tides for the Pensacola Bay system (Figure 6-5a)
include a bi-weekly cycle of variation in the number of tidal
cycles and the tide range. Two tidal cycles occurred on January
13, 26, and 27, and the range of these tides was less than 0.24 m
(0.80 ft). Approximately 7.5 days later the tidal range was 0.7
m (2.3 ft). Low range tides are known as equatorial tides and
they occur when the moon is over the equator; and high range
tides are known as tropic tides and they occur when the moon is
above the northern or southern tropics.
Weather can have profound affects on the tides. Tides on
January 20, 1974 -were unusual, since both the high and low tides
were considerably higher than the tide levels on the previous or
following days (Figure 6-5a). This is typical of the effects of
weather conditions;, Another example of this was an extremely
high tide of 0.76 m (2.5 ft) above MSL that occurred on September
8, 1974 (Figure 6-5b) due to Hurrican Carmen.
The mean tide level (MTL) on a given day usually does not
coincide with mean sea level (MSL) (Figure 6-6a) . The average
MTL in January, February, March, July, and August was below MSL;
in May it was slightly above MSL; and in April, June, and
September it was equal to MSL. The lowest mean tide level,
measured during February, was 0.55 m (1.80 ft) below MSL, which
means that 205.1 x 10* m3 (54.8 billion gallons) of water, or
about eight days of average inflow from all rivers discharging
into the bay, were displaced from the bay. The highest mean tide
level in February was 0.24 m (0*79 ft) above MSL. It should also
be noted that mean- sea level is not constant. Provost (1973)
indicates that MSL is rising at the rate of 0.3 m (1.0 ft) per
124 years at Pensacola.
Mean monthly tide ranges for January through September 1974
were relatively constant (Figure 6-6b). The mean tide range for
this nine-month period was 0.45 m (1.49 ft). The maximum tide
range was 0.98 m (3.2 ft) in September, and the minimum range was
0.06 m (0.20 ft) in January.
Discussion
The Pensacola Bay system is located on a section;of coast
which has the least amount of tidal energy available tb' drive
circulation of almost any coastal location in the United States
6-13
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0.5
8
-> US I
-1.0
II 14 IS 16 17 II 19 >0 II 22 21 24 25 26 27
JIDOtRV 1974
Figure 6-5a. Tides at U.S. 90 bridge during January 13-28, 1971,
34 S 6 7 8 9 10 II 12 13 14 IS 16 17 18
Figure 6-5b. Tides at U.S.
1974.
90 bridge during September 1-18,
6-1
-------
I
-^
(Ji
bJ
CD
K
O
O
00
a.
UJ
a
0.5 -
0.4 -
0.3 -
0.2 -
0. 1 -
0.0 -
0. 1 -
0.2 •
0.3 •
0.4 -
0.5 •
0.6 -
MSL
(
(
<
>
, T X
1 I 1
- -MAXIMUM
>• -MEAN
--MINIMUM
JAN ' FEB ' MAR ' APR ' MAY ' JUN ' JUL ' AUG ' SEP
1974
Figure 6-6a. Mean tide levels during January through September
197U at U.S. 90 bridge.
1 .0 n
0.8 -
I 0. 6 -
UJ
2 0.4-
<•
0. 2 -
o.o -
*
-<
L .
"H
K —
^ -<
r • — <
-
L~~ <
- -MAXIMUM
-MEAN
• -MINIMUM
JAN FEB MAR APR MAY JUN JUL AUG SEP
1974
Figure 6-6b. Mean tide range during January through September
197U at U.S. 90 bridge.
-------
on the Atlantic Ocean or Gulf of Mexico. Two factors contribute
to this: (1) The mean tidal range of 0.31 m (1.1 ft) at the
Pensacola Bay entrance is minimal; and (2) tides are- - diurnal.
Diurnal tides with a low tidal range also occur from Panama City,
Florida to the west as far as Louisiana. Thus,' at an Atlantic
coast estuary, with, the same tidalvrange, but where, the tides are
semidiurnal, twice the .volume of &ater is transported into and
out of the estuary each day. The matter is further compounded by
the occurrence of equatorial tides, about every seven days, that
have a tidal range near 0.15 m (0.5 ft) and last for about three
days.
Tidal ranges of selected southeastern estuaries (U.S. Dept.
of Commerce, 1975) are shown below:
Location
Tide Type
Tide Range
Charleston Harbor Semidiurnal
Savannah River
Semidiurnal
Saint Lucie Inlet Semidiurnal
Tampa Bay
Pensacola Bay
Mixed
Diurnal
m
1.6
2.1
0.8
0.6
0.3
ft
5.2
6.9
2.6
2.0
1.1
Of these estuaries, the tide range for Pensacola Bay is the
lowest; consequently, tidal forces are relatively weak in
Pensacola Bay compared to the other systems.
Marmer (1954) indicated that tidal ranges vary slowly over a
period of 18.6 years due to changes in the inclination of the
moon over the equator. Based on data presented by him for
Pensacola from 1931 to 1919, a period of low mean annual tidal
range is being approached, and the minimum point of the.18.6 year
cycle will be 1977. The mean annual tidal range will not exceed
the mean range until 1982.
. Based on the. above, the tidal contribution to the circulation
of the Pensacola Bay system -is relatively small compared to that
expected in other southeast estuaries.
SALINITY '
Introduction ,. .
In the Pensacola Bay system, as in most other estuaries,
seawater and freshwater combine to form a mixture. The salt
concentration or salinity of the mixture at any location, in the
estuary depends on forces such as river discharge, density,
meteorologic conditions, the earth's rotation, tides, and
6-16
-------
bathymetry of the system. Salinity is the weight (in grams) of
dissolved salts in one kg of water. Since salts are conservative
substances, salinity can be used as a tracer to describe the
effects of the above forces on the circulation of an estuary. A.
knowledge of salinity is also important from an ecological
standpoint, because the salinity regime of a system will
determine the organisms that can survive there.
Estuarine circulation was divided into four major types by
Bowden (1967):
• Salt wedge,
• Two-layer flow with entrainment,
• Two-layer flow with vertical mixing, and
• Vertically homogeneous.
Salt wedge circulation occurs when river flow dominates
circulation. A saltwater wedge sloping downwards in a riverward
(toward the freshwater source) direction extends along the bottom
into the estuary and there is practically no mixing between the
salt and freshwater layers. The earth's rotation, as represented
by the Coriolis Effect, causes the salt-freshwater interface to
slope downwards to the right in the northern hemisphere when
looking seaward.
When river flow is modified by tidal currents, estuarine
circulation becomes two-layer flow with entrainment. Saltwater
from the deeper layer is entrained into the freshwater layer and
the deeper layer remains unchanged. In reality, a certain amount
of mixing occurs between the layers and a transition zone with a
steep salinity gradient, known as a halocline, is formed.
In shallow estuaries, river flow and tidal mixing dominate
circulation and a pattern of two-layer flow with vertica1. mixing
occurs. Freshwater moves seaward in the upper layei and
saltwater moves riverward in the lower layer. This system is
known as a partially mixed estuary. The maximum salinity
gradient occurs near the level of no net motion. The volume of
water transported by this type of circulation in the upper and
lower layers may be many times the river discharge.
When the tidal currents are very strong relative to the river
discharge, vertical mixing can be so strong that the salinity
becomes homogeneous with depth. This is known as vertically
homogeneous circulation. A horizontal salinity gradient still
occurs in this type of estuary.
Methods
Salinity was measured in the field using a Beckman RS5-3
induction salinometer. The dates of the studies where salinity
6-17
-------
was measured are presented in Table 8-1. Surface measurements
were taken 0.3 m (1.0 ft) below the surface and bottom
measurements were taken 0.3 m (1.0 ft) above the bottom. The
mean sampling depth at each station is shown in Appendix 8-3 and
8-U, and the locations of the sampling stations are described in
Appendix 8-2.
The Two-Layer Model, a method of determining the flushing
rate of an estuary, has been described by Bowden (1967) . It is
assumed in the model that the exchange of water between the
estuary and the sea is caused by advection and that horizontal
diffusion is negligible. Accordingly, the rate of flow in the
two layers can be calculated, with a knowledge of the mean
salinity of the inflowing and outflowing layers and the river
discharge. According to Bowden (1967), the depth at which the
maximum salinity gradient is found is the level of no net motion.
Above this depth is the outflowing layer, and below is the
inflowing layer.
From the conditions for continuity of water and salt
Q - Q = R
Solving for the inflow and outflow
Qu = R/(1 - Su/Si)
Ql = R/(Si/Su - 1)
The flushing time of freshwater out of the estuary is
T = V/(Qux86,400) = Vd-Sy/S] )/(Rx86,400)
6-18
-------
where
R = river discharge - m3/sec
Qu = volume transport of outflowing water - m3/sec
QI = volume transport of inflowing water - m3/sec
Su = mean salinity of outflowing water - ppt
S-| = mean salinity of inflowing water - ppt
V = volume of water in the bay riverward of the salinity
measurement point - m3
T = flushing time - days
Using data from the James Estuary, Pritchard (1965) has
developed another method of determining the values of Su and S-\
to be used in the Two-Layer Model. In this method, the level of
no net motion is assumed to be the depth at which the salinity
gradient begins to decrease appreciably but which is above the
level of the maximum gradient. The mean salinity of the upper
two-thirds of the layer above this level is Su, and S] is the
mean salinity of the lower two-thirds of the layer below this
level. Pritchard1 s method of determining S and S-, was used in
this report.
Results and Discussion
Salinity Variation
Freshwater from Escambia River tended to stay on the western
side of Escambia Bay as it moved seaward (Figure 6-7) during
January through September 1974. The mean surface salinity values
in the northeastern portion of the upper bay (Stations EEKV, and
EGLY), were higher than those in the northwestern portion
(Stations EIIL and EIKC) which are farther seaward, but close to
the mouth of the river. Mean surface salinities were
considerably higher on the eastern side of the bay than directly
across the bay on the western side. Mean surface salinity data
also indicated that freshwater entering East Bay from Blackwater
Bay also flowed seaward on the western side of the Bay.
Intrusion of saltwater into the Escambia River is an inverse
function of river discharge. A saltwater wedge was not present
in the Escambia River, 14.2 km (8.8 mi) upstream of the mouth,
(Station ERIO) during any of the 1974 studies. A saltwater wedge
was observed, 7.4 km (4.6 mi) upstream of the mouth of the river,
when the effective Escambia River discharge was less than 85
6-19
-------
Figure 6-7. Mean surface and bottom salinities in the Pensacola
Bay system during January through September, 197U (Pensacola
Bay data from the University of West Florida).
6-20
-------
mVsec (3,012 cfs) . At the U.S. Highway 90 bridge, 2.6 km (1.6
mi) upstream of the mouth of the river, a saltwater wedge was
found in more than half of the studies when the estimated river
discharge was less than 226 mVsec (7974 cfs).
Mean salinities in Pensacola Bay indicate that less saline
water flows seaward along the northern side of the bay. The mean
salinity of seawater entering the bay (as indicated by the mean
bottom value at the inlet, Station P01) is 32.6 ppt. The mean
bottom values throughout the bay in the deep areas are only
slightly less than the salinity of incoming seawater, indicating
water from the lower layer is entrained into the upper layer, but
the reverse does not occur.
The movement of more freshwater seaward on the western side
of Escambia and East Bays and on the northern side of Pensacola
Bay appears due to the Coriolis Effect which is a function of the
earth's rotation. However, vertical stratification throughout
the system indicates that freshwater moves seaward and saltwater
moves riverward throughout the entire bay.
Fluctuations in salinity at most stations were considerable
during the studies in January through September 1974. The mean,
maximum, minimum, and coefficient of variation at each station
sampled is presented in Appendix 6-1.
Analysis of salinities in the Pensacola Bay system and river
discharge indicated that the higher the river discharge into the
system, the lower the salinity (Figure 6-8) . In addition, bays
with river inflows had lower mean salinities. Thus, mean
salinities in East Bay were always higher than those in Escambia
and Blackwater Bay. Pensacola Bay, being closest to the inlet,
had mean salinities 6.8- ppt higher than East Bay on the average.
There was a significant correlation between mean Escambia Bay
salinity and the inverse of the effective flow of the Escambia
River (r = 0.824, df = 11, p <0.01) .
Daily fluctuation of surface and bottom salinity and tide
level (measured in upper Escambia Bay at U.S. Highway 90 bridge)
is presented in Figure 6-9 for selected stations sampled during
the August 1973 water quality studies. During Study III, August
16, and 17, 1973, the variation in surface and bottom salinity
was two and one ppt, respectively, in mid Escambia Bay (Station
ENNB) when the tidal range was about 0.3 m (0.8 ft).. During.
Study IV, on August 23 through 24, 1973 when the tide range was
0.7 m (2.0 ft), the surface salinity varied by eight ppt and the
bottom salinity varied by one ppt. This indicates that tidal
mixing has a considerable influence on surface salinity and that
there was significant horizontal transport of surface water due
to. the tides. This also indicates that movement of bottom water
is limited.
6-21
-------
1200-
^ 1000-
w
" 800-
E
~ 600-
, 400 -
o
^ 200-
0
M
30 -
20-
0 -
l\
I \
I \
V-ALL TRIBUTARIES
«
/A-
A &' / \ %
'TOTAL MEAN ANNUAL FLOW
•ESCAMBIA RIVER
PENSACOLA BAY
ESCAMBIA BAY
^^-
BLACKWATER
JAN FEB MAR APR MAY JUN JUL AUG SEP
1974
Figure 6-8. Mean salinities of the components of the Pensacola
Bay system during January through September, 1974 and the
total effective discharge of the Escambia River and all
tributaries to the Pensacola Bay system (Pensacola Bay data
from the University of West Florida).
6-22
-------
_, 0.25-
„, -0.25-
o
K -0.50-
0.25
"SL
-0.23'
-0.30-
i i t-*x»
00 06 12 IB 00 06 HOUR
AUG. I 7, I97S «ie. IB, 1973
00 06 12 IB 00 06 HOUR
AUG. 24, 1973 WO. 29, 1973
-0.25-
-0.50-
u -0.25-
o
K -0.50-
00 06 12 IB 00 ' 06 HOUR
AUG. 17,1973 . W6. IS,1*71
00 06 12 .16 00 06 HOUR
AUG.24, 1(73 AUG.29, 1973
-0.25-
-0.50-
_, .0.29
w
u "SL
-I
w -0.25-
o
H -0.50-
00 06 12 IB 00 06 HOUR
AUO.16,1973 AUG.17,1973
00 06 12 IB 00 . 06 HOUR
AUG.23, 1973 AUG.24,1973
Figure 6-9. Salinity and tide variation at Stations ENNB, AJFD,
and POOH during the August 1973 water quality studies.
6-23
-------
In East Bay (Station AJFD) there was very little fluctuation
in salinity due to variation in tide level (Figure 6-9),
indicating that transport of water in East Bay was due to other
factors than tide.
In Pensacola Bay (Station POOH - PO5) , the surface water
salinities indicated tide caused the transport of surface water
(Figure 6-9). During Study III (August 17-18, 1973) surface
salinity varied by three ppt and during Study IV (August 24-25,
1973) surface salinity varied by 4.5 ppt. The salinity variation
followed tidal variation during both studies. Bottom salinity
was relatively constant during both studies, indicating
practically no movement of bottom water.
During Studies I and II in April 1973 the rivers discharging
into the Pensacola Bay system were at flood stage and the water
in the bays was essentially fresh.
Chloride concentrations in Escambia Bay were studied during
September 23 to 25, 1969 (USDI, 1970). The chloride
concentration was assumed to approximate chlorinity and the
following equation was used to convert the data collected to
salinity:
Salinity (ppt) = 1.80655 x Chloride (mg/l)/1000.
The mean salinity of Escambia Bay above the Interstate 10 bridge
was 18.4 ppt. At mid Escambia Bay (Station E25-ENNB) the mean
surface salinity was 17.0 ppt with a range of 13.9 to 19.5 ppt,
and the mean bottom salinity was 28.1 ppt with a range of 30.9 to
22.4 ppt.
Unused submerged pilings under the L and N Railroad bridge
were found to hinder circulation during the above study. The
conference on Escambia Bay (USDI, 1970a) recommended that these
excess pilings be removed, and this was accomplished shortly
thereafter.
Salinities were measured in Choctawhatchee Bay during a
survey performed on September 12, 1974. Surface salinities
increased from 0.0 ppt in the lower Choctawhatchee River (Station
Z06X) to about 22 ppt near the inlet (Figure 6-10). Bottom
salinities were near 20 ppt in the shallow eastern and western
ends of the bay, and near 30 ppt in the deep central portion of
the bay. The circulation type in the eastern portion of the bay
(Station ZLQE) was two-layer flow with vertical mixing, and that
in the central and western portions of the bay (Stations YK7U and
YNKF) was of the two-layer flow with entrainment. Thus,
circulation in Choctawhatchee Bay was similar to that in the
Pensacola Bay system.
6-24
-------
Figure 6-10. .Salinities (ppt) in Choctawhatchee Bay on September
12, 1974.
-------
Inflow and Outflow Based on Salinity
Evaluation of salinity-depth profiles for selected stations
in Escambia, East, and Pensacola Bays, sampled in 1974, provided
information on circulation in the Pensacola Bay system. Salinity
profiles in mid Escambia Bay (Station ENNB) indicated that
Escambia Bay has a stratified circulation pattern between
partially mixed and two-layer flow with entrainment (Figure 6-
11). During most studies there were three distinct layers, an
upper layer of homogeneous salinity 1.0 to 1.3 m (3.0 to 4.0 ft)
deep, a transition layer or halocline 0.7 to 1.6 m (2.0 to 5.0
ft) thick, and a lower layer of homogeneous salinity. The upper
layer usually had salinities less than 10.0 ppt and the lower
layer greater than 20.0 ppt.
In East Bay (Station AGJI), there was less vertical
stratification than in Escambia Bay (Figure 6-11). During most
of the studies three distinct layers were present, an upper layer
of homogeneous salinity (9.0 from 19.0 ppt) extending to 1.6 to
2.3 m (5.0 to 7.0 ft), a halocline, and a thin lower layer. The
salinity gradient of the halocline was steeper in East Bay than
in Escambia Bay, indicating less transfer between layers.
Pensacola Bay (Station P05) - sampled by the University of
West Florida) had two-layer flow with entrainment type
circulation during most of the 1974 studies (Figure 6-11). On
most of the sampling dates, a surface layer with a steep salinity
gradient and a homogeneous deep layer were present. The salinity
of the deep layer exceeded 30.0 ppt on all sampling dates. The
steep surface salinity gradient indicated poor mixing in the
surface layer. High salinity in the bottom layer indicated
entrainment of saltwater from the deep layer to the surface layer
was occurring, and that there was practically no transfer of
surface water into the lower layer.
The salinity profiles (Figure 6-11) and the salinity-tide
variation curves (Figure 6-9) both indicate a difference between
the salinity of the upper and lower layers in the bay. It
appears that as far as transport of pollutants in the- bay is
concerned the bay is vertically stratified or there are two
separate layers in the bay with limited exchange between them.
Due to this, the Pensacola Bay system must be regarded as a
three-dimensional system when considering circulation.
Flushing of the Pensacola Bay system was significantly
improved .by increased river inflows and tidal mixing, based on an
analysis using the Two-Layer Model (Table 6-6). The flushing
time increased from 21.2 days during a high river inflow period
(average for Studies I and II, April 1973) to 34.2 days during a
low river inflow period (average for Studies III and IV, August
1973). Tidal mixing accelerated flushing of the bay system by
12.9 days during a high river inflow period and by 62.6 days
during a low river inflow period. Mean river inflows to the
Pensacola Bay system were 1227 m3/sec or 294 percent of the mean
6-26
-------
Pensocolo Boy
to so o. to to
E scorn bio Boy
East Bay
JM.ll.ltM Q rii.ll. IIT4
s
0 10 10
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1
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10 tO
Station AGJI
Figure 6-11. Salinity-depth profiles at Stations P05, ENNB, and
AGJI during water quality studies performed in January
through September, 197U.
-------
annual inflow, during the high inflow period and 2U7 m^/sec or 79
percent of the mean annual inflow during the low inflow period.
Average tidal ranges were 0.4 m during both periods (Table 8-1).
The increase in tidal range associated with cycling from
equatorial to tropic tides caused a 12.7 day acceleration in
flushing of the bay system during the high inflow period and a
U1.7 day acceleration during the low inflow period (Table 6-7).
During ' both flow periods, river discharge was higher during the
studies with equatorial tides (low tidal ranges). Thus, the
acceleration in flushing of the bay system can only be attributed
to increased tidal mixing.
If we assume thatx tidal energy would cause about a 60-day
acceleration in flushing time, as it did during the low flow
period, the flushing time of Pensacola Bay system would be about
200 days for the seven-day, ten-year low flow of 61 m3/sec.
Bottom salinities during both of the high inflow and both of
the low inflow remained about the same even through river inflow
and tidal conditions changed (Figure 6-12). This is an
indication of weak bottom circulation.
The variables used in calculating flushing time are presented
in Appendix 6-2.
WATER TEMPERATURE
Introduction
Fluctuations in water temperatures are an extremely important
factor in determining the type of aquatic community that will
inhabit a body of water. High water temperatures also reduce
saturation values of dissolved gases in water, increase transfer
rates of gas between air and water, and accelerate the metabolic
rates of organisms in the system.
Methods
Temperatures were measured with a Beckman RS5-3 induction
salinometer and thermometer. Surface measurements were taken 0.3
m (1.0 ft) below the surface and bottom measurements were taken
0.3 m (1.0 ft) above the bottom. The mean sampling depth at each
station is presented in Appendix 8-4, and the locations of tfee
sampling stations are described in Appendix 8-2.
Results and Discussion
Mean temperatures in Escambia, East, Blackwater, and
Pensacola Bays during each 1974 water quality study were about
the same. In all of the bays, minimum temperature occurred in
February, and in all bays except Pensacola Bay the maximum mean
temperature occurred in July. Mean temperatures in Escambia Bay
and Pensacola Bay during each water quality study in 1974 are
shown in Figure 6-13. •
6-28
-------
Table 6-6. Flushing characteristics of the Pensacola Day system during high (Studies I and II)
and low (Studies III and IV) river inflow periods in April and August 1973 respectively.
Biver Inflow
flushing time (days)
High
Low
Eisplacemant time (days)
High . •
, Low
Reduction in flushing time
to tidal mixing (days)
High
' • L.°"
, -Table 6 - 7. Reduction
system during 1973.
fay
fscaoibia
East and Blackwater
Fensdcola
Total system
Flow ; >
Tides
Month
Escambia 3ast-Blackwater Pensacola Total
3.7 . 10.8 6.7 21.2
8.6 " 16.2 9.4 ;34.2
3.7 20.8 9.6 -34. 1 -
19.0 38.4 39. U 96.8
due
0.0 10.0 2.9 : 12.9
10.14 22.2 30.0 62.6
in flushing tine (days) due to tiual mixing in the Pensacala Bay
Studies
I II III IV :
0.0 0.0 5.1 :.15.7 .
5.6 14.2 17.1 27.3
0.8 4.9 19.5 U0.4
6.4 19.1 41.7- 33.4
• High High Low Low
Equatorial Tropic Equatorial ' Tropic
; April April August August
-------
2 -
w
Q
Escambia Bay (Station ERPB)
"" Study I
L
1 1 I
"" Study II
L
III
\ Study III
'. '}
1 II
~ Study \IV
: N
i i t
0 10. 20 30 0
SALINITY (ppt)
10 20 30 0 10 20 30 0 10 20
30
East Bay and Blackwater Bay (Station AKAA)
/•^
6 2
PL. ,
W 4
Study I
I II
Study II
II I
0 10 20 30 0
SALINITY (ppt)
Study \III
10 20 30 0
I I
Study ( IV
I I
10 20 30 0 10 20 30
12
16
Study I
Pensacola Bay (Station PQJQ)
II I
Study II
1
0 10 20 30 10 20 30
SALINITY (ppt)
Study III
I _L
I
Study \IV
I
40 10 20 30 40 10
20
I I I
30 40
Figure 6-12. Mean salinity-depth profiles over a tidal cycle at
stations near the center of the mouths of bays in the
Pensacola Bay system during 1973.
6-30
-------
Waters discharged into the Pensacola Bay system by tributary
streams were cooler than waters in the bay during every 1974
study (Figure 6-14, Appendix 6-3). Mean temperatures in lower
Escambia Bay, East Bay, and Pensacola Bay were slightly above
23°C and the mean surface and bottom temperatures were
essentially- the same. In Blackwater Bay and upper Escambia Bay/
mean temperatures were lower than those in the remainder of the
system due to mixing with cool river water.
The lowest water temperatures during the April and August
1973 water quality studies (Studies I through IV) were also found
near the Escambia River delta and were due to cool river water
entering the bay. The highest temperatures usually occurred in
Pensacola Bay. Generally, there was not much diurnal water
temperature^ fluctuation, .but the variation that occurred was
caused by solar heating in the afternoon. Water temperature data
collected, during intensive water quality studies performed ip
April * and August 1973 are-presented in Table*6-8. Surface and
bottom temper aft ur,es at all sampling stations., were 'essentially
20°C dur.ing the April studies I in August 1973 surface and bottom
water temperatures were near 30°C. In lower Escambia,"
temperature ranges." were about three and one °C .on the surface and
bottom, respectively, during the April studies^ and less than one
degree during the August studies. ,
An intensive water quality study'was performed in Escambia
Bay during September 23-25/1969 ,(USDI> 1970).. In lower Escambia
Bay, (Station E27 - ERPB)' the mean .surface and bottom water
temperatures were about 125°C.J The surface water temperature
range was. 23.0 ^to 27.Q°C, and the bottom water temperature range
was 23. 5"to 25.5°C.
The mean water temperature ,in Choctawhatchee Bay was 27.8°C,
with a range .of 25.5 to 29.U during a water quality study
performed there on September 12, t974.
-CIRCULATION IN ESCAMBIA BAY
Introduction
A circulation study was performed in Escambia Bay/that traced
Escambia River water as it mov^d throughout the7 bay under
conditions approximating "mean annual tidal range and river
discharge.
Methods
The study began at 0800 on August 6, 1974, when 45 kg (100
Ibs) of Rhodamine WT fluorescent dye were discharged uniformly
throughout the cross section of Escambia River. -*19 km (12, mi)
above its mouth, and it ended on'August 10, 1974. The tide was
beginning to ebb at"the U.S. Highway 90-tide gage during the dye
dump. The dye was sampled every three hours by two sampling
crews at 30 of the 60 sampling stations established for the study
6-31
-------
40-,
z 30H
111
QC
DC
111
Q.
2 0 •
10-
ESCAMBIA BAY
JAN
FEB
MAR
APR
MAY
1974
JUN
JUL
AUG
SEP
Figure 6-13. Mean temperature in Escambia Bay and Pensacola Bay
for each study performed in 197t (Pensacola Bay data from the
University of West Florida).
Figure 6-14. Mean surface and bottom temperatures for stations
sampled during January through September, 197U (Pensacola Bay
data from the University of West Florida) . •
6-32
-------
Table 6 - 3. Water temperature data (°C) tor 1973 intensive water quality studies.
o\
(JJ
Study
April
April
August
August
Date
13 - 15, 1973 - Study I
surface
bottom
19 - 21, 1973 - Study II
surface
bottom
16 - 18, 1973 - Study III
surface
bottom
23 - 25, 1973 - Study IV
surface
bottom
Mean
17.2
16. 4
19.7
19.8
28.8
29.9
28.0
29.0
Maximum Time
19.3 1250
17.1 2ia7
20.1 1906
20.0 1905
29.2 1619
30.2 1319
29.2 160a
29.4 1859
Date
a/13/73
4/13/73
4/19/73
4/19/73
8/16/73
8/16/73
8/23/73
8/23/73
Minimum Time
16.0 0700
15.9 1541
19.4 0703
19.5 1600
28.4 0320
29.7 0816
26.8 0740
28.7 0746
Date
4/13/73
4/13/73
4/19/73
4/19/73
8/17/73
3/16/73
8/23/73
3/23/73
-------
(Figure 6-15). Bottom dye samples (0.3 m - 1.0 ft above the
bottom) were collected with an incremented rod with a test tube
attached to the bottom. The test tube could be opened and closed
from the boat, to obtain a sample at any depth up to 2.1 m (7.0
ft). At depths greater than 2.1 m (7.0 ft)' a Kemmerer .sampler
was used. The water samples were kept in the dark until
analyzed.
The concentration of dye was measured.'at the EBRS laboratory
using an Aminco Fluoro-Microphotometer Model 4-7102. Dye
standards from 0.1 M9/1 to 3,000 pg/1 were prepared and the
instrument was standardized every 12 hours. All dye measurements
were made at 20.0°C + 0.1°C.
Salinity and temperature measurements were taken with a
Beckman RS5-3 induction salinometer in conjunction with each dye
sample.
Environmental Conditions
The effective flow of the Escambia River was. 190 m3/sec
(6,730 cfs), which is about mean annual flow, during this dye
study., The tide range at the U.S. Highway 90 tide gaging station
was O.Vm (1.2 ft) on August 6, 1974 and 0,.6 m (1.9 ft) on August
10, 1974 (Appendix 6-4) . Prevailing winds were from the south
'during the study and wind velocities were relatively low, less
than 12 km/hr.
There was considerable vertical salinity stratification in
the bay during the study, but the horizontal salinity
distribution remained relatively constant throughout the study.
Salinities were 2.8 and 17.0 ppt at the surface and bottom,
respectively, in upper Escambia Bay (Station D2) at: 1023 on
August 6; and 1.4 and 18.7 at the surface and bottom,
respectively, at the same location at 1018 on August 9. In the
lower bay (Station 13), surface and bottom salinities were 8.0
and 25.3 ppt, respectively, at 2210 on August 7; and 6.5 and 26.1
ppt, respectively, at 1618'on August 9. Water temperature in
Escambia Bay ranged between 26 and 32°C during the study.
Results and Discussion
The time (average time of sa.mpling run) that the first major
dye peak arrived at the surface of each sampling station is shown
in Figure 6-15. The isopleths indicate the location of this dye
peak during odd-numbered runs. A dye peak was first measured in
Macky Bay about 16 hr after the dye dump, indicating that a
significant amount of water from the Escambia River enters Macky
Bay. The dye reached the 1-10 bridge after about 8 hr of travel
in the bay and Devils Point after about 19 hr in the bay. South
of the 1-10 bridge, dye arrived near Indian Bayou on the East
shore of the bay about 26 hr after entering the bay. The first
major dye peak reached-the mouth of the bay 55 hr (2.3 days)
after the dye entered the bay..
6-34
-------
Fishermons Pt.
Mulct Bo you
(Gull Pt.) Devils Pt.
Red Bluff
Escambio Bay
Figure 6-15. Isopeths of the run on which major surface dye
peaks arrived at the given location. Sampling depth 0.3 m.
6-35
-------
The major dye peak was first observed in northeast Escambia
Bay at the mouth of the Little White River 16 hr after the dye
dump. The dye peak moved through the northeast section of the
bay in 13 hr. This period was just prior to and during an ebb
tide. This dye peak moved more rapidly seaward along the
Escambia River delta than along the eastern side of the northeast
section of the bay.
The dye peak did not arrive at the northern inlet to Mulatto
Bay until 10 hr after the peak entered the bay. Due to the
movement of the dye peak in an easterly direction near Mulatto
Bay, it appears that the waste discharges from Air Products and
Chemicals, Incorporated and American Cyanamid Company were forced
along the eastern shore of the bay.
Most of the fresh 'river water 'remained in the surface
outflowing layer since the bay was vertically stratified. Bottom
water was mixed into the upper layer, and some upper layer water
was entrained -into the lower layer. At the center of the upper
bay (Station D2) , the average dye concentration in the lower
layer was U4 percent of that in the upper layer. In the center
of the lower bay (Station H3), the average dye concentration in
the lower flayer was only 3.6 percent of that in the .upper layer.
In summary, Escambia River water tended to flow down the
western side of Escambi.a-Bay as it moved seaward under conditions
of average flow and tides. ,The mean time of travel for river
water on the surface was. 16 hr from the mouth of the Escambia
River to Devils. Point during an ebb tide. . North of Devils Point
Stations G1 to G5) , the dye peaks on the western side, were
approximately eight times higher than those on the east side
indicating most.of the .freshwater was transported across this
transect .down the western side of Nthe bay. South of Devils
Point, freshwater moved seaward on the eastern side of the bay
more rapidly thari on the western side. Since the dye peaks were
about the same concentration on . both sides, the quantity of
freshwater moving down both>rsides of the bay south of Devils
Point appeared to be equal. The major surface dye peak • reached
the mouth of. the bay in about 2.3 days.
In addition, major dye peaks entered Escambia Bay from the
Escambia, Little White, and Simpson Rivers at approximately the
same time. The dye peak entering the bay from the Little White
and Simpson Rivers,moved rapidly "through .the .northeastern portion
of upper-Escambia Bay during an ebbing tide. River water tended
to flow seaward along the Escambia .Riveir. delta, which borders the
western side of the upper northeast faayi.^.This has the effect of
confining the waste discharges from Air ,~ Products and Chemicals
Corporation and American Cyanamid Company near the~ eastern side
df the' upper bay. Discharge from the Escambia River mouth also
tended to force water from the northeast section of the upper bay
towards the eastern shore.
6-36
-------
In the upper bay, approximately UH percent of the dye in the
upper layer, was transported to the lower layer (assuming mid-
depth separates the upper and lower layer) . This means that a
portion of waste discharged in this area would be transported to
the lower layer and would remain in the bay longer than river
water flushed directly from the bay.
DISTRIBUTION OF INDUSTRIAL DISCHARGES IN ESCAMBIA BAY
Introduction
A tracer-was injected' into the effluents of Air Products and
Chemicals, inc. and American Cyanamid Company at different. times
to .de't ermine the steady state distribution of these discharges in
Es&ambia Bay. The results, also described the eff iciencies.of the
outfalls in distributing the discharges in the bay. In addition,
the steady, state distributions described the circulation of upper
Escambia Bay.
Methods
The Air Products Dye Study was performed on August 26 through
30, 1974, and the American Cyanamid Dye Study was performed .on
September 17 through 24, . 197*7 The tracer used during the
• studies wa,s Rhodamine WT fluorescent dye (2(X> percent., solution).
It' wasoLnjected into each effluent 'by syphoning from a constant-
head chamber and a pump was use4 to maintain the leve'l in the
ichamber. The constant-head chamber and syphon wejre necessary to
obtain 'a constant flow of dye into effluent. During the
injection, the effluent str.eam of : each industry was sampled every
half-hour using Serco Automatic Samplers, and the concentration
and mass of dye discharged •'/ was determined .'for each sample.
Effluent flow data was provided by the 'industries. During the
early stages of each study, samples were collected from the bay
every two to three hours, and as the studies progressed, the time
between sampling runs was increased (Appendix 6-5) . The stations
sampled during both dye studies and the Ideations of the
-discharges are shown on Figure 6-16. Two boats were used during
the" initial runs. Each 'boat started sampling near Transect 7
(line connecting stations starting with seven) and then one boat
worked riverward and the other seaward. Surface dye samples were
collected by dipping test tubes by hand. Mid-depth and bottom
samples were collected using the dye, sampler previously
described. The dye samples were kept: in the dark, to minimize
photo decay, until they were- analyzed at the EBRS laboratory.
The concentration of dye in the samples 'wa_s measured using an
Aminco Fluoro-Microphotomer Model 4-7102. Dye standards from 0.1
pg/1 to 3,000 pg/1 .were prepared and the instrument ' was
standardized every 12 hours. .All dye measurement's were made at
20.0°C + 0
The method of superposition used by Bailey, et al. (1966) in
San Francisco Bay and Kilpatrick and Cummings (T972) in Port
6-37
-------
Fishermans Pt.
Mulot Bayou
Gorcon Pt.
Pensacola Bay
Figure 6-16. Locations of stations sampled during the Air
Products and American Cyanamid dye studies.
6-38
-------
Poyal Sound was used to determine the steady state concentration
in Escambia Bay due to discharges from the industries. In this
method, a slug of dye is released and dye concentrations in the
bay are determined. When using this method in a bay, the dye
slug is released over at least one tidal cycle to approximately
quasi steady state conditions. To find the steady state dye
concentration at a location due to continuous discharge of the
same magnitude as the one tidal cycle slug discharge, a number of
identical dye concentration-time curves for that location are
superimposed offsetting each curve by the time of the dye
release. Each of the superimposed curves represents the
contributions from previous and later discharges of the same
magnitude and duration as the actual dye injection. The results
of adding these curves is to reproduce the effects of a
continuous discharge. The actual mathematical method used to
determine the steady state concentration due to a continuous
discharge is described by the following equation:
Cs = ro Ct dt
o'
where
-.»_ f
* J
C = Steady State concentration, in ng/1, resulting from a
continuous release of source strength m
m = Amount of dye released per unit time in kg/day
M = Total mass of dye released in kg
C.j. = Dye concentration at time t in
t = Time in days after the dye release
The integral portion of the equation is the area under the
dye concentration history distribution with units of M9/l~days.
The value of the integral was determined by numerical
integration. The value of m divided by M is the reciprocal of
the time of dye injection. This offsets the superposition
process by the time of dye injection. Because of the voluminous
amount of data collected during the dye study, a Fortran IV
program for an IBM 370 computer was written to perform the
numerical integration.
To standardize the distributions in Escambia Bay due to the
Air Products and the American Cyanamid dye injections, the steady
state concentrations in the bay caused by an effluent loading
rate of 1,000 kg/day (2,205 Ibs/day) are reported. The actual
calculations were performed per the amount of dye injected and
values were increased proportionally to obtain concentrations per
1,000 kg/day.
6-39
-------
Environmental Conditions
The estimated effective freshwater discharge of the Escambia
River during the Air Products Dye Study, August 26 through 30,
1974 was 77 m3/sec (2,720 cfs), which is 41 percent of the
average annual discharge of the river. During the American
Cyanamid Dye Study, September 17 through 24, 1974, the estimated
effective flow of the river was 188 m3/sec (6640 cfs) which is
approximately equal to the average annual flow.
The mean, maximum and minimum tidal range's approximate the
mean tide range of 0.46 m during the Air Products and American
Cyanamid Dye Studies (Appendix 6-5).
During the Air Products Study, the wind was predominantly
from the south and the wind velocities were between 9 and 17
km/hr most of the time (Table 6-9). The wind originated in the
north most of the time during the American Cyanamid Study and
again the predominant wind velocities were between 9 and 17
km/hr. All wind data were collected by the National Weather
Service Office, at Pensacola Regional Airport.
Just before the beginning of the Air Products Dye Study at
0600 on August 26, 1974, 1.04 cm (0.41 in) of precipitation was
measured at Pensacola Regional Airport. No additional
precipitation occurred during this study, arid there was no
precipitation at the Pensacola Regional Airport during the
American Cyanamid Dye Study.
At various times Escambia Bay was either a one or two layer
system. ' Salinity, which should be directly proportionate to
water density in a shallow bay, was used to determine if the bay
was stratified (Figure 6-17a and 6-17b). Based on salinity
profiles, upper Escambia Bay was a one-layer system at the time
of the Air Products Dye Study (Figure 6-17a). Therefore, there
was no barrier to prevent the dye tracer from mixing vertically
in the upper bay.
Tracer Release
A total of 8.5 kg (18.7 Ibs) of tracer was injected into the
Air Products plant effluent from 0845 on August 26, 1974 to 0945
on August 27, 1974, a period of 1.04 days. However, due to
accumulation in a swamp between the discharge point and Escambia
Bay, dye entered the bay for a period of 1.96 days. As a result
of this, the mean dye discharge rate was 4.3 kg/day. The average
Air Products effluent flow was 5.75 x 103 m3/day (1.52 mgd) and
the flow range was between 4.47 and 6.81 x 103 m^/day (1.18 to
1.80 mgd) during the dye release.
A total of 18.6 kg (41.0 Ibs) of dye was discharged into the
American Cyanamid plant effluent for a period of 1.28 days from
0945 on September 17, 1974 to 1600 on September 18, 1974. Thus,
the average dye discharge rate at this plant was 14.5 kg/day.
6-40
-------
Table 6-9. Summary of wind conditions during the Air Products and the
American Cyauamid dye studies.
Velocity
(km/hr)
Calm
1.8 - 7.4
9.3 - 16.7
18.5 - 25.9
27.8 - 44.4
Direction
Nortii
East
South
Vest
Calm
(k
( 1
( '5
(13
(15
Dec
320
50
140
230
LilOtS)
- «»)
- 9)
- 14)
- 24)
jrees
- 40
- 130
- 220
- 310
Air Products Study
Percent 01: time
9.3
16.7
52.1
22.9
0.0
Percent of time
12.5
27.1
41.7
10.4
8.3
American Cyanamid Study
Percent of time
4.7
7.8
65.6
21.9
0.0
Percent of time
54.7
32.8
7.8
0.0
4.7
6-41
-------
ESGAMBIA BAY
DISTANCE FROM STATION 3A (km)
0.
UJ
Q 2
RUN 6
8/26/74
1820-1960
Figure 6-17a. Salinity profile during Air Products dye study at
1820 to 2000 hrs. on August 26, 1974.
ESCAMBIA BAY
DISTANCE FROM STATION 3A (km)
< m
r*-
I 2 3 4 5
m
ro
0
O
e
O.
LU
Q 2
RUN 40
9/I8/74
0900-I030
Figure 6-17b. Salinity profile during American Cyanamid dye
study at 0900 to 1030 hrs. on September 18, 197U.
-------
The average effluent flow was 17.60 x 103 m3/day (4.65 mgd) with
a range of 16.65 to 18.85 x 103 m3/day (4.40 to 4.98 mgd) .
The average concentration of dye in the discharge during the
Air Products Dye Study was 655 pg/1 and the range was 45 to 4050
pg/1 (Appendix 6-6). The concentration in the effluent was less
than 1400 pg/1 95 percent of the time. The concentrations in the
American Cyanamid Plant effluent ranged from 1.55 to 3400 pg/1
with an average of 599 pg/1 and the concentration was less than
2000 ng/1, 97 percent of the time (Appendix 6-7).
The dye was not discharged at a constant rate because factors
such as changes in viscosity of the dye with lower night
temperatures, and retention and short circuiting in a swamp (Air
Products plant) caused the concentration and mass in the effluent
to fluctuate. This should not reduce the validity of the
results, because other investigators using the method of
superposition to analyze tracer study data from a physical model
of San Francisco Bay showed varied injection rates did not affect
the results (Bailey et al., 1966) .
Background Concentration
The first two runs of both the Air Products and American
Cyanamid Dye Studies were performed before the dye tracer was
injected. The actual dye concentrations in the bay after the dye
was injected were obtained by subtracting the background values
from measured values. The dye concentrations during the
background runs were:
Study Background Concentration (vg/1)
Mean Maximum C.V. %
Air Products 0.12 0.20 13.88
American Cyanamid 0.14 0.33 25.63
Background concentrations of 0.20 and 0.33 pg/1 were subtracted
from field measurements to obtain actual concentrations during
the Air Products and American Cyanamid Dye Studies, respectively.
Since the maximum concentrations were used to represent
background conditions, the steady state concentrations were due
only to waste discharges because background effects have been
removed with 99 percent confidence.
Steady State Tracer Distributions
During the Air Products Dye Study the tracer appeared to be
uniformly distributed north and south of the outfall under steady
state conditions at a depth of 0.3 m (1.0 ft) (Figure 6-l8a). A
concentration of 809 pg/1 occurred near the discharge (Station
3A) . The 100 M9/1 isopleth extended from Basshole cove to
Fishermans Point, indicating the tracer moved north and south
along the eastern shore of the bay. Dye isopleths were generally
6-43
-------
parallel to the eastern shore of the bay, and they decreased as a
function of distance from the eastern shore and in a seaward
direction. Below Fishermans Point, dye isopleths were in an
east-west direction decreasing seaward, and the dye moved seaward
across the entire bay moving slightly farther down the eastern
side of the bay than the western side. Concentrations at the
mouths of Mulatto Bayou were higher than at offshore stations,
again indicating the movement of the tracer along the east shore.
Tracer concentrations were very low seaward of the Interstate 10
bridge.
The steady state tracer distribution, due to the Air Products
plant discharge, at a depth of 0.9 m (3.0 ft) was similar to the
distribution for 0.3 m (1.0 ft), as was expected, since there was
very little salinity stratification (Figure 6-18b). However,
higher concentrations were measured farther south along the
eastern shore. A high concentration (35 pg/1) was measured at
the south inlet of Mulatto Bayou, and at a depth of 0.9 m (3.0
ft) higher concentrations occurred west of the channel and south
of the Interstate 10 bridge than occurred at 0.3 m (1.0 ft).
The steady state concentration distribution at 0.3 m (1.0 ft)
above the bottom was similar to that at 0.9 m (3.0 ft). The
concentration at the north inlet of Mulatto Bayou of 98 ng/It was
highest near, the bottom.
Dye from Air Products plant discharge was visible along the
shore for a distance of approximately 1.0 km (0.6 mi) north of
the outfall during two periods on August 27, 1974 (Figure 6-19).
The wind was from the East during these periods and the tide was
ebbing. During both periods, the tracer remained very close to
the shore and concentrations there were much higher than those in
the bay. The tracer was found all along the shore as far north
as Basshole Cove during 0630 through 0800. A concentration of
2744 M9/1 occurred along the shore 1.1 km (0.7 mi) south of the
outfall. The concentration 30 m (100 ft) from the outfall was
102,300 iig/1.
During 1130 and 1300, the dye was visible south of the
outfall along the shore. The concentration 30 m (100 ft) from
the outfall was 10,420 jig/1 and this decreased to about 500 M9/1
approximately 0.20 km (0.12 mi) to the north. About 1.1 km (0.7
mi) south of the outfall the concentration was 2230 pg/1. Dye
was not found in the center of the bay during this period. These
data indicated that the discharge from Air Products and
Chemicals, Inc. plant has a tendency to remain very close to the
shore, because of littoral currents which appeared to reverse
direction. East winds and an ebbing tide did not transport the
discharge away from the shore.
The highest dye concentrations in the bay during the American
Cyanamid Dye Study at a depth of 0.3 m (greater than 50 M9/1)
were to the north of the outfall (Figure 6-2Oa). The dye moved
north and south along the eastern shore of Escambia Bay, but
6-44
-------
^
en
Pensocolo Boy
i Pi. Peniacolo Boy
Figure 6—18a. Steady state^concentrations
( PK/1 * a* a <*ep*n °* P»3 m during the
Air Products dye study for a discharge
of It000 kg/day.
Figure 6—18b» Steady state concentrations
:<. MR/D a* a depth of 0.9 m during the
Air Products dye study for a discharge
of ltOOO kg/day.
-------
0630 to 0800
on August 27, 1974
Upper
0 Escambia
Bay
& Fishermans
'"' -Ay..point
on August 27, 1974
1 0.5
Fishermans
Figure 6-19. Instantaneous surface dye concentrations (pg/1) in
Escambia Bay per 1,000 kg/day discharged by Air Products
plant.
6-U6
-------
A
•o
Pensacola Boy
Figure 6-20a« Steady state .
concentrations (Me/I) at a depth of
0.3 m during the American Cyanamid
dye study for a discharge of 1,000
kg/day.
Figure 6-2Ob. Steady state
concentrations (pg/l) at a depth of
1.2 m (4 ft.) during the American
Cyanamid dye study for a discharge of
It000 kg/day.
-------
concentrated above Fishermans Point. No dye was measured to the
west of the channel at a depth of 0.3 m during this study.
At a depth of 1.2 m, an extremely high concentration, 1208
Mg/1, was measured near the outfall (Figure 6-20b) during the
American Cyanamid Dye Study. The dye plume eminating from the
outfall extended to the north, and with one exception relatively
low concentrations, less than 10 pg/1, occurred to the south of
the outfall. A halocline at a depth of slightly less than 1.2 m
(4.0 ft) existed in the bay during the American Cyanamid Dye
Study and it appears that a significant portion of the discharge
was trapped below the halocline.
The Rhodamine WT dye used in these tracer studies can be
considered a conservative (non-decaying) substance due to its low
decay rate and the short duration of the studies. The dye has
been found to follow first order decay. Hetling and O'Connel
(1966) found a first order dye loss rate constant of 0.031 per
day (base e) as an upper limit. Kilpatrick and Cummings .(1972)
used a dye loss rate constant of 0.03 per day (base e) to correct
Rhodamine WT dye to a conservative substance. If a dye loss rate
constant of 0.03 per day (base e) is used to calculate the steady
state concentrations of a conservative substance in Escambia Bay
from the results of these studies, the steady state dye
concentrations described within should be multiplied "by
approximately 1.1. Therefore, the steady state concentrations of
conservative substances would be slightly higher than those
discussed here..
A mass balance was performed to approximate the quantities of
dye in various areas of the bay under steady state conditions.
This was accomplished by dividing the bay into segments with a
sampling station at or near the center of each segment. The mass
in each segment was determined by multiplying the mean low water
volume of each segment by the steady state concentration.
The analysis indicated 56.1 percent of the discharge from Air
Products plant and 76.6 percent of the discharge from American
Cyanamid plant were in segments along the eastern shore (Figures
6-21a and 6-21b). Steady state concentrations were not
determined along the shore of the bay;.consequently, more dye was
probably along the eastern shore of the bay than indicated here.
Most of the discharges, 76.1 percent from Air Products plant and
90.4 percent :from American Cyanamid plant, were in the segments
north of Fishermans Point, and 3.9 percent of the discharge from
Air Products plant and 1.6 percent of the discharge from American
Cyanamid plant were in the segments at the inlets of Mulatto
Bayou. ...''••
This study indicated that the methods Air Products . and
American Cyanamids Plants used to discharge effluents into
Escambia Bay were insufficient, because their wastes tended to
accumulate near the upper eastern shore of the bay instead of
being rapidly removed from the bay. The study also indicated
6-48
-------
i PI Pensoco/a Boy
Pi. Pff}$OCO/O Boy
Figure 6-21a. Percent of steady state
dye aass in segments of Escaabia Bay
during the Air Products dye study*
Figure 6-2lb» Percent of steady state
dye mass in segments of Escambia Bay
during the American Cyanamld dye
study*
-------
that wastes from both industries entered Mulatto Bayou, the scene
of numerous fish kills. To eliminate the buildup of wastes in
upper northeast Escambia Bay, the effluents should discharge
through submerged outfalls extending to the vicinity of the
Escambia Bay dredged channel. In the case of the American
Cyanamid plant, their^present^outfall would have to be extended
about 1920 m (6, 300,.ft). -x'
CIRCULATION IN PENSACOLA BAY SYSTEM
Circulation in the Pensacola Bay system is weak and not
conducive to a high assimilative capacity. Based on all studies
performed by the Escambia Bay Recovery Study and the University
of West Florida, mean circulation over a tidal cycle in the upper
layer of the Pensacola Bay system normally follows the pattern
shown in Figure 6-22. Although current velocities in some areas
are higher than in other areas, all currents are relatively weak.
Mean current velocities over a tidal cycle in the lower layer are
extremely weak. Due to weak circulation in the system, the
elimination of wastewater discharges should be considered or the
highest degree of wastewater treatment possible should be
provided before discharge.
Furthermore, under certain conditions current reversals occur
in the bay and inflow takes place in the upper layer and outflow
occurs in the lower layer (Figure 6-23) (G. Ketchen, Florida
State University, personal communication). As shown in the
figure, a current reversal of the type described above occurred.
This means that waste discharges to the bay are sometimes
transported riverward and remain in the system for a longer
period than the flushing time suggests. The cause of these
current reversals is most likely wind, and this should be clearer
when Ketchen's study is completed.
CIRCULATION IN MULATTO BAYOU
Introduction
Mulatto- Bayou has been significantly altered by the
construction of Interstate Highway 10 (1-10). In 1965, a channel
connecting the southern portion of the bayou with Escambia Bay
was blocked by 1-10, and an alternate channel was dredged just
north of and parallel to 1-10. During this same period,
approximately 8 x 102 m3 (one million cubic yards) of sediment
was removed from the bayou for 1-10 fill causing deep borrow pits
(approximately 12m).
Mulatto Bayou has been the scene of numerous fish kills (see
Chapter 10). A September 1969 study by the Federal Water
Pollution Control Administration (USDI, 1970) indicated the fish
kills were caused by degraded water quality resulting from waste
discharges near the mouths of the bayou, residential finger canal
dredging within the bayou, and dredging and filling for 1-10
construction. The Florida Department of Transportation also
6-50
-------
Figure 6-22. Mean water transport over a tidal cycle for the
upper layer of the Pensacola Bay system.
Gulf Breej
0.
tu
o
KEY
x
•
Flow into Estuary
Flow out of Estuary
Lino of no Motion
0.2 Current Spted (m/s«c)
Figure 6-23. Current speed on June 12-13, 197U in Pensacola Bay.
6-51
-------
funded a study to evaluate conditions in Mulatto Bayou
(Livingston et al., 1972). They concluded that dredging and
filling strongly influenced circulation patterns of tidal
currents and horizontal and vertical exchanges of water, and have
contributed to a deterioration of water quality in the Mulatto
Bayou area. They recommended that a weir to restrict tidal
exchange between the north and south sections of the bayou be
installed, and a canal connecting the dead-ends of the finger
canals with the main channel of the bayou be constructed. To
provide additional information on circulation in Mulatto Bayou,
dye tracer studies were performed in June and July 1974.
Methods
Tracer studies using Rhodamine WT dye (20 percent solution)
were performed in Mulatto Bayou on June 24 and 25, 1971 and July
1 and 2, 197U. During the June study 0.9 kg (1.9 Ibs) of dye was
discharged at the north and south inlets to Mulatto Bayou, and
1.3 kg (2.8 Ibs) was discharged at each inlet during the July
study. In both studies, the dye was uniformly distributed across
the mouths of the inlets at the beginning of a flood current.
The methods used to collect the samples during the June study
were the same as those described previously (see this chapter;
Circulation in Escambia Bay; Methods). During the July study all
samples were collected at a depth of 0.9 m (3.0 ft) using a pump
system. All dye concentrations were determined at the EBRS
laboratory using equipment previously discussed (see this
chapter; Circulation in Escambia Bay; Methods).
Environmental Conditions
Environmental conditions during the dye studies are described
in Table 6-10.
Results and Discussion
Water movement into Mulatto Bayou through the north and south
inlet on a flooding current was rapid during the tracer studies
(Figure 6-21). The dye discharged at the south inlet was
transported to the mouths of the finger canals and about 0.2 km
into the northern area of the bayou during a flooding current.
The dye discharged at the northern inlet was transported into
most of the northern section of the bayou and Mulatto Bayou
during a flooding current. The dye did not enter the finger
canals or the eastern arm of the northern area of the bayou in
detectable quantities during one flood current. Short circuiting
of waters, which entered the bayou through the south inlet and
exited through the north inlet during a flooding current was
observed by Livingston et al., 1972, but did not occur during
these studies.
A minor fish kill occurred in the southern area of the bayou
during the July study. Wind eventually transported most of the
dead fish that accumulated on the shoreline of the bayou into the
6-52
-------
laole 6 - 1.0. Environmental conditions during tracer studies in Mulatto Bayou
performed on Juuo 24 - 25, 1974 and July 1 - 2, 1974. leather data collected
at Punsacola Airport (U.S. Dept. of Commerce, 1972 - 1974).
lide range (in)
Prevailing wind direction
Average wind speed", (km/hr)
Precipitation (cm) .
Hiniamm salinity (ppt)
Maximum, salinity (ppt)
Minimum temperature (»C)
Maximum tem peratir e (°C)
0.3
North
17.0
. ' . 0,0 ' .
8.3
20.6 .-••:.
26.0
23. 6
0.6
Southeast ,
10. 0 - ' ' ' -
0.2. . ...
15.6 '
1.9 . 6
17.0
31.0
Flooding Current
Northern Area
Southern Area
Soatfi Inllt
Conoll ( porliolly contlrucKH )
Figure 6-24^ Circulation patterns in Mulatto Bayou derived from
tracer dye studies performed during June and July, 197U.
6-53
-------
two eastern finger canals. As the fish decomposed, a highly
visible algae bloom developed in the canals and subsequent east
winds transported the bloom into the main portion of the southern
area. The partially constructed finger canals in Mulatto Bayou
should be sealed off from the rest of the bayou to eliminate
depressed dissolved oxygen concentrations that could be caused by
a slug of organic material entering the bayou from this area.
6-54
-------
7 - BAY SEDIMENTS
SEDIMENTATION
Introduction
The sand and mud sediments of the Pensacola Bay system are a
result of watershed erosion since the Pleistocene Epoch. During
the Pleistocene, the Citronelle deposits were reworked and
intermixed with marine terraces (Marsh, 1966). These deposits
are now eroding and therefore determine the minerology of the bay
sediments.
Terrestrial geology of the Escambia Bay watershed includes
principally unconsolidated sands, silts, and clays of the Coastal
Plain Province, which were deposited before the shoreline of the
continental mainland reached its present position (Walker and
Carlisle, 1960). Horvath (1968) and Goldsmith (1966) reviewed
the literature and reported this layer is underlaid by a veneer
of Pleistocene terrace deposits overlaying Tertiary beds of sand,
silt, and limestone. The Citronelle formation is the only
formation that crops out in this area and consists of layers of
sand, gravel, iron-cemented sandstone, fossil wood, and lenses of
kaolinite (Marsh, 1966). Bluffs along the west bank of Escambia
Bay have many such outcroppings.
Clay contributed by the Escambia River is mainly kaolinite,
with smaller amounts of montmorillonite and some vermiculite,
illite and gibbsite. The Escambia River is intermediate in clay
minerology between the extremely kaolinitic Apalachicola River
and the less kaolinitic Mobile River (Griffin, 1962). Escarosa
I, Figure 184 (1973) effectively shows the influence of the
kaolinitic flows into the northeastern Gulf and the increasing
influence of the montmorillonite group westward and offshore.
The Mississippi River discharges primarily montmorillonite clays.
Practically all clays entering Escambia Bay via the river are
retained within the bay (Escarosa I, 1973). Much is deposited
within the delta area with the remainder settling throughout the
bay.
Much of the sand entering the estuary is dumped in the delta-
area; however, some enters the bay by littoral drift and is moved
indiscriminately by wind and tidal current. Escambia Bay beach
slopes and shoreline configurations are constantly changing due
to these processes.
Horvath (1968) defined the sediment of the Pensacola Bay
system, including Escambia Bay, based on 214 samples taken with a
LaFonde Dietz sampler. Until then, only two other samples had
been taken in the system by Griffin (1962) . One sample from the
nearshore beach area was taken by Hsu (1960), and Martens (1931)
made a study of sand samples in the vicinity of Pensacola.
7-1
-------
Jeffrey and Moskovits (1955) reported on silting in the
Pensacola Bay system. At this Escambia Bay test site, silting
was reported as moderate to heavy.
The bay to the immediate west of Pensacola Bay was studied by
Parker (1968) who did a sedimentological study of Perdido Bay and
the adjacent offshore area. He concluded the deeper water
sediments are composed predominantly of silt and clay and the
nearshore region of the bay to be quartz sand. Goldsmith (1966)
did a sedimentological study of Choctawhatchee Bay which is east
of Pensacola and found a quartz sand shelf around the margin of
the bay, and the center of the bay contained a clay size sediment
brought in by the river. The western portion of the bay lacked
clay deposits and consisted of relict quartz sand.
The University of West Florida, under a Sea-Grant project,
has sampled fifteen stations in Pensacola Bay and are currently
analyzing the top 15 centimeters of each core.
The objective of the EBRS sediment study was to characterize
sediments and their related distributions in the, system.
Relationships of sediment-benthic macroinvertebrates will also be
discussed in another chapter. Previous reports (FWPCA, 1970;
Hopkins, 1973) discuss sludge beds in various portions of the
bay. , The present study was designed to determine the extent of
any unusual organic deposits.
Sampling Stations .
Cores were collected at a total of 207 stations in .the
Pensacola Bay estuary during the present study (Figure 7-1 and
Appendix 7-1). A group of 85 stations was located in Escambia
Bay on east-west transects. The inshore station on each transect
was 15 meters from shore, the next station was 100 meters from
shore, and all others on the transect were 900 meters apart.
Transects were 1000 meters apart in the north-south direction.
Fifty-nine additional cores were taken on the above transects and
transects within East and Blackwater Bays and Santa Rosa Sound,
with location based on cross-sectional profiles of the bay
bottom. Appendix 7-2 is a list of these stations and their
habitat type.
A third group of H8 stations was sampled at discrete
locations in East Bay, Pensacola Bay, and Blackwater Bay. In
addition, six stations were sampled in Choctawhatchee Bay (Figure
7-2) and nine in the Panama City bay system (Figure 7-3).
Methods
Sediment cores were taken with a three-inch diameter piston-
type corer to a depth of one meter. The top 15 cm were removed
for physical and chemical analyses and transported in plastic
containers on ice to the laboratory. when samples were not
analyzed immediately, they were frozen. Of the 207 cores, 85
7-2
-------
Figure 7-1. Sediment core sample locations in the Pensacola Bay
system.
Figure 7-2. Sediment core sample locations in Choctawhatchee
Bay, Florida, 197U.
7-3
-------
GULF
o f
MEXICO
Figure 7-3. Sediment core stations in Panama City bays.
-------
were analyzed for physical parameters by Escambia Bay Recovery
Study using methods described in EPA's Biological Field and
Laboratory Methods, (EPA-670/U-73-001) and the remaining cores
were analyzed by the Sedimentological Laboratory of the Geology
Department, Florida State University. The Sedimentological
Laboratory used a settling tube for the sand fractions and the
,pipette method (Carver, 1971) for separating the silt and clay
^fractions.
EBRS determined all chemical parameters except the metals and
pesticides which were determined by Surveillance and Analysis
Division, Athens, Georgia. Chemical analyses methods were
conducted according to the EPA Chemistry Laboratory Manual,
Bottom Sediments. Great Lakes Region, FWQA, 1969 with
modifications for automated analyses.
Fifteen core samples were taken throughout Pensacola Bay by
the University of West Florida using SCUBA and hand-held core
tubes (Figure 7-1). EPA, Surveillance and Analysis Division,
Region IV conducted the chemical analyses for metals and
pesticides.
Depths of bottom contours were determine! with a survey grade
recording fathometer.
Results
Data from analyses of sediment core samples taken from the
Pensacola Bay system, Panama City bays, and Choctawhatchee Bay
are presented in Appendix 7-3. These data include physical and
chemical parameters for each individual station.
Bay Bottom Profiles
Profiles of bottom contours taken on seven benthos transects
are shown in Figure 7-4. In general, these profiles show a
broad, almost flat central basin of primarily mud gently sloping
to a near-shore zone of steeper gradient (called a transition
zone in this report) and then, next to shore, a sand shelf. The
width of the shelf varies throughout the bay. This condition
exists throughout the adjacent bays in the Pensacola Bay system.
In the Benthic Macroinvertebrate section of this report the
different communities are related to the three types of
sediments, i.e., sand shelf, muddy plain and transition zone.
Sediment Particle Size Characterization
Sand-Silt-Clay
Like most bays in the northern Gulf of Mexico, the near-shore
is predominantly sand in Escambia Bay. Figure 7-5 shows the
relationship of depth to sediment type, with sand above the two m
contour and particles becoming smaller with increasing depth.
7-5
-------
DEPTH Jm
t
2.0 H-
6A GB
GE
CO
GC
2.2
2.4 -
2.1 -
3.0 -
MM
NOTE: See Appendix 7-1 tor mop of Transect location!
Figure 7-U. Bottom profiles and station location along benthic
transects in Escambia Bay.
-------
Normally, sediment types are continuous and parallel to the
shoreline throughout the bay with a more gradual change in
sediment type on the eastern shore. However, there is
discontinuity in this pattern in the lower portion of the bay
where fine to very fine sand interrupts the normal deposits of
sandy silt. The result is a saddle of sand across the muddy
plain. This interruption is shown in Figure 7-5 and also on the
figure for sand fraction grain sizes (Figure 7-6) .
A possible explanation for this saddle effect is the offshore
movement of sand at Devil Point originating from littoral sand
drift. Water depth contours indicated a large bar extending
eastward from this point. During revegetation studies in this
area, plantings were covered with 7.6-12.7 cm (3.0-5.0 in) of
sand in a two-month period. In water depths of 0.6-0.9 m (2.0-
3.0 ft), there is extensive sand movement, and possibly this is
occurring to some degree in deeper waters in this general area.
In East Bay and Blackwater Bay the same trend existed as in
Escambia Bay/ i.e., a gradient from coarse to fine particles
toward midbay. In Pensacola Bay, sediment distribution was
similar except in areas where dredging had occurred (Hopkins,
unpublished data). There has been extensive dredging and filling
throughout Pensacola Bay within the last 60 years, and much of
the shoreline has been filled to provide port development and
various real estate projects. Most of this fill material was
dredged from the bay. Consequently, there are large portions of
the bay that are deeper than normal near the shoreline.
Silt and clay fractions have been combined and are termed mud
in this report. In Escambia Bay, about 50 percent of the bay is
covered with sediments that have a composition of 80 percent or
greater mud (Figure 7-5). This is not unusual as most bays along
the northern Gulf Coast have broad muddy basins. Table 7-1 lists
data from six bays in this area and indicates that all have
similar mud and clay contents. Masch and Espey (1967) discuss
muddy sediments, their resuspension and "fluid mud" phase, in
relation to consolidated or semi-consolidated muds being
resuspended by man's activity or natural activities. Their work.
in Galveston Bay was concerned with resuspenied sediments from
dredging and their effects on oyster reefs. Their consensus was
that sediments with >80 percent mud or >50 percent clay could
develop "fluid muds" which could travel considerable distances
and affect many benthic communities. There are in Escambia Bay
many oyster beds which could be similarly affected if the muddy
central basin were altered, unless remedial measures were taken
during the project. The present study defines the benthic
community (Benthic Macroinvertebrates, Chapter 11) that now
exists in this muddy plain.
7-7
-------
I
00
Figure 7-5. Classification of surface
sediments < top 15 cm* ) in Escambia
Bay during 1973.
Figure 7-6. Grain size distribution of
the sand fraction in Escambia Bay
during 1973.
-------
Table 7 - 1. Percent of mud in sediments (top 15 cm.) from central
basii;s oi six northwest Florida tmys.*
Eay
Number of
Stations
Mean
Depth
Percent
Hod
(*)
Percent
(*)
Escambia Bay
East Bay
Pensacola Bay
ChoctaMhitchee Bay
Bays at Panama City
Blackwater Bay
17.
u.
1. **
6.
7.
1.
3.3
4.2
d.u
5.2
6.3
2.6
91.36
6d.3u
97.47
98.00
91.43
94.73
50.63
64.69
6 0.0 5
73.93
62. 19
70.30
* Data generated from samples that have either greater than 30ft mad
or greater than 50% clay.
**Statioa near a recent channel dredging project and probably this
station dredyed in the past year.
Triangle diagrams are a useful technique for comparing
sediment characteristics by presenting an array of points based
on percentages of sand, silt, and clay fractions from a given
sample as shown at A, Figure 7-7. Mud, sand, and transition zone
stations in Escambia Bay are shown at B, Figure 7-7. The sand
shelf group was classified as sand only; however, the transition
zone and mud plain stations were arrayed from sand to clayey
silt. It is not unusual for the latter two groups to have a wide
classification since station locations were selected by bottom
profiles, depth, and slope of the bottom rather than by sediment
grain sizes. Therefore, the term "mud plain" refers to a
location rather than a muddy bottom; however, in most cases the
mud plain does consist of mud. Ordinarily, these mud plain
stations would not fall into a sand classification in northern
Gulf of Mexico bay sediments. This study was in good agreement
with Shepard and Moore's (1955, p. 15) work in the Central Texas
bays. Arrays of sediment types from East Bay, Blackwater Bay,
Choctawhatehee Bay, Panama City bays, and Santa Rosa Sound are
shown at C through F, Figure 7-7.
7-9
-------
A. Soil Cl.»«ifieilion K«i
100% Cloy
% Clot 6lySonay Cloy ASilK Cloy \«0 « ,.„
30/CloyBy Sand/Sand-Silt-Cloy \Cloy«y Silt \
lOO % Sond 90 80 *O 60 30 4O 30 ZO 10 100 % Silt
XSond
• 3tad Sh«lf
O TTioiltton
• Hud Pliln
E. O.«t«vhai(h.« Ba
Mud Ptiln Station*
Figure 7-7. Sand-silt-clay sediment distributions in three
northern Gulf Bay systems.
7-10
-------
Miles
Fishermans Pt.
Mulct Bayou
Mulatto Bayou
I | 0-2.9 % Vol. Solids
3-9.9 % Vol. Solid!
6-8.9 % Vol. Solid*
9-11.9 % Vol. Solid!
It -•>
Devils Pt
Red Bluff
Pensacola
Bay
Garcon Pt.
Figure 7-8. Distribution of surface sediment (top 15 cm.)
volatile organics in Escambia Bay during 1973.
7-11
-------
Sediment Chemistry
Volatile Orqanics
Volatile organics in Escambia Bay are directly correlated to
the depth of the bay (r = 0.7729, p<.01) (Figure 7-8) . South of
Lora Point, in Escambia Bay, the western shore has a sharp
gradient from low to high percent volatile organics progressing
from nearshore to bayward. Along the western shore north of Lora
Point and throughout the eastern shore there is a more gentle
gradient from shore to deeper water. Volatile organics at the
transition zone stations averaged 3.97 percent, whereas the mud
plain and sand shelf stations averaged 7.38 and 0.59 percent,
respectively. A comparison of upper bay and lower bay stations
(using the L and N trestle as a divider) by analysis of variance
indicated no difference in the volatile organics (F = 2.827, p =
0.091).
Additional samples were taken around the L and N trestle to
determine if high organic sediments were collecting in this area.
Six stations north of the trestle at intervals across the bay
(Figure 7-1) and six stations on the south side revealed no
unusually high organic concentrations.
A comparison of volatile organics in Escambia Bay sediments
with other bays throughout the Pensacola Bay system and other
northern Gulf of Mexico bays indicated no unusual concentrations
in Escambia Bay sediments. EBRS stations in East Bay yielded
concentrations similar to those in Escambia Bay for similar water
depths. Also, the one EBRS deep water station in Pensacola Bay
had a similar value as a comparable deep water station in
Escambia Bay. The University of West Florida Sea Grant Study
concentrations (Hopkins, unpublished data) for East Bay and
Pensacola Bay showed Pensacola Bay had somewhat higher
concentrations of volatile /organics (x = 11.32) than East Bay (x
= 7.46). There was a gradient of lower volatile organic
concentrations from shallower waters in the upper portions of
East and Escambia Bays to deeper waters in Pensacola Bay.
However, volatile organics decreased from mid-Pensacola Bay
toward the Gulf of Mexico inlet where the inlet station had a
value of 0.14 percent.
Volatile organics concentrations from northeast Gulf bays
were similar to those obtained in Escambia Bay (Table 7-2).
Escambia Bay has a normal distribution of organic material
throughout the surface sediments with the exception discussed
below.
Regression analysis of organics vs. depth revealed certain
stations falling outside the upper 95 percent confidence limit.
These stations included three that were near the Northeast Sewage
Treatment Plant, which discharges near the western shore at
Bohemia. It was suspected that the STP effluent was causing
these unusually higher concentrations. The area around the STP
discharge that had higher than usual concentrations covered
approximately 200 acres. Two stations located in the oyster bed
7-12
-------
Table 7-2. Percent volatile or^anics in surface seel imon ts in northeast
Gulf ot Mexico bays and sounds.
Area
Percent Mo. ot:
Volatile Orcjanics stations
Source
Escambia Day
Mississippi River
Mississippi Sound
Mobile I5ay
Mobile Bay
Mobile Bay
Perdido Bay
Pensacola Bay
Ela'cfcvater Bay
East Day (Pensacola)
Choctawhatchee Bay
Choctawnatchee Bay
St. Andraws Bay
North Bay, Panama City
West Day, Panama City
East Bay, Panama City
0.07 -
0.50 -
0. 10 -
0.59 -
5.50 -
10.20 -
2.20 -
18.05 -
4. 30
O.JO -
0.10 -
8. 42 -
4.76 -
13.44 -
12.00 -
4. 92
26. CO
9.40
23. HO
13.81
11.40
19. 30
14. 10
25.30
13.80
27.71
17.20
24. :»2
25.68
16.05
13.00
160
4
38
30
2
2
17
2
10
48
5
6
3
3
2
1
EBKS
Linilbery, E.3. (1973.
?:PA (uupublishsu datal
UPA
Lindbsrg, E.S. (1973.
Lindbery and Hurriss (
KPA (unpublished data)
SDKS
^PA (unpublished data)
KBiiS - UWF
EPA (unpublished data)
h'BRS
KDP.S
E3HS
E38S
2BKS
1973)
,EflKS
areas near the eastern shore also had high concentrations which
were likely caused by physical trapping of organic particles
within the oyster bed and the concurrent fecal droppings of the
oysters. Another area of abnormally high volatile solids was the
ship channel under the Interstate 10 bridge and L and N Railroad
trestle. Microbial activity (discussed further under the
Microbial Activity section) was also high at this site.
Biochemical Oxygen Demand (BODS)
Higher BOD5 values were positively correlated with deeper
waters of Escambia Bay, however, some of the highest concen-
trations were not necessarily related to the deepest areas. The
area with BOD5 values equal to or greater than 900 mg/g was the
deeper portion of the upper half of the bay (Figure 7-9). The
two stations in Escambia Bay with the highest concentrations were
in the northeast sector near industrial discharges and river
delta marshes. Material developing this demand are organic
deposits resulting from both natural and man-produced introduc-
tions. Industries adjacent to the bay are presently discharging
organics, and in years past they discharged even greater amounts.
Dissolved organics from river water sources and industries are
flocculated upon contact with saline water. Although no specific
studies were designed to determine a zone of flocculation in
Escambia Bay, the area of maximum BODS deposits was the zone of
maximum contact of fresh river water with saline waters.
Although flocculation occurred throughout the water column,
including shallow waters, there was resuspension by wave action
7-13
-------
with ultimate deposition in the upper two-thirds of the bay as
shown on Figure 7-9.
Average BOD5 concentrations for sand shelf, transition zone,
and mud plain stations were 306, 603, and 733 mg/g, respectively.
Analysis of variance indicated sand concentrations were different
from transition and mud concentrations, but the transition
concentration was not significantly different from the mud
concentrations. (mud and tran: F = 1.134, df = 22, pr>0.05; mud
and sand: F = 20.848, df = 26, p<0.01; tran and sand: F =
12.378, df = 22, p<0.01)
The eight BOD5 samples taken in East Bay were less than 500
mg/g. Three stations in Blackwater Bay averaged 705 mg/g.
Central portions of Choctawhatchee Bay (eight stations) had
higher concentrations than all but one station in Escambia Bay.
A centrally located station in Mulatto Bayou had a BOD5 concen-
tration of 1110 mg/g. Three other bayous off Pensacola Bay had
equally high concentrations. Catfish Basin off Blackwater Bay
had a low BOD5 concentration, while in the four bayous listed
above with high concentrations various organic wastes were not
assimilated completely.
When compared to other bays, Escambia Bay BOD5 concentrations
were not unusually high.
Total Phosphorus
Spatial distribution of total phosphorus in Escambia Bay
sediments followed the depth contours (Figure 7-10). Higher
phosphorus concentrations were found south of the L and N
Railroad trestle in waters generally deeper than 2.44 meters (8.0
feet). The four stations with highest concentrations (> 0.4
mg/g) were found near the trestle and Interstate 10 bridge.
At comparable water depths, concentrations in East Bay were
lower than those in Escambia Bay. The one station sampled in
Pensacola Bay had a concentration of 0.468 mg/g. The trend in
Choctawhatchee Bay was for higher phosphorus concentrations in
the upper bay (near the river) and lower concentrations near the
Gulf inlet. Depths at these stations, like Escambia Bay, were
shallow in the upper bay and deeper toward the Gulf. Phosphorus
concentrations in Choctawhatchee Bay were similar to the higher
concentrations in Escambia Bay (> 0.3 mg/g). A comparison of
total phosphorus in mud sediments of Escambia Bay to other
northwest Florida bays is presented in Table 7-3.
Phosphorus concentrations in the Panama City bay system did
not have a good correlation (r = 0.515, p<0.01) with depth;
higher concentrations were found near population centers and
industrial complexes. Of the eight stations in this system,
three concentrations were greater than 0.6 mg/g. The highest
concentration in Escambia Bay was 0.54 mg/g near the L and N
Railroad trestle.
7-14
-------
Fishermans Pt.
Mulct Bayou
(Gull Pt.) Devils Pt.
Red Bluff
Pensacola
Bay
Garcon Pt.
Figure 7-9. Biological oxygen demand (BODS) in surface sediments
(top 15 cm.) in Escambia Bay during 1973-1974.
7-15
-------
Fishermons rt.
Mu/at Bayou
Pensacola
Bay
Gorton Pf.
Figure 7-10. Phosphorus concentrations (mg/g) in surface
sediments (top 15 cm.) in Escambia Bay during 1973-197U.
7-16
-------
lable 7-3. Total phosphorus, organic nitrogen, and organic carbon in mud
sediments crom northwest Florida.
Location
fscamoia Bay
East Bay
Panama City bays
Choctavhatcnee bay
Peusacola Bay
Number
of
Samples
19
5
9
6
1
Mean
Total
Phosphorus
(*ig/g)
2U8.8
195.6
463.9
350.7
468.0
Mean
Organic
Nitrogen
(mg/g)
0.57
0.59
1. 18
1.60
0.71
Nean
Organic
Carbon
(mg/g)
31.
-------
Both Escambia Bay and Choctawhatchee Bay had relatively large
river inflows and similar organic nitrogen concentrations.
Conversely, East Bay and Panama City bays had lower organic
nitrogen concentrations and less freshwater inflow. Escambia Bay
sediment did not seem to have unnaturally high organic nitrogen
concentrations.
Organic Carbon
The distribution of organic carbon in the Pensacola Bay
system was similar to that of total phosphorus and organic
nitrogen; that is, as muddy sediments increased, concentrations
increased. Figure 7-12 showed highest concentrations were at
midbay in deeper waters in 1973. These high concentrations were
similar in both the upper bay and lower bay.
Figure 7-13 showed the relationship of organic carbon in
Escambia Bay and East Bay in 1974. In both bays the lower
concentrations were near-shore and higher concentrations in
midbay.
There was no apparent significant change in organic carbon
concentrations in the sediments in 1973 compared to 1974 (Figures
7-12 and 7-13). Table 7-3 compares organic carbon (chemical
oxygen demand) within four bays and indicates Escambia Bay had
the lowest concentrations. The average of the Panama City bays
was high because one station was near a paper mill waste
discharge. Escambia Bay sediments did not have any unusual
concentrations of organic carbon.
Polychlorinated biphenyl (PCS)
Aroclor 1254 (a trade name for a PCB) was found throughout
the sediments of the Pensacola Bay system (Figure 7-14). The
range of values was 0.0 to 1500 pg/kg (ppb). The mean of 54
stations was 71.4 jig/kg, including ten stations where Aroclor
1254 was not detected. Station C-15 located in the Escambia Bay
barge channel had the highest value at 1500 fig/kg. Escambia Bay
transects G and o, each with three stations representing sand,
transition, and mud had the following PCB concentrations in
jjg/kg:
Sand stations Transition stations Mud stations
GC 9.8 GB 45.0 GA 70.0
OC 20.0 OB 43.0 OA 86.0
Analysis of these data indicated a trend to higher PCB's in finer
particles. This trend is prevalent throughout the entire bay
system.
During February 1974, two cores taken near Air Products' and
American Cyanamid's discharges had concentrations of 245 and 250
7-18
-------
-4
H*
CO
°ensaccto Bav
Figure 7—11* Total organic nitrogen
Cmg/g) in surface sediments (top 15
cm* ) in Escambia Bay during 1973—
1974.
Figure 7—12. Organic carbon (mg/gl
distribution in surface sediments
(top 15 cm*) in Bscambia Bay during
1973.
-------
f
Figure 7-13. Organic carbon (tng/g) distribution in surface
sediments (top 15 cm.) in the Pensacola Bay system during
1974.
Figure 7-14. Polychlorinated biphenyls (Aroclor 1254, pg/kg)
distribution in surface sediments (top 15 cm.) in the
Pensacola Bay system during 1974.
7-20
-------
pg/kg of PCB. Since these are relatively high concentrations
compared to most of the bay, ten additional stations on a
transect between these discharges were sampled by coring. The
range of these concentrations was <80 to 340 pg/kg (ppb).
(Analyses performed by the EPA, NERC, Gulf Breeze Research Lab).
Organic scans with gas chromotography and electron capture
detector in 1972 did not reveal any PCB's in either of these
industrial discharges. During this study there was no sampling
of these discharges.
Station B-11C (a channel station) had a concentration of 78
pg/kg while B-11, which was adjacent to the channel bat on the
mud plain, had a concentration of 45 pg/kg. The channel acts as
a trap for fine sediments which in turn are attractants of PCB
molecules. Since PCB can be incorporated with clay and silt
particles and also organisms can accumulate the material,
eventually PCB will accumulate in deep water sediments. Any
material deposited on the sediment will be reworked deeper into
the sediment by organisms, and therefore, be available for uptake
by benthic infauna.
An industrial leak of Aroclor 1254 was discovered and stopped
in 1969 upriver of Station A-10. This station is influenced
greatly by freshwater flow from the river and has a low salinity
(annual average one foot above bottom is 7.8 ppt). There is an
accumulation of upland vegetative debris at this station. This
station had a relatively high concentration of Aroclor 1254 (210
pg/kg) .
PCB's in sediments of Escambia Bay have been analyzed at
intervals since 1969 (Nimmo, et al, 1975). Their discussion of
sediment data from 1969 to 1971 shows a consistent decline of
PCB. Samples for Aroclor 1254 taken in 1972 at eleven sediment
surface stations ranged from <100 to 5700 ng/kq (EPA, Gulf Breeze
Laboratory) .
It appears that PCB is diminishing from the sediments at a
rate of about 90 percent per year.
Pesticides
Sediments were analyzed for twenty-one pesticides listed in
Appendix 7-4. Five pesticides were detected during the present
study.
DDE, a derivative of DDT, was found in sediments during this
study in Blackwater, East, and Pensacola Bays, but not in
Escambia Bay. Concentrations ranged from non-detected to 1.9
jig/kg. In Choctawhatchee Bay, the range was from non-detected to
17.0 pg/kg. ODD was found at one station in Choctawhatchee Bay
(2.5 pg/kg). DDT ranged from 1.2 to 2.8 fig/kg at three stations
in Choctawhatchee Bay.
7-21
-------
Dieldrin was found only in Escambia Bay at concentrations of
0.12 to 0.13 pg/kg at four of the 13 stations.
Mirex was found at the station nearest the Choctawhatchee
River mouth in Choctawhatchee Bay at a concentration of 0.95
Dieldrin is highly toxic to estuarine organisms and its
presence in Escambia Bay sediments creates a definite threat to
the bay ecosystem. This pesticide probably entered the estuary
through lawn fertilization and ant control measures. It is
presently not used to any great extent and in the future will
likely not be available for public use.
Lead
The sandy shelf area along the margin of all bays in the
Pensacola Bay system had lower concentrations of lead (<10 pg/g)
than did deeper mid-portions of the bays. Muddy portions of the
system had concentrations from 10 to 38 pg/g except Bayou Texar
and Bayou Chico, which had values of 5U and 64 pg/g*
respectively. Comparing muddy stations in the upper and lower
portions (above and below the L and N Railroad trestle) of
Escambia Bay, there were higher concentrations below the trestle
by a factor of two. Concentrations in East Bay were about the
same as the lower portion of Escambia Bay. Deep water stations
in Pensacola Bay had higher values than deep water stations in
Escambia Bay except those stations toward the Gulf inlet. Five
stations along the northern margin of Pensacola Bay and in the
bayous along the north shore had concentrations that were the
highest for the entire bay system. These stations were
influenced by the City of Pensacola1 s wastewater discharges.
Lead concentrations in Choctawhatchee Bay were the same as in the
lower portion of Escambia Bay. Lead concentrations did not seem
excessive in Escambia Bay compared to Pensacola Bay and two
relatively unaltered bays. Further comparison (Table 7-U) with
other sediments indicated Escambia Bay had less lead
concentrations than Mississippi coastal areas, Chesapeake Bay,
Galveston Bay, and Mobile Bay.
Zinc
Zinc concentrations were lower in the shallower sand stations
compared to deeper muddy stations in the entire Pensacola Bay
system. Upper Escambia Bay had lower concentrations than the
lower bay within mud stations. There was no significant
difference in lower Escambia Bay and East Bay within mud stations
(t = O.UU, df = 1, p>0.05). Bayou Texar had a high concentration
(150 pg/g) compared to the highest value of 85 pg/g in Escambia
Bay. Bayou Chico had a concentration of 1200 pg/g in its mud,
which was quite high compared to other bay systems in the
northern Gulf of Mexico (Table 7-5) . Escambia Bay values were
lower than those from Pensacola Bay, industralized areas of the
Mississippi coast, Galveston Bay and Mobile Bay. It had values
7-22
-------
Table 7 - U. Lead concentrations in surface sediments of selected bays.
System
Escanbia Bay •
Pensacola Bay ,;
East Bay
Esc a taw pa Biver Estuary
Eascagoula Biver Estuary
Bayou Casotte
-Mississippi Sound
Turkey Creek, Hiss.
Gultport seaway & Bayou Bernard
Bioloxi Backbay
Chesapeake Bay
Galveston Bay
Blackwater Bay
Choctawhatchee Bay
Panama City Bays
Hob lie Bay, Ala.
Table 7-5. iinc concentrations
System
Escambia Bay
Pensacola Bay
East Day
Esc a taw pa River Estuary
Pascauould Piver Estuary
Bayou Casotte
nississippi Sound
Turkey creek. Hiss.
Gulfport seaway & Bayou Bernard
Bioloxi Sack bay
Chesapeake Bay
Galveston Bay
Blackwater Day
Choctaw hate nee Day
Panama City Bays
Mobile bay, Ala.
System
Escambia Bay .
Pensacola bay
East !Jay
Eayou Casotte
Gull" poet Seaway i bayou Bernard
Chesapeake Day
Galveston 3A, Segion IV
13SS
Source
BBSS
UUP - EPA, Eegion IV
SBBS
2PA, Region IV
EPA, Region IV
EPA, Region IV
EPA, Region IV
EPA, Region IV
EPA, Region IV
EPA, Region IV
23RS - EPA, Begion IV
E3RS EPA, Region IV
tBHS
EP4, Begion IV
after J . S. Laurence
(personal come.)
7-23
-------
about the same as Choctawhatehee Bay and Panama City bays and did
not seem to have any unusual concentrations.
Chromium
Stations that were predominantly sand had lower chromium
concentrations than did those in deeper waters that were
principally mud. Within Escambia Bay the muddy stations in the
upper bay had lower concentrations than the lower bay.
Concentrations in muddy stations in East Bay were about the same
as those in lower Escambia Bay. Concentrations in Bayou Texar,
Bayou Chico, and Bayou Grande were similar to the muddy stations
in Escambia Bay. Choctawhatchee Bay concentrations were about
the same as those in Escambia Bay. Chromium concentrations in
Escambia Bay did not seem excessive compared to other bays (Table
7-6).
Cadmium
The range of cadmium in the Pensacola Bay system was from
<0.97 to 2.0 pg/g. Four of nineteen stations in Escambia Bay had
cadmium concentrations >1.0 \*q/g. Concentrations in East Bay
were less than those in Escambia Bay. Bayou Grande and Bayou
Chico had concentrations greater than 1.0 vg/g. Most stations in
Choctawhatchee Bay had concentrations of 1.0 pg/g. Therefore,
cadmium concentrations in sediments of Escambia Bay were lower
than those in the relatively unpolluted sediments of
Choctawhatchee Bay (Table 7-7) .
Copper
Sandy stations had lower concentrations of copper than muddy
stations within the Pensacola Bay system. Muddy stations in
upper Escambia Bay had lower concentrations than muddy stations
in the lower bay. East Bay copper concentrations were lower than
either the upper or lower bay portions of Escambia Bay.
Concentrations in Choctawhatchee Bay were about the same as lower
Escambia Bay. Mulatto Bayou and Bayou Texar had concentrations
of 10 pg/g, while Bayou Chico had 120 pg/g. Bayou chico has a
long history of receiving heavy metals discharged by industries.
Compared to East Bay (U.U pg/g)/ the Escambia Bay system (8.7
jig/g) was somewhat contaminated with copper. Escambia Bay had
greater concentrations than six areas (35 stations) in
Mississippi (Table 7-8). It also had higher values than
Blackwater Bay. If only deep water Escambia Bay stations were
considered, the mean was 11.8 vg/g (n =13) and deep water
stations in Panama City bays (11.6 pg/g) and Choctawhatchee Bay
(11.3 pg/g) were similar. Bayou Casotte, Mississippi, a heavily
industralized area, had a mean of 11.7 pg/g. Conversely,
Pensacola Bay (19.3 pg/g)» Chesapeake Bay (35.2 H9'9) r and
Galveston Bay (28.0 pg/g) had higher.values than Escambia Bay
(Table 7-8) .
7-24
-------
Table 7-8. Copper concentrations in surface sediments of selected bays.
System
Escambia Bay
Pensacola Bay •,
East bay
Escatawpi River Estuary
Pasca Bayou Bernard
Eioloxi Backbay
Chesapeake Bay
Galvestoa Bay
Blackuater Bay
Choctavhatchee Bay
Panama City Bays
Concentration
(ppm) Number of
Mean Sin, Max. Observations Source
8.9
15.7
3.7
6.5
8.0
8.6
7.0
<2.0
4.5
6.6
44.3
27.8
2.3
15.5
11.1
2.0
<2.0
<2.C
<1.6
<2.0
<2.0
2.4
-
<2.0
<2.0
33.0
11.0
1.0
7.8
<4.0
19.0
28.5
15.0
15.0
17.4
12.3
12.1
-
9.4
13.0
57.0
57.0
4.0
20.0
17.0
23
18
1D
18
4
3
4
1
4
4
5
5
5
6
9
EBRS
OHP - EPA, Region IV
EBRS
EPA, Region IV
EPA, Region IV
EPA, Region IV
EPA, Region IT
EPA, Region IV
EPA, Region IV
EPA, Region IV
Sommer and Pyzic, 1974
Holland and Daciolek, 1973
EBRS - EPA, Region IV
EBRS - EPA, Begion IV
EBRS
Table 7 - 11. Aluminum concentrations in surface sediments of selected bays.
Concentration
Systea
Escaabia Bay
Pensacola Bay
East Bay
Blackvatsr Bay
Choctavhatchee Bay
Panama City Bays
Mean
10078
14565
10554
4634
21050
13433
(ppm)
Nin.
300
64
360
1120
16600
4300
Rax.
21030
26000
2000C
1500D
280-70
18800
Number of
Dbservatio'ns
20
18
13
5
6
9
Source
EBBS
UHF - EPA,
EBRS
EBHS - EPA,
EBBS - EPA,
EBRS
Begion
Region
Region
IV
IV
IV
7-25
-------
Concentrations around the discharges of American Cyanamid and
Air Products were higher than other stations in the upper bay.
Copper was apparently accumulating in an area near the
discharges.
Manganese
Sandy stations had lower values of manganese, whereas higher
concentrations were found at muddy stations. Within muddy
stations, concentrations in upper bay stations were much lower
(by <*. 6 times) than lower bay stations. Bayou stations 'tended to
be lower than open bay stations. Concentrations in East Bay were
about the same as those in Escambia Bay (Table 7-9). Panama City
bays and Blackwater Bay had lower values than Escambia Bay.
Pehsacola Bay, Galveston Bay, and Choctawhatchee Bay had higher
values than Escambia Bay (Table 7-9). Manganese concentrations
in Escambia Bay did not seem to be unusual when compared to other
bays in northwest Florida.
Nickel
Nickel concentrations were lower in the sandy stations
compared to muddy stations within the Pensacola Bay system.
Muddy stations above the L and N trestle in Escambia Bay had
lower concentrations than those . in mud below the trestle.
Escambia Bay concentrations were about the same as those in East
Bay and the Mississippi coast (Table 7-10). Pensacola Bay system
bayous and the Pensacola Bay northern shore stations were similar
to Escambia Bay. Mid-Pensacola Bay stations had higher
concentrations than any area of the total system. Chesapeake Bay
and Galveston Bay had higher means than Escambia Bay (Table 7-
10). Choctawhatchee Bay and Panama City Bays had somewhat higher
concentrations, but these two were only sampled in muddy
sediments. Escambia Bay muddy stations were similar to these two
bays. There appeared to be no unusual concentration of nickel in
Escambia Bay as compared to East Bay and other northern Sulf bays
and sounds.
Aluminum
Aluminum makes up a large portion of the clay particle
lattice and consequently is distributed in relation to the mud
deposits in the bay. Thus, the sandy near-shore areas had low
concentrations of aluminum while the deeper parts of the bay had
'higher concentrations. Less clay accumulated in the upper
portion of Escambia .Bay.. Consequently, aluminum concentatibns
were greater in the lower bay. East Bay had about the same
concentrations as the lower Escambia Bay. There were no unusual
concentrations of aluminum in Escambia Bay (Table 7-11).
7-26
-------
Iron
The iron distribution in Escambia Bay was similar to the
aluminum distribution and the above discussion on aluminum holds
true for iron. Choctawhatchee Bay values (48,000 pg/g) were
higher than any bay sampled (Table 7-12).
Cobalt
Cobalt concentrations in sandy stations were lower than muddy
stations throughout Escambia Bay. The upper bay had lower
concentrations than the lower bay. East Bay mud station
concentrations (x = 6.8) were significantly lower (t = 2.58,
df=15) than Escambia lower bay stations (x = 15). Choctawhatchee
Bay concentrations (x = 12) were also significantly lower (t =
6.67, df =13) than Escambia lower bay stations. Accumulations
of cobalt in the lower portion of Escambia Bay within the deeper
water sediments were higher than adjacent Bays. Chesapeake Bay
values were higher than Escambia Bay values (Table 7-13).
Vanadium
Vanadium concentrations were lower in the sandy shallow
stations and higher in the deeper muddy stations within Escambia
Bay. Concentrations were twice as great in the lower bay mud
stations than the upper bay mud stations. Lower bay concen-
trations at muddy stations were not significantly (t = 1.6,
df=15) greater than concentrations in muddy East Bay stations;
however, the mean for lower Escambia Bay was 73.6 pg/g compared
to 37.4 pg/g for East Bay. There was a greater accumulation of
vanadium in lower Escambia Bay compared to East Bay and Pensacola
Bay (Table 7-14) .
Titanium
Titanium is a common metal found in dark colored sand, silt,
and clay particles originating from the upland watershed. These
particles are apparently distributed evenly throughout the bay;
therefore, the distribution of titanium in Escambia Bay was
uniform with no relationship to water depth or sediment type.
Most samples had concentrations greater than UO pg/g. Mud
station concentrations were similar in East Bay and Escambia Bay.
Pensacola Bay concentrations were lower than Escambia Bay, but
the Pensacola Bay bayou stations were the same as Escambia Bay
stations. Table 7-15 compares concentrations within several
northwest Florida bays.
Channel Sediments
In general, channel sediments within Escambia Bay were quite
different from sediments in the central bay mud plain.
Maintenance dredging of the Escambia River and Bay channel was
last performed in 1970 to 3.05 m (10 ft) below MLW. Although the
7-27
-------
table 7-1.
Iron concentrations in surtace sediments of selected bays.
System
Escanbia Bay
Fensacola Day
East Bay
Galveston Bay
BlacKuatec Bay
Choctauhatchee Bay
Banana City Days
Concentration
(ppm) Number of
Mean din. nax. Observations Source
29298
32710
23836
8220
11523
U7967
20522
85?
230
625
5200
2300
31100
630C
54000
53000
430GO
12700
37000
60000
2700C
20
18
10
5
5
6
9
EB2S
(JWF •
EBBS
• EPA, Region IV
Holland and
EBBS
EBBS
EBRS
- EPA.
- EPA.
Jlacialek, 1973
Region
Region
IV
IV
Table 7 - 13. Cobalt concentrations in surface sediments of selected bays.
System
Escambia Bay
Fensdcola Bay
East Bay
Chesapeake Bay
Elackvater Bay
Choctauhatchee Bay
Panama City Bays
Concentration
(ppm) Number of
Mean din. Max. Observations Source
12.
9.
8.
146.
4.
12.
4.
2
8
6
6
8
0
9
5. 0
4.9
<5.0
16.0
2.0
7.0
2.0
32.:
15.0
13.0
260.0
10.0
14.0
5.2
20
18
10
5
5
6
9
EBRS
UHF -
EBRS
Soner
EBRS.
EBRS
EBRS
EPA,
and
- EPA
- EPA
Region
IV
Pyzik, 1974
, Region
, Region
IV
IV
Table 7 - 14. Vanadium concentrations in surtace sediments of selected bays.
Concentration
System
Escambia Bay
Pensacola Bay
East Bay
Chesapeake Bay
Blackvater Bay
Choctavhatchee Bay
Panama City Bays
Jlean
73.6
HI. 3
37.U
108.2
23.it
99.5
34.6
(ppm)
Min.
19.0
< 1 0 . 0
< 1 0 . 0
78.0
8.G
57.0
16.0
Max.
215.0
80.0
71.0
135.0
55.0
151.0
50.0
Number of
Observations
20
13
10
5
5
6
9
Source
EBRS
OWF -
EBRS
Somer
EBKS -
EBHS -
EBRS
EPA, Region IV
and Pyzik, 1971
EPA, Region IV
EPA, Region IV
Table 7 - 15. Titanium concentrations in surface sediments of selected bays.
System
Escambia Day
Fensacola Day
East Bay
Blackuatar Bay
Choctavhatchee Bay
Panama City Bays
Concentration
(ppm) Number of
Mean Min. flax. Observations Source
70.2
33.0
55.0
«7.6
40.2
6U.O
12.0
12.0
12.0
2M.O
21.0
38.0
-------
channel depth is to be maintained at a minimum depth of 2.7
meters (9.0 ft) MLW, existing depth exceeds 2.7 m. Periodic
maintenance work is required due to sediment deposition in the
lower river and bay. An irregular bottom profile has been
created, due mostly to dredging. High river flows cause periodic
scouring to occur in the river, and fine sediment material which
has accumulated is resuspended and moved down river to the bay,
leaving only the coarser sands deposited in the river. There
were, however, pockets of finer sediments scattered throughout
lower reaches of the river.
Four stations sampled in mid-channel from Highway 90 bridge
south to the mouth of the river contained less than 0.68 percent
mud. Mean phi grain size for the sand fraction was 1.28, which
is classed medium sand.
The channel in the bay was deeper than the surrounding bay
bottom and, consequently, it acted as a sediment sink for mud
fractions. Channel sediments only 0.3 km (0.5 mi) below the
river mouth were 45 percent mud. Table 7-16 lists data on
channel sediments and Figure 7-15 shows station locations. All
except Stations B-11 and B-11C were sampled shortly after the
high flow in Spring 1973. The mud fraction of the channel
sediments increased toward the lower bay.
While volatile organics were negligible in the lower river
sediments, they greatly increased 0.3 km (0.5 mi) seaward of the
mouth of the river. From this point south for 5.5 km (3.U mi),
Table 7 - 1o. Ship chancel sediments, Escarcbia Bay, Florida, from Highway 90
to channel entrance.
Station
ER-24
EB-20A
ER-20
ER-19
Ch 18
Ch 16
Ch 15
Ch 14
I10-LH
ft 12
1-10
Ch 12
Ch 10
Ch 7
E11-C
E11
Data
1/73
4/73
4/73
4/73
U/73
5/73
5/73
5/73
5/73
2/74
5/73
5/73
5/73
5/73
2/74
2/74
Depth
(m)
5.2
4.7
4.1
3.8
3.6
4.3
4.6
4.7
4.7
2.6
5.2
4.1
4.1
4.4,
-
3.7
Percent
Mud
(«)
0.08
0. 10
0.68
0.25
45.34
74.57
72.28
60.50
87.65
96.79
89.91
93.25
88.86
94.08
96.69
•
Percent
Clay
(«)
0.07
0.06
o.o
0.11
8.58
26. C6
16.59
15.67
26.08
75.90
22. 79
39.60
35.78
18.77
72.65
—
Percent
Vol. Solids
(8)
0.7
-
-
-
10.0
9.1
13.0
12.8
12.7
19.0
12.3
14.2
10.9
12.1
25.31
12.7
Total
Phosphorus
(mg/1)
C.02
-
-
-
0.40
0.27
0.41
0.38
0.43
0.42
0.43
0.28
0.24
0.37
0.47
0.32
Tot. Org.
Nitrogen
(mg/1)
O.C6
-
-
-
2.17
2.08
2.70
2.65
2.62
0.63
2.41
1.47
1.54
2.41
0.98
0.45
7-29
-------
Fishermons Pt.
Mulct B'ayou
Pensacola
Bay
Gorcon Pt.
Figure 7-15.
Bay.
Ship channel sediment station locations in Escambia
7-30
-------
volatile organics were nearly constant and averaged 11.9 percent.
Station B-11C, 8.7 km (5.U mi) down bay from the river mouth had
25.3 percent volatile organics, the highest value recorded in the
channel.
Nutrient values in the river at Highway 90 were low; total'
phosphorus was 0.02 mg/g and organic nitrogen 0.06 mg/g.•: Total
phosphorus averaged 0.37 mg/g in the bay channel. This compares
closely with mud sediments elsewhere in the bay. Organic
nitrogen at channel stations was considerably higher than in
sediments outside the channel. Bay channel organic nitrogen
averaged 2.1 mg/g in Spring 1973. Below is a comparison of the
sediments at the southern end of the channel 8.7" km (5.4 mi)
below the river. They were sampled concurrently inside and
outside the channel.
T-Phosphorus Organic Nitrogen
mg/g mg/g
In Channel 0.18 0.98
Outside Channel 0.32 0.45
The channel sediments between Interstate 10 and the L and N
Railroad trestle contained the highest organic nitrogen values
recorded in Escambia Bay. Data for this station is below:
Station Date Total Phosphorus Organic Nitrogen Volatile
mg/g [H^Sl Organics (%)
A- 12
A-12
A- 12
A-12
5/4/73
5/3/74
6/5/74
8/5/74
0.40
0.43
0.24
0.42
2.6
4.5
2.1
5.1
12.7
8.5
7.0
8.4
Aroclor 1254, a PCB, was detected at a higher level in the
channel than immediately outside. These data are presented on
Figure 7-14. DDE, dieldrin, and other pesticides were not
detected at stations sampled.
Heavy metals data on channel sediments are presented in
Tables 7-4 through 7-15. Concentrations at a lower .bay station
both inside and outside the channel in February 1974 are given in
Table 7-17.
•The ...channel accumulated, mud sediments containing high
nutrients, volatile organics, PCB's, and heavy metals. These
7-31
-------
Table 7 - 17. Heavy metal concentrations near and in the channel at t«o adjacent
stations in Escarabia Bay, 1974.
Station Cu Mn Al Fe Ni Cd
juy/1 jig/1 jug/1 jug/1 jug/1 jug/1
B - 11C 16.0 540. 19000. 54000. 16. 1.
(in channel)
B - 11 3.0 330. " 15000. 44000. 12. 1.
(out of channel)
Station
B - 11c
(in channel)
Co
Jig/1
23.0
Cr
jug/1
67.
Vi Ti
jug/1 jug/1
110. <80.
Pb
ug/l
38.
ZB
aq/\
85.
B - 11 14.0 47. 99. <80. 27. 62.
(out of channel)
sediments may be periodically resuspended by high river flow and
deep draft vessels. Redistribution of these sediments through
dredging or other activity could jeopardize oyster beds or other
organisms less tolerant than the mud plain community. Care must
be exercised if these sediments are removed and deposited in the
estuarine system.
SEDIMENT NUTRIENT RELEASE
Introduction
The objective of this experiment was to assess the contri-
bution of Escambia Bay sediments to nutrient levels in the
overlaying water. Release of nutrients from sediments is
influenced by such factors as the metabolic activity of sediment
bacteria (Lee, 1970; Martin, 1970), dissolved oxygen in the water
above the sediment, and water currents which affect exchange
processes by transporting leached material away from the release
site and allowing concentration-dependent exchange reactions to
proceed. Another important physical factor is resuspension of
sediments, which exposes sub-bottom sediments to the water and
increases release of nutrients (Lee, 1970). All of these factors
are discussed further in this section.
To accomplish the objective of this experiment, the rates of
sediment nutrient release were determined for several
representative locations in Escambia Bay, and these rates were
used to approximate the total nutrient release in the bay.
7-32
-------
Methods
Sediment samples were taken with plexiglass corers at six
stations in Escambia Bay (Figure 7-16). The square-shaped
corers, with inner dimensions 23 cm by 23 cm, were designed to
collect the samples in the field and to serve as reactors for the
laboratory tests. The design of the corer is shown in Figure 7-
17. The cores were taken by project SCUBA divers. The diver
took the corer down to the desired location and submerged it into
the sediment to a prespecified depth of 15 cm. A top and bottom
were then placed on the corer to hold the sediment and water in
place, and the apparatus was returned to the boat.
The corers, with sediment, and bay water intact, were returned
to the laboratory and placed in an incubator at 20°C. The bay
water was removed and replaced with artificial sea water of the
same salinity. The artificial sea water was kept circulating
constantly by a pump to insure good mixing and to simulate
natural currents over the sediments. Aerobic conditions were
maintained in the water throughout the study.
The first three cores were collected on June 5, 1974,
incubated for 45 days, and terminated on July 22, 1971. The
second group of three cores was collected on July 25, 1974,
incubated for 67 days, and terminated on October 2, 1974.
Samples of the water were taken periodically from the reactor
chambers to be analyzed for five parameters: Total kjeldahl
nitrogen (TKN), ammonia (NH3), nitrate-nitrite (NO3-N02), total
phosphate (T-PO4) , total organic carbon (TOC) . Dissolved oxygen
was read by inserting a D.O. probe in the D.O. bottle (Figure 7-
17). The concentrations in mg/1 were obtained for each nutrient
for each day analyzed, and were converted to total mg in the
chambers (Appendix 7-5). The total mg was plotted against day
number for total nitrogen (Figure 7-18). Also, for total
nitrogen, a rate of release was calculated in terms of mg/m2/day
by using the maximum amount of release, the number of days it
took to achieve the maximum, and the surface area of sediment in
the chamber (Table 7-18).
Total nitrogen is defined as (TKN+NO3+NO2) .
The TOC data were extremely erratic and were not considered
in evaluating the results of this experiment.
Results and Discussion
Phosphorus release from sediments in this study was negli-
gible. The maximum total release was about one mg (Table 7-18).
Various investigators have shown that phosphorus is released very
slowly if at all under aerobic conditions (Mortimer, 1941; Lee,
1970). Aerobic conditions were maintained at all times so the
negligible release of phosphorus was to be expected. Values of
dissolved oxygen are listed in Appendix 7-5.
7-33
-------
-J
00
clomp
Figure 7-16* Nutrient release study
station locations in Escamtola Bay*
Figure 7—17* Sediment nutrient release
study apparatus*
-------
-d
Ul
50 r— EEKV
40
UJ
O 30
O
cc
K
Z 20
_l
I-
O 10
I I I
10
20 30 40 SO
DAY NUMBER
SO i— EKMP
40
5 30
O
(T
(-
= 20
O "0
60 70
I I I I I
10
20 30 40 50 60 70
DAY NUMBER
ISO
I20
EIIL
I I I I I I
I I I - I I I I
30
20 30 40 SO
DAY NUMBER
50 |— EPLP
30
20
10
I I I I I I I
I0
20 30 40 50
DAY NUMBER
60 70
20 30 40 50
DAY NUMBER
50 |— ERPB
40
30
20
10
I I I I I I I
10
20 30 40 50
DAY NUMBER
60 70
Figure 7-18. Plots of total milligrams of total nitrogen against
day number for each station (total nitrogen = TKN + NO
-------
_/\
lable 7 - 13. Maximum amount (rag) and rates of release (mg/m /day) found in the
nutrient release study.
Station Total Phosphorus Nitrate-Nitrite
TKN
Total Nitrogen
Released
i
U)
Oi
EEKV
EGLY
EIIL
EKMP
EPLP
EEPB
average
0
0
0
f\
1
0
0
.43
.57
.74
.27
.08
.22
.55
E
0
0
C
o
0
0
0
ata
.195
.330
.235
.136
.624
.110
.272
Released Sate
1.
C.
13.
1.
10.
10.
6.
47
07
7C
61
64
25
0.
0.
3.
0.
10.
6.
3.
11
84
72
66
55
65
Released Rate
l- 0
159.
17.
7.
25 .
10.
12.
80
24
24
35
52
58
30
0.
126.
8.
5.
10.
r-
O .
6.
26
60
02
39
58
30
11
Released Rate
2.
159.
30.
9.
36.
21.
19.
27
24
31
05
13
22
80
0.37
126. 6C
11.86
6. 1 1
21 .25
12.86
10.49
-------
Since nitrogen forms are interchangeable with one another in
an aquatic environment, it was not possible to assess the release
of each individual form. Only total nitrogen is discussed in
this section.
In order to assess the contribution of sediment nitrogen
release in Escambia Bay, total release in the bay was calculated.
The total release was calculated in two ways: First, the average
rate (in kg/m2/day) of release of total nitrogen was multiplied
by the number of m2 on the bay bottom to obtain a total release
in the bay. Second, the amounts of release by type of sediment
were obtained and these amounts were summed up to get a total
release in the bay. The first of these calculations is shown
below:
Avg. Rate Total Release
Total Area of Release kg/day
of Bay Bottom (m2) (kq/m2/day) (Area x Rate)
9256.2 x 10* 10.5 x 10~* 972
In order to calculate release of nitrogen from each sediment
type, the following breakdown of Escambia Bay sediments was made:
Station Sediment Type
EEKV B = Silty-Sand
EGLY A = Sand
EIIL C = Sand-Silt-Clay
EKMP D = Sandy-Silt
EPLP C = Sand-Silt-Clay
ERBP B = Silty-Sand
E = Silt
F = Clayey Silt
These sediment types were taken from the Escambia Bay sediment
classifications as described in the Sedimentation Section of this
report. A complication in this calculation was that none of the
samples was collected in type E or F. However, since types D, E,
and F are predominantly silt, these three were lumped together as
an approximation. Station EKMP was taken to be representative of
all three.
Data from Station EGLY were not used in the above calcu-
lation. This station was located near industrial outfalls, and
the nitrogen release was so great that it was not representative
of other sediments of the same type.
The results of the calculation are listed below:
7-37
-------
Avg. Rate Total Release
Area in Bay of Release kg/day
Station and Type (m2) kq/m2/day (Area X Rate)
EEKV-ERPB (A-B) 4679 x 10* 6.6 x 10~* 309
EIIL-EPLP (C) 2238 x 10* 16.6 x 10~* 372
EKMP (D-E-F) 2339 x 10* 6.1 x 10~6 143
Total = 824
The two totals of 972 and 824 kg/day compare favorably with
each other considering the limitations of the techniques used to
obtain these figures. These values compare with 2622 kg/day that
the industries are permitted to discharge into Escambia River and
upper Escambia Bay. (The nitrogen release calculated here
occurred under aerobic conditions. Anaerobic conditions would
cause a much greater release.)
Type C (sand-silt-clay) released the most nitrogen. This was
especially obvious since it had the least area. Types A-B (sand)
and D-E-F (silt) released about the same amount per unit area.
The only obvious explanation for the larger release from type C
is that station EPLP was causing a disporportionate effect.
Station EPLP was close to the Northeast Sewage Treatment Plant
outfall, which could have been affecting the sediment in the same
way as Station EGLY was affected by the industries. It appears
that nitrogen release was not correlated in any way with sediment
type, and some other factor was the primary influence.
A comparison of nitrogen release data with sediment microbial
activity data was made to see if any useful correlation existed
(Table 7-19). Nothing in this comparison indicated any
correlation at all.
A comparison of the concentration of nitrogen in the sediment
with rates and total amounts of nitrogen released showed that
nitrogen release increased as nitrogen content of• the sediment
increased (Figure 7-19 and Table 7-20). Data from Station EGLY
was not plotted because it was so abnormally high, as explained
earlier in this section. The influence of waste outfalls on
sediment nitrogen concentrations and on nitrogen release was seen
at Stations EGLY and EPLP in Table 7-20. Station EGLY was near
the industry outfalls and EPLP was near the Northeast Sewage
Treatment Plant outfall.
In summary, considerable amounts of nitrogen and very little
phosphorus were released from Escambia Bay sediments under the
conditions of this study. Two factors were observed to increase
potential for sediment nitrogen release. These were high
concentration of nitrogen in the sediment, and location in the
close vicinity of waste outfalls which discharge large amounts of
nitrogen.
7-38
-------
Table 7 - 19. Comparison of sediment nitrogen
release data with microbial activity data.
Station
EEKV
EIIL
EGLY
EKMP
ERPB
EPLP . .
Total
amount
Released
(rag) **
2.3
30.3
159.2
9. 1
21.2
, 36.1
Nitrogen
Rate of
Release
(mg/m2/:lay)
o.u
11. 9
126. 6
6. 1
12.9
21.2
Microbial
Activity
(*)
264.3
455.6
233.4
1147.0
0 . "
230.5
* (ug - TPF reduced per gram of sediment)
** Total Nitrogen = TKN + N03-N02.
lablf-- 7 - 2J. Cojiparisori or p^ucent or'jariic anJ nitL'oqcn content or sediment with
rates of release oi total nitrogen*.
Station
EEKV
EIIL
EGLY
EKKl'
ERF &
EPLP
P ere en t
0 cyanic
(fe)
0.3<*
3 • y 9
5.83
7.U2
6.29
7.49
Hate of
Release
(r,icj/>fl2/day)
0.37
11. 86
126.60
6. 11
12.8o
21. 25
Tot.il
He lease
(aig)
2.27
.30.31
154.24
9.G5
21.22
36.13
Concen tr dtion or!
TKN in seJiment
(wg/y)
82
5^50
6^50
3350
2250 '
6800
* Total Nitroyen = TKN + N03-N02
7-39
-------
o
•o
UJ /-C1^
§i'f
ii°3
-<-!j
2 ^U
0**
h- H U.
~* o
LJ
Jj
a:
Q
m (VI(/)
H' '">£
2 z o>
-1 + E
o"<
~" H
27
24
•'
ie
12
9
6
3
0
(
45
40
35
30
25
20
15
10
5
O
— ^^
EPLP
— . ' ^
ERPB ^.•**'"
* ^-*"^ EML
^^^
^x*"** EKMP
— ****' •
^**"
— ^""
*'
-------
It should be pointed out that resuspension of sediments could
increase the amount of nutrient release. There was little or no
suspension of sediments in the water during this study. The
sediments remained undisturbed throughout. Suspension of
sediments undoubtedly causes greater nutrient release than was
measured in this study. It is important to note also that even
though aerobic conditions were maintained in the chambers, there
are times when bottom water in Escambia Bay becomes anaerobic.
This would cause much greater release of both nitrogen and
phosphorus than was measured in this study. The reasons for
greater anaerobic release are discussed by Lee (1970).
MICROBIAL ACTIVITY
Introduction
The sediments in a bay can be considered a reservoir of
nutrients which are constantly being released or cycled to the
overlaying water column as one of the sources of nutrients
contributing to the enrichment of a bay ecosystem. Micro-
organisms at the base of the food chain are responsible for
initiating the conversion of sediment to biomass and thus into a
form that can be utilized by higher organisms.
Any method of measuring microbial activity in sediments has
certain limitations. In-situ techniques have not been well
perfected and are frequently plagued with technical difficulties.
Often the change being measured in a given parameter is so slight
that the accuracy of field instrumentation is questionable.
Other problems with maintaining accuracy of instrumentation in
field measurements are humidity and temperature changes
throughout the day. Natural conditions are altered when sediment
samples are collected and brought into the laboratory.
Experimental conditions in the laboratory will very likely have
an influence on the results. Data obtained from laboratory
controlled experiments may be difficult to relate to field
situations.
Considering all of the above factors and the expense of
equipment for measuring radioactive compounds used in other
possible techniques, the dehydrogenase procedure was chosen as
most feasible for this project.
The objectives of this study were: (1) to measure the
microbial activity of sediments as a comparative parameter for
the various sediments of the bay system; and (2) to provide some
information on the microbiological turnover of nutrients or the
mineralization of sediments in the bay.
7-41
-------
Methods
Sample Collection
Sediment samples were collected for this study at the tri-
weekly water quality stations (Figure 7-20). Most of the samples
were collected with a corer constructed of Lexan tubing attached
to a tubular metal corer handle. The Lexan coring tube was 7.0
cm x 117.6 cm.
The corer was lowered over the side of the boat allowing it
to fill with water, raised to a vertical position, and then
lowered to the sediment surface. Downward pressure was applied
to force the corer into the sediment approximately 0.6 m (2.0
ft). Average core length ranged between 0.5 m - 0.76 m (20-30
in). The filled corer was gently raised into the boat and held
in a verticle position until the handle was removed. ft. plunger
was used to push the core through the coring tube until the top
surface of the core came to 1.5 cm (0.59 in).,, from the end of the
coring tube. With _the core held in this position, a combination
Eh and pH probe was inserted into the surface of the sediment
core. After the Eh and pH measurements were completed, the corer
was inverted into a one quart plastic freezer container. Fifteen
cm (5.9 in) of the sediment core was extruded from the surface
end of the corer into the plastic container.
Sediments which were mostly sand could not be retained in the
corer. These stations were sampled with a Peterson Dredge. The
contents of the dredge were gently placed in a tub with the
sediment surface disturbed as little as possible. The Eh and pH
readings were taken as described in the following paragraph, and
a sample of approximately equal diameter and depth to the core
sample was scooped into the plastic container using a spatula.
The containers of sediment were placed in an insulated ice chest
as near to ambient water temperature as could be maintained until
returned to the laboratory for analysis.
Field Measurements
Field determinations of Eh and pH were made with a Corning
Model 610A pH-Mv Meter. The Eh measurements were taken with a
Beckman platinum electrode in combination with a Fisher Calomel
electrode. A Fisher brand glass electrode in combination with
the same Fisher Calomel electrode used in Eh measurements was
employed to determine the pH on each sediment sample.
The pH meter was calibrated to pH 4.0 and pH 7.0 standard
buffer. After a pH reading was taken, the meter was then reset
for Eh at a calibration mark previously determined in Zobell's
redox buffer (Zobell, 1946). The electrodes were placed in the
sediment and allowed to equilibrate for ten minutes. An Eh
reading was then recorded.
7-42
-------
ER10
24.11
MONSANTO CHEMICAL CO.
Figure 7-20. Microbial activity (by TPF reduced per gram of dry
sediment) in the Pensacola Bay system during 197U.
7-U3
-------
Water depth, salinity, temperature, and transparency were
measured and recorded at each station. A bottom water sample,
0.3 m (1.0 ft) above the sediment, was collected for dissolved
oxygen determination on return to the laboratory.
Laboratory Analyses
To determine percent organic matter in the sediment,
approximately 100 g wet weight of the mixed sample was placed in
a tared crucible and oven dried at 105°C for 24 hours. The dried
sample was cooled in a dessicator, weighed, and then ashed in a
550°C muffle furnace for 24 hours. This ashed sample was then
removed, cooled, and saturated with distilled water. The re-wet
sample was placed back in a 105°C oven. After 24 hours in the
oven, the sample was cooled in a dessicator and weighed to
determine the re-wet ash weight. A percent organic content was
calculated from the dry weight and re-wet ash weight.
Chemical oxygen demand of the sediment was determined
according to the procedures outlined in Standard Methods,
(American Public Health Association, 1971). Total phosphorus and
total Kjeldahl nitrogen were analyzed by the standard automated
EPA procedure (USEPA, 1971).
Dehvdrogenase Procedure
Microbial ;activity was determined by measuring the
dehydrogenase activity of the sediment population according to
the method of Cook, (personal communication from D. W. cook.
Microbiology Section, Gulf Coast Research Laboratory, Ocean
Springs, Mississippi). This procedure is similar to one used by
Lenhard, et al. (1965); Bucksteeg (1966); and Pamatmat and
Bhagwat (1973), which employs the reduction of triphenyl
tetrazolium chloride (TTC), a colorless dye in its oxidized
state. Triphenyl formazan (TPF), the reduced form of the dye,
is red. In solution the concentration of TPF can be determined
spectrophotometrically. The TTC was incorporated into the assay
procedure as a substitute hydrogen acceptor (or electron
acceptor) to replace oxygen in aerobic systems and organic
compounds which would become more reduced in anaerobic systems.
This required an oxygen free atmosphere, which was accomplished
by incubating the reaction mixture in an evacuated dessicator
throughout the 24 hour incubation period.
On their return to the laboratory, each sample was thoroughly
mixed with a teflon coated spatula. A one-gram quantity of the
stirred sediment sample was weighed into each of five tared 50 ml
tapered centrifuge tubes on a top loading balance. Dehydrogenase
assays were performed in triplicate on each sediment sample. A
fourth tube was used as a reagent blank with TTC withheld. The
fifth tube was autoclaved and used as a sterile blank to
determine any non-microbial reduction of TTC.
7-44
-------
Reagents used for the assay were: (1) 0.05 M Tris buffer (pH
8.4), 0.5 ml; (2) 1.0% TTC, 0.5 ml; (3) 50 jjg CaCo3; and 1.0 g of
mixed wet sediment. The TTC was added to the sterilized blank
after it was removed from the autoclave and allowed to cool. An
additional 0.5 ml of Tris buffer was substituted for the 1.0% TTC
solution in the TTC blank. The reagents were thoroughly mixed on
a Vortex Jr. Mixer, and placed in a dessicator. The dessicator
was then evacuated and the tubes incubated at 25°C for 24 hours.
The dehydrogenase reduction of TTC was terminated by addition
of 10 ml of methanol to each tube. The methanol also served as a
solvent for the reduced TPF. The sediment and methanol were
thoroughly mixed and then centrifuged for 5 minutes to separate
the sediment from the TPF-methanol solution. The procedure was
repeated three additional times and the final volume of TPF-
methanol brought to 50 ml with methanol. The concentrations of
TPF were determined spectrophotometrically at 485 nm by comparing
the absorbance of the extracted TPF to a standard curve derived
from known concentrations of TPF. Microbial activity of the
sediment as measured by the dehydrogenase assay procedure was
expressed as pg TPF/g dry sediment.
Results
In general, all the tributary stations (ER10, EEDR, EHBD,
EEEM, EQGM, BFEI, and BJIV), were low in microbial activity
(Table 7-21). These stations were also high in sand content and
were low in percent organic matter. Two Escatnbia Bay stations,
ETQE and EPRF, located in the proximity of the eastern shore,
also had very low microbial activity. The sediment from these
stations, like the sediment from the tributary stations, was high
in sand content and low in organic matter. One major exception
to this was Station ERPB which had zero microbial activity yet it
ranked third of all stations in organic matter content. The zero
reading for Station ERPB was due to the extremely high activity
of the sterile blank which canceled out the activity observed in
the triplicate reaction tubes. One possible explanation for the
high activity observed in the sterile blank for sample ERPB would
be chemical reduction due to large concentrations of reduced
compounds in the sediment as shown by "Effenberger (1966, cited
by Pamatmat and Bhagwat, 1973)".' Pamatmat and Bhagwat (1973),
however, did not observe this in their work. The +300 mv Eh of
sample ERPB was no indication of a highly reduced sediment and
would reinforce their observations.
Examination of the data showed stations higher in organic
matter content and chemical oxygen demand generally had higher
microbial activity. By statistical analysis, a significant
correlation was shown for chemical oxygen demand and sediment
microbial activity (r = 0.7, df = 38, p <0.01). Percent organic
matter and sediment microbial activity showed less correlation
than chemical oxygen demand but still a significant correlation
(r = 0.42, df = 38, p <0.01). Other parameters tested which had
significant correlations with sediment microbial activity were
7-45
-------
Table 7 - 21. Suonary of sediment oicrobial activity.
Date Station
07/18/70 E8-10
07/18/70 EEDR
07/18/71 EHGD
07/15/71 EEIX
07/15/70 EEEn
07/15/71 EUGH
07/22/71 EEKV
07/22/70 EGLY
07/25/71 EGLY
07/22/71 EIKC
08/05/70 EIIL
08/05/70 EKLQ
08/05/70 EKHP
08/05/70 EHPK
08/08/70 EBQC
08/12/71 EBQC
08/12/71 ENNB
08/12/71 EPLP
07/25/71 EPLP
08/15/70 ETQE
08/15/71 EPHP
08/15/71 EBPB
08/15/71 ETLQ
10/09/71 PEOB
09/30/71 BPEI
09/30/71 BJIV
09/30/70 BNGA
10/02/70 BREH
10/02/71 ADGV
10/02/71 AGPH
10/07/70 AGJI
10/07/71 AJPD
10/07/71 ALEX
10/09/71 P-08
10/09/71 P-13
Deptli
(m)
1.8
0.0
5. 8
1.2
2. 3
3.1
1. 5
2.1
2.1
1. 8
2.0
2. 1
2.6
1.5
2.1
2.6
2.6
2.3
2. 1
2.1
2.7
3.7
1.6
2.1
3.5
2. 1
3.0
3.0
2.7
1.8
3.1
3.0
0.3
10.1
5.5
Trans.
(m)
C.8
0.8
0.9
0.6
0.6
0.8
0.5
n.8
0 . 8
fl.fl
1.0
0.9
1.2
0.9
1.2
1.0
1.0
1. 0
0.5
,0
.5
.5
.0
.5
2.0
2.0
2.1
2. 1
1.8
Bottom
Salinity
(PPt)
0.0
5.7
11.5
11.3
10.0
15.5
15. 1
19.2
19. 2
17.7
16.9
17. 1
18.0
13.0
18.1
23.2
21.9
17.9
25.5
28.2
26. 1
29.2
30.2
22.5
20.0
21. 2
25.3
19.7
19.8
19.7
28.1
25.7
28.5
31.6
30. 1
Sed.
Temp.
PC)
27.0
29.0
30.5
32.0
30.0
30.0
31.0
32.0
30.0
31.0
27.0
28.0
29.0
29.0
29.0
31.0
31.0
31.0
30.0
29.0
29.0
29.0
29.0
25.0
26.0
26.0
26.0
21.0
25.0
20.0
25.5
26.0
25.0
25.0
25.0
Bottom
D.D.
(ug/1)
6.2
0,6
8.2
7. 1
5. 1
2.0
6.0
6.0
6.0
7.1
5. 1
2.1
6.9
5.6
2.3
2.2
7.3
6.5
10.0
0.6
6.6
2.3
1.3
8.2
0.6
7.0
2.1
7.6
6.5
7.1
6.1
8.8
7.3
7.2
6.1
Sed.
pH
(std un)
6.7
7.0
8.0
7.2
7.2
7.2
7.9
a. o
8.1
6.5
0.5
3.6
5. 1
6.1
7.1
3.8
6.5
7.5
8.9
8.0
7.8
7.9
7.3
8.0
6.3
6.1
7.1
7.0
7.0
6.0
7.2
Sed.
Eh
»30C.
• 110.
• 10.
• 70.
«93.'
•00.
»95.
-BO.
-80.
»i3r, .
-130.
-5.
-5.
*20.
-200.
-150.
-105.
••280.
»170.
• 190.
*300.
• 275.
-60.
• 160.
-160.
-160.
-270.
-120.
-180.
»00 .
»30.
-100.
-80.
• 10.
(TPP)
(TPP)
Percent nicrobial Sterile
T-P01
(09/91
13.0
21.0
10.0
96.0
11. 0
70.1
66.5
205.0
30C.O
220.0
131.0
36.8
120.0
116.0
370.0
310.0
510.0
190.0
295.0
18.0
290.0
38C. 0
530.0
210.0
22.1
18.1
39.0
350.0
250.0
32.0
230.3
178.0
510.0
310.0
350.0
TKN-N
°19/y>
26.
31.
1 18.
385.
10.
182.
200.
1100.
1550.
950.
5300.
1980.
5100.
6201.
5950.
60CO.
7?00.
2600.
2100.
1860.
1900.
5800.
6300.
6000.
1960.
1910.
1900.
7550.
5950.
1700.
6003.
5000.
6150.
6300.
7850.
COD
(P9/9)
208.
3120.
5200.
20803.
620.
3323.
16613.
63100.
92563.
93600.
53590.
8703.
118270.
78503.
80083.
90550.
109963.
87600.
62103.
1813.
20330.
86860.
96103.
116120.
7590.
13323.
23100.
115993.
1 11803.
16630.
110883.
68380.
110880.
112730.
109030.
organics Activity
(*>
:.so
0.61
0.67
1.61
0.22
3.6.1
1.32
5.08
1.66
6.63
2.93
3.69
8.38
5.26
13.87
6.35
2S.22
11.27
27.81
3.60
1.32
21.38
13.01
9.56
9.58
1.09
2.15
13.19
7.56
1.02
13.66
6.07
11.78
9.31
16.60
(pg/i)
20. 11
8. 18
00.26
187.20
0.00
0. 18
260.30
238.38
.356.99
335.70
055.57
07. C8 •
1107.01
127.87
515.59
170.51
802.79
230.52
267.68
18.70
8.01
0.00
019.85
213.00
0.00
20.52
193.82
1733.52
596.75
6.1.38
086.77
615.93
261.52
192.72
1069.08
Blank
(jig/g)
0.00
31.03
26.08
69.69
55.07
25.28
52.01
09.33
276. 3B
B2.69
31.61
.12.50
02.29
0.00
96.13
201.92
199.77
113.03
18.57
78.00
611.16
089.73
322.81
15.00
20.89
119.02
339.83
031.97
66.60
170.16
82.06
295.86
771.96
360.10
-------
total phosphorus (r = 0.56, df = 38, p <0.01), and total Kjeldahl
nitrogen (r = 0.54, df = 38, p <0.01).
Two stations in Escambia Bay were subject to the influence of
industrial or domestic effluent entering the bay. One of these
stations was EGLY near the American Cyanamid outfall. Effluent
from Air Products holding ponds also flows through a swamp into
the bay within 2.2 km (1.2 nautical miles) of Station E3LY.
Microbial activity at Station EGLY was observed to be 356.99 /jg
TPF/g of dry sediment. This value is very close to the average
of 332.91 M
-------
outfalls nor did they reveal inhibited microbial activity due to
presence of toxic substances in the sediment.
Examination of the data showed, in most instances, increased
microbial activity at all stations which had an organic matter
content of one percent or greater. Any increase in organic
matter, content of the sediment over one percent was not
necessarily accompanied by a corresponding increase in microbial
activity. This indicated that a one percent organic matter
content will support a maximum microbial population to a steady
state of growth. Any fluctuations in microbial activity are
organism!c responses subject to numerous stimuli. Variations in
microbial activity can be attributed to: (1) variations in
microbial species or metabolic types of organisms; (2)
differences in the growth phase of a major portion of the
pqpulation; (3) differences in the type of organic matter, and
thus its recalcitrance to microbial conversion; (U) availability
of other nutrients; and (5) conditions favorable for growth.
Nutrient cycling and mineralization could not be specifically
determined. By inference, the measured microbial activity can be
related to nutrient cycling and mineralization. The greater the
sediment microbial activity, the greater the quantity of material
converted to energy, biomass, and released metabolic products. A
major portion of the nutrients converted to biomass would return
to the sediments after the death of the organisms.
Microbial activity of sediment in Escambia Bay did not
markedly differ from that observed in Blackwater Bay or East Bay.
Escambia Bay sediments appeared to be normal, based on microbial
activity, since East Bay and Blackwater Bay were used as
controls.
7-48
-------
8 - WATER QUALITY
INTRODUCTION
The Pensacola Bay system is an extremely valuable resource to
the residents of the area, the state, and the nation. Its
principal values are derived from recreation and commercial
fisheries. The continued value of this resource depends on
maintaining a healthy aquatic ecosystem which is dependent on the
quality of the waters of the system. Consequently, it is
imperative to determine the quality of the water in the bay to
properly evaluate the system.
The water quality of the Pensacola Bay system, with emphasis
on Escambia Bay, was monitored to determine seasonal, tidal, and
spatial variations. The purposes of the water quality studies
were to:
• describe water quality conditions in Escambia Bay and
the Pensacola Bay system and to compare them to other
Gulf of Mexico estuaries.
• determine if changes in water quality have occurred
between 1969 and the present.
• determine what the effects of wastes discharged into the
bays have on the system.
Interpretation of water quality data will provide information
for the development of water resource recommendations.
METHODS
Water Quality Studies
Water quality studies were initiated in the Pensacola Bay
system between April 1973 and September 1971. In April and
August 1973, diel (2U-hour) water quality studies were performed
in the Pensacola Bay system when periods of high and low river
discharge, repsectively, normally occur. During each period,
separate studies were performed during equatorial and tropic
tidal conditions. Water quality studies were also performed in
Escambia Bay on October U, and December 5, 1973. The University
of West Florida (UWF) conducted water quality studies every two
weeks in Escambia and East Bays during 1973. The EBRS and the
UWF performed water quality studies in the Pensacola Bay system
every three weeks from January to September 1974. The sampling
dates and times are depicted along with tide level on Appendix 8-
1. The locations, STORET station numbers, and parameters sampled
for all sampling stations are presented in Appendix 8-2.
In this report, samples referred to as surface were collected
0.3 m (1.0 ft) below the surface, and those referred to as bottom
8-1
-------
were collected 0.3 m (1.0 ft) above the bottom. The mean
sampling depths for all stations occupied during EBRS are
presented in Appendix 8-3 for diel studies performed in 1973, and
in Appendix 8-4 for January through September 1974 studies.
Analytical Methods
The analytical, sample collection, and preservation methods
used during this study are presented in Appendix 8-5.
ENVIRONMENTAL CONDITIONS
Environmental conditions, such Kas rivsr discharge, tides,
wind, and precipitation, must be known when evaluating water
quality because they are the cause of significant variation. A
summary of environmental conditions is presented in Table 8-1 for
the water quality studies performed by the Escambia Bay Recovery
Study. Tide stage and wind vectors for each study are presented
in Appendix 8-1.
WATER QUALITY STANDARDS
Florida has enacted Water Quality Standards to protect the
surface waters of the state. The Pensacola Bay system has been
designated as either Class:II or Class III waters. The criteria
for Class II waters are designed to permit harvesting of
shellfish safe for human consumption. The criteria for Class III
waters are to provide satisfactory water quality for propagation
and maintenance of fish and wildlife populations, and for
recreational activities, including water contact sports. Class
III waters include upper Escambia Bay and tributaries above the L
and N Railroad bridge, Pensacola Bay west of a line from Emanuel
Point to the south end of Highway 98 bridge at Gulf Breeze, and
Blackwater Bay inclusive of the river north of a line from
Robinson Point on the west to the mouth of Broad River on the
east. All the remaining areas of Escambia Bay, Pensacola Bay,
East Bay, Little East Bay, and Blackwater Bay are Class II waters
(Figure 8-1). The criteria for the Florida Water Quality
Standards are discussed in Florida Administrative Code (1973).
Appropriate sections from Chapter 17-3, Pollution of Waters are
presented in Appendix 8-6.
There are no compulsory Federal water quality standards for
specific states or bodies of water. However, the State of
Florida Water Quality Standards are subject to review and
approval by the United States Environmental Protection Agency
pursuant to Section 303 of the Federal Water Pollution Control
Act Amendments of 1972.
The National Technical Advisory Committee, a joint committee
consisting of members from the National Academy of Science and
the National Academy of Engineering, compiled a report,
recommending water quality standards, at the request of the
Secretary of Interior. Their report, published as Water Quality
8-2
-------
Table 8-1. Environmental conditions during water quality studies.
s Es-timated total flo»
t
Study Date
9/23-25/69
4/13-15/73
4/19-21/73
8/16-18/73
8/23-25/73
10/4/73
12/5/73
1/23/74
2/12/74
J/5/74
3/2 7/7 4
4/16/74
5/7/74
5/29/74
6/18/74
7/9/74
7/30/74
8/2C/74
9/11/74
u Escambia
d River
y m 3 /sec
(cfs)
132
(4657)
I 1398
(49,400)
II 600
(21180)
III 173
(6119)
IV 122
(4295)
109
(3840)
88
(3120)
333
(11760)
737
(26040)
226
(7974)
203
(7180)
506
(17865)
85
(3012)
178
(6294)
126
(4433)
71
(2505)
69
(2442)
147
(5178)
7UU
(2773.C)
Yellov
River
m 3 /sec
(cfs)
.
211
(7470)
108
(3818)
72
(2546)
53
(1888) '•
-
-
81
(2860)
205
(7243)
73
(2590)
90
(3161)
120
(4247)
42
(1483)
48
(1708)
33
(1165)
32
(1130)
38
(1342)
56
(1977)
167
(5S97)
Black Mater
River Total
D 3 /sec n 3 /sec
(cfs) (cfs)
-
88
(3092)
49
(1718)
41
(1443)
33
(1158)
-
-
41
(1443)
128
(4534)
39
(1374)
53
(1855)
70
(2479)
27
(953)
39
(1377)
23
(812)
23
(812|
23
(812)
31
(1095)
(5790)
-
1597
(59,920)
757
(26739)
286
(10100)
208
(7340)
-
-
455
(16070)
1070
(37780)
338
(11940)
346
(12220)
696
(24580)
183
(6460)
265
(936C)
182
(6426)
126
(U449)
130
(459C)
234
(8263)
1115
(39370)
ride
Range
m
(f)
0.7
(2.3)
0.1
(0.4)
0.6
(2.1)
0.2
(0.5)
0.6
(2.0)
0.4
(1.4)
3.2
(0.7)
3.5
(1.6)
0.5
0.6
(1.8)
0.5
0.3
(1.3)
0.6
0.2
(0.6)
0.5
(2.1)
0.3
(1.3)
0.5
(1.')
0.2
(0.7)
0.5
(1.7)
Hean
leva! rurront
m a
(f) (f)
0.0
(0.3)
0.3
(0.9) -
-0. 1
(-0.2) -
0.0
1-0.1) -
0.3 E
(0.3)
3.1 F
(0.3)
-0.2 LKS
(-0.3)
-0.2 f
(-0.6)
-0. 1 P
(-0.2)
-0.1 F
(-3.4)
-0.1 P
(-0.3)
0 H 85
(3.)
0. HNS
(-0..1I
-0.1 BUS
(-3.3)
0. F
(-0.1)
0.1 E
(5.2)
0.1 LUS
(0.2)
-0.2 E
(-0.6)
- Kind
Mean Prevailing
Speed Direction
ka/hr
(mph)
8.1 N-NB
(5.3)
15.5 Variable
21.9 SE
(13.6)
4.8 E
(3.0)
(5.8)
9.5 H
(5.9)
13.3 HE
(8.5)
10.9 SI
(5.3)
9.7 SE
(6.0)
16.7 S
(10.4)
14.3 E
(8.9)
8.5 H
(5.3)
10.1 NE
(6.3)
12.2 SH
(7.6)
9.5 SE
(5.9)
12.6 Variable
(7.3)
13.7 SE
(8.5)
8.5 Variable
(5.3)
10.0 SE
(6.2)
Precipitition
CB
(in)
0.
0.
(0.)
0
(0)
2.97
(1.17)
D
(0)
o.m
(0.16)
0
(0)
0
(0)
0.03
(0.01)
3.78
(1.49)
0
(0)
0
(Ol
0
(0)
0
(0)
0
(0)
0
(0)
0
(0)
8-3
-------
Figure 8-1. Classification of the Pensacola Bay system under the
Florida Water Quality Standards.
8-
-------
Criteria (1972), suggests criteria for the following water uses:
(1) Recreation and Aesthetics; (2) Public Water Supplies; (3)
Freshwater Aquatic Life and Wildlife; (4) Marine Aquatic Life and
Wildlife; (5) Agricultural Uses of Water; and (6) Industrial
Water Supplies.
PRINCIPAL NUTRIENTS
Carbon
Introduction
The total organic carbon (TOC) measurement was used to assess
the concentrations of organic material in the Pensacola Bay
system. Carbon is a major component of microbial biomass and an
oxygen demand is exerted by aerobic microorganisms as they
consume carbon. Consequently, total organic carbon occurs in the
biomass of plant and animal organisms, and as natural
decomposition products. Waste discharges also add TOC to the
Pensacola Bay system. An excessive concentration of TOC, greater
than 2.0 mg/1 (see Principal Nutrient Index section), can be an
indicator of over enrichment which can depress dissolved oxygen
levels by causing excessive populations of microorganisms.
Results and Discussion
Mean TOC concentrations in all components of the Pensacola
Bay system were greater than the 2.0 mg/1 calculated standard
during all surveys performed in 1974 with the exception of the
surveys performed on June 18 and July 30, 1974 (Table 8-2).
Consequently, sufficient carbon was usually available in the
Pensacola Bay system to theoretically cause the dissolved oxygen
concentrations in the waters to be depressed below the
concentrations specified in the Florida Water Quality Standard
(Appendix 8-6).
Mean TOC concentrations during the 1974 water quality surveys
were distributed uniformly throughout Escambia Bay (Figure 8-2) .
Mean concentrations throughout the bay were generally lower than
those in the river. There were no obvious increases in TOC
concentrations near waste discharges during this period.
Throughout East and Blackwater Bays the mean TOC
concentrations were essentially the same during January through
September 1974. In Pensacola Bay, TOC concentrations generally
decreased in a seaward direction with the lowest mean
concentrations occurring at Station P04, at the western end of
Santa Rosa Sound.
A statistical analysis of TOC data collected during the 1974
surveys indicated that the mean TOC concentration in Escambia Bay
was statistically higher than mean concentrations in Pensacola
and East Bays (Table 8-3).
8-5
-------
Table 3-2. Moan total organic carbon concentrations in the Psnsacola
Bay system duriny January through September, 1974 (Pensacola Ray data
from the University of west Florida).
. Date
1/23/74
2/12/74
3/05/74
3/27/74
0, U/16/74
1
** 5/C7/74
5/29/74
6/1d/74
7/09/74
7/30/74
8/2n/74
9/11/74
affective
Flow (1)
( in 3/sec )
455
1C 70
338
346
696
183
265
182
126
13C
234
1115
Escambia
(mg/1)
4.8
7.2
4.6
3.2
5.2
4.5
3.8
4.0
6. 1
3.2
4.6
- 8.2
East
(mg/1)
1.9
6.0
4.3
2.5
3.4
3.1
3.8
2.4
5.0
1. 3
4.8
6.9
Blackuater
(mg/1)
4.6
n.2
2.9
3.0
4.4
3.9
3.5
1.9
4. 1
3.7
-.-;-. ".9
12.8
Pensacola
(raj/1)
3.3
4.9 •
5.3
4.7
3.6
2.2 .
2.6
-
3.6
2. 7
3.2
3.:
(1) Totdl eLrcctivG tlow into the Pensacola 3ay system.
-------
00
I
Figure 8-2. Mean total organic carbon (mg/l-C) in the Pensacola
Bay system during January through September, 1974.
(Pensacola Bay data from the University of West Florida).
-------
Table 8-3. Statistical comparison of mean total organic carbon concentrations
in Escambia Bay with those in other components of the Pensacola Bay system
during January through September, 197U (Pensacola Bay data froia the
University of West Florida).
Bay
Escambia
East
Blackwater
Pensacola
Mean TOC
concentration
(mg/1)
5.15
3.9U
5.25
3.7U
Calculated t
-
6.U1 (1)
0.29 (2)
6.88 (1)
Degrees o±
freedom
-
36
38
60
(1) The hypothesis that the mean TOC concentration in the given bay was
less than that in Escambia Bay can be accepted with greater than
99 percent coufidence.
(2) The hypothesis that the mean TOC concentrations in Escambia and
BlacKvater Bays are equal can not be rejected.
During the water quality survey performed in Choctawhatchee
Bay on September 12, 197U, the surface and bottom values of TOC
generally decreased in a seaward direction as shown in Figure 8-
3). A comparison of the mean TOC concentration in Choctawhatchee
Bay on this date with the mean concentration in the Pensacola Bay
system during the period March through August 1971 indicated all
bays had about the same mean concentrations as shown below:
BAY
Choctawhatchee
Escambia
Pensacola
East
Blackwater
TOC
U.4
3.7
3. a
3.6
The river discharge into the Choctawhatchee and Pensacola Bay
systems were 71 and 75 percent of mean annual flow for the
comparison periods. Again, the mean concentrations in all bays
were above the 2.0 mg/1 calculated standard.
; Mean TOC concentrations in the components of the Pensacola
Bay system were slightly lower during the 1973 low flow diel (24-
hour) water quality surveys than during the high flow surveys
(Table 8-4). Mean concentrations in all components of the system
8-8
-------
Table 8 - 1• Mean total organic carbon concentrations in components of
the Per.sacola ' Bay' system during 1973 diel water quality surveys.
Survey,
Tide
Depth
Sscambia
Bay
(rag/1)
East
Bay
(mg/D
Pensacola
,Bay
(rag/1)
Eq uatorial
8.0
11.2
8.0
11. 1
7.6
10.7
II
Tropic
7.8
10. 1
3.0
10. 3
7.9
11.7
III
Eq uatoria1
7. 3
6. 1
6.6
5. 2
7.0
u. 1
Tropic
A
E
5.6
5.5
14.14 U . 2
3.6 2.9
were about the same. All mean concentrations during all
surveys were greater than the 2.0 mg/1 calculated standard.
four
There were no obvious patterns in the mean surface and bottom
TOC data in Escambia Bay during September 1969 (USDI, 1970) as
shown in Figure 8-4. A comparison was made of mean TOC
concentrations during the 1969 water quality survey with those
during the 1973 and 1974 water quality studies (Table 8-5). The
stations considered were E1, E3, E7, E9, E10, E13, E18, and E20
during 1969; and EEIX, EEKV, EIIL, EKLQ, EIKC, EKMP, and EGLY in
1973 and 197U. All the above stations are located in upper
Escambia Bay. The mean TOC concentration was 45 percent greater
during August 1973 than during September 1969. During all the
1974 surveys considered, the mean TOC concentrations were lower
than the 1969 mean, and the greatest decrease, 24 percent,
occurred between September 1969 and June 1974.
Most TOC concentrations measured during surveys performed by
the Escambia Bay Recovery Study and the University of /Jest
Florida were greater than the 2.0 mg/1 standard calculated by the
method used in Water Quality Criteria (1972). Little variation
in •• TOC concentrations occurred throughout the components of the
8-9
-------
Figure 8-3. Total organic carbon (mg/l-C) in Choctawhatchee Bay
on September 12, 1974.
Figure 8-U. Mean total organic carbon (mg/l-C) in Escambia Bay
during September 23 to September 25, 1969.
8-10
-------
Table 8-5. Comparison of mean total organic carbon concentrations in upper Escambia
3ay between Septenber, 1969 water quality surveys and the surveys in 1971 and 1971.
Total Organic Carbon
Date
September 23-25, 1969
August 23-25, 1973
May 5, 197«
Juno 18, 197H
August 2C, 197«
Summer 197U*
Mean
total organic carbon
concentration
(ng/1)
1.9
7. 1
4.5
3.7
1.8
1. 3
Change in
mean from
1969
(*)
-
+ 15.
- 8.
- 2U.
- 2.
- 12.
Percent of
1969 floti
<*)
.-
92.
86.
95.
1 11.
89.
* ("ean for studios performed during May through August 1971.
Pensacola Bay system, and distinct patterns of TOC concentrations
due to waste discharges were not observed. A summary of TOC data
by stations for January through September 1974 is presented in
Appendix 8-7.
Nitrogen
Introduction
Nitrogen is present in most aquatic environments dus to such
processes as dieoff of organisms and release of nutrients from
their biomass into the waters, sediment nutrient release
(discussed in the Sediment Nutrient Release section) , inflow from
tributaries, and land runoff. When wastes which contain large
amounts of nitrogen are introduced into an aquatic system, an
imbalance is created which can cause eutrophication if the
necessary concentrations of other nutrients such as phosphorus
are present. Another problem with industrial nitrogenous wastes
is that some of them are toxic to aquatic organisms and so
present a threat to the health of the system.
Significant quantities of nitrogen can also enter an aquatic
system from the atmosphere due to both.precipitation and "dry
fallout". This problem was not evaluated during this study.
8-11
-------
A criterion for assessing the extent of nitrogen imbalance in
an aquatic system is the nitrogen to phosphorus . (N-P) ratio.
This ratio, which on a weight basis is about 7.25:1, relates
total nitrogen to total phosphorus (Water Quality Criteria, 1972;
Redfield, et al., 1963). It holds true generally for the open
oceans, but in coastal and restricted waters such as estuaries,
the ratio is usually considerably .different. This is because
productivity is usually so much greater in estuaries, and inputs
of nitrogen are so variable.
Water Quality Criteria recommends that a total nitrogen
concentration of 0.360.mg/l in a marine ecosystem is excessive.
This value is based on stoichiometric calculations which show
that 0.360 mg/1 total nitrogen together with 6.05 mg/1 total
phosphorus would produce enough organic matter to exhaust the
oxygen content of the water at the warmest time of the year with
poor circulation. The assumption made in these stoichiometric
calculations is that 212 moles of oxygen are consumed in
oxidizing each mole of phosphorus, and 4.0 moles of oxygen are
consumed in oxidizing each mole of nitrogen (Redfield, et al.,
1963). These calculations assume that all nitrogen and all
phosphorus will eventually be biologically utilized. However,
these values are the only reference standard available to assess
nitrogen and phosphorus concentrations in an estuary. Even
though they were used in this report, their limitations should be
kept in mind.
Florida Department of Environmental Regulation criteria do
not give specific limits for nitrogen. .
Results and Discussion
All but two of the mean concentrations of total nitrogen in
Escambia Bay during 1974 studies exceeded the reference standard
of 0.360 mg/1 (Water Quality Criteria, 1972) (Table 8-6). These
two occurred during the June 18, 1974 and July 30, 1974 surveys.
Total nitrogen concentrations in East, Blackwater, and Pensacola
Bays were generally less than the 0.360 mg/1 standard. On the
basis of this standard, there was enough nitrogen in Escambia Bay
during virtually all of the 1974 study period to theoretically
deplete dissolved oxygen concentrations below the Florida Water
Quality Standard specification of 4.0 mg/1.
The mean 'total nitrogen to total phosphorus ratios for the
components of the Pensacola Bay system during the study period
January through September 1974 are listed below:
8-12
-------
Escambia
Pensacola 10.5: 1
East 18.5:1
Blackwater 14.6:1
These ratios are all considerably higher than the 7.25:1
ratio in the open ocean. According to these data, more than half
of the time the limiting nutrient for phytoplankton in the
Pensacola Bay system appears to be phosphorus, since nitrogen is
usually available in sufficient amounts for biological
utilization, and little soluble phosphorus was found in the
Pensacola Bay system during the study period. Phosphate is
utilized by microorganisms in the soluble form (USEPA, 1971) .
Mean nitrate-nitrite concentrations in the Pensacola Bay
system during January - September, 1974 decreased in a seaward
direction from Escambia River to lower Pensacola Bay (Figure 8-
5). Nitrate-nitrite was the only nitrogen parameter that showed
this upper to lower bay pattern.
There were some localized elevations in nitrogen
concentrations near waste outfalls in the Pensacola Bay system
during the study period. These occurred in northeast Escambia
Bay (Stations EEDR and EGLY) near the Main Street outfall
(Station PO7) and near Bayou Texar (Station P11) (Figures 8-5
through 8-7). Organic nitrogen, ammonia, and nitrate-nitrite
concentrations were affected.
A comparison of mean concentrations in components of the
Pensacola Bay system during January through September 1974 showed
that Pensacola, East, and Blackwater Bays had virtually identical
nitrogen concentrations with the exception of one value. This
exception was nitrate-nitrite in Blackwater Bay (Table 8-7), and
this undoubtedly reflects tributary influence. Using a 't'-test,
concentrations of all types of nitrogen were significantly higher
in Escambia Bay than in Pensacola Bay with 99 percent confidence,
as shown below:
NOa-NOg-N NHa-N Orq. N.
t df t df t df
3.6 22 2.8 24 6.3 27 6.9 22
The major portion of nitrogen in the Pensacola Bay system in
1974 was organic nitrogen. The other nitrogen forms were
relatively insignificant compared with organic nitrogen.
8-13
-------
Table 8-6. Mean nitrogen concentrations in the conponents of the Pensacola Bay system durinq January
throuqh September, 1970 (Pensacola Bay data from the Oniversity of Wast Florida).
00
Escanbia Bay
Date
V23/7U
2/12/7U
3/05/70
3/2 7/7 0
O/ 16/7 «
5/07/714
5/29/7U
6/18/7U
7/09/7U
7/30/70
8/2; /7U
9/11/70
?lo»
( m3 /sec
U55
1070
338
3146
696
183
265
182
126
130
230
1115
Total
Nitrogen
) (nq/D
0.5U9
C. 507
O.UI4U
C. 399
• C.uoo
C.551
C.020
0. 167
0.366
0. 307
C.395
0.517
Nitrate-
Nitrite
(mg/1)
0.085
0.095
0.127
0 . r. 70
0.093
O.C58
0.038
0.030
O.T2C
o.r 16
0.008
r.C56
Ammonia
(mq/1)
0.112
0.076
0.002
1.062
o.oae
0.030
0.023
0.1U7
0.023
0. 020
f\075
0. 19ft
Organic
Nitrogen
(mq/1)
0.352
0.376
0.275
0.267
0.261
0.063
0.359
C.086
0.323
r.307
0.272
0.263
Total
Nitrogen
(Bg/1)
C.007
0.360
0.280
0.278
0.315
0.617
0.200
0.100
0.203
0.133
0.207
1.305
Blacknater Bay
Date
1/23/70
2/12/70
3/05/7 U
3/27/70
0/16/70
5/C7/70
5/29/7 U
6/18/70
7/C9/7H
7/30/714
8/2 0/7 U
9/11/7«
Flow
( m 3 /sec
1455
1070
338
3U6
696
183
265
182
126
130
230
1115
Total
'litroqen
) (aiq/D
0.398
0.371
C. 229
0.3142
0.2711
0.391
0.229
0. 117
0,261
0.237
0.361
0.3C1
Nitrate-
Nitrite
(oq/i)
".C5h
O.C50
C.C91
0.0«0
0.067
C.03U
•1. 03U
0.038
0 . C 2 9
0.038
0.056
O.C36
Aumonia
(mq/l)
0.077
0.069
G. 015
0.052
0.077
0.010
0 . C 1 0
0.033
0.021
0.021
0.079
0.095
Organic
nitrogen
(mg/1)
0.265
0.252
0.123
0.250
0.130
0.303
0.181
. 0.006
0.211
". 178
0.226
0.170
Total
Nitrogen
(mq/1)
T.305
C.237
0.221
7.596
0.276
0.250
0.095
-
0.120
?. 167
0.179
1.280
East Bay
Nitrate-
Nitrite
(mg/D
0.028
0.053
0.055
0.025
0.030
0.011
0.010
0.010
0.010
O.C10
0.012
O.C21
Pensacola
Nitrate-
Nitrite
(mq/1)
0.020
0.06S
0.006
0.002
C.035
0.010
0.012
0.011
0.018
0.013
0.010
0.020
Ammonia
(mg/1)
0.055
0.056
0.038
0.036
0.080
0.036
0.010
D.027
0.015
0.010
0.060
D. 117
Bay
Aanonii
(ng/1)
0.001
0.067
3.022
0.073
0.111
0.022
0.026
-
0.010
0.027
D..016
0.092
Organic
Nitrogen
(ng/1)
0.320
1.251
0.191
fl . 2 1 7
0.205
0.570
0.220
0.067
0.218
0.163
0. 135
0. 167
Organic
Nitrogen
(mg/1)
C.280
0.105
0. 153
0.081
0. 130
0.222
0.057
C. 133
0.092
0.127
0. 153
0.168
-------
\
t
Figure 8-5. Mean nitrate-nitrite nitrogen (mg/l-N) . in the
Pensacola Bay system during January through September, 197U.
(Pensacola Bay data from the University of West Florida) .
Figure 8-6. Mean ammonia (mg/l-N) in the Pensacola Bay system
during January through September, 1974 (Pensacola Bay data
from the University of West Florida).
8-15
-------
Figure 8-7. Mean organic nitrogen (mg/l-N) in the Pensacola Bay
system during January to September, 1974 (Pensacola Bay data
from the University of West Florida).
8-16
-------
Air Products and Chimicol Inc.
Amir icon Cyonomid Co.
Fithvrmani Pi.
*fu/ot BofOu
i PI. Ponsocolo Bay
Figure 8-8. Predicted steady state total nitrogen concentrations
in pg/1 per 953 kg/day (2100 ppd) and 131U kg/day (2897 ppd)
discharged by American Cyanamid Co. and Air Products and
Chemicals, Inc., respectively.
8-17
-------
table 8-7. Mean nitrogen concentrations in components of the Pensacol'a Bay system
during January to September, 197U (Pensacola Bay data from the University of,West
Florida) . , . i .
Eay
Escambia
Pensacola
East
Blackwater
nitrate-nitrite
(mg/1)
0.062
0.025 •
0.023
0.0«7
ammonia organic -nitrogen
(aig/1) (mg/D
0.066
O.OU5
O.CU5
O.OU7
, .0.30C
0.209
0.228
0. 198
total nitrogen
(rag/1).
0.«28
0.279
0.296
0.292
The models for the distribution of wastes from Air Products
and Chemicals and American Cyanamid plants (See Chapter .6) were
used to determine the relationship between actual and predicted
concentrations. Predicted total nitrogen concentrations in \ij/\
per 953 kg/day (2100 Ib/day) and 1314 kg/day (2897 .Ib/day)
discharged by Air Products and American Cyanamid plants,
respectively, (interim NPDES limits) are presented in Figure 8-8.
The wastes remain relatively concentrated in the upper northeast
portion of the bay. The highest concentrations occur near Air
Products and Chemicals Plant discharge as was expected since
.wastes from American Cyanamid plant also concentrate in this
area. Significant quantities of the nitrogen, 47 and 14 M3/1/
reach the north and south inlets of Mulatto Bayou, respectively.
The nitrogen isopleths indicate that portions of the wastewater
move seaward along the eastern shore of Escambia Bay and are well
diluted when they reach the mouth of Indian Bayou. The
concentrations predicted here do not represent critical
conditions because of high river discharges during the American
Cyanamid Dye Study.
The relationship between the predicted surface steady state
total nitrogen concentrations due to discharges from Air Products
and Chemicals, Inc., and American Cyanamid Co., (Interim NPDES
limits) and actual average values measured in the bay during
August, and September, 1974 are shown in Table 8-8. The
discharge accounted for a significant percent of the total
nitrogen in upper Escambia Bay, and 8, 23 and 29 percent of the
total nitrogen concentrations near the mouth of the Little White
River (Station EEIX), the center of the upper portion of the bay
(Station EEKV), and Fishermans Point (Station EGLY),
respectively, appeared to be due to the waste discharges. Three
percent of the concentrations at both the channel, near Marker
"18" (Station EIKC), and in Macky Bay (Station EIIL) appeared due
8-18
-------
to these waste discharges. At the channel near the Interstate 10
bridge, one percent of the total nitrogen concentration appeared
due to these waste discharges.
A. .comparison of nitrogen data from Choctawhatchee Bay sampled
on September 12, 1974 and the pooled average of Pensacola Bay
nitrogen data from March through August 1974 showed that
Choctawhatchee Bay had low nitrogen concentrations and Escambia
Bay had the highest concentrations for all nitrogen species, (see
listing below and Figures 8-9 through 8-12).
NH3-N
N03-N02-N Org. N. Total N.
Bay
Choctawhatchee
Escambia
East
Blackwater
Pensacola
The mean total nitrogen concentration in Choctawhatchee Bay
was significantly less than in Escambia Bay, but was about the
same in the rest of the Pensacola Bay system. Choctawhatchee Bay
0.016
O.OU6
0.035
0.036
0.03U
mgx
0.050
0.056
0.019
0.048
0.022
• j.-—
0.19
0.29
0.22
0.19
0.22
0.256
0.392
0.27U
0.27U
0.276
Table 8-8. Predicted percent of actual surface total Ditrogen concentrations
due to Air Products and Chemical Inc. and American Cyanamid Co.
Surface Total Nitrogen concentration (jig/1)
Station
EEIX
EEKV
EGLY
EIKC
EIIL
EKHP
Mean actual
August - September, 197U
233
A 325
3U4
353
299
318
Predicted based on
Interim NPDES Limits
18
7U
100
12
9
2
Percent of
Actual
8
23
29
3
3
1
8-19
-------
Figure 8-9. Ammonia (mg/l-N) in Choctawhatchee Bay on September
12, 1974. '
Figure 8-10. Nitrate-nitrite (mg/l-N) in Choctawhatchee
September 12, 197U.
Bay on
8-20
-------
Figure 8-11. Organic Nitrogen (mg/l-N) in Choctawhatchee Bay on
September 12, 197a.
Figure 8-12. Total nitrogen
September 12, 1974.
(mg/l-N) in Choctawhatchee Bay on
8-21
-------
had a mean total nitrogen concentration of 0.256 mg/1, which was
well below the maximum of 0.360 mg/1 recommended in Water Quality
Criteria (1972) .
Total nitrogen concentrations in Escambia and East Bays
during the August 1973 low flow diel (24-hour) water quality
surveys were noticeably higher than concentrations during the
April high flow surveys. This probably reflects higher
biological productivity in summer, rather than flow conditions.
Mean total nitrogen concentrations in Pensacola Bay remained
essentially the same in April and August. All mean total
nitrogen concentrations during the August low flow surveys, and
most concentrations during the high flow surveys, exceeded the
0.360 mg/1 standard (Table 8-9) .
During the September 1969 survey (USDI, 1970), concentrations
of ammonia and nitrate-nitrite in Escambia Bay were the major
portion of the total nitrogen (Table 8-10 and Figures 8-13
through 8-15). At Station E7f near Air Products and American
Cyanamid Plant outfalls, there were elevated surface and bottom
mean ammonia and nitrate-nitrite concentrations. Upper Escambia
Bay data from the 1969 water quality survey were compared to the
corresponding data from 1973 and 1974 studies (Table 8-10). The
stations considered were E1, E3, E7, E9, E10, E13, E18 and E20
during 1969; and EEIX, EEKV, EEIL, EKLQ, EIKC, EKMP, and EGLY
during 1973 and 1974. The data in Table 8-10 show that all
nitrogen parameters have decreased since 1969 except for organic
nitrogen, xwnich remained about the same (The 1974 values used for
comparison .were the May-August means) . Mean total nitrogen
concentrations^ for the stations considered in Summer, 1974 were
just about one-half of what they were in September 1969. Ammonia
and nitrate-nitrite decreased by even larger percentages. Based
on these limited data, water quality in Escambia Bay as it
relates to nitrogen has improved considerably in five years, even
though total nitrogen in 1974 still exceeded the 0.360 mg/1
standard recommended by Water Quality Criteria. A summary of the
1974 nitrogen data by station is presented in Appendices 8-8
through 18-11.'- \
Phosphorus
Introduction
Phosphorus is important in considering water quality due to
its role in aquatic productivity. In excessive amounts it is
associated with algal blooms which are the cause of much water
quality degradation. Phosphorus compounds in the aquatic
environment almost always occur in the oxidized state. Three
forms occur most frequently: orthophosphate (H2P04, HP04, and
PO4), polyphosphate (P2O7, P3O9, P3OIO)» and organic phosphorus.
Organic phosphorus, which also occurs almost exclusively in the
oxidized state, is combined with organic molecules in the cell
biomass of plants and animals. Phosphorus is usually in an
8-22
-------
Table 8-9. Bean Nitrogen concentrations in components ot the Pensacola Bay system during 1373 diel
water quality surveys.
Escambia Bay
Date
April i
April ,
August
August
Tide
Equatorial
Tropic
Equatorial -
Tropic
Nitrate-
Ammonia Nitrite
(mq/1) (mg/1)
A
.E
A
E
A
.' . E
A
E .
O.C61
0.059,
0.057
0.061
0.035
0. 138
0.019'
0. 120
o.
C.
0.
C.
0.
0.
0 O
071
069
122
117
092
057
017
030 .
A mmonia
(ag/1)
0.311
0.051
0.028
0.015
0.3 10
0.128
0.010
0.150
Escambia Bay
Cate
April
April
August
August
Tide
Equatorial
Tropic
Equatorial
Tropic
Table 8 - IT. Comparison
quality survey and the
Date
Organic Total
Nitrogen Nitrogen
(mg/1) (mg/1)
A
E
A
E
A
E
.A
E
ot mean
stud ies
0.237
0. 168
0.363
0.395
0.512
0.177
0.183
0.180
o .
6.
c.
0.
0.
0.
0.
o.
375
296
512
573
639
672
519
630
nitrogen concentrations in
in '1973 and 1971.
Upan
ni trate-ni trite
concentration
(mq/1)
September 23-25, 1969
Auqust 23-25,
nay 5, 1971
June 18, 1371
1973
Auqust 2~, 1971
Summer 1971*
Date
September 23-
Auqust 23-25,
Bay 5, 1971
June 18, 1971
0 . 11 C
T.083
0..-99
?.082
0 . C 7 3
'•.017
..lean
ammonia
concentration
(mq/1)
25, 1969 '
1973
C.290
"'.11?
• . <• u 7
r ."66
Auqust 2r., 1971 C.GSr
Su nmer 1 97u *
•"'.06U
Change in
mean from
1969
•"<*>
- 11.
- 29.
- 13.
- 50.
- 66.
Ammonia
Change in
mean from
>1969
• '-'
- 62. '
- 81.
- 77.
- 72.
- 78
Organic
Nitrogen
(mg/1)
0. 195
0. 191
0. 171
0.257
0.111
0.157
3.188 '
0.513
East Bay
Nitrate-
Nitrite
(mg/1)
0.061
0.061
0.035
0.030
'0.010
- 0-.010
0.010
. . .• 0.022
East Bay
..Total
Nitrogen
(og/1)
0.303
0.309
0.237
0.332
0.131
• ,0.595
'••'-•"0.508 '
0.685
Pensacola Bay
Ammonia
(mg/1)
D.095
3.C39
3.C12
0.011
3. 151
3.C13
. , 0.063
Nitrate-
Nitrite
(mq/1)
0.058
0.037
0.017
0.021
0.010
C.012
C.G10
C.011
Pensacola Bay
Organic
Nitrogen
(mg/1)
C.253
C.268
3.395
0.155
0.173
3.287 , .
0.382
3.307 ' .
upper Escambia Bay between the September,
Percent of
1969 flow
-
92
86
95
111
89
.
.
.
.
Percent of
1969 flow
.' ' '
92
86
95
1 1 1
89
.
•
•
Mean
organic nitrogen
concentration
(nq/1)
0.280
0.180
0.160
0.08C
0.190
n.270
.Mean
total nitrogen
. concentration
(mg/1)
0.710
0.670
0.606
C.228
'••.313
^.392
Organic Nitrogen
Chanqe in
mean from
1969
<*)
.
* 71
* 61.
- 71 .
- 32.
- ' 1.
Total Hitroqen
Chanqe in
mean from
1969
(M
-
- 6.
- 11.
- 68.
- 52.
- 15.
Total
Nitrogen
(mq/l)
0.369
0.1C9
0.181
0.518
0.191
.0.150
G.10-2 '
0.381, '
1969 water
Percent of
1969 flow
;'.-. ;
92.
86. "
95.
111.
89. Y
\
\
Percent of
1969 flow
(*)
-
92.
86.
95.
111.
89.
for studies performed duriny May throuqh August 197U.
8-23
-------
CD
I
Figure 8—13. Mean ammonia In Escambla
Bay during September 23 to September
25, 1969.
Figure 8-14. Mean nitrate-nitrite < mg/l-
N) in Escambia Bay during September
23 to September 25f 1969*
-------
Miles
Fishermons Pt.
Mulat Bayou
(Gull Pt.) Devils Pt
Red Bluff
1-5 Surface Value
2.3 Bottom Value
Figure 8-15. Mean organic nitrogen (mg/l-N)
during September 23 to September 25, 1969.
in Escanbia Bay
8-25
-------
insoluble form in an estuarine environment where there is a
significant amount of biological productivity. This is due to
three factors-: much soluble phosphate is taken up into cell mass
and so is kept out of solution; phosphate is readily adsorbed
onto insoluble residues in the water; and the pH is in the range
(slightly basic) in which phosphate combines with ' multivalent
cations to form insoluble precipitates. ' .
i ' ' , , '
Phosphorus in significant quantities can enter the aquatic
environment from the atmosphere as a result of precipitation or
"dry fallout". This problem was not evaluated during the study.
Florida Department of Environmental Regulation (FDER)
criteria do not give specific limits for phosphorus in estuaries.
The recommendation in Water Quality Criteria (1972) is that 0.05
mg/1 total phosphorus should be considered the upper limit for a
marine ecosystem. This reference standard is discussed further
in the nitrogen section.
A. criterion for assessing phosphorus concentrations is the
nitrogen to phosphorus ratio, which relates total phosphorus to
total nitrogen. It is discussed in detail in the nitrogen
section.
Results and Discussion
Mean dissolved orthophosphorus concentrations were negligible
throughout the Pensacola Bay system during the 1974 study period
(Figure 8-16) . Mean orthophosphorus concentrations in; Escambia
Bay generally decreased in a seaward direction (Figure 8-17).
Mean total phosphorus concentrations in Escambia Bay decreased in
a seaward direction on the eastern side of the bay, and remained
relatively constant on the western side (Figure 8-18) .
Phosphorus concentrations in the Pensacola Bay system during
January - September 1974 varied relatively little among bays
(Table 8-11). All of the total phosphorus concentrations except
during the April 16 and July 9, 1974 surveys were well within the
0.05 mg/1 recommended WQC standard (Table 8-12).
A comparison of September 12, 1974 Choctawhatchee Bay total
phosphorus data with Pensacola Bay system total phosphorus data
from March - August 1974 showed little variation among bays.
Orthophosphorus concentrations were identical for all bays. The
data are listed below:
Total Ortho-
Phosphorus Phosphorus
Choctawhatchee 0.030 0.013
Escambia 0.028 0.016
Pensacola 0.030 -----
East 0.018 0.012
Blackwater 0.021 0.013
8-26
-------
Figure 8-16. Mean dissolved orthophosphorus (mg/l-P) in the
Pensacola Bay system during January through September, 1974
(Pensacola Bay data from the University of West Florida).
f
Figure 8-17. Mean orthophosphorus (mg/l-P) in the Pensacola Bay
system during January through September, 1974.
8-27
-------
Figure 8-18. Mean total phosphorus (mg/l-P) in the Pensacola Bay
system during January through September, 1974. (Pensacola
Bay data from the University of West Florida).
8-28
-------
Table 8 - 11. Mean total and orthophosphorus concentrations
in the components of the Pensacola 3ay system during
January through September, 1974 (Pensacola Bay data from
the University ot West Florida).
Eay
Escambia Bay
Fensacola Bay
East 3ay
Blackwater Bay
Total
Phosphorus
(ing/1)
Ortho-
Phosphorus
(mg/i)
C.028
0.026
0.016
0.020
0.018
-
0.011
0.014
Table d - 12. ttean total phosphorus (T-P) and orthopbosphorus (3-P) concentrations in the Pensacola
8ay system during January through September,1974 (Pensacola Day data from the University of Best Florida),
Date
1/2 3/7 u
2/12/7 U
3/C 5/7i|
3/27/74
-1/16/74
5/07/74
5/2 9/7i4
6/18/74
7/09/714
7/30/714
8/20/714
9/1 1/7 «
Effective
Flow*
( m 3 /sec )
it55
1070
33 1)
31*6
696
183
265
182
126
13:
2314
1115
Escdmbia
0-P
(ng/1)
C
c
C
c
0
c
c
0
c
0
c
c
.0114
.C37
.019
.011
.019
.017
.013
.018
.017
.019
.014
.024
T-P
(Dig/I)
0.020
0.023
0.035
C.013
0.026
0.020
0. 327
0.122
O.T30
0.333
0.332
o.ouit
Zast
0-P
(oy/1)
0.011
0.011
0.018
•5.011
0.012
0.011
3.010
0.012
0.310
0.012
0.01 0
'3.01 0
T-P
(ng/1)
0.011
0.012
3.023
0.016
0.022
0.0.15
0.0 in
0.015
0.013
3 . 0 26
0.015
0.013
Blackvater
0-P
(as/I)
.1.011
0.02U
• 0.016
0.011 .
O.C-10
O.D16
D.OK
3.312
3. -01 i
0 . 0 1 U
3.012
0.318
T-P
(ng/1)
0.
0.
0.
0.
0.
0.
0.
0.
r\
0.
0.
0.
012
024
025
020
022
018
025
015
013
027
019
022
Pensacola
0-P T-P
(t.g/1) (mg/1)
0.
~ I •
0.
r
^ •
c.
c.
0.
0.
0.
0.
r
\, •
0.
020
C15
310
335
054
C2C
023
030
358
023
017
023
* Total effective flo» into the Pensacola Bay system.
8-29
-------
Figure 8-19. Dissolved orthophosphorus
Choctawhatchee Bay on September 12, 1971.
(mg/l-P) in
Figure 8-20. Total phosphorus (mg/l-P)
September 12, 197U.
in Choctawhatchee Bay on
8-30
-------
Figure 8-21. Orthophosphorus (mg/l-P) in Choctawhatchee Bay on
September 12, 197a.
-------
Dissolved orthophosphorus concentrations were negligible (Figure
8-19) . Phosphorus concentrations in Choctawhatchee Bay generally
were greater on the eastern, freshwater end (Figures 8-20 and 8-
21). This again reflects the influence of freshwater sources.
All concentrations were well below the 0.05 mg/1 recommended WQC
standard.
Mean total and orthophosphorus concentrations in the
Pensacola Bay system were higher during the 1973 high flow diel
surveys than during the low flow surveys (Table 8-13). Mean
total phosphorus concentrations in Escambia Bay during Survey II
exceeded the 0.05 mg/1 standard.
Mean phosphorus data from the 1969 water quality study (USDI,
1970), showed elevated concentrations near industrial discharges
in northeast Escambia Bay (Figures 8-22 and 8-23). Phosphorus
concentrations in upper Escambia Bay from the 1969 survey were
compared to the corresponding data from 1973 and 1974. The
stations considered were E1, E3, E7, E9, E10, E13, E18, and E20
in 1969; and EEIX, EEKV, EIIL, EKLQ, EIKC, EKMP, and EGLY in 1973
and 1974. Mean concentrations for various periods are listed in
Table 8-14. The concentrations of orthophosphorus dropped by 50
percent between 1969 and 1971 while total phosphorus
concentrations decreased by 75 percent. These decreases brought
phosphorus concentrations under the 0.05 mg/1 standard in 1971.
The indication of these limited data is that phosphorus
concentrations in Escambia Bay have decreased since 1969. A
summary of the phosphorus data by stations is given for January
through September 1974 in Appendices 8-12 through 8-14.
Principal Nutrient Index
Introduction
To evaluate water quality in an estuary like Escambia Bay, a
massive data base for numerous parameters is required to describe
natural and induced variation in the system, and to understand
conditions in the bay relative to other bays. Evaluation can be
simplified by combining water quality parameters in such a manner
that a standardized distance from a control or an index can be
calculated. Harkins (1974) suggested the use of a nonparametric
classification procedure to compute an index.
8-32
-------
Table 3 - 13. tiaan total and orthophosphorus concentrations in components of tae
L'ensacold Bay system during the 1973 diel wator quality surveys.
00
I
Ul
Co
Survey
I
II
III
IV
Survey
April
I
III
IV
Tide
Equatorial
Tropic
Equator ial
Tropic
Ti j«
Equatorial
Tropic
Equatorial
Tropic
Depth
A
T?
A
E
A
p
A
E
Depth
A
E
A
E:
A
T?
A
Sscaubia
0.050
o.oua
0.061
0.063
C . 0 3 1
0.038
O.C17
0.035
F.scambia
O.OU2
O.OU2
O.OU2
O.OU3
0.013
0.018
0.011
0.021
Total Phosphorus
Bay East Bay
0.017
0.017
0.035
0.036
O.Oli*
0.030
0.012
0.033
Ortho Phosphorus
Bay East Bay
0.020
0.024
0.021
0.030
•'.' 0.008
0.015
0.013
0.016
(mg/1)
Pensacola Bay
0.024
0.015 -.
0.039
0.025
0.019
0.027
0.016
0.020
(ing/1)
Pensacola Bay
0.032
0.015
0.021
0.012
0.010
0.019
0.010
0.'012
-------
CO
I
Figure 8—22. Mean total phosphorus (me/I—P)
In Escambla Bay during September
23 to September 25, 1969.
Figure 8—23* Mean orthophosphorus (mg/l-
P) In Escambla Bay during September
23 to September 25* 1969.
-------
Table 8 - 14. Comparison of mean total and orthophospborus concentrations in upper Escambia
Bay between September, 1969 water quality surveys and the surveys in 1973 and 1971.
Date
September 23-25, 1969
August 23-25, 1973
Hay 5, 197«
June 18, 197«t
August. 20, 197«
Summer 197U
Date
September 23-25, 1969
August 23-25, 1973
Nay 5, 197«
June 18, 197<»
August 20, 197H
Summer 197U*
Mean
total phosphorus
concentration
(mg/1)
0.08
0.03
l.?2
0.02
0.03
0.02
Mean
ortho phosphorus
concentration
(mg/1)
o.ou
0.02
0.02
0.02
0.01
0.02
Total Phosphorus
Change in
mean from
1969
(*)
-
- 63.
- 75.
- 75.
- 63.
- 75.
Ortho Phosphorus
Change in
mean .from
1969
(*)
-
- 50.
- 50.
- 50.
- 75.
- 50.
Percent of
1969 flow
(%}
'
92.
86.
95.
1 11.
89.
Percent of
1969 flow
(X)
-
92.
86.
95.
111.
89.
* Mean for studies performed during nay through August 1971.
8-35
-------
Using Harkin's method, the Principal Nutrient Index (PNI) was
calculated from Escambia Bay Recovery Study data, University of
West Florida Sea Grant data, and data from other Gulf Coast
estuaries. Total organic carbon, total nitrogen, and total
phosphorus were used as parameters in the PNI because high levels
of these substances are an indication of possible enrichment.
Because the total concentration of each nutrient was used,
dissolved and particulate components of each parameter are
included in the index.
The index is advantageous because it simplifies evaluating
carbon, nitrogen, and phosphorus concentrations by combining them
into one value that can be compared to a water quality standard
(see Methods) and used as a water resources management tool.
High values of the index indicate high concentrations of one or
all of the parameters. Even though only one of the parameters
has high concentrations, unacceptable water quality may still
exist. Use of the index does not eliminate the need to evaluate
the individual parameters in detailed water quality studies.
Method
The first step in the calculation of PNI was to assign a
control value to each parameter. A control value of zero for
each parameter was used in this analysis. The next step was to
assign a rank by.ascending order to each value by parameter,
including the control value. Tied ranks within a given parameter
were split by assigning each replicate value the mean rank of
that group. The rank variance for each parameter was obtained
using the following equation:
Variance ( R. ) =
n3 -n)-
.CD
where
J
where
n
P
k
t
= 1,2.
= 1,2,
12n
»P
tk
= the number of observationst including controlst
= the number of parameters used*
= the number of groups of tiest
= the number of observations in the Jth group of ties*
PNI =
(Ri-Rc)2 / Variance (Bt ))
(2)
8-36
-------
where
R. = the rank of the observation
8 = the rank of the control
All other notation is the same as above. The minimum value of
PNI possible is zero and the maximum value is p times 12 which
was 36 .for this analysis.
The values of PNI calculated using the method described above
are initial values. Their data base is presented in-Appendix 8-
15.
The method used to calculate the initial PNI values limits
the use of PNI as a water quality index because, for a given
sample, the PNI value will change when the data base is altered.
This problem can be eliminated by developing a multiple
regression model of the initial PNI values. Since the data base
used in calculating the initial PNI values consisted of 3574 sets
of data from various Gulf Coast estuaries and rivers with varying
water qualities, the multiple regression model can be used to
calculate an index value for any set of data. The equation for
the model is:
PNI = 20.601 + 3.995 (Ln P) + 6.062 (Ln C) + 3.451 (Ln N) 3
with the limits
If PNI < 0.0 then PNI =0.0
If PNI > 36.0 then PNI = 36.0
where PNI = Principal Nutrient Index value
P = total phosphorus concentration - mg/1 as P
C = total organic carbon concentration - mg/1 as C
N = total nitrogen concentration - mg/1 as N
The multiple correlation coefficient for the model *as 0.88,
indicating it provided a good fit of the data. The standard
partial regression coefficients were 0.49, 0.45, and 0.38 for
total phosphorus, total nitrogen, and total organic carbon,
respectively, indicating each parameter has about the same
influence on PNI. In addition, for the data base described in
Appendix 8-15, the cumulative frequency distributions for the
initial PNI values and for values of PNI calculated from Equation
'3 were quite similar (Figure 8-24).
A PNI value representing a maximum allowable standard for
acceptable water quality has been developed using values
8-37
-------
00
I
CO
00
35 n
30 •
25-
20 -
z
d.
15 -
10 -
5 -
CALCULATEOi
(INITIAL
10 20 30 40
50
60
70
80 90
I
100
CUMULATIVE PERCENT
Figure &-2U. Cumulative frequency distribution of initial PNI
values and PNI values calculated from multiple regression
model.
-------
suggested and the method used in Water Quality Criteria (1972).
The Criteria recommend that available nitrogen and phosphorus in
waste discharges should not increase the total nitrogen and
phosphorus concentrations in the receiving waters above 0.36 and
0.05 mg/1, respectively, to avoid exhausting the oxygen content
of the water during critical conditions. The nitrogen and
phosphorus values presented above were derived from the work of
Redfield,. et al., (1963), who gave the following ratios as
characteristics of the principal elements present in living
marine plankton and the stoichoimetric relationship between these
elements and oxygen.
0: C: N: P:
276: 106: 16: ' 1. by atoms or
138r 40: 7.25: 1 by weight.
Based on the ratio above, the recommended carbon value was
estimated to be 2.0 mg/1 of total organic carbon.
Although the above concentrations are recommended for
critical conditions, in reality, they are too high to be used as
a maximum standard. These concentrations could produce enough
organic material to reduce the dissolved oxygen concentration in
the receiving waters to below the minimum standard of 1.0 mg/1
during any flow and temperature conditions. Nevertheless,
concentrations of 0.05 mg/1 of total phosphorus, 0.36 mg/1 of
total nitrogen, and 2.0 mg/i of total organic carbon were used to
determine a standard PNI value; however, it should be understood
that this value is high and- problems could occur at lower PNI
values. The standard PNI value calculated using Equation 3 was
9.3; to simplify matters, a PNI value of 9.0 will be used as a
standard to distinguish between excessive nutrient enrichment and
acceptable aquatic conditions with respect to nutrients.
Results and Discussion
Mean PNI values in Escambia Bay during September 23 through
September 25, 1969 were generally much greater than the 9.0
standard (Figure 8-25). Mean surface values in northeast
Escambia Bay (Stations E3 and1 E7) were higher than mean surface
values at the mouth of the river. This appears due to the
industrial discharges located in the northeast area of the bay.
The PNI values in the Pensacola Bay system during diel (21-
hour) studies in April and August 1973 generally indicated
Escambia Bay was the most nutrient-enriched component of the
system (Table 8-15). Pensacola and East Bays had similar mean
PNI values and were less nutrient-enriched than Escambia Bay.
Mean surface and bottom PNI values in Escambia Bay daring the
high river inflow studies (I and II) were greater than values in
the Escambia River (Station ER10), which tends to indicate
resuspension of material from the sediments. During the low flow
studies (III and IV), mean surface values in Escambia Bay were
generally lower than mean values in the Escambia River (Station
8-39
-------
Fishermans Pt.
Mulaf Bayou
(Gull Pt.) Devils Pt.
Red Bluff
5.2 Surface Value
3.7 Bottom Value
Figure 8-25. Mean surface and bottom PNI values for samples
collected during September 23 to September 25, 1969 (USDI,
1970) .
8-40
-------
Table 8-15. Heau PHI values froa pooled data for the Pensacola bay system daring studies
in April (I and II) and August (III and IV).,Number of observations ace in parentheses.
Studies
Bay
Escambia Bay
Surface
Bottom
East Bay
Surface
00
I Bottom
Pensacola
Surface
Bottom
Escambia River
Surface
Bottom
I
18.4
(37)
21.0
(31)
11.8
(ID
15.3
(12)
11.6
(21)
15.H
(21)
15.1
(3)
20.9
(<•)
II
22.9
(44)
26. 2
("KM
13.9
(11)
18. 4
(12)
16.6
(24)
1 9. 1
(24)
19. 1
CO
22.8
CO
III
18.0
(55)
18.0
(52)
9.8
(12)
1U.9
(12)
13.2
(24)
10.0
(24)
19.4
I")
21.3
(3)
IV
10.8
(58)
17.1
(60)
6.5
(12)
15.3
(12)
6.6
(24)
5.7
(24)
13.7
0»)
14.0
(<»)
-------
ER10), depicting normal dilution of river inflow by tidal mixing.
In addition, mean bottom PNI values in Escambia and East Bays
were higher than values in Escambia River inflow, again
indicating resuspension of material from the sediments. Only
mean surface values in East Bay and mean surface and bottom
values in Pensacola Bay, during Study IV, were less than the 9.0
PNI standard.
The PNI values in the Escambia River (Station ER10) were
highly correlated to the effective discharge of the Escambia
River during January through September 1974 (r = 0.71, df = 11, p
<0.05). Thus, high PNI values occurred when river discharge was
high and lower values occurred during low flow periods (Figure 8-
26) .
The mean PNI value for each bay of the Pensacola Bay system
during each 1974 sampling date followed the trend of river
discharge (Figure 8-27). High river discharges in the spring
caused high mean PNI values in the bays, and conversely, low
river discharges caused low PNI values in the bays.
Mean PNI values in Escambia Bay during the 19.74 studies
generally decreased in a seaward direction (Figure 8-28). There
was no increase in PNI downstream of the Monsanto Corporation
Plant discharge. In the northeast area of the bay, (Stations
EEKV and EGLY) the mean PNI values were about 13 percent higher
than values near the mouth of the river, indicating enrichment
due to waste discharges in this area. Mean PNI values in Mulatto
Bayou were higher than those in Escambia Bay, indicating
enrichment in the bayou.
Mean surface and bottom PNI values were similar throughout
Blackwater and East Bays and no pattern was evident (Figure 8-
28) .
In Pensacola Bay, the highest surface mean PNI value occurred
near the outfall of the Main Street STP (Station P07) (Figure 8-
28). In fact, surface PNI values during all 1974 studies were
highest at this location. Mean PNI values generally decreased in
a seaward direction. The surface mean value near the Pensacola
Beach bridge (Station P04) was considerably higher than the value
at the nearest station in Pensacola Bay (P03). This was probably
due to discharges from the Gulf Breeze and Pensacola Beach Sewage
Treatment Plants, which are located near the bridge.,
No pattern of PNI values was observed during the water
quality study performed in Choctawhatchee Bay on September 12,
1974 (Figure 8-29) . The estimated effective discharge ,. of the
Choctawhatchee, River , was about :120 m3/sec (4,223 cfs) , -or about
61 percent of the mean annual flow of 198 m3/sec (6,981 cfs)
during the study.
The water quality of the Pensacola Bay system was evaluated
by comparing the PNI values to the standard value of 9.0 (Table
8-42
-------
3° "I STATION E R 10
25-
20-
u
3
10
. 5-
A SURFACE VALUE
BOTTOM VALUE
FLOW
JAN FEB MAR APR MAY
1974
JUN ' JUL AUG SEP
790
-300
-230
o
-i
u.
Figure 8-26. PNI values at Station ER10 during the 1971 water
quality studies.
1000 -i
f 500 -
* 250 -
o
UJ
5
20-,
I 5-
10 -
5-
Eicombla Bay
Blockwattr Boy
JAN FEB MAR APR MAY JUN JUL AUG SEP
1974
Figure 8-27. Mean PNI values in the components of the Pensacola
Bay system during the 1974 water quality studies.
8-U3
-------
f
Figure 8-28. Mean PNI values in the Pensacola Bay system at
stations sampled during the 1974 water quality studies
(Pensacola Bay data from the University of West Florida).
Figure 8-29. Surface and bottom values of
Bay on September 12, 1974.
PNI in Choctawhatchee
8-44
-------
8-16). (The bays should only be compared within study periods -
columns on Table 8-16 - because sampling frequency and station
locations differed during the various study periods). During
September 1969, 91.0 percent of the PNI values were greater than
9.0, indicating nutrient enriched conditions in the bay. In
1973, about twice the percent of PNI values exceeded 9.0 in
Escambia Bay than in East Bay. The percent of PNI values that
exceeded 9.0 was greater in Pensacola Bay than in East Bay during
1973. Escambia Bay had PNI values during the 1974 studies that
exceeded 9.0 in more than 50 percent of the samples, indicating
that nutrient-enriched conditions existed more than half of the
time. Pensacola and Blackwater Bays had nutrient-enriched
conditions during slightly less than 25 percent of the sampling
times in 1974. East Bay had the least amount of nutrient
enrichment during January through September 1974. Values of PNI
in Choctawhatchee Bay indicated that the potential for problems
existed, since 28.7 percent of the samples exceeded a PNI value
of 9.0.
The water quality of the Pensacola Bay system and
Choctawhatchee Bay was also evaluated by comparing mean values
(Table 8-17). In order to reduce the fluctuation of PNI values
due to changing environmental conditions in the Pensacola Bay
system, all PNI data collected in the system from March through
August 1974 were pooled and compared to Choctawhatchee Bay PNI
data collected during September 1974. Statistical tests
indicated that the mean PNI values in Escambia and East Bays were
higher and lower, respectively, than the mean in Choctawhatchee
Bay, and that the hypothesis that the mean PNI values in
Blackwater and Pensacola Bays are equal to the mean value of PNI
in Choctawhatchee Bay cannot be rejected. It was assumed in this
analysis that the PNI values during September 1974 in
Choctawhatchee Bay were representative of summer PNI values.
Nutrient enrichment in Escambia Bay was greater than in
Choctawhatchee Bay, and nutrient enrichment in East Bay was less
than in Choctawhatchee Bay. The nutrient enrichment in
Blackwater and Pensacola Bays was not statistically different
from' that in Choctawhatchee Bay.
Values of PNI in upper Escambia Bay during a two-day diurnal
(24-hour) study in September 1969 were statistically compared to
values during 1973 and 1974 with comparable river inflows (Table
8-18) . Although the 1969 study period was limited, PNI values at
that time were always higher than those during the periods of
1973 and 1974. Thus, nutrient enrichment in Escambia Bay has
decreased between 1969 and 1974.
Gulf Coast estuaries outside the Pensacola Bay system were
included in the PNI data base in order to further evaluate the
water quality of the Pensacola Bay system. These estuaries were
Perdido Bay, Florida-Alabama, sampled during June 1972 (USEPA,
1972), and Bayou Casotte and Escatawpa River, Mississippi,
sampled in July 1972 (Environmental Protection Agency, Athens,
Georgia, unpublished data). The evaluation indicated that
8-45
-------
Table 3 - 16. Percent of PN1 va\lues greater than or equal to 9.0 for
the Pansacola Bay system and^Ghoctawhatchee Bay.
Eay
September 1969
Date
1973 (1) January to September 1974
Escambia 91.3
East
Blackwater
Pensacola
Choc taw hatches
81.4
43.8
-
62.4
-
53.
13.
24.
22.
28.
3
0
1
5
7
(2)
(1) Includes surface and bottom values during EBRS diel studies in
and August, 1973, and surface values tor UH?1 biweekly studies.
(2) Valuas from September 12, 1974 study.
Table 8 - 17. Statistical comparison of mean PNI values in the Pensacola Day
system during studies performed in Hay through August 1974, with "hoctawhatcLee
Day on September 12, 197U.
Eay
Choc
Escambia
East
Mean I'M I
whatchee 6.
ia 9.
14.
ater 5.
ola 5.
Value
3
a
6
3
6
Calculated t
-
U.83 (1)
2.17 (2)
0.97 (3)
0.9« (3)
Degrees of Freedom
-
356
125
90
221
(1) The hypothesis that the mean PNI in Escambia Bay is greater thau that in
Cho:tawhatchee Bay can be accepted with greater than 99 percent confidence.
(2) The hypothesis that the mean PHI in East Bay is less than that in 3hoctav-
hat:hee Bay can be accepted with greater than 95 percent confidence.
.(3) The hypothesis that the mean PNI value of the bays compared are equal can
not be rejected.
8-46
-------
table 8 - 13. Statistical comparison of mean PHI values ia upper ijscaobia Bay during September 1969
'and given dates in 1973 and 197U.
00
I
Eate (lean PHI
Value
September 23-25,1969 (3) 17.9
August 23-25,1973 (4) 1U.9 ;
. ' .flay 5, 1974 (4) 11.2
;' .June 18,19714 (
-------
Escambia Bay was considerably less nutrient-enriched than Bayou
Casotte and the Escatawpa River (Table 87.19) , 'two polluted
Mississippi estuaries. The comparison between Escambia and
Perdido Bays indicated that nutrient enrichment in these bays
during the periods compared was statistically equal.
OXYGEN RESOURCES
Dissolved Oxygen
Introduction
Of all the chemical substances in natural waters, oxygen is
one of the most significant as both a regulator of the metabolic
processes of communities and organisms, and as an indicator of
conditions (Reid, 1961). The dissolved oxygen concentration in
waters may be affected by a number of factors.
1. inflow of tributaries: Rivers discharging into Gulf
Coast Estuaries usually flow through swampy areas that
contribute water low in dissolved oxygen to the river,
and in addition, they receive discharges from subsurface
springs or seeps containing water low in dissolved
oxygen. These tend to dilute dissolved oxygen
concentration in the river before it enters the estuary.
2. Respiration of organics: Respiration of plants and
animals while oxidizing organic matter utilizes
dissolved oxygen. The organic material will be
allochthoribus (substances which originate outside of the
system such as waste discharges or swamp drainage), and
they will be autochthonous (substances originating in
the estuary such as organism biomass or recycled
material from the sediments) . The effects of
respiration are more conspicuous at night because they
are masked by photosynthesis during the day.
3. Inorganic Reactions: Inorganic activities such as
oxidation of iron may cause the loss of oxygen.
U. Photosynthesis: Phytoplankton and attached plants
contribute significantly to the oxygen content of an
estuary. Since sunlight is required for photosynthesis,
oxygen is produced in this manner during daylight hoars
causing diurnal variation in dissolved oxygen
concentrations. Large diurnal fluctuation is an
indication of poor conditions in the estuary.
5. Turbulance: Aeration of an estuary, an important source
of oxygen, is a function of turbulence which is caused
by tidal and river discharge currents and wind forces.
8-U8
-------
6. Temperature: The solubility of oxygen varies inversely
with temperature. Thus, raising the water temperature
could result in a loss of oxygen from the estuary. At
the same time, an increase in temperature should
increase the metabolic rates of the organisms within the
estuary. This will increase the rate of both
photosynthesis and respiration.
7. Salinity: The solubility of dissolved oxygen is also
inversely proportional to the salinity of the water.
Re sults
Pensacola Bay System - 1974
Mean surface dissolved oxygen levels during January through
September 1974 were usually near saturation at stations sampled
in the Pensacola Bay system. (Figure 8-30 and 8-31; Appendix 8-
16 and 8-17). The mean concentration in Escambia River water
entering the bay (Station ER10) was 6.9 mg/1 (77 percent of
saturation) and the mean deficit was 2.0 mg/1. Mean surface
concentrations near the Escambia River Delta (Stations EEIX,
EIKC, and EIIL) were slightly greater than 7.0 mg/1, or 80 to 100
percent of saturation. In the remainder of Escambia Bay, mean
surface concentrations were slightly greater than 8.0 mg/1, or
100 percent of saturation. Mean surface dissolved oxygen
concentrations in East and Blackwater Bays were at similar levels
to those in Escambia Bay.
Mean bottom dissolved oxygen concentrations, during January
through September 1971, were lower at deeper stations,. The mean
bottom concentration at a shallow station in upper Escambia Bay
(EEKV; mean sampling depth 1.1 m) was 5.7 mg/1 and the mean
concentration at a deep station in the lower bay (ETLQ; mean
sampling depth 4.0 m) was 3.4 mg/1. Mean bottom concentrations
in East and Blackwater Bays were again at similar levels to those
in Escambia Bay.
Mean surface dissolved oxygen concentrations in Escambia and
East Bays, pooled by bay for each survey during the 1974 study
period, steadily declined from near 9.0 mg/1 in February to about
6.0 mg/1 in September (Figure 8-32). Percent of dissolved oxygen
saturation for the same period actually increased slightly
(Figure 8-33), indicating that the reduction in mean surface
concentration was due to increased temperature and salinity.
Mean surface dissolved oxygen concentrations in Escambia and East
Bays during each study in 1974 were within one mg/1 of each other
and followed a similar trend throughout the year.
During each study, pooled mean bottom dissolved oxygen
concentrations were usually lower than surface concentrations.
Mean bottom dissolved oxygen concentrations were usually lower in
East Bay than in Escambia Bay during the studies performed from
8-49
-------
Figure 8-30. Mean dissolved oxygen concentrations (mg/1) in the
Pensacola Bay system during January through September, 1974.
Figure 8-31. Mean values of percent dissolved oxygen saturation
in the Pensacola Bay system during January through September,
1974.
8-50
-------
10.On
„. 8.0-
0.0
O
—• ESCAMBIA BAY SURFACE
—A ESCAMBIA BAY BOTTOM
-O EAST BAY SURFACE
-A EAST BAY BOTTOM
JAN FEB MAR APR MAY JUN JUL AUG SEP
Figure 8-32. Mean dissolved oxygen concentrations in Escambia
and East Bays during each study performed in January through
September, 1974.
I25-1
100-
I "'
OT
50-
u
O
25-
0--
ESCAMBIA BAY SURFACE
ESCAMBIA BAY BOTTOM
--© EAST BAY SURFACE
--A EAST BAY BOTTOM
JAN FEB MAR APR MAY JUN JUL AUG SEP
I 9 74
Figure 8-33. Mean values of percent dissolved oxygen saturation
in Escambia and East Bays during each study performed 4~
January through September, 197U.
in
8-51
-------
January through May 1974, and higher during all studies after May
1974 (Figure 8-32). Two periods of low bottom dissolved oxygen
concentrations occurred during the 1974 study period, one in
spring and one in late summer.
Surface dissolved oxygen concentrations were rarely less than
4.0 mg/1 (the minimum level allowable in Class II and III waters;
see Appendix 8-6) in Escambia and East Bays during the 1974
studies, and bottom concentrations were often below this level
(Table 8-20). No surface dissolved oxygen concentrations less
than 4.0 mg/1 occurred in East Bay and only 1.7 percent of the
surface concentrations in Escambia Bay were less than 400 mg/l0
In East and Escambia Bays, 31.7 and 31.2 percent of the bottom
dissolved oxygen measurements, respectively, were less than 4.0
mg/1. Of all the bottom dissolved oxygen samples with
concentrations less than 4.0 mg/1 collected from Escambia Bay
(31.2 percent of the total), 3.8 percent of the total were
collected from the bottom of the dredged channel at times when
the concentrations at the depth of the natural bottom were
greater than 4.0 mg/1. Thus, low dissolved oxygen concentrations
occurred throughout the bottom of the bay, and not just in the
dredged channel.
A chronological examination of dissolved oxygen
concentrations at selected stations indicated there was an
inverse correlation between dissolved oxygen and salinity (Figure
8-34). In the freshwater reach of the lower Escambia River
(Station ER10), dissolved oxygen concentrations were always above
5.2 mg/1. In central northeast Escambia Bay (Station EEKV; mean
sampling depth, 1.4 m), the bottom concentrations were only lower
than the 4.0 mg/1 minimum standard on three occasions. On the
other hand, near the American Cyanamid plant discharge (Station
EGLY, mean sampling depth, 2.0 m), bottom dissolved oxygen
concentrations were less than 4.0 mg/1 in seven of the eleven
samples collected. At the entrance to the Escambia Bay channel,
(Station ERPB; mean sampling depth, 3.2 m) the bottom dissolved
lable 8 - 20. Frequency distribution of dissolved oxygen concentrations in
Escambia and East Bays during January through September, 1971.
Bay Depth Number of Observations % less than U mg/1
East Bay Surface 60 0
Bottom 60 31.7
Escambia Bay Surface 240 1.7
Bottom 2UO 31.2
8-52
-------
1.0
I.I
-J—I—I—I—I I I I
0.0
10.0
10 o;
10.0 '
I •
1114
I I I
: io
1.0
2.0
0.0
MO
•
\
I
u.«.*.^.*^..
1114
I.I
11. 1
11. 1
00
yi
(JO
0.0
10.0
ib.o
0.0
10.0
>0.0
lint
» I J
19)4
Figure 8-34. Bottom dissolved oxygen and salinity levels during
January through September, 1974 at selected stations in the
Pensacola Bay system. (Pensacola Bay data from the
University of West Florida).
-------
oxygen concentration was only lower than 4.0 mg/1 in four of the
12 studies performed during 1974 as shown in Figure 8-34. At the
deepest station in lower Escambia Bay (ETLQ; mean sampling depth,
4.0 m) concentrations were below 4.0 mg/1 in eight of the 12
samples collected. Dissolved oxygen concentrations of less than
4.0 mg/1 occurred during late winter, early spring, and during
the entire summer.
University of west Florida (UWF) dissolved oxygen data from
Pensacola Bay were compared to Escambia Bay Recovery Study (EBRS)
data collected in East, Blackwater, and Escambia Bays. A Delta
Scientific dissolved oxygen probe was used for this analysis by
UWF while the EBRS used the modified Winkler titration method.
Dissolved oxygen concentrations at Stations ETLQ (EBRS) and P12
(UWF), which are 2.7 km (1.7 mi) apart, were strongly correlated
during the January 23 through May 29, 1974 studies (r = 0.96, df
= 12, p < 0.01). After this study date, there was no correlation
between data at the two stations. This indicated that the
dissolved oxygen probe was not operating properly after May 29,
197U. Bottom dissolved oxygen samples collected, between January
23, and May 29, 1974, at Station ETLQ in Escambia Bay and Station
P10 in Pensacola Bay, showed that the bottom dissolved oxygen
concentration at Station ETLQ was consistantly lower than those
at P10, indicating that a bottom water mass from Pensacola Bay
did not cause low dissolved oxygen concentrations in Escambia Bay
during the spring. Figure 8-34 depicts bottom dissolved oxygen
concentrations at Stations P12 (mean sampling depth, 5.1 m) and
P10 (mean sampling depth 8.4 m) .
Bottom dissolved oxygen concentrations were also Isss than
4.0 mg/1 in early spring and late summer in East Bay (Station
AGJI; mean sampling depth, 3.0 m) and in Blackwater Bay (Station
BNGA; mean sampling depth 2.1 m) (Figure 8-34) .
Pensacola Bay System - 1973
Dissolved oxygen concentrations were measured every three
hours during diel (24-hour) water quality studies performed in
1973. Studies during both tropic and equatorial tidal cycles
were performed during high and low river inflows (Table 8-21).
Mean concentrations and percent of saturation at each station
sampled are shown in Appendix 8-18.
Mean dissolved oxygen deficits in the Escambia River during
each study were similar as shown below:
Date (1973) P.O. deficit (mg/1)
I April 13-15 2.4
II April 19-21 2.7
III August 16-18 2.7
IV August 23-25 2.8
8-54
-------
Table 8 - 21. Dates of and environmental conditions during the 1973
diel water quality studies.
Study
I
II
III
IV
Dates
April 13-15
April 19 - 21
August 16 - 18
August 23 - 25
Tide Range
ra
0.1 . .
.. '"' 0.6
0.2
0.6
River Inflow
m 3 /sec
1697
757
286
2C3
00
I
anil IV. (August, 1973).
SfUDI III
Bay
Escamuia
East
F ensacoli
Cult
Depth
Surtacc
Bottom
Surface
Bottom
Sur£acc
Do tt'oo
Surface
Bottom
No. on Ob:;.
98
96
214
2
-------
There1 were high dissolved oxygen concentrations_ in the
Pensacola Bay system during Study I. Mean surface and bottom
concentrations in Escambia Bay ranged between 80 and 90 percent
of saturation. Because river discharge was extremely high during
this study, Escambia Bay was essentially fresh and there was no
vertical stratification. In East Bay, mean surface arid bottom
dissolved oxygen concentrations were all above 7.0 mg/lf or 75
percent of saturation. Mean surface dissolved oxygen
concentrations in Pensacola Bay were all near 90 percent of
saturation, and mean bottom concentrations were slightly below
7.0 mg/1, or 80 percent of saturation. No samples collected
during this study had dissolved oxygen concentrations less than
4.0 mg/1.
During Study II, dissolved oxygen concentrations were
essentially the same as those during Study I. Only one sample
collected during this study had a dissolved oxygen concentration
less than 4.0 mg/lr and this occurred in upper East Bay (Station
ADGV) .
During Study III, when the river inflow was about the average
annual flow, dissolved oxygen concentrations Were lower than
those in April 1973. In upper Escambia Bay near the Escambia
River delta, mean surface concentrations were 6.0 mg/lr or 75
percent of saturation. In the lower bay, concentrations were
near 8.0 mg/1. Two percent of the surface samples collected in
Escambia Bay had concentrations of less than 4.0 mg/1 (Table 8-
22) » Mean bottom concentrations in the dredged channel were all
less than 2.0 mg/1. Throughout the rest of the bay mean bottom
concentrations ranged between 2.1 and 6.3 mg/1, or 36 and 97
percent of saturation. Fifty-six percent of the bottom samples
collected in Escambia Bay had concentrations of less than 4.0
mg/1 (Table 8-22).
In East Bay, during Study III, all mean surface
concentrations were near 100 percent of saturation. Conversely,
mean bottom concentrations were extremely low, ranging between
1.4 and 2.7 mg/1 or 22 and 43 percent of saturation, and 75
percent of all bottom samples were less than 4.0 mg/1.
In Pensacola Bay, all mean surface concentrations during
Study III were slightly greater than 100 percent of saturation
and 12.5 percent of the surface samples contained less than 4.0
mg/1 of dissolved oxygen (Table 8-22). Mean bottom
concentrations varied from 5.0 mg/1 at the inlet to 0.7 mg/1 in
the eastern portion of Pensacola Bay, and 74.5 percent of the
bottom samples contained dissolved oxygen concentrations less
than 4.0 mg/1.
Study IV was performed during tropic tides and low river
inflow conditions and dissolved oxygen concentrations were lower
in Escambia and East Bays, and higher in Pensacola Bay than
during Study III. Mean surface concentrations in Escambia Bay
ranged from 74 to 113 percent of saturation, and no surface
8-56
-------
samples had concentrations below 4.0 mg/1 (Table 8-22). Samples
from stations at the channel bottom had mean concentrations
ranging from 1.1 to 2.4 mg/1, and the rest of the bottom stations
in Escambia Bay had mean concentrations ranging from 2.4 to 7.1
mg/1 or 60 to 100 percent of saturation. Sixty-three percent of
all bottom samples collected from Escambia Bay had dissolved
oxygen concentrations less than 4.0 mg/1.
Dissolved oxygen concentrations in East Bay were generally
lower during Study IV than during Study III. All mean surface
concentrations were near 100 percent of saturation and no samples
had concentrations less than 4.0 mg/1 (Table 8-22). Mean bottom
concentrations at. stations in East Bay were extremely low,
ranging from 20 to 31 percent of saturation, and 95.8 percent of
all samples collected had concentrations less than 4.0 mg/1.
Dissolved oxygen concentrations in Pensacola Bay during Study
IV were generally higher than those during Study III. Mean
surface concentrations were all slightly greater than 100 percent
of saturation, and mean bottom concentrations ranged between 43
and 101 percent of saturation. During this study, there were no
surface samples with dissolved oxygen concentrations less than
4.0 mg/1 (Table 8-22), and 29.5 percent of the bottom samples
were less than 4.0 mg/1 compared to 74.5 percent during Study
III.
Dissolved oxygen concentrations near the bottom of Pensacola
Bay were higher during Study IV than during Study III,, and this
appeared to have been due to tidal exchange. Since the bay was
stratified, during these studies dissolved oxygen in the bottom
water did not come from reaeration. Thus, the bottom water that
existed in the bay seaward of the Pensacola Bay bridge during
Study III was diluted by Gulf water transported into the bay by
tropic tides (Table 8-22) .
Large diurnal variations are an indications of stressed
aquatic conditions. There were no large diurnal variations in
dissolved oxygen concentrations in the Pensacola Bay system
during Studies III and IV (Figure 8-35). Surface diurnal
variations were always less than 2.0 mg/1. In northeast Escambia
Bay and East Bay there were significant diurnal variations in
bottom dissolved oxygen, but since benthic algae were not found
in the system, this variation was due to changing tides and
winds.
Escambia Bay - 1969
During a study of Escambia Bay on September 23-25, 1969
(USDI, 1970), mean surface dissolved oxygen concentrations were
slightly greater than 5.0 mg/1 adjacent to the Escambia River
delta (Figure 8-36). Mean surface concentrations increased to
greater than 8.4 mg/1 near the L and N Railroad bridge, and then
increased slightly in a seaward direction. Mean bottom dissolved
oxygen concentrations of less than 4.0 mg/1 occurred over 43
8-57
-------
00
en
00
—
0>
.VED OXYGEN
0
(^
w
o
^ Northeast Escambio Bay Station EEKV
9
8
7
6
5
4
3
2
1
C
- 9
— B
— 7
_ — \/V .J^ 6
i-^r' \
— " / 5
I
/ "
- /
/ 2
(
- f
1
1 --"1 1 1 1 1 o
—
-
/x__
/\ // ^
V/ i
_ / 1
/ 1
\
-
-
-
1 1 1 1 1 1
5 10 15 20 0 5 O 5 10 15 2O 0 5
8/16/73 8/17/73 8/23/73 8/24/73
Lower Escambia Bay Station CNNB
9
B
7
6
5
4
3
2
1
C
— 9
— 8
\ f~~~
— 6
— ' 5
— :. 4
— 3
— 2
— 1
i i---7~\i---r""i
r^~^~^
- /
-
-
-
-
— V---'' \
\
-
1 1 1 1 1 1
) 5 10 15 2O 0 5 0 5 10 15 2O 0 5
8/16/73 8/17/73 8/23/73 8/24/73
9
8
7
6
5
4
3
2
1
C
9
8
7
6
5
4
3
2
1
Q
C
East Boy Station
— 9
— 8
/ 1
- /I
- /
,'' t
1 4
1 / ''
/
'i
- 1 _,' 1
1 1 1 1 1 1
) 5 10 IS 2O 0 5 (
8/17/73 8/18/73
1 B St t'
| — 9
X->/~^^
— 7
— 6
- , /'\ 5
V"--.//
— 3
~~ 2
— 1
) 5 10 15 20 0 5 <
8/17/73 8/18/73
AJFD
—
-
; "^
—
\ -*''' ~VN
i i i i i i
3 5 10 15 2O O 5
8/24/73 8/25/73
on POOH
/\
- ^^ ^^^.
— — x t
_ "" '
-
— KEY
1 1 1 III
3 5 ID 15 20 0 5
8/24/73 8/25/73
Figure 8-35. Dissolved oxygen concentrations during Studies III
and IV (August 1973) for selected stations in the Pensacola
Bay system (Pensacola Bay data from the University of West
Florida).
-------
Fishermons Pt.
Mu/at Bo you
5.2 Surface Value
3.7 Bottom Value
Figure 8-36. Mean surface and bottom dissolved oxygen
concentrations in Escambia Bay during September 23 to
September 25, 1969 (USDI, 1970).
8-59
-------
percent of the area of the bay. This includes all of the central
and northern sections of the bay, except for the shallow areas
near the delta (USDI, 1970).
Large diurnal variations in dissolved oxygen, indicative of
high phytoplankton concentrations, were observed in Escambia Bay
during the 1969 study. In the northeastern area of the bay
(Station E3), the range was 7.3 mg/1 at the surface. The surface
range in the central part of the upper bay (Station E9) , in the
eastern section of the upper bay (Station E18) , and in the lower
bay (Station E29) were 6.8, 6.8, and 3.5 mg/1, respectively.
Large diurnal variations did not occur in August 1973.
Choctawhatchee Bay - 1974
Surface dissolved oxygen concentrations in Choctawhatchee Bay
on September 12, 1975 were about 70 percent of saturation near
the mouth of the Choctawhatchee River (Figure 8-37 and 8-38).
Values increased to greater than 100 percent of saturation by
mid-bay. The dissolved oxygen deficit in the Choctawhatchee
River was 2.9 mg/1, which was similar to that in the Escambia
River. Bottom dissolved oxygen concentrations were considerably
lower than surface values, and nine of the 21 bottom samples
analyzed (43 percent) were lower than the 4.0 mg/1 minimum
standard. Bottom dissolved oxygen concentrations were lowest in
the deep center section of the bay, and bottom concentrations in
this section ranged between 0.2 and 0.9 mg/1.
Discussion
Dissolved oxygen concentrations in Escambia Bay appeared to
improve between 1969 and 1973 through 1974. The high diurnal
variation in dissolved oxygen observed in 1969 was not observed
in 1973. During the 1974 study period, there were two periods of
low dissolved oxygen, one in the early spring and other in late
summer. The period in early spring occurred after high river
inflows and the one in summer occurred when salinities in the
system were high, indicating poor flushing. During both periods,
lower bottom dissolved oxygen concentration occurred near the
industrial discharges in northeast Escambia Bay (Station EGL5f) .
The data that was available for Pensacola Bay during 1974
indicated that low dissolved oxygen concentrations in Escambia
and East Bays during the spring of 1974 were not caused by a
water mass from Pensacola Bay entering these systems. Benthic
oxygen demand from the sediments appeared to have been a
significant factor in causing low bottom dissolved oxygen
concentrations.
Vertical stratification in the system was observed in the
salinity data and also in the dissolved oxygen data. Bottom
dissolved oxygen concentrations were always lower than surface
concentrations. This occurred because the dissolved oxygen
removed from the lower layer by benthic demand was not
8-60
-------
Figure 8-37. Dissolved oxygen concentrations in Choctawhatchee
Bay on September 12, 1971.
Figure 8-38. Values of percent dissolved oxygen saturation in
Choctawhatchee Bay on September 12, 1974.
8-61
-------
continuously replaced when the system was stratified, since there
was very little exchange between reaerated upper layer water and
lower layer water.
Based on dissolved oxygen concentrations in East Bay, low
dissolved oxygen concentrations occur during critical periods
(high temperatures, low river inflow) even in the bays that do
not directly receive point source waste discharges.
Consequently, due to naturally poor circulation in the Pensacola
Bay system, the assimilative capacity of the system with respect
to oxygen resources should be extremely limited.
Biochemical Oxygen Demand
Introduction
Biochemical Oxygen Demand (BOD) is the amount of oxygen used
by bacteria while stabilizing biologically degradable material
(Sawyer, 1960). As such, it is a reasonably good measure of
materials available for biochemical stabilization, as well as an
indicator of the oxygen demanding capacity of an aqueous system.
The oxygen demand of polluted waters is exerted by three
classes of materials (Std. Methods, 1965): (1) carbonaceous
organic material available as a food for microorganisms; (2)
nitrogenous material susceptible to microbial oxidation; (3)
chemical agents susceptible to chemical oxidation, which belong
in the category of Chemical Oxygen Demand. It is generally
assumed in the analysis of long-term BOD results that there are
two distinct stages in the BOD process; the utilization of
carbonaceous material by saprophytic bacteria, followed by
oxidation of nitrogenous material by nitrifying bacteria (Sawyer,
1960; EPA, 1971). The reproductive rate of the nitrifying
bacteria at 20°C is slow enough that a minimum of 5 to 10 days is
usually required to establish a sufficient population to exert an
appreciable oxygen demand. This is the basis for the sequential
carbonaceous and nitrogenous demands.
Florida Department of Environmental Regulation (FDER)
criteria do not give specific limits for BOD in estuaries. They
state that BOD in Class II or Class III waters shall not be high
enough to cause D.O. (dissolved oxygen) concentrations to be
depressed below H.O mg/1 (Florida Administrative Code, 1973).
There are drawbacks to the BOD test. The conditions under
which the BOD test is done in the laboratory are not
representative of conditions in the natural environment. Samples
are incubated in the dark and algae in the water die off soon
after incubation, exerting an oxygen demand as they decompose.
Large amounts of algae can significantly affect the BOD results.
On the other hand, substances which are toxic to bacteria
suppress BOD. This interference is particularly serious in five-
day BOD because there is not enough time for tolerant organisms
8-62
-------
to become established. Thus, ultimate BOD is preferable to
short-term BOD in assessing BOD levels in an aquatic system.
Results and Discussion
Mean ultimate BOD values (Lu) during the 1974 study period
were slightly lower in Escambia River than in Escambia Bay
(Figure 8-39 and Table 8-23) . The mean ultimate BOD at Station
EGLY, near Air Products and American Cyanamid, was 4.0 mg/1
higher than mean ultimate BOD at Station ER10 in Escambia River.
Mean ultimate BOD and rate constants (kc and kn) generally
decreased in a seaward direction from Station EGLY to Station
ERPB.
In order to determine if BOD values and rate constants were
influenced by die-off of algae in the BOD bottles, a correlation
was run between chlorophyll a concentrations in all surface water
samples in the 1974 water quality studies and ultimate and five-
day ' BOD in the same samples. Very little correlation was found
between any type of BOD and chlorophyll a. There was no
correlation at all with ultimate BOD (Lc^Ln) , and only a
correlation of 0.36 with ultimate carbonaceous BOD (Lc). The
correlation of chlorophyll a with five-day BOD was only 0.27.
Thus, even though many of the patterns observed in these BOD
studies were typical of the influence of algae die-off, no
correlation could be seen using chlorophyll a as the indicator.
Some of these patterns are discussed further in this section.
Mean five-day BOD values in Escambia Bay in 1974 were all
quite low (Table 8-24). The overall average for the study period
was 1.4 mg/1. Only during one water quality study (May 29, 1974)
did the mean five-day BOD exceed 2.0 mg/1. During two studies,
it was less than 1.0 mg/1 (March 5 and April 16, 1974). The
overall average of 1.4 mg/1 was very close to the overall 1973
five-day BOD average of 1.8 mg/1.
The data in Table 8-24 and Appendix 8-19 did not reveal any
definite patterns in mean ultimate or five-day BOD by month or
season. One striking pattern was the unusually high kc values
during the August 1974 water quality study. This probably can be
attributed to increased algae populations in August. The die-off
of algae in the BOD bottles could cause this initial rapid
depletion of oxygen.
A comparison of ultimate and five-day BOD with dissolved
oxygen values does not explain variations in dissolved oxygen
concentrations during the 1974 study period (Figure 8-40) . Large
decreases in dissolved oxygen values are not accompanied by large
increases in BOD. This indicates that BOD is not the controlling
factor in monthly dissolved oxygen variations in Escambia Bay.
Other factors involved in dissolved oxygen fluctuations are
discussed in the dissolved oxygen section.
8-63
-------
00
I
HONSAMTO CHEMICAL CO.
\
\
Figure 8-39. Mean ultimate BOD (mg/1) in Escambia, East, and
Blackwater Bays during January through September, 1974.
-------
Table 8 - 23. Wean ultimate biochemical oxygen demand data for Fscambia Bay
stations during January through September, 1974.
Station
EE10 -
ER10 -
EGLY -
EGLY -
EKHP -
EKHP -
ENNB -
ENNB' -
ERPB -
ERPB -
S
B
S
B
S
B
S
B
S
B
Lu
(mq/1)
5.6
5.9
.8.0
11.5
10. 1
6.5
12.1
,6.8
u.u
8.5
kc
(day'l)
0.310
C . 3 1 3
C.22U
C.13C
0. 173
0. 158
0.1U7
0. 118
0.153
0.108
kn
(day-1)
C.090
O.GUO
0. 115
0.078
0.081
0.087
0.072
0.055
0.137
0.065
Lc
(mq/1)
3. 1
2.7
tt.U
7.9
3.3
5.0
.5.0
4.1
4. 3
Ln
2.9
3.9
3.6
tt.-O
6.8
3.1
7. 1
3.5
3.2
7.0
tn
(days)
2U
22
23
20
20
2« '.
22
23
22
BOD
0.9
1.8
1.U
1.4
1.3
note:
Lc = ultimate carbonaceous BOD
Ln = ultimate nitrogenous BOD
Lu = ultimate BOD (Lc+Ln)
kc = carbonaceous rate constant
kn = nitrogenous rate constant
tn = time at which nitrogenous stage begins
8-6.5
-------
Table 8 - 24. Mean biochemical oxyqen demand data at.Escambia Bay stations during January
through September, 1974.
Date
(m -
1/23/74
2/12/74
3/05/74
3/27/74
4/16/74
5/07/74
5/29/74
' . 6/18/74
00
1 ' 7/09/74
^ 7/30/74
8/20/74
9/11/74
•avq. 1974
April 1973
August 1973
Flow*
J /sec)
333
737
226
203
506
1 14
178
126
71
6y
147
784
Lu
7.7
7.5
6.6
6. 1
11.9
6. 1
6. 1
8.5
8. 1
8.3
5.6
16.5
8. 3
5.7
19.5
kc
(day>l)
0.
c.
C.
0.
C.
o1-.
0.
C.
n
0.
0.
0.
C.
C.
0.
136
195
048
333
061
114
224
108
065
058
743
057
177
011
304
(da
0.
0.
o..
C.
0.
0.
0-.
0.
0.
0.
0.
0.
0.
0.
kn
085
025
055
C77
163
062
133
067
109
124
078
051
103
-
047
Lc
(mg/1)
4.
2.
4.
1.
5.
3.
3.
4.
4.
5.
2.
10.
4.
-
4.
0
3
7
7
7
5
9
5
4
8
4
1
4
C
Ln
(mg/1)
3.7
5.2
1.9
4. 4
6. 2
2.6
2.2
4.C
3.7
2.5
3. 2
6. 4
3.9
-
6.4
BOD
(mg/1)
1.8
1.2
0.8
1. 1
0.9
1. 1
2.5
1.8
1.2
1. 4
1.5
1.0
1.4
0.6
2.9
tn
(days)
27
18
23
14
23
27
19
27
27
27
16
22
22
-
15
note:
* Total effective flow into Escambia Say.
Lc = ultimate carbonaceous BOD
Ln = ultimate nitrogenous BOD
Lu = ultimate BOD (Lc+Ln)
kc = carbonaceous rate constant
kn = nitrogenous rate constant
tn = time at which nitrogenous stage begins
-------
I I
II I I I I II
1974 STUDY PERIOD
Figure 8-40. Mean bottom ultimate BOD (mg/1) and dissolved
oxygen (mg/1) values in Escambia Bay plotted against each
date sampled in 1974.
20 30 40 SO
DAY NUM8EB
20 30 40 90
DAY NUMBER
20 30
OAT NUMBER
Figure 8-41. Typical long-term BOD curves from the 1974 water
quality studies (• = NLINBOD results)
8-67
-------
Some examples of typical long-term BOD curves are shown in
Figure 8-41. The sequential carbonaceous and nitrogenous phases
can be seen in each of these curves, as well as tn, which shows
the breaking point between the two phases. The typical pattern
is that there is a rapid initial rise in oxygen depletion,
followed by a flattening out as available carbonaceous material
is stabilized. There is usually not such a rapid initial rise in
the nitrogenous phase, and this is reflected in the k values.
The point where the flattening out occurs in each phase is the
ultimate BOD.
Ultimate BOD was determined on two stations in Choctawhatchee
Bay during the September 12, 1974 water quality study. Station
ZIMY, near the eastern freshwater end of the bay, had higher
surface and bottom ultimate BOD and kc values than Station YNKF
at the western saltwater end (Figure 8-42 and Table 8-25). This
was the same pattern seen in EsGambia Bay. Station ZIMY had a
five-day BOD that was more than twice the five-day BOD at Station
YNKF. Two stations do not provide sufficient information to
generalize about the whole bay, but if ultimate BOD at Station
ZIMY is typical of a significant portion of Choctawhatchee Bay,
then there was a BOD problem in September 1974.
Mean ultimate BOD, rate constants, and five-day BOD were
considerably lower during the April 1973 water quality study than
the August 1973 study (Tables 8-26 and 8-27) . There were no
nitrogenous phases to any of the four samples on which BOD was
analyzed during the April study. The average ultimate BOD in
August was about twice the average in April, and the average kc
value in August was about 30 times the average kc in April. This
again could reflect the presence of algae in August, which affect
the BOD and kc values by die-off in the BOD bottles. No obvious
upper to lower bay pattern could be seen in either study for
ultimate BOD or rate constants. Escambia River ultimate BOD in
both months was less than in Escambia Bay (Figures 8-43 and 8-
44) .
In summary, mean ultimate BOD and rate constants did not
differ greatly between 1973 and 1974. There was no indication of
either deteriorating or improving conditions in Escambia Bay with
respect to BOD in 1974. It is possible that much of the BOD
observed in this study was due to algae die-off in the BOD
bottles, but this cannot be substantiated by correlations of
chlorophyll a and BOD.
No definite indication of excessive BOD levels in Escambia
Bay in 1974 was observed in this study. A summary of 1974 BOD
data by station and date is presented in Appendix 8-19.
8-68
-------
Table 8 - 25. Ultimate biochemical oxygen demand data for Choctawhatehee Bay on
September 12, 1974.
Station
ZIMY
ZIHY
YNKF
YNKF
S
B
S
B
Lu
(mg/1)
6.2
13.6
5.2
1.8
Lc
(mg/1)
2.0
2.3
2.6
0.9
Ln
(mg/1)
4. 2
11.3
2.6
0.9
kc
(day-1)
0.814
0. 149
0. 1U6
0.121
kn
0.026
0.005
0.055
0.253
tn
(days)
27
32
33
BOD
(mg/1)
2.3
1.4
1.3
O.U
Figure 8-42. Ultimate BOD (mg/1) values in Choctawhatchee Bay on
September 12, 1974.
-------
Table 8 - 26. Ultimate biochemical oxygen demand data foe l-'scarobia Ray
statior.3 durinq April, 1973 dicl water quality surveys.
Station
2R1C - 3
3 R i r - B
EFLU - 5
EFLU - B
EKMP - S
EKHP - B
EHPB - S
ERPQ - 3
averaqe
Date Tide
U/19/73 Tropic
U/19/73 Tropic
u/19/73 Tropic
U/19/73 Tropic
U/19/73 Tropic
U/19/73 Tropic
U/19/73 Tropic
L
(mg
a
3
5
5
n
5
9
4
5
C
/I)
.8
. B
.U
,2
.5
.9
,5
.U
.7
kc
(day'1)
0 . 0 1 2
0 . 0 ' 8
0.009
0.01 •:
0. 010
0.. 0 1 1
0.007
0 .017
0.011
BOD
(tng/1
0 . 6
0.7
0.6
T.5
r.7
'".7
0.7
1.0
".7
aote :
Lc = ultimate carbonaceous FDD
kc = carbonaceous rate cor, stan t
Table 8 -
Auqust
Station
ER10 - S
ER10 - B
ER10 - S
ER10 - B
EIME - S
EIHE - B
EIHE - S
EIHE - B
EKM? - S
EKHP - B
EHQC - S
EHQC - B
ERPB - S
ERPB - B
ETLQ - S
ETLQ - B
averaqe
27. Ultimate biochemical oxygen
, 1973 water quality surveys.
Date Tide Lu
(mq/1)
8/16/73 Equatorial 4.5
8/16/73 Equatorial 9.2
8/23/73 Tropic 9.5
8/23/73 Tropic 6.6
8/16/73 Equatorial 11.0
8/16/73 Equatorial 15. 1
8/23/73 Tropic 11.1
8/23/73 Tropic 12.7
8/16/73 Squatorial 17.1
8/16/73 Equatorial 10. 1
8/16/73 Equatorial 14.3
8/16/73 Equatorial 9.8
8/16/73 Equatorial 8_. 4
8/16/73 Equatorial 8.3
8/16/73 Equatorial 11.8
8/16/73 Equatorial 7.5
10.5
demand data for ^scambia Bay
kc
(day'1)
0.403
0.417
0.545
0.382
0.273
0.249
C.179
0.180
C.310
0.422
0.476
0. 141
C.320
0. 123
0.323
C. 118
C.304
. kn Lc
(day'1) (mq/1)
C.146 2.8
0.041 2.5
0.01? 1.9
0.017 1.7
0.032 5.2
O.C17 4.0
0.097
0.046 6. 1
0.009 5.5
0.036 2.5
0.010 3.9
0.039 5.6
0.028 4.U
0.090 5.6
0.014 4.tt
C.113 4.2
0.047 4.0
stations during
Ln tn
(mg/1) (days)
1.7
6.7 22
7.6 6
U.9 12
5.8 16
11.1 11
6.6 14
11.6 16
7.6 9
10.4 5
4. 2 22
U.O 9
2.7 30
7.4 12
3.2 29
6.« 15
BOD
(ng/1)
3.6
2.2
1.8
1."
3.8
2.8
3.9
3.5
4.2
2.3
3.6
2.8
3.4
2.8
3.6
2.0
3.0
note:
Lc = ultimate carbonaceous BOD
Lo = ultimate nitroqenous BOD
Lu = ultimate BOD (Lc+Ln)
kc = carbonaceous rate constant
kn = nitroqenous rate constant
tn = time at which nitroqenous stage begins
8-70
-------
00
-J
Figure 8—43. Mean ultimate BOD (mg/l ) In
Escarabla Bay during April» 1973*
Figure 8-44. Mean ultimate BOD
-------
TOTAL AND FECAL COLIFORM BACTERIA
Introduction
Coliform bacteria have traditionally been used as indicators
of the potential presence of enteric pathogens and the degree of
fecal pollution of a body of water. Although no correlation of
pathogen densities to coliform densities can be made for general
use, adherence to the coliform standards set for potable water,
recreational water, and shellfish harvesting has contributed to a
reduction in the incidence of diseases due specifically to water
borne enteric pathogens.
The coliform group occurs in the intestinal tract of warm-
blooded animals and are the most numerous group of bacteria found
in human excreta. Several bacterial genera with similar
biochemical properties comprise the coliform group. Some members
of the coliform group occur naturally outside the intestinal
tract, a fact -that has resulted in the criticism of the total
coliform group as indicators of fecal pollution.
Much of the criticism of the coliform group was overcome with
the development of the fecal coliform test. The fecal coliform
group represents that portion of the coliform group most
representative of indicating fecal pollution, and is presently
the most reliable indicator of fecal contamination.
Enumeration of both total and fecal coliforms in this study
was conducted to determine compliance with water quality
standards using both groups, and' also to monitor bacterial
contamination that resulted from sources other than warm-blooded
animals.
Results
Coliform Surveys of Shellfish Waters
A summary of the bacteriological data for shellfish growing
area number 32 during the 1970-71 and 1971-72 harvesting season
is presented in Tables 8-28 and 8-29. Station locations are
shown in Figure 8-45, (State of Florida, Department of Health and
Rehabilitative Services, Bureau of Sanitary Engineering,
Pensacola, Florida, Unpublished Data) .
Water samples analyzed for the 1970-71 harvesting season were
collected from October 1970 through May 1971. Median coliform
densities for these eight monthly samples ranged from 6 to
>1300/100 ml. The median coliform shellfish standard of 70/100
ml was exceeded at Stations 58, 61, and 90 in the area open to
oyster harvesting. The highest fecal coliform median densities
during the 1970-71 season were 109 and 130/100 ml. These
densities were for Stations 93, and 95, respectively, both
located outside the area open to oyster harvesting.
8-72
-------
Table 8 - 28. Total and lecal colifom iata (densities per 1DO nl) foe oyster harvesting Are* 32 during the 1973-1971 season.
Date 10/14/70
Sta *"-•• °
60
63
67
71
74
58
61
64
68
79
80
82
83
86
88
90
91
93
95
96
• 1UL •
343.
918*.
«9.
2.
<2.
49.
914.
243.
918.
<2.
<2.
a.
>2433.
241.
243.
>2403.
913.
918.
1629.
>2403.
1639.
e *n. •
<2.
<2.
<2.
2.
<2 .
<2.
4.
4.
4.
<2.
<2.
<2.
26.
2 .
2
7.
27.
109.
14.
79.
542.
11/C9/70 11/30/70
Tot.
<2.
2.
5.
<2.
<2 .
<2.
<2.
2.
5.
2.
<2.
6.
5.
4.
9.
23.
13.
23.
13.
25.
23.
r ei. • lui.
<2. 349.
<2. >2400.
<2. >2400.
2. 542.
<2. >21 00.
<2. >2430.
<2. 542.
<2. 49.
<2. <2.
<2. 130.
<2. 79.
<2. <2.
<2. 240.
<2. 23.
<2. 5.
<2. >2430.
2. 1609.
5. >240C.
<2. 348.
8. >240C.
8. >2400.
*
49.
34.
1609.
210.
>2100.
1.
7.
13.
<2.
<2.
2.
<2.
2.
<2.
<2.
240.
1609.
>2i:o.
2.
240.
23.
01/11/71 33/38/71
*
918.
221.
> 2 1 0 " .
312.
160^.
1 6 : 9 .
130.
22.
79.
2i .
23.
5.
22.
130.
21.
>24 JO.
8. 1639.
2. 542.
<2. 79.
2. >2430.
<2. 49.
8. 918.
5. >240CI.
2. 542.
<2. 34b.
<2. 348.
<2. 24?.
<2. 49.
8. 348.
<2. 7-J.
<2. 34H.
2. 318.
542.
243.
240.
348.
240.
918.
240.
13.
542.
k 3.
542.
210.
79.
79.
8.
23.
22.
23.
19.
8.
13C.
3'. 8.
130.
240.
130.
19.
01/12/71 05/17/71
318.
240.
33.
49.
240.
918.
33.
23.
33.
23.
33.
23.
2.
2.
5.
79.
240.
1639.
>240C.
>2400.
1609.
<2. 542.
<2. 542.
<2. 17.
<2. 17.
<2. It.
22.
2.
2.
<2.
<2. 7.
<2.
2.
<2.
<2 .
4 .
8.
2.
<2.
8.
221.
79.
05/25/71 Relian
Tot.* P 3 C • Tot • "**
<2.
79!
490.
<2.
2.
<2 .
<2.
<2.
<2.
2.
<2.
<2 .
<2.
2.
2.
33.
5.
6.
490.
133.
790.
348.
390.
64.
53.
64.
918.
130.
23.
33.
15.
23.
6.
22.
23.
9.
214.
391.
579.
519.
>1303.
>1100.
rei..*
u.
2.
<2.
2.
<2.
6.
5.
3.
<2.
<2.
<2.
<2.
5.
2
<2.
a.
27.
109.
8.
133.
49.
State of Florida, Department of Health and Rehabilative Services, unpublished data.
Table 8 - 2'J. ratal ana Lecal coliform data (Jen^ir.ies pe.r i:) nl) ror oyster harvesting irei 32 during the 1371-1972 season.
Date
Sta.
60
63
67
71
72UCC.
<2. 160C.
2. >240",.
b. >240':.
<2. 920.
<2. 19.
<2. 920.
<2. 19.
<2. d.
<2. 49.
<2. 540.
<2. 49 .
<2. 130.
<2. <2.
< 2 . 2 .
<2. 7.
<2. 130.
4. 79 .
<2. 240.
<2. 130.
<2. 160.:.
<2. 130.
<2. 79.
<2. 2UO.
<2. <2. <2.
<2. <2 . <2 .
<2. <2 . <2 .
<2. 2 . <2 .
<2. 49 . 5 .
<2. 24:. 79.
<2. > 2 4 .: ' . 79.
<2. 79. 14.
<2. 5. <2.
<2.
<2.
<2 .
<2.
<2. 30:. 79.
<2. 13. <2.
<2. 24?. 33.
<2. 92:. 22.
<2. 92v. 350.
<2. 160.1. 150.
<2. 35:. 13C.
02/14/7?
Pot. Foe."
1 6 0 0 .
54:.
92: .
1600.
547.
54:.
33.
150C.
350.
240.
13:.
24C.
1600.
13'..
1SJJ.
i6o:.
>240? .
920.
> 2 4 0 C .
>24vC.
79.
33.
33.
130.
5.
27.
6.
34.
23.
<2.
<2.
2
1.K.
<2.
79.
79.
33.
23.
27.
23.
02/28/72 04/10/72 Hedian
Tot. Fa:. Tot. Fee. TDt. Pac.
927.
1600.
24'.
79.
23.
54-;.
8.
13.
33.
130.
>2UOO.
92C.
1600.
920.
>2400.
>2i:o.
2UO.
3.
33.
49.
5.
5.
8.
2.
<2 .
22. 33.
33. <2.
49. 23.
S'40. 79.
8. 240.
240. 33.
240. 1600.
434 .
49.
295.
31.
28.
144.
20.
31 .
21 .
3.
<2 .
4 .
U45.
<2. 79.
<2. 240.
<2. 350.
5. 1600.
<2. 920.
<2. 16D2.
23. 1600.
4.
1.
6.
<2.
3.
3.
4.
<2.
<2.
<2.
<2.
<2.
U.
<2.
<2 .
<2.
5.
<2.
2.
23.
State of Florida, Dept. or Health a ni 3«habili. tativs Services - unpublished data.
-------
During the 1971-72 harvesting season, (a total of seven
sampling periods from September 1971 through April 1972) total
coliform densities exceeded the median coliform shellfish
standard at four stations out of ten within the harvesting area.
These four stations, 58, 83, 88, and 90, were on the outer
borders of the oyster beds. The median total coliform density
ranged from <2 to 1600/100 ml for all stations,- including those
not in the harvesting area. The highest mean fecal coliform
density was 23/100 ml for Station 96, located outside the area
open to oyster, harvesting.
'". ; ColiformjSurvey - 1973 .
\
In 1973, twenty-six stations, were sampled (Figure 8-45).
Twelve of the eighteen Escambia .Bay stations were sampled only
one time in December 1973. No significance can be placed on
these densities, since they are based on a single sampling period
and are higher than mean densities obtained over an extended
period. Most of the total coliform densities at the Escambia Bay
stations in December 1973 were.above 1000/100 ml and all fecal
coliform densities but .one were greater than 200/100 ml for that
same period (Table 8-30). The East Bay Station, AJFD, had low
total and fecal coliform densities for this sample period. One
of the three East Bay stations was sampled twice. The other
;stations were sampled at four-hour intervals during two opposing
•tidal cycles in April and in August 1973. All of the samples
analyzed were surface samples.
During these studies total coliform densities for all but two
stations (EEKV and EFLU) were below a geometric mean of 1000/100
ml (Table 8-30). Geometric mean densities of 1140 and 1170/100
ml at these respective stations in upper Escambia Bay slightly
exceeded the Class III standard. Total coliform densities at
Escambia River Station ER10, also in Class III waters, exceeded
2400/100 ml, the maximum permissible for any day. Total coliform
densities at this station complied with a geometric mean of
575/100 ml for the year. The other stations in Class III waters,
PIVP, PJPD, PPJV, and PQJQ, are west of the Highway 98 Pensacpla
Bay bridge. Total and .fecal coliform densities at all of these
stations complied with the Class III standard, including PJPD,
the; station at the mouth of Bayou Chico. The bayou formerly
received industrial effluent and the station was also located in
an ;area not too distant from the Pensacola Main Street Sewage
Treatment Plant outfall.
All of the. remaining stations sampled in 1973 were located in
Escambia Bay'and East Bay in , Class II. ..waters, for shellfish
harvesting. Total coliform densities at East Bay Station AKAA
complied with the median of 70/100 ml as stated in the shellfish
standards. The standard was exceeded at Station ADGV, with a
median density of 77/100 ml, and densities greater than 230/100
ml in 50 percent of the samples. Of the four remaining stations,
only EMQC was within the area classified as Class II waters not
closed to oyster harvesting. The total coliform density at this
8-74
-------
Ul
one EBBS. 1973- 74
Numorel preceded by > p Oni,. of Uejt
Fie.
Huoerel only st,te of n..
ebellflah Aree
132
Figure 8-U5. Locations of total and fecal coliform bacteria
sampling stations (four letter stations are EBRS 1973-74,
numerals preceded by P are University of West Florida,
numeral only is the State of Florida, Shellfish Area f32).
-------
Table 8 - 30. Summary of the total and facal coliform data (densities per 100 ml) for tha Pansacola
Bay system during 1973.
Total Coliform / 100
Station
£JFDA
ECGMA
EDIPA
EEDRA
EEEKA
EEHFA
EEIXA
EGLYA
EHGDA
EHPKA
EIILA
EIKCA
EKLyA
EEKVA
EFLUA
EKMPA
EHQCA
EPLPA
EHPEA
ADGVA
AKAAA
fIVPA
FJPBA
EPJVA
PQJQA
EH10A
NO. of
samples
2
1
1
1
1
1
1
1
1
1
1
1
1
9
6
17
15
8
7
14
13
15
14
6
u
16
Maximum
5
3480
3480
2400
920G
5420
3480
22 1C
3480
920
160:
3480
542
2780
.. 2210
1600
92:
542
92 J
348
348
1090
2400
94
348
3480
Arithmetic
Minimum Mean
4
3480
348.}
2400
9200
5420
348G
2210
3480
920
1600
3480
542
130
542
240
9
14
221
5
4
2
2
49
2
7
5
3480
3430
2400
9200
5420
3480
2210
3480 .
920
1600
3480
542
1449
1.348
672
282
127 -••-
559
1 Vi
61
149
754
72
94
1 134
oil.
Seoiietric
Mean
'4
3480
3480
2400
9200
5420
3480
2210
3480
920
1600
3430
542
1140
1173
590
141
71
497
75
24
29
210
69
36
575
Fecal Coliform / 10D
Maximum
2
542
542
1600
2210
700
920
920
343
130
348
348
240
240
130
348
79
a
50
13
49
79
460
23
49
2400
Arithmetic
Minimum Hean
2
542
542
1600
2210
700
920
920
348
130
348
348
240
2
33
2
2
2
27
2
2
2
2
5
2
2
2
542
542
1630
2210
700
920
920
348
130
348
348
240
55
76
92
24
5
39
5
7
21
101
13
10
212
ml.
Geometric
Mean
2
542
542
1600
2210
700
920
920
348
130
348
348
240
23
70
42
10
4
38
4
4
3
35
11
4
62
-------
station exceeded the standard, with a median density of 260/100
ml and densities greater than 230/100 ml in 63 percent of the
samples. Stations EKMP and ERPB are channel stations which were
on the boundary of the area closed to oyster harvesting. Total
coliform densities at these stations violated the standard for
Class II waters, but complied with the Class III standard.
Station EPLP, in the vicinity of the Northeast Sewage Treatment
Plant outfall on the west side of Escambia Bay, was in the
portion of the .bay closed to harvesting oysters. Total coliform
densities at this station were less than the median of 70/100 ml
for Class II waters, but exceeded the 230/100 ml maximum in 13
percent of the samples analyzed during 1973.
( •• ' ". ; ' '
The geometric mean fecal. coliform densities were less than
70/100 ml for these same stations. This was well below the
Florida Standard of 200/100 ml specified for Class III waters
used for body contact recreation. The geometric mean fecal
coliform density for Station EMQC in the oyster harvesting area
was 10/100 ml. -
Coliform Survey ~
Escambia Bay Study
Total and fecal coliform analyses were conducted on surface
and bottom water samples at eleven stations in 1974 (Figure 8-
45) . These stations were sampled a total of 12 times from
January through September 1974. During this sampling period,
only the surface and bottom water samples of the Escambia River
Station ER10 and the surface sample of the Blackwater River
Station BFEI exceeded the geometric mean total coliform standard
for Class III water (Table 8-31) . Bottom samples from Stations
EGLY and PEUE, also in Class III water, met the total coliform
standard of 1,000/100 ml. The surface samples of these stations
exceeded the maximum of 2,400/100 ml allowed for any day.
All of the remaining stations were located in Class II waters
but only EMQC in Escambia Bay and AGJI in East Bay were within
the area open to oyster harvesting. Total coliform densities at
both of these stations complied with the shellfish standard.
Stations \EKMP, ENNB, ERPB, arid BNGA were on the boundary of
areas closed to oyster harvesting in Class II waters. Both the
surface and bottom densities at Station BNGA, and the surface
samples of EKMP, ENNB, and ERPB were greater than the 230/100 ml
total coli forms in more than 10 percent of the samples. Total
coliform densities for bottom samples at EKMP, ENNB, and ERPB
complied with the Class II standard. At Station EPLP on the west
side of Escambia Bay, total coliform densities exceeded the
standard in the bottom sample with a median density of 89/100 ml,
but complied with a median density of 70/100 ml in the surface
sample.
8-77
-------
Table 8 - 31.
Bay system
Summary of the
during 197U.
total and fecal coliform data (densities per 100 ml) for the Pansacola
Total Coliform / 100 ml.
Fecal Coliform / 103 ml. .
Station
ER10A
ER10E
EGLYA
EGLYE
EKMPA
0> EKMPE
^ EMQCA
CD IMQCE
ENNBA
ENNBZ
EPLPA
EPLPE
ERPEA
ERPBE
EEDEA
PEUEB
BFEIA
EFE1E
ENGAA
ENGAE
AGJIA
AGJIE
No. of
samples
12
12
12
12
12
12
11
11
12
12
12
12
12
12
9
9
5
5
12
12
12
12
Maximum
9200
16000
3480
2400
3480
2400
1600
79
3430
109
1720
5420
1600
79
5420
1720
5420
16000
9200
9200
630
460
Arithmetic
Minimum Mean
346
172
14
6
46
4
5
2
4
2
5
4
2
2
79
79
920
49
49
15
2
2
1978
3807
944
472
728
245
329
35
530
26
365
540
373
15
2125
600
2226
3287
1852
1434
112
44
Geometric
Mean
1184
1566
322
85
357
37
65
23
98
13
94
62
48
8
833
389
1693
240
794
194
17
6
Maximum
5420
2210
700
1090
542
240
172
23
920
33
348
348
348
13
1410
542
542
172
542
' 920
94
109
Minimum
23
46 .
2
2
2
2
2
2
. 2
2
2
2
2
2
2
13
33
2
5
2
2
2
Arithmetic
Mean
669
468
157
131
116
25
31
4
135
6
53
36
45
3
301
108
300
49
222
143
21
11
Geometric
Mean
157
194
22
11
31
5
8
2
15
3
13
6
9
3
67
59
162
18
74
12
6
3
-------
Fecal coliform analyses of these same stations during 1974
revealed fecal coliform densities at some stations exceeded
800/100 ml, the maximum allowed in Florida for Class III waters.
These:violations included the surface and bottom water samples
from the Escambia River Station ER10, the bottom sample of
Station. EGLY in upper Escambia Bay, and the surface sample of
Station PEUE in Bayou Texar, all in Class III waters. The
surface sample of Station ENNB in Escambia Bay and the bottom
sample of Station BNGA in Blackwater Bay (both in Class II waters
near the boundary of waters closed to oyster harvesting), also
had fecal coliform densities greater than 800/100 ml.
The Class III standard for maximum daily permissible fecal
coliform density was exceeded at these stations; however, during
1974, the mean fecal coliform densities did not exceed the
recommended monthly geometric mean of 200/100 ml for contact
recreation.
Fecal coliform densities were very low at stations EMQC and
AGJI in Class II waters opened to oyster harvesting. The highest
geometric mean density being 8/100 ml, was found for the surface
samples of station EMQC. The surface samples of station AGJI had
a geometric mean density less than 6/100 ml and the bottom
samples for both stations were 3/100 ml.
Pensacola Bay Study
Total and fecal coliform analyses of surface and bottom water
samples from six stations in Pensacola Bay were conducted for the
University of West Florida during their 1974 study (Figure 8-45).
The highest total coliform density was 24,000/100 ml (Table 8-
32). This density was found for one bottom sample at Station P04
collected in Santa Rosa Sound. The highest .fecal coliform
density observed for bottom water at station P04 was 11/100 ml,
the same water sample giving the high total coliform density.
The highest total and fecal coliform densities observed from the
surface samples at this station were 348/100 ml and 33/100 ml,
respectively.
A surface sample from Station P07 exceeded the maximum total
coliform density permitted in the Florida Standard for Class in
waters (2400/100 ml). The maximum total coliform density of
3480/100 ml and fecal coliform density of 240/100 ml for this
sample were next to the highest densities, observed for all
stations sampled in Pensacola Bay. A geometric mean total
coliform concentration of 310/100 ml and the fecal coliform
density of 42/100 ml for Station P07 were the highest mean
densities observed for all the Pensacola Bay surface and bottom
samples.
The next highest geometric mean total and fecal coliform
densities of 45/100 ml and 11/100 ml, respectively, were observed
at Station P11 in Pensacola Bay. The highest fecal coliform
8-79
-------
Table 8 - 32. Summary of total and fecal conform data (densities per 100 ml) for Pensacola Bay
during 1974 (data from the University of West Florida).
Total Colifocm / 100 ml.
Fecal Coliform / 103 ml..
No. of
Station samples Maximum
arithmetic Geometric
Hinimum Bean Mean
Hajcimum-
Arithmetic Geometric
Minimum Mean Mean
P-02A
P-02E
P-OUA
P-04E
P-07A
P-07E
P-08A
P-08E
P-11A
P-11E
P-13A
P-13E
11
11
11
11
11
10
11
11
11
11
10
10
920
130
348
2*000
3480
920
1090
109
920
348
278
49
2
2
2
2
79
5
2
2
5
4
2
2
mo
30
aa
2186
585
148
120
16
175
43
39
12
26
a
8
8
313
1(7
22
5
45
14
8
7
79
31
33
11
2 UO
79
94
17
348
17
172
23
2
2
2
2
2
2
2
2
2 .
2
2
2
15
7
6
3
87
15
15
3
44
4
19
5
6
3
4
2
42
6
6
2
11
3
3
4
density of 350/100 ml was observed in a surface sample collected
from this station.
Comparison of 1973-1974 Values
The total coliform analyses of samples collected during 1973
and 1974 in Escambia Bay and contiguous waters had total coliform
densities ranging from <2/lOO ml to 16,000/100 ml. This excluded
the abnormally high density of 24,000/100 ml observed at Station
POU in Santa Rosa Sound. One of the three high counts of
16/000/100 ml was from a bottom water sample taken at Station
ER10, the Escambia River station, in January, 1974. The other
two were observed in bottom water samples taken at Station ER10,
the Escambia River Station, and BFEI, the Blackwater River
Station, in September 1974 (Table 8-31).
During the same two-year period, the highest fecal coliform
densities, 5,420 and 2,210/100 ml were observed in January 1974
at the Escambia River Station ER10 in the surface and bottom
water samples, respectively. In most instances, the stations
having the highest fecal coliform densities corresponded to the
stations having the highest total coliform densities.
Discussion
The area of Escambia Bay classified as Class II waters and
approved for shellfish harvesting by the Division of Health,
Florida Department of Health and Rehabilitative Services,
included the eastern half from the barge channel to the eastern
8-80
-------
shore, south of the L and N Railroad bridge and into the
adjoining waters of East Bay (Figure 8-45).
Most stations in the areas open to oyster harvesting meet the
shellfish standards for bacteriological quality. The stations
which did exceed the 70/100 ml median total coliform density in
harvesting years 1970-1971 and 1971-1972 were located near the
boundaries separating open and closed areas. Unusually high
counts, as was observed on February 14, 1972 (Table 8-29), were
attributed to periods of heavy rainfall. The effective flow of
the Escambia Bay tributaries for this sampling date was 554
m3/sec (19,577 cfs) which is more than three times the average
flow of 170 n\3/sec (6,000 cfs) for the Escambia River at Century,
Florida.
No domestic waste effluents were known to be entering the bay
in the area open to oyster harvesting. The only point source of
domestic waste entering Escambia Bay was the Pensacola Northeast
Sewage Treatment Plant which emptied secondary treated effluent
into the west side of the bay. The Escambia Bay Recovery Study
Station EPLP in the vicinity of this outfall complied with the
Florida Standard for Class II waters in 78 percent of the samples
analyzed over the two-year sampling period during 1973-1971.
This particular station was in Class II waters, but was not open
to shellfish harvesting.
Escambia Bay north of the L and N Railroad bridge and
Pensacola Bay west of a line from Emanuel Point to the south end
of the Highway 98 bridge at Gulf Breeze are classified Class III
waters for recreation, propagation, and management of fish and
wildlife.
The geometric mean coliform densities obtained in this study
complied with the Class III standard at most of the bay stations.
In 1973, total coliform densities at Stations EEKV and EFLU
exceeded the geometric mean of 1,000 total coliforms per 100 ml.
These stations in the northern end of Escambia Bay were
influenced by tributaries which had higher coliform densities.
This portion of the bay was also enriched by additional nutrients
from the effluents of Air Products and Chemicals, Inc., and
American Cyanamid Company. The stations which exceeded the Class
III standard \ most frequently were the tributary stations in
Escambia River, Blackwater River, and Bayou Texar. Densities
greater than 2,400 total coliforms per 100 ml were found in the
channel stations of Escambia Bay and Blackwater Bay.
Station P04 in the University of West Florida, Pensacola Bay
Study, is located in the center of Santa Rosa Sound at the bridge
connecting Gulf Breeze and Pensacola Beach. The effluent from a
small sewage treatment plant on Pensacola Beach enters Santa Rosa
Sound approximately 2.6 km (1.4 nautical miles) southeast of this
station. Effluent from the Gulf Breeze Sewage Treatment Plant
enters Santa Rosa Sound about the same distance (2.2 km or 1.2
nautical miles) northwest of the station. Although the effluent
8-81
-------
from the treatment facilities enters Santa Rosa Sound in close
proximity to the sample station, they were not likely the cause
of the 24,000/100 ml total coliform density observed. A remark
on the bench card indicated there was settled sediment in the
bottom of the sample bottle. The low fecal coliform density of
11/100 ml, which was observed for this same sample, would
indicate the high total coliform density was due to sediment in
the sample and not to treatment plant effluent or animal waste.
Total and fecal coliform densities at all the stations sampled in
Pehsacola Bay complied with the Class III water standard, but the
mean densities for Stations P07 and P11 were noticeably higher
than the other stations sampled.
The highest geometric mean densities in Pensacola Bay were
attributed to the effluent from the Pensacola Main Street Sewage
Treatment Plant (Station P07). The geometric mean total coliform
densities of 310/100 ml and 17/100 ml were for surface and bottom
water samples, respectively. The geometric mean fecal coliform
density of 42/100 ml for the surface sample at this station
exceeded all others. These densities were well within the Class
III standard, but they were ten-fold greater than the average
mean density for other stations in Pensacola Bay.
Station P11, having the second highest geometric mean total
and fecal coliform -densities, was located at the north end of
Highway 98 bridge near the mouth of Bayou Texar. The coliform
discharge from Bayou Texar appeared to be the major contributing
factor to the higher counts at this station.
The highest densities were observed in the Escambia River and
Blackwater River as discussed previously in this report. The
geometric mean densities were 1,150/100 ml tota-1 coliform and
150/100 ml fecal coliform at the Escambia River Station (ER10),
and 1,690/100 ml total coliform and 160/100 ml fecal coliform at
the Blackwater River Station (BFEI). The highest geometric mean
density for any Escambia Bay station for total coliforms was
360/100 ml and for fecal coliforms was 31/100 ml at Station EKMP.
These high background coliform densities are similar to those
reported by West, et al. (1964); Gallagher, et al. (1969); and
USEPA (1972) for similar Gulf and East Coast estuaries.
Escambia Bay mean total coliform density easily complied with
the state standards for Class III waters, but exceeded the
maximum permissible total coliform density of 230/100 ml in
greater than ten percent of the surface samples, from areas
located in Class II waters which were closed to oyster
harvesting. Only one violation from Class II bottom waters was
observed in 1974; none were analyzed in 1973.
Total coliform and fecal coliform densities for all stations
varied from one sampling time to another. The general tendency
was for coliform densities to rise following periods of heavy
rainfall. This indicated that the high counts which were more
8-82
-------
frequently observed in the tributaries were probably due to land
runoff and swamp drainage. The high coliform counts observed in
the barge channels could possibly be attributed to the barge
traffic, either churning up sediments or from domestic waste
discharged from tugs or other watercraft. Whenever violations
of the Florida bacteriological standard for total coliforms
occurred, they did not appear to be the result of domestic waste
discharges. Stations where violations of the. Florida Standard
for total coliforms were observed seldom showed violations of the
fecal coliform standard.
PARTICUIATE MATTER
Introduction
Particulate matter diminishes light entering a body of water.
The ' light diminishing effect reduces photosynthesis which in
turn, reduces primary productivity. This can cause a reduction
of fish food organisms that can reduce fish production.
Diminishing light will also reduce the standing crop of benthic
vegetation.
Particulate matter in the Pensacola Bay system was evaluated
using turbidity. Turbidity is the degree of opaqueness produced
in water by suspended or colloidal particulate matter. it can be
produced by microorganisms, organic detritus, mineral*substances
clay and silt; and can be caused by natural erosion man-caused
erosion, and waste additions. Turbidity is not' equal to
suspended or non-filtrable solids, but is an expression of their
light diminishing effect.
Results and Discussion
The mean turbidities in Escambia, East, and Blackwater Bays
for each water quality study in 1974 followed the same trend as
the effective river discharge (Figure 8-46) . A correlation
analysis of mean Escambia Bay turbidities during all 1974 water
quality studies indicated that 72 percent of the variation in
turbidity was due to variation in effective flow of the Escambia
River (r = 0.85, p < 0.01). No correlation was found between the
mean turbidity in Escambia Bay and the average wind velocity
during each day in 1971 that a water quality study was performed.
The highest values of turbidity were measured in the bay during
the winter and spring when rainfall in the drainage basins of the
bays was high. The lowest values were measured in the summer.
Mean turbidities decreased in Escambia Bay in a seaward
direction during 1974 studies (Figure 8-47 and Appendix 8-20).
The highest mean surface and bottom turbidities of 19.7 an(j 20.8
JTU, respectively, occurred in the Escambia River (Station ER10).
Near'the 1-10 bridge (Station EKMP) , the mean turbidities of 12.9
JTU at the surface and 14.6 JTU on the bottom were lower than
river values. Turbidities were considerably diluted by the
8-83
-------
1000 •
800 •
• 600 -
*200-
30-,
-» 20-
= 10-
• » ESCAMBIA BAY
»---» BLACKWATER BAY
• •-•• EAST BAY
A',-'
JAN FEB
MAR APR MAY JUN JUL AUG SEP
1974
Figure 8-U6. Mean turbidity in Escambia, East and Blackwater
Bays during each study performed during January through
September, 197U, and total effective flow into the Pensacola
Bay system during each study.
Figure 8-U7. Mean turbidity in Escambia, East, and Blackwater
Bays during January through September, 1974.
8-8U
-------
entrance to the Escambia Bay dredged channel (Station ERPB) where
the mean surface value was 6.3 JTU and the mean bottom value was
7.4 JTU. Mean turbidities were higher on the western side of the
bay than on the eastern side. This occurred because much of the
turbidity in the bay comes from the Escambia River; thus, the
turbidity distribution is similar to the freshwater distribution
in the bay.
The mean surface and bottom turbidities in Blackwater and
East Bays were considerably lower than those in Escambia Bay, and
there was very little spatial variation throughout both bays. No
turbidity data was collected in Pensacola Bay by the University
of West Florida.
A frequency analysis for all 1974 data (Table 8-33) shows the
magnitude of the difference in turbidities in the bays. All the
turbidity distributions were squewed toward lower turbidities.
East • Bay had the lowest turbidities and Blackwater Bay was
slightly more turbid. None of 'the turbidities measured in any of
the bays during the 1974 surveys were greater than the State of
Florida water quality standard of 50 JTU. One sample in the
Escambia River, at Station EHGD, and one in the Little White
River, at Station EEEM, did exceed the turbidity standard.
Turbidity in Choctawhatchee Bay was lower than in Escambia
Bay. The mean turbidity in Choctawhatchee Bay was 2.0 JTU during
the September 12, 1974 water quality study (Figure 8-48), and the
lowest mean turbidity in Escambia Bay of 3.6 JTU occurred on May
29, 1974. Even though these mean turbidities for these dates
appear the same in both bays, turbidities in Escambia Bay were
statistically higher than those in Choctawhatchee Bay (t = 3.73,
df = 89, p < 0.01). The lowest mean turbidity in East Bay of
1.6 JTU was measured on July 9, 1974. This value is not
Table 8 - 33. Percent of the samples in turbidity ranges durinq the 197U
water quality studies.
Turbidity
JTD
0 - 9.9
10.0 - 19.9
20.0 - 29.9
greater J:ha n 30.0
Percent within range
Escambia Ray East Eay Blackwater Bay
60.7 93.9
22.7 6.1
11.7 0.0
U.9 0.0
35. U
11. 5
3. 1
1.0
8-85
-------
00
I
03
ON
\
Figure 8-18. Turbidity values in Choctawhatehee Bay on September
12, 1974.
-------
statistically different than the mean value in Choctawhatchee Bay
on September 12, 1974 (t = 0.73, df = 62. Thus, turbidities in
East and Choctawhatchee Bays were similar.
Turbidity studies were performed on August 15, 1974, and
November 20, 1974 in the drainage basins of the Escambia,
Blackwater, and Yellow Rivers to evaluate turbidity differences
within these basins. Three replicate samples were collected at a
depth of. 0.3 m (1.0 ft) at each station. The description of each
sampling station is presented in Appendix 8-21. Mean turbidities
at each sampling station during each.study are shown in Figure 8-
49 and all data is presented in Appendix 8-22. Rain occurred
during both, studies 'and the river discharges as measured at the
furthest downstream stream gages on each river .are presented in
Table 8-34. Effective river discharges on the Escambia,
Blackwater, and Yellow Rivers were almost-twice as high on August
15, 1974, than on November 20, 1974, but effective flows for both
study dates were below the mean discharges for the period of
record.
Turbidities in the Escambia River were statistically greater
during the.August 15, 1974 study than during the November 20,
1974 study (t = 2.15, df = 70, p < 0.05). The same was true for
the Yellow and Blackwater Rivers (t = 4.09, df = 64, p < 0.01).
Since flow was higher during the first study, this also indicates
that turbidity is proportional to river discharge.
Turbidities were much greater in the Escambia River than in
the Yellow and Blackwater Rivers during both studies (August 15,
1974, t = 8.34, df = 67, p < 0.01; November 20, 1974, t = 5.19,
df = 67, p < 0.01). Within the Escambia River basin, turbidities
were high in the upper reaches of the basin, and increased in the
Table 8 - 31. Effective river discharges foe Escambia, Yellow, and Blackwater Rivers.
Effective rivet discharges in /sec
(cfs)
Date .
Sugust 15, 197«
November 20, 197U
Bean period of record
Escarubia River Blackwater River
1 17
(U1UO)
67
(2370)
170
(6016) •••"•
19
(687)
13
(UU6)
23
(820)
Yellow River
51
(1797)
29
(1014)
62
(2175)
8-87
-------
E2 Station Designation
4.2 "JTU. 08/15/74
6.3 JTU. 11/20/74
of »e*ic°'
Scati CMO.OOO
Figure 8-49. Mean turbidity values in the Pensacola Bay system
drainage basin during August 15, 1974 and November 20, 1974.
8-88
-------
Conecuh River until the Florida State Line. They then decreased
in the Escambia River. A significant increase in turbidity in
the Conecuh River downstream of the Container Corporation
discharge was not observed. The higher turbidities in the upper
reaches of the Conecuh-Escambia River basin are due to erosion of
clay from the soils. Most of the drainage basins of the
Blackwater and Yellow Rivers are in areas with sandy soils. This
accounts for the lower turbidities in these rivers.
NUTRIENT LOADINGS INTO THE PENSACOLA BAY SYSTEM
Point sources of waste contributed the greatest portion of
the load to the Pensacola Bay system based^ on NPDES permit
limitations during January 1975 and 60-day, 10-year low flows in
rivers tributary to the bay system. Tributary rivers and non-
point sources of waste followed with decreased loadings. The
loadings from tributary rivers were measured at the upper limit
of saltwater intrusion.
The nutrient loadings into the bay system from all tributary
rivers were estimated from mean concentrations in the lower
Escambia River (Station ER10) during January through September
1975 and 60-day, 10-year low flows. Mean concentrations from the
Escambia River were used because the greatest amount of data was
available for this location, concentrations in all tributary
rivers were similar, and there was only slight correlation
between concentration and river inflow necessitating the use of a
mean concentration.
An analysis of U.S. Geological Survey data from the Escambia
and Yellow Rivers during January 1970 through February 1975
(Table 8-35) indicated mean total nitrogen and TOC concentrations
in the Escambia River at Century, Florida, and in the Yellow
River at Milligan, Florida were not statistically different.
Based on the same data, the mean total phosphorus concentration
in the Yellow River (0.051 mg/1) was significantly higher than
that in the Escambia River (0.032 mg/1), and the mean BODS
concentration in the Escambia River (1.0 mg/1) was significantly
higher than that in the Yellow River (0.7 mg/1). Even though
there was a significant difference between mean total phosphorus
and BOD5 concentrations, the mean values were quite close. A
November-December 1971 study comparing the Escambia River with
other northwest Florida streams indicated there was strong
evidence that the water quality of these streams was comparable,
and an analysis of historical STORET data for the same area
yielded the same conclusion (USEPA, 1972f). Based on both of the
above studies, water quality of the tributary rivers of the
Pensacola Bay system was similar.
As expected, nutrient loads in the Escambia River (Station
ER10) were lowest during low flow periods (Table 8-36 and 8-37).
These low flow periods generally occurred in late summer and
early fall when the water temperatures of the bays were . highest,
the bottom dissolved oxygen concentrations were lowest, the
8-89
-------
Table B - 35. Comparison of water 'jUality data for the "scambia Siver at Century, F lorida, and tha
Yellow liivor at Hilliyan, Florida. (Data from U. S. Geological Survsy)
Flow
( m 3/sec )
Total
Phospnorus
(mg/1)
Total
Nitro-jen
(ng/1)
3005
TOC
(fflg/l).
Escambia River
tle.iu
Maximum
Niniuun
n
r, cone. vs. flow
110
722
20
26
0.032
0.060
0.010.
20 '
-0. 16
0.555
1.4CO
0.300
15
-0. U
0.98
2.20
0.10
26
0.24
5. 1
12.D
' 0.0
20
0. 16
Jellow River
Me.in
Kaxiirum
:i iaimuin
n
r, cone. vs. flow
20
62
5
22
0.051
0.1.UO
.0 .0 1 3'
19
-0. 31
0.473
1.403
0. 179
12
-O.C3
0.68
1.60
0.30
2?
0.08
4. 25
3.00
1.00
18
Difference between
leans in rivers
calculated t
2.6«
0.5
2.1
1.2
* Difference 'between the means statistically different with yfater than 95 percent confidence.
** Correlation coefficient statistic. illy signi Eic-'intq with 95 percsnt confidence.
Table 8 - 36. Nutrient values in the Escambia River (Station EH10) by date during January through
September, 197i».
Total
Date*
1/23/74
1/23/74
i/12/74
2/12/74
3/0 5/7 a
3/0 5/7 U
3/2 7/7 U
3/27/7 It
4/16/74
4/16/74
5/0 7/7 4
5/0 7/7 U
5/29/74
5/29/7 U
• 6/1H/7U
6/1 8/7 a
7/09/7U
7/C9/74
7/30/74
7/30/7 U
8/20/7U
8/20/74
9/11/71*
9/11/71*
Flow
(m 3/sec)
333
333
737
737
226
226
203
203
506
5C6
114
114
178
178
126
126
71
71
69
69
147
147
784
781 .
Phosphorus
cone.
(mg/1)
0.051
O.C'70
0.04V,
O.C27
0.044
0.037
C.C24
0.032
0.036
C.038
0.039
0.033
0.047
0.043
0.038
O.C42
0.03C
0.033
0.021
0.028
0.044
O.C38
C.C55
0.054
load
(kg/day)
1,467
2,014
2,6 11
1,719
859
722
421
561
1,574
1,661
384
325
723
661
4 14
457
184
202
185
167
559
483
3,726
3,658
Total
Nitrogen
cone.
(ng/1)
0.500
0.503
0.5C2
0.497
0.315
0.315
0.350
0.360
0.377
0.385
0.480
0.485
0.405
0.452
0.355
0.285
0.282
0.420
0.342
0.235
0.225
0.227
0.449
0.385
load
(kg/day)
14,336
14,386
31,966
31,647
6,151
6,151
6,139
6,314
16,482
16,832
4,728
4,777
6,229
6,951
3,865
3,103
1,730
2,576
2,039-
1,401
2,853
2,383
30,414
26,079
BOD5
cone.
(mg/1)
1.6
1.3
0.7
0.8
0. 5
0.4
1. 3
1. 4
0.9
1.0
D.7
0.5
1.9
1. 6
0.8
0.9
0.5
0.4
3'. 5
0.5
0.8
0.9
3.8
1.0
load
(kg/day)
46,034
37,403
44, 574
50,941
9,763
7,81 1
22,801
24,555
39,347
43,718
6,895
4,925
29,220
24,607
8,709
9,798
3,067
2,454
2,981
2,981
10. 161
11,431
54, 190
67,738
TOC
cone.
(mg/l)
8.5
10.0
11.0
10.0
5.5
6.5
6.0
5.0
7.5
8.2
8.2
6.0
6.5
5.7
5.7
5.7
2.5
3.5
1.0
2.5
4.5
9.0
11.0
9.5
load
(kg/day)
244.555
287,712
700,445
663,606
107,395
126.922
105, 2J5
87,696
327,888
353,491
83,767
59,098
99,965
87.661
62,052
62,052
15,336
21,470
5,962
14.904
57,154
114,307
745,114
643,507
* First value for each date Is for the surface and the second value Is for the bottom
8-90
-------
chlorophyll a concentrations (phytoplankton) were highest, and
when most of the fish kills occurred. Accordingly, the
contributions from the tributary rivers during low flow
conditions (60-day, 10-year low flow) were used to calculate
river loadings and to compare them with other sources of
nutrients. The 60-day, 10-year low flow of 72 m3/sec from all
tributary rivers was also used to determine the contributions
from tributary rivers because the flushing time of Escambia Bay
is approximately 69 days at this level of inflow. Thus, the 60-
day, 10-year low flow will affect most of Escambia Bay. The
estimated loadings are shown in Table 8-37.
The percent contributions to the Pensacola Bay system from
tributary rivers, point sources under January 1975 conditions,
point sources when final permit limits are in effect, and non-
point sources are presented in Table 8-38. Under January 1975
conditions, for all parameters, point source discharges
contributed the greatest amount, with tributary rivers and non-
point sources following in decreasing order. When the final
permit limitations are in effect, the most significant source or
sources will be tributary rivers for BODS, tributary rivers and
point sources for total nitrogen, and point sources for total
phosphorus.
-he theory held by many, that point source discharges are
insignificant compared to tributary river contributions and non-
point sources, is incorrect. Even after all point source
discharges are reduced to their final effluent limitations, point
source discharges will still be the greatest contributors of
total nitrogen and total phosphorus to the Pensacola Bay system.
8-91
-------
Table 3 - 37. summary of nutrient values in the Escambia Rivsr (Station ER10) during January through
September, 1971 and estimated nutrient loads entering the Pensacola Uay system from ths Esraabia Biver
and from all rivers.
Flow ?ho
cone.
(
-------
9 - PLANKTON
PHYTOPLANKTON PRODUCTIVITY
The Escambia Bay Recovery Study (EBRS) did no specific
studies on either phytoplankton or zooplankton species in the
Pensacola Bay system. EBRS, in cooperation with the University
of West Florida, did determine chlorophyll concentrations
throughout the Pensacola Bay system from January to September
197U. There have been primary productivity studies recently by
the University of West Florida (UWF) in 1973 (Hopkins,
unpublished data) on East and Escambia Bays.
In Escambia Bay, primary productivity ranged from 0.0 to 2.98
mg C/m3 per hr, while East Bay ranged from 0.0 to 2.16 mg C/m3
per hr (Hopkins, et al., unpublished STORET data). The annual
mean for Escambia Bay was 0.68 mg C/m3 per hr while East Bay was
0.62 mg C/m3 per hr. Paired monthly means during 1973 showed no
difference between these two bays (t = 0.27, df = 14) . Monthly
data was calculated on a per hour basis and was not extrapolated
to a per day production; even so, the relationship between the
two bays is relevant and a direct comparison of their
productivities is possible. EBRS turbidity data (discussed more
fully under the water quality section) for a nine-month period,
from" January to September 1974, gave an average turbidity value
of 3.90 Jackson units for East Bay and 10.27 units for Escambia
Bay. The UWF primary productivity data was for the top meter of
the water column. Therefore, even though primary productivity
means for the surface waters of the two bays were nearly the
same, it is likely that total primary productivity, that is, the
productivity of the water column from the surface down through
the euphotic zone, was higher in East Bay since light penetration
was greater there.
Data from Port Royal Sound, South Carolina (Thomas, 1972),
for three sampling periods in 1970 averaged 0.0197 g C/m3 per hr.
This was much higher than the values from Escambia Bay. Port
Royal Sound was described as a productive estuary capable of
contributing to the growth of aquatic organisms (Thomas, 1972).
Escambia Bay was several times less productive than Port Royal
Sound. Compared to several systems throughout the Gulf coast
(Steidinger, 1973), Escambia Bay had a low primary productivity.
PHYTOPLANKTON CROP
Cell Counts
The abundance, seasonality, and spatial distribution of
phytoplankton in Escambia and East Bays has been investigated by
Hopkins, et al. (unpublished) during the year 1973. This data
indicated that the general trend in seasonal succession of
phytoplankton within Escambia and East Bays was similar.
Dinoflagellates were abundant in the late winter and early spring
months. In late spring a small blue-green alga was abundant in
9-1
-------
both bays. In early fall, diatoms were the dominant group and
they persisted well into midwinter.
Cell counts in Escambia Bay ranged from 17 to 230,000
cells/ml. The range for East Bay was 1100 to 70,000 cells/ml.
During the cooler months the counts were in the thousands/ml,
whereas in warm months the counts increased a magnitude to tens
of thousands. A student t-test indicated no significant
difference in the means of East Bay and Escambia Bay for cell
counts/ml (t = 0.87, df = 121) . Although there was not an
overall difference in cells/ml in the two bays, Escambia Bay had
a less uniform distribution. During the high river flow period,
plankton was flushed from the areas of greater freshwater influx.
ZOOPLANKTON CROP
Zooplankton was sampled by the University of West Florida six
times between February and September 1973, at seven stations in
Escambia Bay and six stations in East Bay. Averages of total
counts of organisms per m3 were 36,674 in Escambia Bay and 32,253
in East Bay. A student t-test indicated no significant
difference in these means (t = 0.67, df = 75). Also, monthly
means had no consistent trend, either between bays or with time.
No differences were noted between the bays within the dominant
groups of organisms. Acartia tonsa, a calanoid copepod,. was the
dominant organism in both bays.
CHLOROPHYLL
Introduction
Since all algae contain chlorophyll a, this pigment concen-
tration can give an insight into the relative amount of
phytoplankton standing crop. The physiological condition of the
cells determines the amount of pigment per algal cell, which
biases this method of the estimation of biomass; however, it is a
widely accepted technique for comparing phytoplankton crops in
estuarine waters. In this study, four bays were compared;
therefore, the technique has even greater validity since samples
were taken concurrently in all bays.
Methods
Water samples were taken 0.3 meters (1.0 ft) below the
surface at three-week intervals from January to September 1974,
at the stations shown on Figure 9-1. Variable volumes of water
(depending on filtering speed) were filtered through a 0.45
micron millipore filter. Residue was dissolved in 90% acetone
while cells were ground in a tissue grinder. The method used
follows Stickland and Parsons (1972) trichromatic method of
spectrophotometric determination of chlorophylls. A Beckman
Model DB-6 Spectrophotometer was used to obtain optical
absorptions. These readings were used in the SCOR-UNESCO
9-2
-------
I
CO
Figure 9-1. Pensacola Bay system stations and chlorophyll a
averages (jjg/1) from January to September, 1971 (Pensacola
Bay data from University of West Florida) .
-------
equations to calculate chlorophyll concentrations (Strickland and
Parsons, 1972). Corrections were not made for phaeopigments
during this study.
Results
Chlorophyll a concentrations in Escambia Bay ranged from 0.6
to 17.9 pg/1 during the period January to September 1971.
Seasonal trends are shown in Figure 9-2 for pooled data for all
stations in the bay. Appendix 9-1 summarizes all data for the
Pensacola Bay system for the period of study. There was no
significant difference between the upper Escambia Bay compared to
the lower bay. The upper bay average for the period was 6.7 pg/1
while the lower bay average was 6.0 M9/1- Chlorophyll a
concentrations were much higher in the bayous of the system. For
example. Mulatto Bayou concentrations averaged 16.0 vg/1 and
Bayou Texar averaged 12.0 t*g/l for the same period. The two
highest averages within Escambia Bay occurred near the outfalls
from Air Products and Chemicals, Inc. and American Cyanamid
Company. Both concentrations here were 8.0 pg/1 chlorophyll a.
Escambia and Blackwater Bays had trends toward higher
concentrations from January to September as the water temperature
rose (Figure 9-2). East Bay tended to remain around 2.5 pg/1
throughout this period except for July, August, and September,
when there was an increasing trend up to 6.0 pg/1. All three
bays had a peak in April and another peak in September.
Pensacola Bay had concentrations about equal to Escambia Bay
during the winter; however, in the summer the concentrations in
Pensacola Bay were the lowest of all four bays (Figure 9-2).
Chlorophyll a concentrations averaged 6.3 pg/1 in Escambia Bay,
4.5 pg/1 in Blackwater Bay, 4.6 ^g/1 in the Escambia River Delta,
3.5 pg/1 in East Bay, and 3.4 pg/1 in Pensacola Bay. The station
at the inlet from the Gulf (P01) averaged 3.0 \tg/1. There was a
significant difference (t = 7.45, df = 237) in the averages for
Escambia Bay and East Bay.
Chlorophyll a values for Choctawhatchee Bay were determined
for one sample per station (Figure 9-3) on September 12, 1974.
Concentrations were higher nearer the river mouth and decreased
toward the Gulf inlet. Concentrations ranged from a high of 8.0
pg/1 to a low of 0.0 pg/1 at the inlet. Concentrations were
higher near bayous and the Santa Rosa Sound. The average
concentration for Choctawhatchee Bay during this study was 4.2
pg/1.
Discussion
\
Nutrients from the industrial outfalls were stimulating
phytoplankton growth in the northeast sector of Escambia Bay
(Figure 9-1). This enrichment affected all of Escambia Bay and
caused chlorophyll a concentrations to be higher than in other
bays throughout the system (Figure 9-1) . These wastes also
entered Mulatto Bayou and caused phytoplankton bloom conditions
9-4
-------
x
a.
o
3
i
u
KEY
\
ESCAIfiBIA BAY
EAST BAY
BLACKWATER BAY
PENSACOLA BAY
\
I II
I L
J I
1/23 2/12 3/3 3/27 4/16 5/7 5/29 6/18 7/9 7/30 8/2O 9/11
1974
Figure 9-2. Chlorophyll a. seasonal concentrations In Escamblat
Bast and Blackwater Bays*
Figure 9-3. Chlorophyll a ( M«/l> concentrations In Choctawhatehee
Bay on September 12« 1974.
9-5
-------
(over 15 pg/1 [Hobble and Copeland, 1975] unpublished) that
reached nuisance levels and probably contributed to fish kills
during summer periods (Figure 9-1).
Escambia River Delta waters and Blackwater Bay.had similar
chlorophyll a concentrations (Figure 9-1) and since these waters
flow into Escambia Bay and East Bay respectively, it is likely
that concentrations in Escambia Bay would be similar to East Bay
were it not for the enrichment from industrial waste discharges.
Should industrial waste discharges cease, there would be a
dramatic decrease in phytoplankton biomass in Escambia Bay. The
high phytoplankton populations ;in Bayou Texar were the result of
domestic waste . discharges and storm drainage (Hannah, et. al.,
1973) . .Reduced flushing in both Bayou Texar and Mulatto Bayou
contribute to the eutrophication problems in these bayous and to
expedite their recovery all waste must be excluded. Limited
flushing by local rainfall is helpful but this same runoff water
has poor water quality and therefore increases enrichment. The
bayou inlets are narrow, which restricts the tidal flushing of
the bayous.
9-6
-------
10 - FISHES AND PENAEIDS OF ESCAMBIA BAY
SURVEY AND STATUS OF THE FISHES, SHRIMPS, AND FISHERIES
Introduction
Escambia Bay, the northwestern extension of Pensacola Bay, is
a polluted estuary. The discharge of industrial pollutants,
storm drainages, agricultural runoff, and the occasional overflow
of domestic sewage have created deleterious conditions in water
quality. Consequently, the stressed aquatic environment has led
to a serious decline in both sport and commercial fishery yields,
as well as to reduced production on the nursery grounds.
Data on the commercial shrimp landings document the declining
yields. For example, the penaeid shrimp fishery in Escambia Bay
declined from a high of 62,000 Ibs (heads-off weight) in 1968 to
the eventual collapse of the shrimp fishery in 1972, when no
shrimp were harvested from this bay. Commercial shrimp landings
in Pensacola Bay, which connects with lower Escambia Bay,
declined from over 902,000 Ibs in 1968 to 17,000 Ibs in 1971
(U.S. National Marine Fisheries Service, 196U-73).
Estuaries are essential for the maintenance of fishery
resources in the Gulf of Mexico. The young of numerous
finfishes, crustaceans, and other organisms inhabit low salinity
waters where there is an adequate food supply and an absence of
marine predators; thus, estuaries function as nursery grounds.
Many of these species are estuarine-dependent, in that the
critical juvenile phase of their life cycles is directly related
to the estuaries.
Previous studies on the fishes of Escambia Bay and associated
environs provided useful information on species occurrences, on
the general biology of selected species, and on a survey of
freshwater fishing yields. Unfortunately, many of these reports
were of little value in assessing changes in the abundance of
estuarine fishes because of pollution, since the baseline data
were often not in terms of catch-per-unit-effort. An inclusive
species inventory was provided by Cooley (in press) who sampled
quarterly with a bottom trawl at two stations in Escambia Bay
over a three-year period. The food habits, migration, and
relative abundance of the Atlantic croaker (Micropoqon undulatus)
were documented for Escambia Bay (Hansen, 1969). Livingston, et
al., (1972) investigated the cause of fish kills in Mulatto
Bayou. Aspects of the seasonality and relative abundance of
young Gulf menhaden (Brevoortia patronus) were investigated in
Little East" Bay and Pensacola Bay (Tagatz and Wilkens, 1973).
Freshwater and euryhaline fishes of the Escambia River system of
Florida and Alabama, including the tidal waters at the mouth of
the river, were inventoried by Bailey, Winn, and Smith (1954).
In 1973, members of the Bream Fishermen Association conducted a
10-1
-------
creel census on the Escambia River sport fishery (Hixon, Niven,
and Hopkins, 1971). It is anticipated that this data base will
be compared with a similar census in the future to evaluate the
subsequent role of pollution on the freshwater fishery. Early
surveys of the fishes of the Pensacola area were provided by
Jordan and Gilbert (1882), Bollman (1886), Gilbert (1891), and
Evermann and Kendall (1900) .
It is well-established that polluted waters directly
influence the species composition, distribution, and abundance of
estuarine fishes and shrimps. Shifts in population structure can
be employed to detect environmental changes if the population
levels are assessed against an adequate data base. The
objectives of this investigation were: (1) to develop baseline
data on the fishes and shrimps; (2) to relate the distribution of
fishes to various environmental variables; and (3) to assess the
present status of fish and shrimp populations in the bay. Data
obtained from this study will provide background information for
the development of fishery management recommendations to
accelerate the utilization and recovery of the bay fisheries.
Material and Methods
Sampling Stations, Procedures, and Gear
Fish collections were taken every two months at eleven
trawling stations and four seine stations in Escambia Bay and
adjacent waters. Designation and location of the trawling
stations were as follows: Station I—Delta tributary (Simpson
River), Station II AND III—upper reaches of Escambia Bay,
Stations V and VI—middle reaches. Stations VII and VIII—lower
reaches, Stations IV and IX—bayous (Mulatto and Texar), and
Stations X and XI—East Bay. Seine stations were at Floridatown
(Station A), Mulatto Bayou (Station B), eastern shore in middle
reaches (Station C), and Hernandez Point (Station D) . Sampling
stations and areas are depicted in Figure 10-1.
To standardize trawling effort, a similar procedure was
followed for all collections. The otter trawl was towed in a
straight line for a 10-minute period at a speed of 2000 rpm. At
the completion of the tow, the trawl was retrieved by hand. Two
tows were taken at each trawling station.
Water temperature and salinity were taken with a salinometer
for each collection. Surface and bottom readings were taken 0.3
m (1.0 ft) beneath the surface and 0.3 m above the bottom,
respectively.
The trawling gear consisted of a 4.9-m (16-ft), semi-balloon,
otter trawl (Marinovich Trawl Co., Biloxi, Miss.) that was
constructed of 2.54-cm, bar-mesh netting with a 0.61-cm, bar-mesh
innerliner in the codend. The trawl was attached to a 30.5 m
(100 ft) tow line.
10-2
-------
ico
GUI'
Figure 10-1. Study area in Escambia Bay and adjacent waters,
-------
The 21.3 m (70 ft) bag seine was constructed of a 6.U-mm (1/U
inch) , bar-mesh netting in the wings and a center bag of 3.2-nun
(1/8 inch) t bar-mesh netting. The seine was 1.2 m (H.Q ft) in
depth.
Fish collections were taken during the biological year, which
extended from October 1973 through September 197t». Large
specimens were processed in the field, whereas the more numerous
small individuals were preserved in a 10 percent solution of
formalin in sea water for subsequent sorting, counting, and
identification in the laboratory. All length measurements were
of total length (tip of snout to the end of compressed caudal
fin) taken to the nearest 1.0 mm, unless noted otherwise.
The names of fishes and their phylogenetic order follow the
recommendations of the American Fisheries Society (Bailey, et
al., 1970).
Community Structure
Species diversity indices provide a means of assessing the
effects of environmental stress or pollution on the structure of
fish communities. Also, information on the number of individuals
per species is reduced to a single value, which facilitates the
analysis of the catch data.
Diversity was calculated using the Shannon- Weaver formula
(Shannon and Weaver, 1963) . The diversity of the catch sample
from the population was estimated by (H1) :
N N
where N-j is the number of individuals in the i— species and N is
the total number of individuals in the catch.
Since Shannon-Weaver values may increase in response to
similar increases in both number of species and relative
abundance or equitability of species, these two components are
usually calculated separately. Thus, the "species richness"
(Margalef, 1969) component of diversity (D) was calculated by the
following equation:
D = (S-1) / loge N,
where S represents the number of species and N is the number of
individuals. This formula gives more weight to the number of
species than to the number of individuals. The "evenness" index
(J) , developed by Pielou (1966) , is a measure of relative species
abundance that was calculated by:
J = H'/ H max = H1/ loge S,
10-4
-------
where loge S is the maximum value of H1 and H1 = H1 max when all
species are equally abundant. Thus, the maximum value of J is
1.0. Similar indices, particularly the Shannon-weaver formula,
were employed in assessing the pollution-stressed, fish
communities in the estuarine waters of Patuxent River, Galveston
Bay, and Mystic River. ...
Fish kills
Historical r.ecprds on, the fish kills in the Pensacola Bay
system were based on our interpretation of -the unpublished log
maintained by Mr. William T. Young, Florida State Department of
Environmental Regulation (FDER). Starting in ; 1969, all .fish
kills observed by personnel of Florida Marine Patrol, by members
of Bream Fishermen Association in Pensacola, .and by concerned
citizens were reported to FDER. Subsequently, a biologist,
usually Mr. Young, performed an on-site inspection. In addition,
personnel of the Escambia Bay Recovery Study (EBRS) investigated
kills that occurred from August 1973 through December 1974. In
this report, chronic kills, which often persisted for several
days or on occasion, even weeks, and multiple reports of the same
event were tabulated as a single fish kill.
Assessing the number of fishes involved in an extensive kill
in the estuary is often a difficult task due to the vast areas
and often remote shorelines. More accurate estimates of the size
of the kills came from the bayou habitats than from those in the
open bays.
Commercial landings
Data on the commercial landings from Escambia County and
other Florida areas were obtained from reports of the Florida
Department of Natural Resources (1964-72) and the U.S. National
Marine Fisheries Service (1973). Information on commercial
shrimp catches from specific bays was provided by U.S. National
Marine Fisheries Service (1964-73).
Results , .
Relative Abundance
A total of 79,372 individuals, representing 57 species and 32
families, was taken in the bimonthly collections. Of the total
catch, 69,876 individuals, or 88 percent, were taken in the otter
trawl collections; the remainder were captured with -the seine
(Table 10-1). An average of 568 individuals was taken per trawl
sample during the year. , Bimonthly distribution of the total
otter trawl effort during the survey is tabulated by station and
by area in Appendix 10-1.
In decreasing order of abundance, the most numerous species
were bay anchovy, (Anchoa mitchilli), Gulf menhaden (Brevoortia
patronus ), spot (Leiostomus xanthurus), Atlantic croaker
10-5
-------
Table 10-1. Summary of the number of fisnes caotureu with otter trawl and seine during the bimonthly survey
in Escambia Bay durinn 197.1 throuqh 1974.
Species
Atlantic stingray (Uasyatls sablna)
Rluntnose stingray (Oasyatls sayi)
Longnose gar (Leplsosteus osseus)
Ladyfish (Elops saurus)
Gulf menhaden (Brevoortia patronus)
Scaled sardine (Harengula pensacolae)
Threadtin shad (Dorosoma petenense)
Striped anchovy (Anchoa nepsetus)
o Bay,anchovy (Anchoa mitcnilll)
"* Inshore llzardflsh (Synodus toeteus)
Channel cattish (Ictalurus punctatus)
Sea catfish (Arlus fells)
Gafftopsall catfish (Bagre marinus)
Gulf toadflsn (Opsanus beta)
Atlantic needlefish (Strohgylura marina)
Sheepsnead minnow (cyprinodon variegatus)
Gulf Killitlsh (Fundulus grandls)
Longnose Killlflsh (Fundulus slrcilis)
Rainwater killiflsh (Lucanla parva)
Tidewater sllverslde (Menldla beryllina)
Chain Pipefish (Synqnathus loulslanae)
Gulf pipefish (Syngnathus scovelll)
Largemouth bass (Mlcropterus salmoides)
• » J=juvenile A=adult
Total trawl
catch
Number
123
2
2
2*
H
9,305
255
15
4,693
30,566
11
5
123
1
1
0
0
0
0
0
6
1
1
0
Total seine
catch
ot samples
24
0
0
0
2
5,499
20
0
2
1.448
4
0
2
0
0
3
6
70
10
2
942
0
0
2
Total catch
2
2
29
10
14,804
275
15
4,695
32,014
15
5
125
1
1
3
6
70
10
2
948
1
1
2
Life history stage*
JA
A
A
J
J
J
A
JA
JA
JA
A
JA
4
A
,1
JA
JA
JA
A
JA
J
A
JA
-------
Table 10-1 (cent). Summary of tne number of fishes captured with otter trawl and seine during the bimonthly
survey In Escamoia Bay during 1973 through 1974.
Species
Crevalle Jack (Caranx hippos)
Atlantic bumper (Chloroscombrus cnrysurus)
Leather Jacket (Ollgoplltes saurus)
Lookdovn (Selene vomer)
Mangrove snapper (Luthanus qrlseus)
Spotfln mo-Jarra (Euclnostomus arqenteus)
Sheepshead (Archosargus probatocephalus)
Pinflsh (Lagodon rnomboldes)
silver perch (Bairdiella chrysurfs)
Sand seatrout (Cynosclon arenarlus)
Spotted seatrout (Cynoscion nebulosus)
Spot (Leiostomus xanthurus)
Southern klngfisn dent iclrrhus amerlcanus)
Gulf Kingfish IMent iclrrhus llttoralls)
Atlantic croaker (Mlcropogon undulatus)
Atlantic spadeflsn (Chaetodipterus faber)
Striped mullet (Mugil cenhdlus)
Atlantic threadfln CPolydactylus octonemus)
Violet goby (Gobloides broussonnet i )
Sharptall goby (Coblonellus hastatus)
Naked goby (Goblosoma ooscl)
Code goby (Gobiosoma robustum)
Freshwater goby (Goblonellus shufeldtl)
Atlantic cutlassflsh (Trlchlurus lepturus)
Spanish mackerel (Scomboromorus maculatus)
Harvestfish (peprllus alepldotus)
Bighead searobln CPrionotus tribulus)
Bay Mhift (Cithar Icthys spllopterus)
Fringed tlounder (Ktroous crossotus)
Southern flounder (Parallchthys lethostlgma)
HogchoKer (Trlnectes maculatus)
Blackcheek tonguetlsn (Symphurus plaglusa)
Least puffer (Sphoeroldes parvus)
Striped burrtlsn (Cnllomycterus scnoepfl)
TOTAL
Total trawl
catch
Dumber
123
23
6?5
3
4
0
113
11
25
84
1 ,587
11
13,826
12
5
7,915
1
24
467
1
17
0
0
1
25
3
20
2
12
10
t
8
1
9
1
69,676
Total seine
catch
of samples
24
0
299
5
0
2
61
0
64
0
33
2
171
1
0
488
0
317
10
0
0
1
1
1
0
0
0
0
I
1
0
1
0
25
0
9,496
Total catch
23
924
a
4
2
. 174
11
89
84
1 ,620
13
13,997
13
5
8,403
1
341
477
1
17
1
1
2
25
3
20
2
13
11
6
9
1
34
1
79,372
Life history staye*
J
J
J •
J
JA
JA
A
JA
JA
JA
JA
JA
JA
J
JA
J
JA
JA
J
JA
J
A
A
JA
J
J
J
JA
JA
JA
JA
J
J
J
J=]uvenlle - A=adult
10-7
-------
(Micropogon undulatus), striped anchovy (Anchoa hepsetus), sand
seatrout (Cynoscion arenarius), tidewater silverside (Menidia
beryllina), and Atlantic bumper (Chloroscombrus chrysurus) (Table
10-1). The bay anchovy, representing 40 percent of the total
catch, was the most abundant species in Escambia Bay. The other
seven species accounted for 57 percent of the year's total catch.
Members of three families of fishes represented 96 percent of
the total catch with both trawl and seine, and, thus, dominated
the catches from Escambia Bay. The most abundant families were
Engraulidae (anchovy) , Sciaenidae (drum) , and Clupeidae
(herring). Anchovies, composed of two species, represented
nearly half of the total catch. The sciaenids were represented
by seven species and accounted for 30 percent of the total catch,
while the three clupeid species represented less than one-fifth
of the catch. The other 29 families, represented by 45 species,
accounted for the remaining four percent of the total catch.
Distribution by Area
Among the five study areas, the largest catches-per-unit-
effort (trawling) occurred at the bayou and river stations (Area
4) (Figure 10-2). An annual mean catch of 924 fishes was taken
in the waterways adjacent to the bay which represented a two- to
three-fold increase over the other areas. In the open waters of
Escambia Bay, the annual mean catch ranged from 326 to 498
individuals (Areas 1-3). The largest catch occurred in the upper
reaches of the bay (Area 1) in the vicinity of the industrial
outfalls. East Bay stations served as a control, since this bay
was considered to be less polluted than Escambia Bay. The annual
trawl catch of 535 fishes in the control area (Area 5) surpassed
the returns from the three areas in Escambia Bay (Appendices 10-2
and 10-3) .
Variations in catches among estuarine areas were real
differences as indicated by ANOVA (F = 3.27, p < 0.05).
Differentiation of group means (Student-Newman-Keuls multiple
range test) revealed that the increased catch in the bayous (Area
4) was significantly different from those "of other areas. The
catches from the three open water areas in Escambia Bay were
statistically similar to each other, as well as to the control
area in East Bay. Area comparisons were shown diagramatically as
follows:
Area and rank 321 5 4
Annual mean catch 325.9 481.3 498.5 534.1 923.8
Means enclosed by the range line were not significantly different
from each other; means not underlined were significantly
dissimilar. It was conclusively shown that the bayous were the
most productive waters in the estuary.
10-8
-------
E
3
o
u
20 -
1000 -I
800 -
600 -
400 -
200 -
N- 69,876
n
12 3 4 5
AREA
Figure 10-2. Annual mean catch of fishes per trawl sample by
number and by percent for each study area, 1973-197U.
10-9
-------
Peak bimonthly catches varied among the five areas during the
biological year. During October and August, the trawl catches in
East Bay (control) exceeded the return from the other areas
during October and August (Appendix 10-3). Conversely, the
catches in Escambia Bay (Area 1-3) in December, February, and
June generally exceeded the catches from the control area (Area
5). December catches were composed largely of pelagic species,
whereas in June, the majority of fishes were those that typically
inhabit the benthic environment. In August, low levels of
dissolved oxygen (0.0 to 6.5 ppm) near the bottom were
responsible for the smallest catches of the year at the stations
in Area 1-3.
Among the four seine stations, the largest annual catch (945
individuals) occurred at Station A (Area 1) largely due to the
occurrence of several menhaden schools at the seining site in
October 1973 (Appendices 10-4 and 10-5). Disregarding the catch
of juvenile Gulf menhaden, there essentially was no difference in
the catches among these stations. Seine collections supplemented
the list of species from the shallow shoreline habitat, but these
data were not employed in making comparisons on catch-per-unit-
effort with other estuaries.
Seasonality
Usually, the seasonal occurrence of two or three species
dominated the bimonthly trawl collections (Appendix 10-3). For
instance, incoming postlarval and juvenile Gulf menhaden and the
resident bay anchovy accounted for 79 percent of the total catch
in February. In June, juvenile spot and Atlantic croaker were
the most abundant fishes in the bay and represented more than
half of the catch. Juveniles of these two species, which were
members of a new, incoming year-class, were first captured in
December.
Among the clupeid fishes, the Gulf menhaden was seasonally
dominant in the bayou and delta tributary stations (Area 4) from
February through June (Appendix 10-3). Young menhaden, upon
entering the estuary, initially seek out brackish waters within a
salinity range from 0.0 to 5.0 ppt.
The major movement of larval fishes from the offshore
spawning grounds in the Gulf of Mexico to Escambia Bay generally
commences in November with the greatest influx occurring from
January through March. Because of prolonged and often
overlapping spawning seasons, young of various incoming year-
classes reached their greatest abundance on the nursery grounds
in early summer. Coinciding with the progressive decrease in
water temperatures from October through December, most of the
juveniles have migrated back to Gulf waters. This sequence is
also applicable to most estuarine fish species across the
northern Gulf of Mexico.
10-10
-------
Distribution Records
There were several new distribution records for the
ichthyofauna of the Pensacola Bay system, as well as for Escambia
Bay. Fishes collected for the first time from the estuarine
waters near Pensacola included the bluntnose stingray (Dasyatis
sayi)r violet goby (Gobioides broussonneti) , freshwater goby
(Gobionellus shufeldti), pink wormfish (Microdesmus longipinnis)
(See Chapter 11), and least puffer (Sphoeroides parvus). It
should be noted that Bailey, Winn, and Smith (1954) collected
Gobionellus shufeldti in the lower freshwater portions of the
Escambia River. In addition, the single specimen of the violet
goby represented the first time that this species had been taken
along the west coast of Florida. This specimen, which measured
287 mm SL, is cataloged as Accession No. 1.9.13 in the museum of
the . U.S. Environmental Protection Agency, Gulf Breeze
Environmental Research Laboratory, Gulf Breeze, Florida.
Fishes not previously reported from Escambia Bay included the
gray or mangrove snapper (Lutjanus griseus) , southern kingfish
(Menticirrhus americanus), Gulf kingfish (M. littoralis) ,
Atlantic spadefish (Chaetodipterus faber) , guaguanche (Sphyraena
guachancho) (see following section), Atlantic treadfin
(Polydactylus octonemus, bighead searobin (Prionotus tribulus),
fringed flounder (Etropus crossotus), and striped burrfish
(Chilomycterus schoepfi).
Community Structure
Among the five areas of the estuary, average species
diversity values, as calculated from the trawl data and expressed
by the Shannon-Weaver formula (H1), ranged from 0.707 to 0.923.
The lowest annual diversity occurred in the upper reaches of
Escambia Bay (Area 1), whereas the highest diversity was recorded
from the control area (Area 5) in East Bay. Apparent
dissimilarities among at least some of the areas were not
statistically significant, as indicated by an ANOVA test (F =
0.922, p > 0.05).
Seasonal fluctuations in H1 were apparent with the highest
readings (mean, 1..100) occurring in the summer months and the
lowest (mean, 0.540) in the fall. The spring (April) and summer
(June and August) and the fall (October) and winter.(December and
February) diversity values formed two homogeneous groups which
differed significantly from each other (Table 10-2). Seasonal
shifts were largely related to the influx of larval and juvenile
fishes (both species and numbers) into the estuary during the
spring and the exodus of young fishes in the fall. Annual cycle
of H1 from three habitats (Escambia Bay, Bayous and River, and
East Bay) paralleled each other (Figure 10-3).
Past pollution studies have established, as a general rule,
that with an increase in distance from the point sources, there
is a corresponding increase in diversity, i.e., community
structure. Although the H1 values from the three stations on the
10-11
-------
lablt 1C - 2. Seasonal means and significance of species diversity
indices as determined by Student-Neu;i>.an-Kauls multiple range test,
Means not underlined are significantly different from each other
at tha 95 percent level of confidence.
liversity index
H'
E
J
Fall
0.5UC
0 . 6 1 b
0.365
Winter
0.599
0 . rf 1 tt
0.351
Spr iny
1 .056
0.71J5
0.606
Summer
1.
1.
0.
1-::-
132
56U
eastern side of Escambia Bay were homogeneous, a plot of the
annual mean values showed the presence of a diversity gradient,
which increased from a value of 0.76 in the upper bay to 0.98 in
the lower bay. The H1 values of stations III, VI, and VIII, and
the distance of these stations from the discharge points, are
plotted in Figure 10-4 with statistics on sampling variations.
Presumably, the inhibitory or toxic effects of industrial wastes
in the upper bay were responsible for the depression of species
diversity.
"Species richness" diversity (D) is more a measure of the
addition or subtraction of species than of changes in abundance.
Thus, seasonal movements should be reflected more often in D,
than in H1, values. This interpretation agrees with the
observations of McErlean, et al. (1973).
The seasonality of D was shown by the low values in the
winter which steadily increased during the spring and summer and
peaked in the summer (Figure . 10-5). Multiple range tests showed
that the fall through winter seasons were homogeneous and
significantly different from the summer period (Table 10-2).
"Species richness" values for the three areas of Escambia
Bay, bayous, and East Bay did not differ significantly from each
other. However, environmental stress in Escambia Bay may account
for the lower species values in that bay in comparison to East
Bay.
The "evenness" index (J) in regard to the three estuarine
areas was non-significant. However, the J values tended to be
higher in East Bay than in Escambia Bay and in the bayous (Figure
10-6) .
10-12
-------
UJ
_J
<
>
X
1.40 -
1.20-
1.00-
0.80-
0 0.60H
0.40-
0.20
ESCAMBIA BAY
EAST BAY
BAYOUS AND
RIVER
OCT DEC
i
FEB
APR
JUN AUG
MONTH
Figure 10-3. Temporal distribution of species diversity index
(H1) in three estuarine areas, 1973-1974.
10-13.
-------
1.5-
1.2-
>-
H
£ °-9'
UJ
>
0.6-
z
UJ
5 0.3-
0.0-
Station vni
Station ~P"T
Station TTT
I I
0 8
DISTANCE FROM POLLUTION SOURCE(km)
16
Figure 10-4. , Relationship between species diversity (H1) and
distance of three stations (1.6 km = 1 mile) from major point
sources of pollution in Escambia Bay.
1.40 n
I.20-
I.OO-
0.80-1
x
Ul
a
z
~ 0.60H
0.40-
0.20
--'•£
A-* -•••
ESCAMBIA BAY • •
EAST BAY A-----A
BAYOUS AND g -
RIVER
OCT DEC FEB APR
JUN AUG
MONTH
Figure 10-5. Temporal distribution of species diversity index
(D) in three estuarine areas, 1973-1974.
10-
-------
The seasonal aspects of "evenness" index (J) were apparent,
with the lowest values occurring in the fall and winter and the
highest in the spring and summer (Table 10-2). Thus, the
relative species abundance was significantly different during the
warm months in comparison to the colder periods.
Seasonal increases in both the D and J indices paralleled
similar changes in H* diversity. It was evident that the higher
H1 values reflected increases in both the number of species, as
well as their relative abundance. This observation is contrary
to those of Dahlberg and Odum (1970), who, during a survey of the
fishes in a Georgia estuary, found that "species richness" (D)
was homogeneous with respect to seasons. Along the Gulf Coast,
both juvenile and adult fishes evidently exhibit stronger
migration responses than do the Georgia species.
.Environmental Relationships
It is always of interest to inquire into the possibility that
the distribution of fishes may be influenced by various
environmental factors. For instance, fishes must be able to
tolerate continual shifts in salinity due to tidal flow. At the
time of sampling with the otter trawl, salinity values ranged
from 0.0 to 32.0 ppt. The lowest salinities occurred in February
and April in the bay due to heavy rains; the highest salinities
were recorded in December. Freshwater flow from the Escambia
River and delta tributaries influences the salinity gradient,
which gradually increases from the upper to the lower reaches of
the bay. Erratic catches of estuarine fishes at Station I near
the mouth of the Simpson River were attributed to abrupt changes
from highly saline conditions in December to freshwater
conditions in February and April. Salinity and temperature
values at four typical trawling sites (Stations III, IV, VI, and
VIII) are depicted in Figure 10-7.
Environmental variables (bottom readings) consisting of
salinity, temperature, sediment organic content, principal
nutrient index (PNI) , and dissolved oxygen were tested
statistically against the numerical catch. None of these six
variables was significantly correlated with fish numbers. The
fact that salinity has no significant influence on the total
distribution was not entirely unexpected, since most estuarine
fishes are euryhaline, i.e., they possess physiological
adaptations which permit survival during wide fluctuations . in
salinity/
Among the above variables, species diversity (H1) was
significantly correlated only with PNI (r = -O.U70, p < 0.01) and
temperature (r = 0.327, p < 0.01). Water temperatures paralleled
the seasonal cycle of H1 diversity. The "principal nutrient
index" (PNI) combined total nitrogen, total phosphorus, and total
organic carbon into a single value (Refer to Chapter 8). The
presence of a high PNI had a negative effect on species
diversity, whereas a low PNI improved Hf. Multiple regression
10-15
-------
I.OOn
0.80-
UJ
0.60-
x
UJ
o 0.40H
0.20-
0.00
OCT DEC
ESCAMBIA BAY
EAST BAY
BAYOUS AND
RIVER
I
I
FEB APR
MONTH
JUN AUG
Figure 10-6. Temporal distribution of species diversity index
(J) in three estuarine areas, 1973-1974.
10-16
-------
30-
UJ
< 20
IT
llJ
Q.
2
UJ
10
TEMPERATURE • •
SALINITY A---A
STATION HI
OCT DEC FEB APR JUN AU6
MONTH
- 30
a.
a.
-20 —
- 10
30-
u
o
< 20
IT
HI
Q.
2
I 0
TEMPERATURE •—
SALINIT Y *--•
STATION TTT
OCT DEC FEB APR
MONTH
JUN AUG
- 30
a.
-20—
- 10
30-
Ul
cc.
< 20
cc.
UJ
0.
2
Ul
I 0
TEMPERATURE
SALINITY
STATION
OCT DEC FEB APR JUN AUG
MONTH
- 30
a.
a.
20 —
h 10
to
30-
a:
LU
a.
2
UJ
20-
10'
TEMPERATURE
SALINITY
STATION 31
i I I I I I
OCT DEC FEB APR JUN AUG
MONTH
- 30
a.
a
- 2 0 —
>-
t-
- 10
to
Figure 10-7. Water temperature and salinity readings on the
bottom for trawl stations III, vi, and VIII in the open
waters of Escambia Bay and Station IX in Mulatto Bayou, 1973-
1974.
-------
analysis revealed that nutrients contributed 42 percent to the
variance of species diversity and temperature contributed 24
percent. The remaining 34 percent of the variance was related to
undetermined factors, such as biological interactions.
Shrimp Distribution
During the survey in Escambia Bay, the penaeid catch was
composed of 75 percent brown shrimp (Penaeus aztecus), 17 percent
white shrimp (P. setiferus), and 8 percent pink shrimp (P=
duorarum) (Appendix 10-6). Brown and white shrimp are also the
dominant species in other estuaries of the northern Gulf. The
low percentage composition of pink shrimp in our catches was
expected since the Pensacola area is on the northern fringe of
its distribution. Major concentrations of pink shrimp are
located off the southwestern coast of Florida (Farfante, 1969).
The average sample catch was 3.9 penaeid shrimp per trawling
effort during 1973-1974. Again, as in the case of the abundance
of fishes, the largest collections were taken in the productive
bayous (Area 4) with an average catch of 7.0 shrimp per trawl
sample (Figure 10-8). However, none of the catches among the
five areas (Area 1-5) was statistically different from each other
(F = 1.84, p > 0.05). The homogeneous catches from the upper,
middle, and lower reaches of Escambia Bay indicated that
distribution of the shrimp was not related to the major point
sources of pollution in the upper bay.
Shrimp were most abundant in June when the average sample
catch was 10.3 individuals (Appendix 10-7). In fact, over half
the total shrimp catch was caught during the June survey, which
coincided with the peak bimonthly catch of fishes.
Commercial shrimp landings provide an indirect method of
evaluating past and present conditions within a given bay and
among bays. Since the bottom area of various bays differ, the
only valid comparisons are provided on a catch per-unit-effort
basis; in this instance, the calculated poundage per trip. A
single trip is reported for each voyage. Pounds of shrimp are
reported as heads-off weight (U.S. National Marine Fisheries
Service, 1964-73).
In the estuarine waters near Pensacola, the shrimp landings
declined sharply in 1969 and collapsed in Escambia Bay and East
Bay in 1970. In Escambia Bay, the annual five-year catch
decreased from 150 pounds per trip during 1964-68 to 57 pounds
during the 1969-73 period, a decline of 62 percent (Appendix 10-
8). During the same period, the number of fishing trips dropped
by nearly two-thirds. In both East Bay and Pensacola Bay, the
average catch per trip declined by 94 and 83 percent,
respectively, during the second five-year period compared with
the 1964-68 period (Appendices 10-9 and 10-10). The total value
of the shrimp catch in the Pensacola Bay system decreased from
10-18
-------
O
O
10 -i
8 -
o
I
z
< 6 H
4 -
2 -
N=482
3
AREA
200-1
100-
Choctawhotchee Bay
73
Figure 10-8* Average catch of penaeid
shrimp per trawl sample (catch—per—
unit-effort) for the various
estuarine areas in Escambia Bay?
1973-1974.
Figure 10-9* Average catch of penaeid
shrimp per commercial fishing trip
Pensacola Bay system and
Choctawhatchee Bay (control)t 1964-
1973.
-------
342,421 dollars per year (1964-68) to 89,352 dollars per year
(1969-73) , an average decline of 74 percent (Figure 10-9) .
The decreased yields apparently were not a reflection of weak
year-classes, since the annual catch per trip in Choctawhatchee
Bay remained essentially unchanged between the five-year average
catch in 1964-68 and in 1969-73 (Appendix 10-11). Choctawhatchee
Bay, which served as a control area, is a relatively non-polluted
estuary about 40 miles east of Pensacola. Thus, the decline in
the commercial catch in the Pensacola Bay system was attributed
to the polluted status of the bays.
Fish kills
Recurring fish kills have occurred in the bays, bayous, and
rivers in the Pensacola Bay system since the late fifties. In
the five-year period from 1970 through 1974, 166 individual kills
were recorded, mainly from estuarine waters. Of this total, 81
(49 percent) of the fish kills occurred in the Escambia Bay sub-
system, 15 (9 percent) in the East Bay sub-system, and 70 (42
percent) in the Pensacola Bay sub-system (Table 10-3 and Figure
10-10).
Traditionally, the most frequent kills have taken place in
the eutrophic waters of Escambia Bay and contiguous waters.
Since 1970, 30 kills (37 percent) occurred in the open waters of
the bay, while the remainder (63 percent) took place in a total
of 13 separate protected areas adjacent to the bay (Table 10-3).
For instance, nearly one-fourth of the kills in the Escambia Bay
sub-system occurred in Mulat-Mulatto Bayou complex, which is near
the industrial outfall area. Semi-enclosed bodies, such as this
bayou complex, often have restricted entrances which tend to
impede water circulation and confine the buildup of pollutants to
the waterway.
During the past five years (1970-74), more than half of the
fish kills occurred during the summer months and nearly two-
thirds of the kills happened from July through September
(Appendix 10-12). The seasonal increase in the temperature of
the waters coincides with the frequency of kills. High
temperatures accelerate metabolic rates and lower dissolved
oxygen levels, which create additional stresses on the aquatic
environment. Conversely, few kills (less than two percent) were
recorded during the cold winter months (December through
February) .
Pollution-caused fish kills have been attributed to excessive
levels of nutrients, toxic metals, sewage, pesticides, and other
industrial by-products. Eutrophication stimulates high algal
production (or blooms) during the summer which, in turn, often
causes the depletion of dissolved oxygen concentrations during
the night. Low dissolved oxygen levels were believed to be the
main cause of death, particularly among menhaden. Other kills
were attributed, either alone or synergistically, to industrial
10-20
-------
Table 10 - 3. Temporal and spatial distribution of fish kills in the Pensacola Bay
system duriny 1970 through 197U.
location J 1970 1971 1972 1973 197U Total
Escairbia Bay subsystem
Esc iira bi a'' Bay
Fscd'mbia Kiver '
Thompson Bayou
Governors Bayou
Saultsman Bayou
Dead Siver
Simpson River
Bass Hole Cove
Judges Bayou
Mulat Bayou
Mulatto Bayou
Trout Bayou
Indian Bayou
nacoon Bayou
Subtotal
East Bay subsystem
East Bay
Blackwater Bay
Littla East Bay
bellow Siver • ••
East Bay aiver
Subtotal'
Pensacola Bay subsystem
Pensacola iiay
Bayou Texar
Bayou Chico
Star Lake
3ayou Grande
Hoffman Bayou
Woodland 3ayou
Gilinore Bayou
Santa Rosa Sound
8
0
1
0
C
1
C
2
. 1
. 6
' 4
7
2
3
~35
0
0
C
0
0
~~o .
C
4
8
' 0
• 3
2
3
1
C
11
^
0
1
2
0
1
5
4
2
f\
0
o . -
3
~29
0
0
0
D
r\
"o
2
1
1
.**.
1
2
0
2
4
2
1
. ' 0
n •
.j
r\
0
0
0
0
1
1
0
0
c
"~5
3
5
, 2
. 1
2
"3;
3
' 6
2
0
. 3
2
0
0
1
3
. 0
0 .
0
c
0
•\
0
J •
1
2
L
. 1
7
7
?
0
1 : *^
j
.3
j
2
1
1
2 '
0
1
1
0
4
3
0
C
0
. 0
0
0
0
0
1
1
2 v
?
?
~5
2
o
;- 3
'y
0
2
1
0
2
<**
1 '
0 .
f\
6
3
30
1
1
1
2
1
1
1
5
11
3
7
3
3
~aT
5
5
2
1
2
"15
a
12
1 4
2
8
7
4
3
12
Subtotal 21 13 17 12 7 - - . 70
lotal 56 42 35 19 14 166
10-21
-------
o
I
K)
to
Hoffman Boyou
Woodland Boyou
Gilmore Bayou
Figure 10-10. Location of fish kill sites in the Pensacola Bay
system, 1970-1974.
-------
chemicals, pesticides, and other toxic substances. Hansen and
Wilson (1970) found that residues of DDT and its metabolites (ODD
and DDE) sometimes reached levels up to 1.3 ppm in many estuarine
fishes from Escambia Bay and Pensacola Bay. Determination of the
exact cause of fish kills in Bayou Chico was compounded by
stresses due to the presence of phenols, oils, resins, and heavy
metals. The major pollutant in Bayou Texar was domestic sewage
which had repeatedly overflowed from an upstream lift station,
but runoff from residential lawns and from nearby shopping center
parking lots also contributed stresses.
In 1972 in Escambia Bay, a chronic fish kill, mainly
menhaden, was attributed to a nonhemolytic streptococcus
infection (Plumb, et al., 1974). They felt that environmental
stresses had lowered the resistance of the fishes, thereby
increasing their susceptibility to infection. No characteristic
symptoms of this streptoccocal disease, such as saddle-shaped
discolorations on the dorsal and lateral surfaces of the fishes,
were observed during any of the kills in 1973 and 1974. Although
bacterial and parasitic infections may at times cause death in
isolated fishes, these organisms are seldom the cause of large-
scale kills in nature.
Numerous dead and dying fish and crustacean species were
observed during various kills. Most mortalities were multi-
species kills. However, deaths of Gulf menhaden, often
mistakenly called the alewife in the Pensacola area, occurred in
more fish kills than any other species. In fact, many extensive
kills in which thousands of individuals died, might more aptly be
called "menhaden kills." The estuarine-dependent nature of this
species, its planktonic food habits, preference for low salinity
waters, schooling behavior, and apparent inability to withstand
moderately low levels of dissolved oxygen for short periods, are
conditions that contribute to the concentration of menhaden in
bayou areas, where the majority of kills have occurred since
1970. Other species frequently occurring in various kills
included striped mullet, Atlantic croaker (locally known as
ronker), spotted seatrout, spot, pinfish, sea catfish,
sheepshead, crevalle jack, sand seatrout, tidewater silverside,
bay anchovy, various flounders, and shellfishes, such as blue
crab and penaeid shrimps. During the period from 1968 through
1971, large adult fishes, transients from the Gulf, such as the
bluefish (Pomatomus saltatrix), crevalle jack, ocean sunfish
(Mola mola), as well as a bottlenose dolphin, were often
associated with late summer and fall kills in the open bays
(William T. Young, personal communication).
In 1974, only five fish kills occurred in Escambia Bay and
adjacent bayous (Table 10-3). These were: (1) a chronic kill,
mostly adult striped mullet, that occurred throughout the open
waters of Escambia, East, and Pensacola Bays from mid-April until
early June; (2) an acute, multi-species kill was investigated in
Mulat Bayou on June 14; (3) several species died in a small kill
in the upper northwest corner of Escambia Bay on June 27; (4) an
10-23
-------
acute, single species kill of juvenile Gulf menhaden in the south
entrance canal to Mulatto Bayou also on June 27; and (5) an
acute, multi-species kill off the Floridatown Beach, .in the
northeast corner of Escambia Bay on September 3.
During the prolonged mullet kill, prevailing winds and waves
caused dead fish to drift towards the windward side of the bays.
We were unable to obtain any distressed fish for a critical
examination. It was estimated that 10,000 to 15,000 fishes,
mostly striped mullet, perished during April and May. All of the
mullet were adult individuals; many were in the 0.9 to 1.4 kg
(2.0 to 3.0 Ibs) size range.
Although the cause of the kill was not established, the
commencement of the mullet die off occurred concurrently with a
spill of sodium thiocyanate from industrial waste ponds on April
13 and again on April 30. Subsequently, all 58 water samples,
that were collected throughout Escambia Bay and East Bay on May
7, contained concentrations of thiocyanate ranging from 0.02 to
1.70 ppm (mean, 0.28). However, no cause and effect relationship
could be shown between the striped mullet kill and the
thiocyanate.
The second and third kills during 1974 in Mulat Bayou and
Escambia Bay, respectively, were both small kills. In Mulat
Bayou, around 4,300 fishes were found on the beach, as well as
floating in the water. The species composition of dead fishes
was 80 percent juvenile Gulf menhaden, with the rest composed of
Atlantic croaker, sand seatrout, and a single striped mullet. A
lack of dissolved oxygen following a phytoplahkton bloom caused
the kill. No specific cause was found for the kill in Escambia
Bay (third) which involved about 55 individuals (longnose gar,
striped mullet, crevalle jack, and ladyfish) .
Approximately 50,000 juvenile Gulf menhaden died in the
fourth kill of 197U in Escambia Bay at Mulatto Bayou. Death was
attributed to low dissolved oxygen concentrations. The morning
following the kill, oxygen levels were still depressed in the
bottom waters; at six of eight locations throughout the south
entrance canal, oxygen concentrations were between 0.2 and 3.9
ppm. Two conditions that contribute to the low oxygen levels are
the submerged borrow pits and dead end finger canals.
Livingston, et al., (1972) described the environmental impact of
dredging in this area."
In the fifth fish kill of 1974 in Escambia Bay at
Floridatown, approximately 3,000 fishes and crustaceans,
distributed among 11 species, perished in September. The species
composition and estimated percent occurrence of the organisms
were as follows: . :
10-24
-------
Species Percent occurrence
Spot 80
Atlantic croaker 10
Bay whiff
Southern flounder
Hogchoker
Gulf menhaden
Sea catfish
Tidewater silverside
Stingray (Dasyatis sp.)
Blue crab. .
Although this fish kill was near the industrial outfall area, no
specific cause could be determined for the mortality.
A gradual reduction in the frequency, as well as the
magnitude, of the kills in the Pensacola Bay system has taken
place in the past five years (Figure 10-11). Overall, the number
of kills per year have declined from 56 to 14, a decrease of 75
percent. The occurrence of major kills peaked in 1970, when over
59 million individuals were estimated to have died (Appendix 10-
13) . By 1974, fewer than 200,000 fishes perished during the
year. Fish kills in Escambia Bay and adjacent waters have shown
a dramatic decline of 86 percent since 1970. Similar encouraging
trends were also noted in the waters of East Bay and Pensacola
Bay sub-systems.
Freshwater Sport Fishery
An active freshwater sport fishery is located in the lower
Escambia River and delta tributary streams. The major source of
data on this fishery was obtained during two creel surveys
conducted by members of Bream Fishermen Association (BFA) from
April 25 through May 30, 1970 (Hixson, Niven, and Hopkins, 1971)
and from May 4 through June 2, 1974 (W. Carroll Hixson, personal
communication). The survey area extended from the mouth of the
Escambia River northward to the township of Molino, Florida,
which represents approximately 80 miles of fishing waters.
The dominant group of fishes in the creels were sunfishes
(Centrarchidae). Representatives of this family, in decreasing
order of abundance, included bluegill (Lepomis macrochirus),
redear sunfish (L. microlophus) , warmouth (L. g_ulosus) , spotted
sunf ish (L. punctatus) , longear sunf ish (L. mecjalotis) ,
largemouth bass (Micropterus salmoides) , and black crappie
(Pomoxis nigromaculatus), which accounted for over 90 percent of
the total catch in 1974. Other fishes in the creel included
bowfin (Ajnia calva), catfishes, gars, chain pickerel (Esox
niger), and several estuarine fishes from the tidewater portion
of the river.
From a preliminary analysis of the creel survey data, it was
apparent that, overall, few changes have occurred in the fishery.
10-25
-------
50 -
40-
30-
~ 20-
UJ
o
UJ
5 10-
o
o
0
u_
o o.
ESCAMBIA BAY SUBSYSTEM
UJ
o
UJ
tr
u.
30-
20-
10-
1970
PENSACOLA BAY SYSTEM
N = I66
1971
1972
YEAR
1973
1974
Figure 10-11. Annual distribution of fish kills in Escambia Bay
subsystem and total Pensacola Bay system, 1970-197U.
10-26
-------
Similar catch rates ,were recorded with 0.94 fish per fishing hour
in 1970 and 1.06 fish per hour four years later (Table 10-4).
Catch rates are reliable indicators of angling success. No
abrupt gains or losses occurred in the percent occurrence of
individual species in the creels. However, the occurrence of the
three most popular sport fish (bluegill, redear sunfish, and
largemouth bass), as a group, shifted from 81 percent in 1970 to
62 percent in 1974. The meaning of this shift is unclear, but
the downward trend was alarming. The spring season is considered
one of the better fishing periods, when fishermen seek out the
productive spawning areas, such as the "shellcracker beds" in
Thompson Bayou (now a refuge area). Ferry Pass Bayou under
Highway 90 bridge, and marsh grasses near the mouth of the river
(Hixon, Niven, and Hopkins, 1971). The similarity in fishing
pressure during both surveys indicated that the fishermen's
attitude toward the river remained essentially unchanged during
the first half of the 1970 decade.
Biology of Major Species
Gulf menhaden (Brevoortia patronus)
A total of 14,804 Gulf menhaden, the second most abundant
species in the bay, was collected during our survey. This annual
catch consisted of 9,305 individuals that were caught with the
trawl and 5,499 with the seine. The average trawl catch was 65.4
individuals in the upper Escambia Bay, 11.2 in the middle -bay,
10.6 in the lower bay, 22.1 in East Bay, and 231.9 in the bayous
and river. The largest catches of juvenile fish occurred in
February and April.
The life history of the Gulf menhaden is well-known (Gunter
and Christmas, 1960; Fore, 1970; Fore and Baxter, 1972; and
Tagatz and Wilkens, 1973). In Escambia Bay, members of the 1973-
74-year-class were captured from December through April, which
verified the winter spawning period of this species. After the
juveniles had spent approximately 6 to 10 months (depending on
the date of entry) in the estuarine nursery, they had grown to. 92
to 137 mm (mode, 122 mm) in length (Appendix 10-14). The
emigration of this species to offshore waters coincides with the
commencement of the adult spawning season.
Gulf menhaden fishery is the most valuable finfish fishery in
the Gulf of Mexico. In 1973, 486,555.6 metric tons, valued at
44.6 million dollars, were landed in the northern Gulf (U.S.
National Marine Fisheries Service, 1974). By-products from
menhaden, a non-edible fish, include fish meal, oils, and
solubles. Processing plants in the northern Gulf are located in
Louisiana and Mississippi coastal waters. A former plant at
Appalachicola, Florida ceased operations following the 1969
fishing season. There is no active menhaden fishery in the
Pensacola area, which accounts for the minuscule landing (200 Ibs
in 1973) in Escambia County.
10-27
-------
Table 10 - <;.' Summary of two creel surveys of freshwater sports fishery
•on-tha lower Escambia River, April 25 to Hay 30, 1970 and Hay 4 to
June 2, 197U..
Item
Number of fishiny parties
Average number of fishermen per party
Numbnr of man-hours spent fishing
Total number of fishes caught
Average catch per man-hour
Metiian catch per man-hour
1970
760
2.09
9251
8671
0.9U
0.69
197U
751
2.01
8730
9223
1.06
C.73
Data supplied by W. Carroll Hixson, BFA
10-28
-------
Atlantic bumper (Chloroscombrus chysurus)
The Atlantic bumper, a non-commercial species, was the most
abundant carangid in the collections from the bay. A total of
625 were taken in the trawl collections and 299 in the seine
hauls. The occurrence of these fish showed a disjunct
distribution; over 60 percent were caught in East Bay, the
remainder in Escambia Bay, and none in the bayous.
Young of C. chysurus moved into Escambia Bay during the
summer and re-entered the Gulf with the onset of cooler
temperatures in the fall. Length-frequency distribution showed
that the population consisted entirely of juvenile individuals
(Appendix 10-15). Most of the population was present only from
August until October. MacFarland (1963) previously reported that
this species was absent from Texas waters during the fall and
winter months.
Sand seatrout (Cyngscion arenarius)
This species was the sixth most abundant species in our
catches. Of the total catch of 1,620 individuals, 1,587 were
taken in trawl collections and 33 in seine hauls. The average
trawl catch was 6.8 specimens in Escambia Bay, 9.6 in East Bay,
and 30.5 in the bayous and river. Distribution was widespread
throughout the estuary and specimens were taken in all sampling
months. In a survey of fishes in Alabama estuaries. Swingle
(1971) found that Cynoscion arenarius was the eighth most
abundant species in his collections.
Length-frequency distribution of sand seatrout showed that
there was a wide size-range in this estuarine population
(Appendix 10-16). Analysis of our data confirms the prolonged
spring and summer spawning season of this species.
Sand seatrout and probably a few silver seatrout (C. nothus)
constituted approximately five percent of the:composition of the
industrial bottomfish catches in the northern Gulf of Mexico
(Roithmayr, 1965). In 1973, 195,590 Ibs were landed in Escambia
County, which represented 8.8 percent of the total landings along
Florida's west coast.
Spotted seatrout (Cynoscion nebulosus)
Eleven spotted seatrout were taken with trawling gear and two
with seine. Trawl collections occurred in Areas 2, U, and 5; the
largest number were taken in the bayous. Most of the catch
consisted of young fish. Few adults were taken as they are more
readily caught in gill and trammel nets. The loss of grass
flats, an essential habitat for the young, severely limits the
production of this species in Escambia Bay.
The spotted seatrout often spends its entire life cycle in
the estuary. This species spawns at night in the deeper holes of
10-29
-------
bays, lagoons, and sounds over grass beds (Tabb, 1966). Spawning
occurs in Florida waters when spring water temperatures reach
25.5°C (78°F). Following spawning, the fertile eggs are demersal
and are found attached to submerged vegetation and debris.
Hatching period lasts several weeks. Tabb (1966) reported that
at six to eight weeks, juveniles form schools and this schooling
behavior persists until the age of five to six years, at which
time the adults acquire a semi-solitary existence. The bulk of
this predator's diet consists of forage fishes and penaeid
shrimp. Spotted seatrout are basically non-migratory, but they
will move offshore to escape winter cold and sudden drops in
salinity.
Spotted seatrout, or "speck", is a favorite of sports
fishermen in the Pensacola area. Artificial lures, live pinfiqh,
and live shrimp are the most popular baits. After an absence of
several years, this species is again being caught near the
railroad trestle in Escambia Bay. No records are available on
sport fishing harvests.
o
The west coast of Florida produced an annual commercial catch
of 2.3 million pounds from 1969 to 1973. The average landings
from Escambia County during the same years were almost 70,000
Ibs, or 3.1 percent, of west coast landings (Table 10-5). The
1973 poundage (89,528 Ibs) in Escambia County represented nearly
a three-fold increase over the low returns in 1966 and 1967.
Spot (Leiostomus xanthurus)
The spot was the second most abundant species in our
bimonthly survey. A total of 13,997 individuals were taken by
trawl and 171 by seine. This species constituted approximately
20 percent of the total trawl catch. Specimens occurred
throughout the estuary, but were most abundant on the shallow mud
bottoms at the bayou stations. The smallest catches were made in
February, the largest in June. This species is abundant along
both the Atlantic and Gulf Coasts. Nelson (1969), while studying
the biology of the spot in Mobile Bay, observed that the spot
decreased in abundance, moving from east to west in the northern
Gulf. This westerly decline was in agreement with the comparison
of our bimonthly catches from Escambia Bay, with catches in
Mobile Bay, Alabama, and Biloxi Bay, Mississippi (Table 10-6).
Spot, 15 to 25 mm, were first taken in Dacember, and these
members of 1974-year-class continued to enter the estuary until
April. The length-frequencies of juvenile and adult spot taken
during the bimonthly surveys are presented in Appendix 10-17.
The spawning season lasts from December through March, which
agrees with Swingle's (1971) findings from Mobile Bay. During
the fall months, the adults emigrate to offshore waters in
preparation for the spawning season.
Along the Gulf Coast, the spot is not an important food fish,
as it is along the Atlantic Coast. However, in the Gulf of
10-30
-------
Table 1C - 5. Summary ot commercial landings of spotted seatrout, Cynoscion
nebulosus, along tne west coast of Florida and Escambia County trooi 1964
through 1973.
Year
196U
1965
1966
1967
1968
1969
1970
1971
1972
1973
Annual avg.
Landing
Fla. west coast
(Ibs)
2,798,659
3,369,726
3,173,816
2,636,888
3,065,206
2,U18,70U
2,6U2,810
1 ,96C ,866
2,1UC,127
2,226, 180
2,6U3,298
s
Escaiubia Co.
(Ibs)
75, SC?
<45,09U
31,611
31 ,07U
55,327
52,U37
66,397
67,606
72,812
89,523
53,769
Percentage of wast
coast landings
2.7
1. 3
1 . 0
1.2
1.8
2. 2
2.5
3.U
3. a
U.O
2. 2
Five-year average 3,008,859 47,781
(1964-1968)
Five-year average 2,277,737 69,756
(1969-1973)
Table 1C - b. Comparison of the average; bimonthly trawl catches or spot from
three estuaries in the northern Gulf o£ Mexico.
ailoxi t3ay, Miss. Mobile 3ay, Ala. Escambia Bay, Fla.
1968-69 (Christmas 1968 (Swingle, 197.3-74 (present
Month and Waller, 1973) 1971) stu;ly)
October
Deceaber
February
April
June
August
Bimonthly average
AV*
7.3
0.5
V* • *..
3.6
13.5
0.5
4. 1
srage eaten/
6.
96.
1.
46.
220.
6.
62.
tra»i sample
1
7
^
6
2
9
9
S3. 7
21.6
86. 7
132. 3
279.6
42. 7
1C 9. 4
10-31
-------
Table V: - 7. Summary of commercial landings of spot, Loiostoinus xanthurus,
along thfe- west coast ot Florida and "scarabia County, 196« turougn 1973.
Landings
Year
1964
1965
1966
1967
1968.
1969
1970
1971.
1972
1973
Annual average-
Fla. west coast
(Ib.S)
353,07b
314,516
3^8,350
293,915
311 ,396
297,3 19
249,784
432,216
245,893
13.3,293
3^.2,976
Sscamoia Co.
(Ibs)
..2} ,."31
15,3CO
11,776
13,713
24,2C5
39,436
61,313
80,092
71,223
39,523
42,702
Percentage of west
coast landings
5.
4.
3.
4.
7.
13.
24.
13.
29.
4-j.
14.
S
9
4
7
8
3
6
5
5
8
1
five-year average 324,251
(1964-1968)
Five-year 'average 261,701
(19&Q-1973)
17,:ri5
6B,31B
5. 3
24.2
Table 10 - 8. Comparison of the average binionthly trawl catches of Atlantic
croakar, Hicropogon undulatus, from three estuaries in the northern Gulf
of Mexico.
Bonth
Biloxi Bay, Miss. Mobile Bay, Ala.
1968-69 (Christmas 1968 (Swingle,
and,Waller,1973) 1971)
Escambia Bay, Fla,
1973-7U (present
study)
October
December
February
April .
June
August
Bimonthly average
:--AV(
2.8
2.0
4.5
55.0
268.5 .
75. 5
68.0
srage car.cn/trawi sampi
6.8
9.9
889.3
•• • ' '244.6 '
. 209.3
51.9
235.3
e
10.6
4. 2
19.0
98. 7
190. 1
41.0
60.6
10-32
-------
Mexico, this species constitutes a large portion of the
industrial bottomfish fishery (Roithmayr, 1965) . Along the west
coast of Florida, the annual commercial catch from 1969-73
averaged 281,701 Ibs. The landings in Escambia County, during
the same five years, averaged 68,318 Ibs, or 24 percent of the
west coast landings (Table 10-7) . Spot landings have steadily
increased in Escambia County since 1968 and represented nearly
half of the Florida west coast landings of spot in 1973.
Atlantic croaker (Micropoqon undulatus)
Atlantic croaker, the fourth most abundant fish in our
survey, was evenly distributed throughout the study area. Of the
total catch of 8,<*03 individuals, 7,915 were taken with the trawl
and 488 with the seine. Specimens were taken at all salinities,
from freshwater conditions (zero salinity reading with the
salinometer) in the Simpson River in April to 29.6 ppt in the
lower portions of Escambia Bay in August.
The largest catches of M. undulatus were taken in June and
the smallest in December in Escambia Bay, which paralleled the
bimonthly catches in Biloxi Bay, Mississippi (Christmas and
Waller, 1973) . The high catches from Mobile Bay, Alabama
(Swingle, 1971), possibly were indicative of an unusually
successful year-class in 1968 (Table 10-8).
^.
Analysis of the length-frequency distribution for Atlantic
croaker showed that new young-of-the-year were initially
recruited into our trawl catches in December and continued to
enter the estuary until April (Appendix 10-18). In Louisiana,
Ferret, et al., (1971) reported that incoming juveniles were
encountered from October through April. Three age classes were
present in Escambia Bay in June that had modal lengths of 77,
139, and 227 mm. Adults generally leave the estuary during the
colder months.
Since 1966, the catch of Atlantic croaker has become
increasingly important to the commercial interests in Escambia
County (Table 10-9). In 1973, almost two million pounds were
landed in Escambia County, which represented 83 percent of the
total landings of this species along Florida's west coast.
Interest in harvesting Atlantic croaker has accelerated since the
development of the bottomfish fishery (Roithmayr, 1965) and the
use of large croakers for food.
Striped mullet (Mugil cephalus)
The striped mullet was the tenth most abundant species.
Twenty-two were taken by trawl and 317 by seine. This species is
an agile fish that usually eludes the trawl. The majority of the
mullet catch consisted of juvenile fishes from the seine hauls
along the sandy beaches of Escambia Bay. Mullet are found
throughout the estuary, although the smaller juveniles tend to
concentrate along the shoreline of the bay and in the bayous.
10-33
-------
Table 10 - 5. Summary of commercial landings of Atlantic croaker, Micropogon
undulatus, along the west coast of Florida and 2scambia County from 1964
througn 1973.
Land ings
Xear Fla. west coast
(Ibs)
1964
1965
1966
1967
1966
1969
1970
1971
1972
1973
Annual average
five-year average
(1964-1968)
Five-year average
(1969-1973)
64,596
35, US9
49,889
87,228
116 ,900
409,694
936,075
1 , DC 3, 522
1.587.7b9
2,357, 172
667,841
76,836
1 ,258,846
Table 10-10. Summary of commercial
cephalus, along the west coast of
1964 through 1973.
Escaabia Co. Percentage of west
(J-bs) coast landings
1,123
745
2,036
57,D98
77,012
221,387
633,170
762,632
1,395,757
1,954,920
507,583
27,603
937,573
1.
2.
4.
65.
52.
54.
64.
76.
67.
32.
76.
35.
73.
landings of striped mullet,
Florida and Escambia County
7
1
1
5
4
3
u
0
3
9
•>
9
4
Magil
during
Landings
Year Fla. west coast
(Ibs)
1964
1965
1966
1967
1969
1970
1971
1972
1973
Annual average
Five-year average
(1964-1968)
Five-year average
(1969-1973)
34,995,616
31,367,895
26,957,866
23,283,184
25,473,111
23,'l38,324
23,817,999
26,863,573
26,653,642
26,291,428
27,393.527
25,189,330
Escambla Co.
(Ibs)
771,598
673,144
583,769
617,637
812,30.8
1,098,278
853,184
1,016,167
921,664
813,053
685,786
940,320
Percentaqe of west
coast landings
2.2
2.2
2.2
2.6
3.2
4.6
3.6
3.8
3.5
3.1
2.5
3.5
10-34
-------
Fish often observed jumping out of water in the estuary are
generally mullet.
The life history of striped mullet in Florida's waters was
reviewed by Futch (1966). Spawning occurs offshore in the Gulf
from October through February. Adult females may extrude from
1.2 to 2.7 million eggs at a single spawning and fertile eggs
usually hatch in 48 hours. Generally, ocean currents transport
the postlarvae from the spawning ground to estuarine nurseries.
In the fall, adults usually form large schools before returning
to sea.
The mullet is an excellent food fish and an active mullet
fishery exists along both Florida coasts. Mullet are taken
commercially by gill nets and by seines. A five-year average
(1969-73) of over 25 million pounds was taken along the west
coast of Florida. During the same period, an average of over one
million pounds was landed yearly in Escambia County (Table 10-
10) . Most of these fish came from local inshore waters.
Spanish mackerel (Scomberomorus maculatus)
Only three Spanish mackerel were taken in the trawl
collections. They were caught in the middle reaches of Escambia
Bay in October. All were juveniles ranging from 78-85 mm in
length, which indicated that these specimens were spawned near
the Pensacola area.
Adults seldom venture into the lower salinity waters of
Escambia Bay, but large schools were frequently observed during
the summer and fall in Pensacola Bay and in the Gulf waters near
the outer beaches where they are actively pursued by the sports
fishermen. Spanish mackerel is not an estuarine-dependent
species, but occasional usage is made of inshore waters.
This species supports a valuable commercial fishery in
Florida waters. Along the west coast, the five-year (1969-73)
average landing was 7,258,857 Ibs with the largest catches
occuring between Tampa and the Florida Keys. In Escambia County,
the five-year catch from 1969-73 averaged 136,883 Ibs, which was
down from the 196U-68 period (Table 10-11).
Discussion
Much of this investigation was addressed toward answering
several intriguing but nonetheless interwoven and complex
questions concerning the status of finfish and shellfish
populations and their respective fisheries. How does Escambia
Bay compare with other estuarine systems? There are no proven
guidelines in the field of pollution-ecology for finding answers
to these questions in terms of absolute number, percentage, or
rank. However, from a fisheries standpoint, it was evident that
a valid appraisal of present conditions could be obtained by
using selected biological indicators, whose status, although
10-35
-------
Table 1C - 11. Suran.ary of commercial landings of Spanish mackerel, Scombe romorus
maculatus, along the west coast of Florida and Escambia County durin.; 1964
through 1973.
Landings
Year
1964
1965
1966
1067
1968
1969
1970
1971
1972
1973
Annual average
five-year average
(1964-1968)
Five-year average
11969-1973)
Fla. west coast
(Ibs)
3,879,384
4,883,400
7,004,241
5,667,500
7,065,588
6,174,574
8,009,947
7,363,233
6,532,300
6,194,232
6,499,440
5,740,C23
7,258,857
Escambia Co.
(Ibs)
206,975.
162,647
270,544
241,1uO
14C, 476
174,651
172,893
65,618
39,111
132,141
170,620
"••"'
136, B93
Percentage of west
coast landings
5. 3
'3.3
3.9
4. 1
2. :
2. 1
2. 2
'0.9
1.4
2.9,
3.0 „
4. "j
1.9
10-36
-------
frequently in relative terms, often required the development of
novel and innovative approaches in the comparatively new area of
estuarine assessment and rehabilitation.
Data were comparable on catch-per-unit-effort among sstuaries
when the other studies employed similar gear and sampling
procedures. In Escambia Bay, the annual average trawl catch was
568 fishes per 10-minute tow. This return was in agreement with
other recent surveys in Gulf estuaries. Average catches in
Alabama waters of 517 and 426 individuals were reported from
Mobile Bay and Perdido Bay, respectively (Swingle, 1971). Trawl
catches from Biloxi Bay, Mississippi contained an average of 661
fishes (Christmas and Waller, 1973). The similarity in both the
annual numerical catches and species composition revealed that
Escambia Bay is functioning as a productive estuarine nursery for
young fishes. It was not possible to obtain precise information
on past abundances in Escambia Bay, since no comparable data were
available.
Diversity indices have been successfully employed in the
assessment of environmental quality (Bechtel and Copeland, 1970;
and Wilhm and Dorris, 1968). Of a number of possible formulas
for the measurement of diversity, the Shannon-Weaver index (H»)
has been employed with fish populations more often than any
other. At present, the evaluation of diversity from one estuary
to another has mainly relied on a comparison of ranges. During
an investigation of the fishes in the more polluted portion of
Galveston Bay (Bechtel and Copeland, 1970), the seasonal changes
in H1 (pooled) were 0.13 to 0.91, compared to a range of 1.05 to
1.75 in Escambia Bay. In the polluted estuarine section of the
lower Mystic River, which flows through downtown Boston, seasonal
diversity values ranged from 0.33 to 1.03 (Haadrich and Haedrich,
1974). The species composition of the trawl collections from
Escambia Bay was composed of 48 species, whereas only 23 species
contributed to the diversity of the Mystic River. The Patuxent
estuary, a polluted waterway, had H1 values from 0.2 to 1.2
(McErlean, et al, 1973). In an essentially non-polluted estuary
near Sapelo Island, Georgia, Dahlberg and Odum (1970) reported
that species diversity (H1) ranged from 0.7 to 1.8.
Few annual pooled H1 values appear in the literature. To
make comparisons with Escambia Bay, it was necessary to calculate
such values from the numerical totals of other trawl studies. An
annual H* provides an objective, quantitative evaluation of
environmental conditions not possible with range values that
often overlap. Other advantages of an annual pooled H1 are that
it employs all the available data on species and numbers in the
determination, compensates for chance sampling variations, and is
adaptable for making comparisons, since H1 is independent of gear
selectivity and sample size. This is frequently not true of
catch-per-unit-effort data. During the past five years, annual
diversity values obtained from estuaries with dissimilar levels
of environmental quality were:
10-37
-------
Location Pooled Annual H* Source
Mystic River, 1.19 Haedrich and Haedrich (1974)
Mass.
Mobile Bay, 1.29 Swingle (1971)
Ala.
Escambia Bay, 1.63 Present study (1973-7U)
Fla.
Vermillion Bay, 1.97 Ferret and Caillouet, Jr.
La. (197U)
Estuary near
Sapelo Island, 2.10 Dahlberg and Odum (1970).
Ga.
Lower diversities were associated with polluted waters, whereas
the higher values were representative of presumably undisturbed
environments. The position of the pooled H1 value from Escambia
Bay indicated that pollution-oriented stresses still exist in the
bay.
The role of industrial discharges, particularly nutrients, in
estuarine environments is often difficult to ascertain. In
Escambia Bay, species diversity was inversely related to nutrient
levels. In other words, H* diversity was significantly depressed
during periods of high PNI (nitrogen, phosphorus, and organic
carbon content). To our knowledge, this was one of the few
instances where the buildup of nutrients in a bay has been shown
to have a measurable influence on -community structure. Future
scheduled reductions of these pollutants to the bay should
benefit this biological community. *
In addition to nutrient pollutants, both salinity and benthic
grasses influenced the annual H1 value. Salinities in Escambia
Bay were at the lower half of the expected salinity range for
temperate estuaries. A larger number of fish species normally
inhabit the higher salinity portions of an estuary. This
potential depression of annual diversity in Escambia Bay, due to
location of the sampling sites in the upper reaches of the
estuary and not to any statistical association between salinity
and distribution, should be recognized when making comparisons
with fish surveys conducted throughout an entire system. Since
the surveys in Mobile Bay, Alabama (Swingle, 1971) and the
estuary off Sapelo Island, Georgia (Dahlberg and Odum, 1970) fell
into this category, their annual values of H1 were apparently
somewhat inflated compared to Escambia Bay.
Marine meadows are recognized as irreplacable habitats for
numerous species. The loss of grass beds apparently due to toxic
conditions - and subsequently, their faunal assemblages - in
Escambia Bay largely accounted for the general absence of
10-38
-------
pinfish, gobies, pipefishes, young of spotted seatrout, and
decreased abundance of other species. Hoese and Jones (1963)
stated that pinfish and penaeid shrimp were the major fish and
invertebrate species with the greatest biomass in the grass
communities of Texas bays. Thus, the depressed diversity was due
partially to the absence of these typical grass bed inhabitants
from the bay's faunal community.
Comparison of the sample shrimp data with catches in other
Gulf estuaries provided an indication of the condition of the
shrimp grounds in Escambia Bay. For instance. Ferret, et al.,
(1971) caught an average of 53.8 penaeid shrimp per trawl sample
in Louisiana waters, 13 times greater than the average catch from
Escambia Bay. The species composition in Louisiana was 30
percent white and 70 percent brown shrimp. In the estuarine
waters of Mobile Bay, Alabama, the average catch (10.3 penaeids
per collection) was 2 1/2 times the catch from Escambia Bay
(Swingle, 1971). The small catches in Escambia Bay were
indicative of the depauperate condition of the shrimp habitat.
The disappearance of the shrimp fishery from Escambia Bay
coincided with the initial discovery in 1969 of high
concentrations of a polychlorinated biphenyl (PCB), known as
Aroclor 1254, in the water column, sediments (up to 30.0 ppm) and
tissues of shrimps (up to 14.0 ppm), fishes, and blue crab (Duke,
Lowe, and Wilson, 1970; and Nimmo, et al., 1975). The source of
the PCB was an accidental spill which entered the effluent from a
chemical plant on the lower Escambia River. Nimmo, et al.,
(1971a) demonstrated that Aroclor 1254 was readily absorbed by
penaeids from contaminated bay sediments. Laboratory bioassays
showed that Aroclor 1254 killed juvenile pink shrimp at about 1.0
ppb range in water in 15 days. Mortality of the less susceptible
adults occurred at concentrations of 2.4 to 4.3 ppb (Nimmo, et
al, 197lb). Adult shrimps were more sensitive to Aroclor 1254
than were fishes. However, the larval sheepshead minnow was the
most sensitive organism tested; few larvae survived PCB
concentrations greater than 0.1 ppb (Schimmel, Hansen, and
Forester, 1974) .
Besides measurements of mortality (LC50), sublethal levels
must be weighed in any consideration of harmful effects.
Sublethal concentrations of PCB were shown to alter behavior,
physiology (osmoregulation and enzyme systems) , and cellular
structures. Also, the bio-accumulation of a 2.5 ppb
concentration of PCB in water by pink shrimp was 1,800 times in
two days and 7,600 times in nine days, whereas spot concentrated
PCB (1.0 ppm in water) 17,000 times in four weeks (Duke and
Dumas, 1974).
The synergistic effect of a man-made and a natural stressor
was shown to cause mortality. PCB stress in brown shrimp
(residues of 14 ppm) and the additional stress of low saline
waters produced death (Nimmo and Bahner, 1974). Due to the
diurnal tides in Escambia Bay, salinities are continually
10-39
-------
shifting between the daily low and high periods. Ninuno and
Bahner (1974) postulated that PCB residues found in feral shrimp
from the Escambia estuary in conjunction with salinity stresses
(such as that imposed in the laboratory) would have been lethal.
No one should implicate Aroclor 1254 for being the sole cause
of the shrimp decline in Escambia Bay. Circumstantial evidence,
however, strongly suggests that PCB*s and other unidentified
toxic substances played a role in the. degradation of shrimp
habitat. Fortunately, since the 1969 spill, PCB residues in the
sediments have- shown a 100-fold decline from former
concentrations. Low PCB concentrations in the sediments in 1974
(Chapter 7) implied that this persistent chemical may still be
suppressing the shrimp populations.
Creel surveys are recognized valid indicators of the status
of a "hook-and-line" sport fishery, and thus by implication, of
environmental quality. However, this biological indicator in
1974 was largely unchanged since the 1970 survey in the lower
Escambia River. The yield to the average angler in 1974 remained
roughly one fish .per hour spent fishing on the river. This
catch-per-unit-effort was low in comparison to many of the other
coastal rivers in northwest Florida and south Alabama. Since the
resident fishes in the creel are adult-sized individuals, an
additional period of time apparently must pass before the gradual
improvements in water quality (Chapter 8) will be reflected in
this freshwater fishery. Present status of the fishery was aptly
summarized by Hixson (personal communication) when he stated,
"The river continues to have a relatively bad reputation with
local fishermen."
In summary, the status of finfish populations and fisheries
in Escambia Bay were judged to be in an intermediate stage of
recovery, whereas the shrimp nursery and fishery apparently were
in an early recovery stage. Various biological parameters
demonstrated that environmental conditions have undergone vast
improvements during the past five years. At present, fish
populations are compatible with othe~ Gulf estuaries and the bay
is serving as a productive nursery for young fishes. Fish kills,
visible indicators of estuarine quality, documented the
deplorable past and the improved present. However, the continued
suppression of the shrimp populations was apparently related to
low concentrations of toxic and nutrient materials in the bay
waters and sediments. In the water column, higher nutrient
levels acted as stressors which limited the diversity of fish
communities. Future recovery is largely dependent on reductions
in these waste discharges. The data base on fishes and shrimps
will provide a sound, reproducible format for the assessment of
future trends, as well as needed guidelines for studies in other
damaged estuarine ecosystems.
10-40
-------
FISH COMMUNITIES OF OYSTER-SHELL AND MUD BOTTOMS IN A.
POLLUTED ESTUARY WITH COMMENTS ON SUBSTRATE ALTERATION
Introduction
The degradation of estuarine waters in Escambia Bay was
caused by the discharge of industrial and municipal pollutants.
The subsequent deterioration of the aquatic environment has led
to a reduction in the usage of the nursery areas by young fishes
and pehaeid shrimps, to massive fish kills, and to reduced
catches for both sport and commercial fishermen.
A major biological value of estuaries is that they function
as irreplacable feeding and growing areas for juveniles of
important marine species, many of which are estuarine-dependent.
It was felt that the alteration of the existing bottom sediments,
such as the dominant soft, mud or compact, shell substrates,
might provide a means of increasing the carrying capacity of the
nursery grounds. Since there is no pertinent information on this
topic in the literature, the objectives of this study were:
1. to investigate the fish communities associated with mud
and shell substrates in a polluted estuary, and
2. to determine the feasibility of altering the bottom
sediments to increase the utilization of the nursery
grounds.
Methods
Description of Study Area
This study was conducted in the middle reaches of Escambia
Bay, the northwest extension of Pensacola Bay (Figure 10-12).
Escambia Bay is relatively shallow and the bottom gradually
slopes to a depth of U.6 m (15 ft) in the middle. The freshwater
flow from the Escambia River enters the north end of the bay;
the south end is contiguous with Pensacola Bay.
Two study areas were selected because, except for the bottom
composition, they possessed several desirable similarities. A
uniformly flat bottom with a water depth of 2.U m (8.0 ft), as
determined with a recording fathometer, characterized both areas.
Their location in the middle reaches of the bay insured that a
similar range of environmental factors, such as .salinity and
temperature, were present at the time of sampling.
The oyster-shell and mud bottoms were the major variables in
each habitat. The compact shell bottom was largely composed of
fragmented and whole shells, with a few small clusters of live
oysters scattered about. This shell area, on the east side of
the bay, was on the fringe of a very productive and elevated
10-41
-------
Fishermons Pt.
Mulat Bayou
Gorcon Pt.
Pensacola , Bay
Figure 10-12. Study area and sampling sites in Escambia Bay.
10-42
-------
oyster reef, which had been rehabilitated in 1971 when the
Florida Department of Natural Resources spread thick layers of
clam (Rangia cuneata) cultch on this formerly non-productive bed.
The mud substrate area consisted essentially of soft, black mud.
Sediment Analysis
Characterization of the bottom sediments was performed by
taking eight samples (three pooled grabs/sample) from each area
with a weighted Ekman dredge. Only the upper 2.0 cm of sediment
were used in the analyses. Subsequently, the particle-size
distribution was obtained by sifting the sediment through a
graded series of sieves (U. S. Standard Mesh Nos. 8, 10, 35, 120,
and 230) and following the procedures described by Folk (1968).
Sampling Procedure
All fish collections were taken with a semi-balloon, otter
trawl, which the shrimpers call a try-net. The otter trawl,
constructed of 1.9-cm, bar-mesh netting, was 4.9 m (16 ft) wide,
with a 0.64-cm, bar-mesh liner in the codend. The tow line was
30.5 m (100 ft) long.
A standardized sampling procedure was followed each month.
The otter trawl was towed in a straight line for a period of ten
minutes, using a 4.9 m fiberglass boat with an 80 hp outboard
motor running at 2000 rpm. An average distance of 1400 m was
covered during each tow. At the completion of the tow, the net
was retrieved by hand.
The monthly sampling effort was equally divided between both
stations, a total of either four or ten tows (two or five
collections/station) being taken in a given month. At each
station, multiple tows were taken on parallel tracks and readings
of water temperature and salinity were obtained with a
salinometer.
Larger specimens were processed in the field, whereas the
more numerous smaller individuals were preserved in 10 percent
solution of formalin in sea water and later sorted, identified,
and enumerated in the laboratory.
Names of fishes and phylogenetic arrangement follow the
recommendations of the American Fisheries Society (Bailey, et
al., 1970).
10-43
-------
Results
Sediments
Sediment analyses provided a precise description of the two
substrates. Almost 72 percent of the dominant components at the
mud station were silt and clay (Table 10-12). By definition, mud
is composed of the silt and clay fractions. No shell material
was present at the mud station. At the other sampling area,
oyster shell (whole and fragments) and an occasional clump of
living oysters characterized the bottom. Shell material
accounted for 74.1 percent of the sediment composition. Most of
the clay and silt fractions were located near the south end of
the sampling area where the shell fringe intergrades with a mud
flat. Thus, it was quite evident that at each site, the major
textural class adequately described the bottom habitat.
Fish Collections
A total of 22,611 fishes, representing 32 species and 18
families, were tabulated from 58 trawl collections (29
collections at each station) in Escambia Bay (Table 10-13).
There was nearly a two-fold difference in the fish catches
from the two stations. Sixty-three percent (14,349 individuals)
of the fishes were captured over the mud bottom, whereas 8,262
individuals (37 percent) were taken in the trawl collections over
the shell bottom. The yearly mean catches were 491 and 285
fishes per trawl sample over the mud and shell bottoms,
respectively (Table 10-13). There was a statistically
significant difference (t = 2.11, p < 0.05) between the mean
catches over the two substrates.
table 10 - 12. Sediment composition at the mud and shell stations.
Grain
size (an)
2.38
2.01 - 2.38
0.51 - 2.00
0.126 - D.50
0.0626 - 0.125
0.0626
Textural
class
Granule (shell)
Granule (shell)
Coarse sand
Fine sand
Very fine^sand
Silt o^nd clay
Sediment c
Mud station
(X)
O.C
0.0
0.6
3.9
13.6
71.9
:oi position
Shell station
(*)
64. 5
9.6
3.7
18.0
1.6
2.7
10-44
-------
lable 10 - 13. COB pa ri sou of the number of fishes cj tight by otter trav L over ayster-shaLl and nui bottoas in
Escaabia Day r roa October 1973 to Septsaber 1 97«.
Species
Lagodon rhomboiaes
(Piufish)
EairdLella chysura
(Silver perch)
Cynosc:ion arenarius
(Sand seatrout)
Cynoscibn nebulosis
(Spotted seati-out)
ieiostomus xanthurus
(Spot)
tticropogon undulatus
(Atlantic croaker)
Polydictylus octonemus
(Atlantic threadfin)
Trichiurus lepturus
(Atlantic cutlassfish)
Sccntbe romor us Baculatus
(Spanish mackerel)
Feprilus alepidotus
(Harvdstf isn)
Citharichthys spi Loptprus
(Bay tfhict)
Etrofus crossotus
(Fringed flounder)
Lepisostaus osseuc
(Longnosa gar)
Erevoortia patronus
(Gulf meuhaden)
Hacer.gula pensacolae
(Scale sardine)
Anchoa hepsetus
(Striped anchovy)
Anchoa mlcchllll
(Bay anchovy)
Synodus foetans
(Insnore llzardflsn)
Arius falis
(sea cattish)
Caranx hippos
(Crevalle jack)
Ch Icroscocbrus chrysurus
(Atlantic bumper)
Selene votser
(LockJO'n)
Archor-ai-jus pionatocephalus
(Least pur lor)
Cthat species*1
Total
* Ir.ciuips snijifc i>jrcisi-iiG oi
(tusanus n. ?a| , southern Mn
Bottom Oct. Dec. ?eii. Hat. Apr.
type Number ot trawl
14 14 14 10 14
mud
shell 2
mud 2 6
shell 7 1
mud 950
shell 6
mud 1 2
shell
mud 21 35 299 296
shell 22 112 63 13
mud 2 8 131 5U 271
shell 3 3 39 39 138
iiud
shell
mud
shell
mud 3
shell
mud
shell 3 1
mud
shell
mud 2
shell 1
mud
shell
mud 13 563 Kd
shell 14 68 131
DUd 1
shell
mud 1US 16
shell 147 1059
mud 489 1167 • 66U • 358
shell 2141 1850 598 188 226
mud 1
shell 3
mua 1
shell 1 1
mud
shell
mud
shell 15d 1
Qua
shell
mud 1 1 1
shell 11 11
u>ud
muJ 1
shell 1 1 1
uuci o5a 1223 -i.Vi Us", 677
.shell '454 2067 ir: 3 363 5--2
Atlantic SLID |ray (Jasyjtis s>ibinj. Sept
samples
1C u 10 14 14
2 1 2
111 141 92 10
77 80 39
1 1
7714 161411 996 2
796 213 .5
7«5 396 553 76 1
701 2«0 111 1
318 81 . 51
12 6<4
5 3 3
1 71
1 1
1
1
U 11 6 - •
7 3
5
• 7
1 3 U
1 15
I49H 305 26U7 12
US 115 1487 15
1 7
1
36 5 52 1C 1
3 8 31 11
.12 . 1
3 146 6
It 22
11
3 -1 1
•j
1
1 1
1
2535 i'-*<)C af>:5 113 17
1S16 725 717 145
ii3h ("lop.s saurus). Cult tocdiish
tipajefish (- na'at ud ipt a rus faber).
' r,tll
2
13
8
2714
202
5
14066
12514
2231
1330
U50
76
11
3
72
8
i
2
1
1
1
707
213
6
7
172
1122
6136
3773
9
14
108
148
14
55
197
11
3
9
7
1
3
14
1U3I49
B262
10-45
-------
1,500-
500
250 —
'c- •
•3; '
' 0
0>
Q.
1,250
o
(J
Q)
1
•£ " 750 —
Q>
500
250 —
Shell Bottom
Pelagic species
Benthic species
Mud Bottom
Pelagic species
Benthic species
Oct. Dec.
1973
Feb. Mar. Apr. May June July Aug. Sept.
1974
Figure 10-13. The average monthly catch of pelagic and benthic
fishes over mud and shell bottoms.
10-U6
-------
x Because of the significant dissimilarity in the abundance of
fishes at the two sites, the possibility existed that certain
species with similar behavioral traits may have shown a
perference for a given habitat. This hypothesis was tested by
separating the catches on the basis of the portion of the water
column that the various species typically inhabit (Figure 10-13) .
Thus, the pelagic species, such as anchovies. Gulf menhaden,
scaled sardine, Atlantic bumper, and spotted seatrout, did not
show a .preference for either substrate at the 95 percent level of
confidence (t = 0.81). However, benthic species, such as spot,
Atlantic croaker, sea catfish, and Atlantic threadfin, were more
than three times more abundant over the mud than over the shell
bottom (t = 2.38, p < 0.05). An interpretation of the benthic
vs. pelagic distributions indicated that the pelagic species were
swimming in the upper water column with little regard to the
bottom type, whereas the mud bottom was preferred over shell by
fishes that live in close association with the benthos.
The preponderance of fishes in the catches from the two sites
were members of the drum family (Sciaenidae) . The sciaenid
catch, composed of five species, totaled 9,383 individuals in the
collections, 70 percent being taken at the mud station and the
remainder over the shell (Table 10-13). Sciaenid fishes are the
dominant species in estuaries of the northern Gulf of Mexico.
Juveniles of both Atlantic croaker and spot were the major
benthic species in the catches. The mud bottom was preferred as
a nursery area by both species: 63 percent of the Atlantic
croaker and 76 percent of the spot were captured in this habitat.
Peak catches occurred in the month of June with an average catch
of 198 Atlantic croaker and 822 spot over the mud bottom compared
to 107 spot and 120 croaker per trawl sample over the shell
bottom. During the year, an average of 140 spot/trawl sample
from the mud habitat differed significantly from the average
catch of U3 individuals/trawl over the shell (t = 2.28, p <
0.05). Although more Atlantic croaker occurred in the
collections over the mud bottom than over the shell, the
difference between the annual catches was non-significant (t =
1.67, p > 0.05) .
Distribution of Shrimps
Three species of commercial shrimp that frequented the waters
of Escambia Bay were the white (Penaeus setiferus), the brown (P.
aztecus) and, to a limited extent, the pink shrimp (P. daorarum).
The brown shrimp was the most abundant species (Table 10-1U).
Since penaeid shrimp often burrow into the substrate with
only their antennae extended, one would expect that certain
bottom materials would be selected over others. Analysis of the
shrimp collections by species showed that a highly significant
increase existed in the number of shrimp from the mud station
compared to. the shell station (F = 35.1, p < 0.05).
Subsequently, a highly significant difference was obtained
10-U7
-------
Table 10 - 14. Comparison of the number of penaeid shrimp caught by otter trawl over oyster-shell and aud bottoms
in Escambia Bay rrom October 1973 to September 1974.
Species
Fenaeus aztecus
Fenaeus duorarum
Fenaeus setiferus
Total
Bottom
type
mud
shell
mud
shell
mud
shell
mud
shell
Oct.
4
6
1
0
0
0
0
6
1
Dec.
4
2
0
0
0
5
4
7
4
Feb
4
13
1
6
1
0
0
19
2
. Mar.
Number of
10
7
0
3
1
4
0
14
1
Apr.
trawl
14
9
2
0
0
1
n
10
2
Hay
samples
10
47
31
0
0
2
0
49
31
June
4
13
4
0
0
0
0
13
4
July
10
29
5
0
0
0
0
29
5
Aug.
4
0
0
0
0
1
0
1
c
Sept.
4
0
0
0
0
0
0
0
0
Tatil
126
44
9
2
13
'4
143
5D
00
I
o
-------
between the group means of the penaeid distributions (Student-
Newmann-Keuls mutliple range test), which showed that brown
shrimp inhabited the mud more frequently than the shell bottom.
The distributions of the white and pink shrimps were non-
significant possibly due to their sparce occurrence. As a group,
there was a three-fold increase in the number of penaeids
captured over the mud, as opposed to the shell substrate.
Discussion
The mud-bottom habitat was more heavily utilized as a nursery
ground than was the shell bottom. Presumably, benthic fishes
could forage more readily on the soft, mui bottom for bottom-
inhabiting invertebrates. Darnell (1958) stated that the
harpacticoid copepods, polychaetes, isopods, amphipods, mysids,
and shrimps were important foods in the diet of juvenile spot and
Atlantic croaker, the two dominant species in the bay. In a
study of the food habits of the Atlantic croaker in Escambia Bay,
Hansen (1969) reported that annelid worms were the dominant
organism in their diet, accounting for 60 percent of the total
food volume. Although not entirely unexpected, the pelagic
fishes, as a group, did not show a preference for either habitat.
The substrate itself, as a source of cover, exerts an
influence on the distribution of shrimp. In a series of
laboratory tests, Williams (1958) showed that white and brown
shrimp (Penaeus spp.) burrowed more readily into soft, muddy
substrates, whereas pink shrimp most often occupied coarser,
shell-sand material. The tendency of brown shrimp to seek out
muddy substrates partially explains why the shell area was
generally avoided in Escambia Bay.
In Chincoteague Bay, Maryland, the bottom habitat was altered
by spreading oyster shell over old, silt-covered, oyster bars
(Arve, 1960). Subsequently, more fishes were trapped over the
planted areas than over the control. The dominant species was
the black sea bass (Centropristes striatus) , which represented
over half the total catch. The black sea bass is a typical reef
inhabitant in high salinity waters. The distribution of spot in
Chincoteague Bay agreed with our data in that this species was
twice as abundant over the control area than over the shell
plantings. Arve concluded that fishes were attracted to, and
concentrated around, the dense oyster-shell plantings. However,
the Chincoteague Bay project differed from the present study in
that (1) the fish communities were dissimilar and (2) there was
no evaluation of the nursery function of the shell areas.
Presumably, the improved carrying capacity mainly benefited the
adult populations.
In Escambia Bay, the evidence indicated that neither the mud
nor 'the shell substrates should undergo major alterations. At
present, the mud-bottom habitat is very productive and should be
maintained as a nursery area. Conversely, compact, shell areas
are an important habitat for selected species, such as the
10-49
-------
sheepshead, and the adjacent reefs serve as the center of an
active oyster fishery. Thus, it was concluded that large-scale,
artificial changes in the existing substrates would not improve
the carrying capacity of the bottom habitat for young fishes and
penaeid shrimps.
10-50
-------
1 1 - BENTHIC MACROINVERTEBRATES
INTRODUCTION
Since there are no published studies on the benthic fauna
within Escambia Bay, an objective of the present study was to
determine if distinct communities existed in Escambia Bay and the
distribution of these communities. Sedimentation studies
discussed in Chapter 7 revealed three major benthic habitats in
Escambia Bay: (1) a broad central plain of mud sediments, (2)
the transition zone close to shore, where the gradient changes to
a steeper slope with sediments grading from mud to sand, and (3)
a sandy shelf along the bay margin. In this study,
macroinvsrtebrates in the following eight habitats were
categorized and sampled: (1) sand shelf, (2) transition zone,
(3) mud plain, (4) oyster bed, (5) grass bed, (6) near a sewage
treatment plant discharge, (7) near industrial discharges, and
(8) mud in the deepest part of the bay. Macroinvertebrates are
defined as organisms one mm or larger while meiofauna are those
organisms of smaller size.
Other objectives of this study were to determine the effects
of recovery techniques such as revegetation of grass beds on the
benthic fauna, and to determine the effects of domestic or
industrial waste discharges on the nearby benthic fauna.
Comparisons were made between assemblages of organisms in
Escambia Bay and other bays in the Pensacola Bay system as well
as other bays in the Gulf of Mexico.
METHODS
Sampling Locations
Most benthic macroinvertebrate sampling stations were
selected on previously selected sediment sampling transects to
represent each type of sediment; that is, sand, mud, or
transition. If two stations were established in the mud plain,
the shoreward station (B) was located to show the shoreward edge
of the mud plain. The other station (A) was established well out
in the mud plain. Station C was typically in the transition zone
and Stations D and E were on the sand shelf (Figure 11-1).
Benthic macroinvertebrate stations in Escambia Bay are shown on
Figure 11-2, and stations throughout the Pensacola Bay system are
shown in Figure 11-3.
To determine differences in benthic populations in summer
versus winter, six stations were sampled in both periods.
Transects G and 0, each with three stations, were selected in
Escambia Bay. During the summer, transects G and Of with
stations A, B, C, and D were sampled; however, in winter,
stations A, B, and D were sampled. Therefore, only three
11-1
-------
I
to
a.
u
o
SA
-4
Mud Plain
' ! Transition
Zone
Shore
Figure 11-1. Fathometer tracing of transect »S' showing the
three sampling zones.
-------
Fishermans Pt.
ulot Boyou
;•. (Gull Pt.) Devils Pt.
Red Bluff
0
Gorcon Pt.
Pensacola
Bay
Figure 11-2. Benthic macroinvertebrate station locations in
Escambia Bay.
11-3
-------
UON3WITO CHEMICAL CO.
Figure 11-3.. Benthic macroinvertebrate station locations in the
Pensacola Bay system.
-------
stations in common for both periods were considered in this
particular discussion. In both transects, for the summer, A
represented a mud station, C a transition station, and D a sand
station. In the winter A was a mud station, B was a transition
.station and C was a sand station for both transects.
The upper bay was defined as the area above the Interstate 10
bridge, conversely the area below the bridge was the lower bay.
There were three transects in the upper bay (E, G, and I).
Transects K, M, MM, O, Q, and S were in the lower bay.
Sampling and Analytical Techniques
Two types of benthic grabs were used to sample the benthic
fauna. The Van Veen grab was used to sample all stations that
were in at least one m (three ft) of water. This grab sampled a
0.16 m2 area to a depth of approximately HO cm. The soft muds
allowed the Van Veen to sink below the mud-water interface, thus
allowing a bite deeper than the 28 cm depth possible in harder
sediments. A screen on top of the grab, with one mm openings,
helped prevent washout (shock wave) and assured that organisms
were not lost from the sampled mud column. The 35 foot R/V
Dolphin (loaned by the EPA, Gulf Breeze Environmental Research
Laboratory) was used for all stations at depths of one m or
greater. A ponar grab was used from a 16 foot boat in the
shallow inshore stations. This grab took a 0.05 m2 sample to a
depth of about eight cm in sand. Sanders (1956) suggested this
depth is the lower limit for most infaunal invertebrates.
At each station sampled with the Van Veen grab, five
replicates were taken, encompassing a total area of 0.80 m2 per
station. Stations sampled with the Ponar grab usually had 12
replicates for a total area of 0.60 m2.
The samples collected were seived and preserved in the field,
and sorted and identified in the laboratory. The sieves used to
separate organisms from sediments had one mm mesh openings.
Special sieving sinks with two shower heads, one fixed and
spraying upward, and the other free and used downward to break up
the sediment lumps, greatly reduced sieving time. Retained
organisms were preserved with an eight percent formalin-rose
bengal stain solution. The stained organisms were sorted in
white enamel pans with the aid of magnifiers.
Of those macroinvertebrates retained by the one mm sieve,
only those specimens with a body thickness equal to or greater
than one mm were quantified and identified. This procedure
facilitated analyses, but regretably excluded a certain
recognized segment of the benthos which this project was not
prepared to examine. Several commonly collected polychaetes were
totally excluded as a result of this method, including
Mediomastus sp. and probably two spionid species. A nemertean
worm was also not enumerated, since it seldom attains a one mm
11-5
-------
size. Biomass determination, however, included all organisms
retained by a one mm sieve, regardless of individual size. Less
than five percent of all retained individuals were less than one
mm in diameter; therefore, biomass values were essentially
congrous with values for all individuals one mm or greater in
diameter.
Many organisms were not collected because of the sieve size
(one mm)- used in this study. One millimeter was the arbitrary
size break between the meiofauna and macrofauna. If meiofauna
(less than one mm) are sampled, a decision must be made to how
small an organism is to be sampled in this group. With
decreasing size of selves used, the-amount of' mineral particles
retained on the sieve increases, thus compounding the sorting
problem. Larger sample areas decrease the effect of "patchiness"
and assure a more complete sampling of the assemblages of
organisms. It is usually necessary to compromise sieve size or
sampling area because of manhour restrictions. -
For this study of the Pensacola Bay system, the
'hemichordates, eight species of dermersal fishes, and
Branchiostoma caribaeum (a Lancelot), were taken by benthic grabs
and were included in the summary tables and diversity
calculations as though they were macroinvertebrates. These
species were infrequently encountered and were not significant in
this study.
To obtain biomass, organisms were dried in the oven at 105°C
for 24 hours, weighed, and then burned in a muffel furnace at
550°C for one hour. Residues were cooled in dessicators and
weighed on a Metteler -balance. Thus, biomass was defined as the
ash-free weight.
The majority of the benthic sampling was completed in August,
1973; however, samples were also taken in the winter of 1974 to
determine seasonal variation. Additional samples were taken in
the summer of 1974. The-listing in Appendix 13-1 gives the dates
various stations were sampled.
The Morisita index for faunal affinity between communities
(Morisita, 1959) was calculated by the following formula:
CA =
2
j=
I pi) pi)
= 1 ' \ N! / \ N2 /
11-6
-------
where:
nt = number of individuals in j— species in
sample 1
n2 = number of individuals in j
sample 2
.th
species in
= total number of individuals in sample 1
N2 = total number of individuals in sample 2
C, = index of similarity between communities
C\ = 1 for same communities
C\ = 0 when there are no common species
Diversity was calculated using the Shannon-Weaver formula
(Shannon and Weaver, 1963). The diversity at each station was
estimated by (H1):
log
N
.th
Where': N.J is the number of individuals in the i— species and N
is the total number of individuals in the sample.
Sampling Adequacy
Previous studies by various workers have used many sample
sizes and'techniques to determine an estimate of the benthic
macro-invertebrate population. Thorson (1957) stated that a
benthic fauna sample should cover at least 0.1 m2. Later workers
have followed this advice, either by design or through expediency
of manpower and time restraints. Some workers have studied fauna
within mud sediments (Holland, et al., 1973; Stauffer, 1937).
Others have worked within sand sediments or sand-vegetation
habitats (Bloom, et al., 1972; Santos and Simon, 1971; Nichols,
1970). Young and Rhoads (1971), Sanders (1958), and Taylor
(1973) sampled both mud and sand sediments for benthic organisms.
Also, various workers have sampled multiple substrates such as
sand, mud, transitional, gravel, and vegetation (O'Connor, 1972;
Lie and Kelly, 1970).
The studies cited above took from one to four samples per
station and covered an area ranging from 0.016 to 0.6 m2. The
present study sampled sand, mud, transition, and vegetation
substrates and took either five samples with the Van Venn grab or
10 - 18 samples (mostly 12) with the Ponar grab. These samples
encompassed 0.6 to 0.8 m2 per station with the Ponar and Van Veen
grabs, respectively.
To characterize sampling adequacy, species-area curves were
developed for several benthic habitats and these are in the
discussion below.
11-7
-------
RESULTS
The results of analyzing samples from the Ponar and Van Veen
grabs during the course of this study are discussed below. Each
habitat is considered and the number of species, biomass, number
of individuals, and diversity are discussed under each habitat.
Also, comparisons within Escambia Bay and within bays of the
Pensacola Bay system are discussed for each habitat. Appendix
11-2 lists all species taken during this study throughout the
Pensacola Bay system.
Sand Shelf Assemblage
The sand shelf on the perimeter of the bay comprises
approximately 25 percent of the bay. The sand shelf
macroinvertebrate population during the summer was dominated by
Mulinia lateralis and Grandidierella bonnieroides which made up
60 percent of the total number of organisms. These two species,
along with Laonereis culveri, Odostomia sp A., Tagelus plebeius,
and Haustorius sp., made up 89 percent of the total organisms.
Grandidierella bonnieroides was found only in sandy sediments
throughout the bay. Distribution of this amphipod was patchy
with aggregations as high as 1000 per m2. The next most abundant
sand inhabitant was the bivalve mollusk Mulinia lateralis, which
reached a population of 693 per m2. Populations of this bivalve
varied greatly within a sampling area.
Seasonal variations in benthos included a reversal of the two
summer dominants so that in the winter Grandidierella
bonnieroides was the most dominant and Mulinia lateralis was the
second most dominant. Two other winter dominants were Neanthes
succinea and Monaculodes edwardsi. Tagelus pleheius was a summer
dominant. At sand stations for both summer and winter, the sane
species tended to be dominant; however, they did shift their
order of dominance.
Species-area curves for sand shelf stations during the winter
of 1974 indicated sampling was adequate, except at Stations EBED
and BWC (Figure 11-1), and, therefore, accurate conclusions can
be determined from the data. Summer curves for sand shelf
stations exhibited the same trend; however, five of the eleven
stations were not quite adequately sampled. Therefore, the
number of species, biomass, and numbers of individuals in the
sand shelf sediments during the summer of 1973 were
underestimated and with better sampling would have had even
higher values.
The average number of species collected at the eleven
stations on the sand shelf was thirteen. Table 11-1 gives a
comparison of species at various substrates and habitats within
Escambia Bay. Three stations on transect G and three on transect
O were sampled in both the summer and winter to determine
seasonal variation. The average number of species in the summer
for both transects was 13 per station; and in the winter, the
11-8
-------
25 -
20 -
V)
£ 15-
o
Ul
Q.
U.
O
o: 10
UJ
CD
5 -
OC2
-• EBWC
EBED
I
3
i
7
i
8
456789
NUMBER OF SAMPLES
i
10
12 13
Figure 11-4. Cumulative curves of species taken per grab at sand
shelf stations with the Ponar dredge during the winter of
1974 in the Pensacola Bay system.
-------
average was 18.5 per station (Table 11-2). There were 36 species
collected at the 11 sand shelf stations during the summer and 2U
species taken at two stations in the winter. Thus, the average
number of individuals per station during the summer at eleven
stations was U86 per m2 (Table 11-1). The two stations in common
for both summer and winter yielded values of 337 individuals/m2
and 106U per m2 respectively (Figure 11-2). These data indicated
substantial seasonal differences, with winter having about three
times as many individual organisms as summer.
The biomass (ash weight) per station averaged 0.65 g/m2 for
the 11 stations in summer. Biomass at Stations GD and OD
averaged 0.95 g/m2 in the summer and 0.21 g/m2 in the winter.
These sand shelf stations were the only stations that decreased
in biomass during the winter; mud and transition stations
increased in winter.
Comparisons of Sand Areas Within qscambia Bay
Sand stations within Escambia Bay had similar numbers of
species and biomass but not numbers of individuals. In the upper
part of the bay there were 12.0 species per station, while the
lower bay had 13.6 species per station (Table 11-3). Biomass was
1.33 and 0.27 grams/m2, respectively, for the upper and lower bay
(Table 11-3). The number of individuals per m2 were 638 in the
upper bay and 400 in the lower bay (Table 11-3). Although the
biomass and number of individuals were higher in the upper bay
there was no statistical difference between the upper and lower
bays at the 95 percent level of confidence for number of species,
biomass, and numbers of individuals.
There was a trend toward higher numbers of individuals in the
upper bay to lower numbers in the lower bay on both sides of the
bay.
The trend for biomass was also from higher values in the
upper bay to lower values in the lower bay on both the east and
west sides.
Stations on the east side of Escambia Bay were compared to
those on the west side of the bay for sand habitats (Table 11-U)
and no differences were found at the 95 percent level of
confidence for the number of species and biomass. There was,
however, a significant difference between the number of
individuals found on the east side verses the west side (t =1.99,
df = 9) .
Diversity (H1) was not significantly different on the east
side compared to the west side of the bay (t = 2.15, df = 9).
Whereas the trend for numbers of individuals and biomass
decreased from north to south on both sides, the diversity had no
definite trend. Diversity values are given in Appendix 11-3 for
each station during the study.
11-10
-------
ble 11 -
ot 1973
1. Habitats anu related bcnthic ui.icroinvert'-ibcatti dita in Fsc
-------
Table. 11-3. Comparison of bioutass, species, and number
or individuals in upper and lower ^scambia Bay.
NUMBEit OF
Upper Bay
Lower Bay
BIOMAJS
Upper Bay
Lower Bay
NUMBER. OF
Upper Day
Lower Bay
.Mud
SPECIES PS3 STATION
U.1
1.6
2
(grams/ai )
O.OU
0. 10
INDIVIDUALS per m2
U5.8
37. 4
Habitat
Transition
13.2
10.0
0.59
0.15
133. U
92.1
Sand
12.0
13.5
1.33
0.27
638.0
tt 0 0 . j
lable 11 - U. Comparison of biomass, species, and number of
individuals near the east shore and the west shore of Sscambia Bay.
NUMDEf. OF SPECIES
East Shore
West Shore
BIOMASS (grams/m2
East Shore
Hest Shore
Mud
PER STATION
b.O
3.7
)
0.07
O.C3
Habitat
Transition Sand
13.2 13.5
7.5 12.4
0.18 C.U1
O.U2 0.95
NUMBER OF INDIVIDUALS per ra2
East Shore
Hest Shora
57. 1
19.5
135.6 2U3.9
90.3 776. R
11-12
-------
Transition Zone Assemblage
The transition zone is defined in this report as a narrow
band, paralleling the shore, between the sand shelf and the mud
plain. It is characterized by a much steeper slope than the very
gradual sloping mud plain. Sediment types in this zone included
six different classifications varying between sandy mud and fine
sand. Figure 11-3 is a profile of transect S which illustrates
the three areas.
Species-area curves for transition zone stations during the
winter of 1974 in the Pensacola Bay system showed two of the five
were adequately sampled. Only five of the ten stations sampled
in the summer of 1973 were adequately sampled and estimates of
the population will be conservative. , .
» .i
Ten stations in the transition zone yielded a total of 34
species and averaged 9.8 species per station (Table 11-1). The
dominant species, by number of individuals, in this zone were
Mulinia lateralis and Parandalia fauveli. These two species
constituted 43 percent of the total organisms found. These two,
plus Qdpstomia sp A., Laoriereis culveri, Cerebratulus lacteus,
Grandidierella bonnieroides, and Amphicteis gunneri floridus,
constituted 80 percent of the total. There was little change of
dominant species between the summer and winter samples. However,
the number of individuals taken in summer, 89.1 per m2, was about
one-tenth of the 1090.2 per m2, collected in winter (Table 11-2).
Species increased to 19.5 per station in winter compared to 8.5
in summer for the two stations that were sampled in both seasons.
Biomass of the benthic organisms was intermediate of the sand and
mud areas with 0.33 g/m2. Winter samples at the two stations
averaged 0.43 g/m2, while the same two stations in the summer
were 0.16 g/m2. Therefore., species, number of individuals, and
biomass increased during winter in the transition zone.
Comparison of Transition Areas Within Escambia Bay
3
Transition zone stations in Escambia Bay had similar numbers
of species per station, biomass, and numbers of individuals.
There were no statistical differences at the 95 percent level of
confidence in stations in the upper bay compared to the lower bay
or in the easts side compared to the west side of the bay for the
three , parameters stated above. Table 11-3 lists data for the
transition zone at both the upper and lower portions of the bay.
Table 11-4 lists transition zone data for the east and west sides
of the bay. Diversity (H1) was similar in the upper bay compared
to the lower bay and the east side was similar to the west side.
In summary, there was some variation in benthic
macroinvertebrates at transition stations, but in general they
were similar throughout the bay.
11-13
-------
Mud Plain
The mud plain covers approximately 70 percent of Escambia
Bay. Typically, there is a thin flocculant soupy layer at the
mud surface which changes in firmness with sediment depth.
Generally, at a sediment depth of 15 cm, the mud has the
consistancy of a sticky gel. At greater depths, interstitial
water is reduced and the mud is firmer. High winds and increased
currents can cause this surface sediment to be resuspended.
The two most dominant species throughout the mud sediment
were the polychaete worms Siqambra bassi and Paraprionospio
pinnata. These made up 18.3 and 17.5 percent, respectively, of
the total individuals sampled. Other dominant species included
Odostomia sp A., the Nemeretean Cerebratulus lacteus, the
Hemichordate species, Parandalia faureli, and Haplosoloplos
fragilis. All of these species combined were 85 percent of the
sampled community. All mud plain stations were adequately
sampled except OA and EBEA. The latter two stations needed
additional grabs to obtain an adequate sample. In general, the
mud plain stations were adequately sampled. The average number
of species per station within the mud plain was 4.4 (Table 11-1).
Stations on the G transect and the O transect were sampled
both summer and winter. At these two mud plain stations there
were 5.5 species per station in the summer and 14.5 species per
station in the winter (Table 11-2) . Dominant species in the
summer were Parandalia fauveli, Paraprionospio pinnata, and in
the winter Tellina sp., Mulinia lateralis, Glycinde solitaria,
Mactra fragilis, and Paraprionospio pinnata were dominant. This
indicates a shift from hemichordates and polychaete worms in the
summer to mollusk and polychaetes in the winter.
Average biomass per station for the fourteen mud stations was
0.08 g/m2 (Table 11-1). Summer-winter comparison of 3 and O
transects were 0.20 g/m2 in the summer and 0.58 g/m2 in winter
(Table 11-2).
Numbers of individuals per station averaged 41/m2 in the mud
plain sediments (Table 11-1). The summer average at the G and O
transect stations was 112/m2 while the winter average at the same
sites was 231/m2 (Table 11-2). Thus, number of individuals,
biomass, and species increased during the winter sampling.
Comparison of Mud Stations in Escambia Bay
Biomass, number of individuals, and number of species found
at ;mud plain stations, showed no statistical differences between
; the upper and lower bay or in the east side compared to the west
side of the bay. Data for these stations are summarized in
Tables 11-3 and 11-4. Diversity (H?) averaged 0.94 in the upper
bay and 1.14 in the lower bay and 1.04 on the east side of the
11-14
-------
bay and 1.07 on the west side. Therefore, diversity was similar
throughout the bay within the mud plain.
Oyster Bed Assemblage
Oyster beds provide one of the most productive habitats in
Escambia Bay for an assemblage of macroinvertebrates. Oysters
are found on pilings throughout Escambia Bay; however, normal
beds occur only in the central portion of the bay near the east
and west shores. These beds represent a normal distribution
relative to salinity, hydrology, and other influencing factors
for oyster production. Profiles of beds found on the east side
of the bay are shown in Figure 7-4 on the MM and Q transects.
Oyster bed stations include MMA, MMB, MMC and QC. Beds shown on
transect Q were established by the Florida Department of Natural
Resources as experimental cultch material (Mr. Ed Little,
personal communication). At Station QC, near the experimental
bed, the sediment was similar to the surrounding area since the
bed has not been active long enough to alter the sediments.
Percent volatile organics in the sediment at QC was 0.5 but at
MMA and MMB (natural oyster beds), the percent volatile organics
were 9.0 and 3.6, respectively.
Quantitative sampling of oyster habitats is a difficult task.
Most benthic dredges are inadequate on oyster beds and allow grab
samples to escape by not closing properly. Oysters also tend to
exist in a clumped distribution. If sampling effort is adequate
to collect 90 percent of the species in a sand or mud habitat,
this same effort might not be adequate in oyster beds.
Therefore, sampling effort must be greatly increased or modified.
In this study, oyster tongs were used to augment the Ponar grab;
five grabs taken with each sample. Generated data indicated more
intensive sampling of oyster habitats would have been desirable
and would yield a greater number of species.
All oyster bed stations were inadequately sampled and all
data generated from these grabs will be an underestimate of the
population dynamics.
The dominant species by number of individuals included:
Neanthes succinea, Brachidontes recurvus, B. exustus,
Cerebratulus lacteus, Paraprionospio pinnata, Melita nitida,
Parandalia fauveli, Glycinde solitaria, Marphysa sanguinea, and
Gyptis capensis. These nine species represented 89 percent of
the habitat total. Thirty-five different species were collected
in the four oyster bed stations in Escambia Bay. This compared
to 25 different species found at one station in an oyster bed in
East Bay. There was an average of 19 species per station in
Escambia Bay and 25 species per station in East Bay. Biomass on
Escambia Bay oyster beds was higher than for any other habitat in
the bay. The average biomass per station was 8U.6 g/m2 (Table
11-1). Biomass of the oyster bed station in East Bay (EBEC) was
1.6 g/m2 per station (Appendix 11-3). Although the number of
species and the number of individuals per station were much
11-15
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higher in East Bay, the biomass was low in comparison to Escambia
Bay. At oyster bed stations, the two bays had 16 species in
common, while 28 were collected only in Escambia Bay. Of the ten
species dominant in Escambia Bay, two species, Neanthes succinea
and Brachidontes exustus, were also among the dominants in the
East Bay bed. These species are often dominant in oyster beds
elsewhere along the Gulf. Paraprionospio pinnata and Marphysa
sanguinea, both dominant in Escambia beds, were not collected at
the East Bay station. M^ sanquinea was not found anywhere else
in Escambia Bay, except at the oyster habitats. Conversely,
several dominant East Bay species were not represented in
Escambia Bay. Two relatively common boring type bivalve
mollusks, Martesia cuneiformis and Martesia smithi, were found
boring into oyster shell. Therefore, since so many common
species were not collected in both bays, these four stations were
not adequately sampled to yield a meaningful comparison.
However, even with inadequate sampling, it was still obvious that
an oyster bed had greater diversity than any other habitat during
the present study.
Grass Bed Assemblage
At present, there are no marine grasses in Escambia Bay.
Vallisneria americana, a fresh to brackish species, does,
however, exist in the upper reaches of the bay. V. americana was
found fringing the delta area of the Escambia River and one
isolated bed (ESG) was located approximately one mile south of
the delta on the west shore of the bay. This isolated bed
produced 23 macroinvertebrate species while a similar bed in
Blackwater Bay (BWG) had 24 species (Appendix 11-3). A marine
grass bed (EBEE) of Halodule wrightii in East Bay produced 26
macroinvertebrate species.
Biomass of organisms from both Escambia Bay (ESG) and
Blackwater Bay (BWG) beds was similar at 5.45 g/m2 and 5.2 g/m2,
respectively (Appendix 11-3) . Biomass of the vegetation in the
bed from Escambia Bay was 106.6 g/m2 and 213.9 g/m2 in the bed in
Blackwater Bay.
The total individuals collected in Escambia Bay grass was 921
per m2 compared to 705 per m2 in Blackwater Bay and 1527 per m2
from East Bay (Appendix 11-3) .
Comparing the 24 species found in Blackwater Bay with 23
species from Escambia Bay, there were 16 species (52 percent) in
common. Of the seven dominant species in Escambia Bay compared
to the seven dominant species in Blackwater Bay, six were in
common. These seven dominants constituted 87 percent of the
total individuals in the Escambia Bay bed and 93 percent in the
Blackwater Bay bed. V. americana habitats in both bays had
essentially the same invertebrate assemblages. There were five
species from the total bay system found only in the V. americana
beds: a grass shrimp, Palaemonetes sp. and four fishes,
11-16
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Gobigsoma sp., Trinectes maculatus, Myrophis puntatus, and
Gobiosoma bosci.
The seven dominant species of the East Bay Halodule wrightii
bed composed 90 percent of the total individuals found there.
Thirteen species, or 50 percent/ of those found in H. wrightii
were not in either Vallisneria bed. Erichsonella filiformis and
Leptochelia sp. were found only in the Halodule bed. This study
indicated quite different communities existed in the two types of
grass beds. The two species found in both types of grasses and
no other habitats were Palaemonetes puc[io and Gammarus
mucronatus. Therefore/ there were nine species found only in
grass beds of Escambia, Blackwater, and East Bays.
A. comparison of before and after the loss of Zostera marina
in Woods Hole, Massachusetts revealed the benthic
macroinvertebrates species were reduced one-third (Stauffer,
1937). The present study indicated it is possible to have a
reduction of one-half of the total species in the bay with the
loss of Vallisneria from Escambia Bay. A comparison of a sand
station (EBED) and a Halodule bed station (EBEE) in East Bay
indicated there could be a loss of 69 percent of the species if
the grass ,were eliminated. However/ a conservative approach by
using data from another sand station across East Bay (EBWC) would
indicate a species loss of 54 percent with a loss of grass.
All three stations for submerged vegetation were adequately
sampled and no new species were added with additional sampling
effort. All data generated from these stations were a true
estimate of the total population according to these sampling
techniques.
Sewage Treatment Plant Discharge Assemblage
The Northeast Pensacola STP discharges into Escambia Bay
about 366 m offshore in two m of water (Figure 11-1). This plant
provides secondary treatment and chlorination for 4,000 m3/day of
wastewaters. Sediments at this station were silty sand with some
organics. Sand particles ranged from very fine sand to particles
larger than one mm. Ten grabs with a Ponar dredge were made,
with the first grab 20 feet from the outfall and each succeeding
grab on 0.9 m (3.0 ft.) intervals southward.
This station (NES) was sampled in August 1974; therefore, any
comparisons of data from this station must consider annual
variations in benthic populations since summer samples at other
stations were taken in 1973. The river flow, water quality,
local rainfall, and other factors must also be considered when
comparing these data with 1973 values at nearby stations.
A species-area curve indicated this station (NES) was not
adequately sampled and the estimate of the population will be an
underestimate.
11-17
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Ash free dry weight of the benthic invertebrates was 0.43
g/m2 and there were 25 species and 778.1 individuals/m2 at this
station (Table 11-1).
Paraprionospio pinnata, the most dominant species at this
station and the other dominant species were also common at mud
and transition stations throughout the bay.
As shown on Table 11-1.r the benthos at the STP discharge area
had higher numbers of individuals and biomass than other
transition stations in the bay. The number of species at the STP
site was also higher than other transition sites. The water
quality of the discharge is apparently responsible for the
increases by providing food, altering the sediment BOD, and in
general, raising the productivity .level. However, as stated
before, the STP station (NES) was sampled a year later than other
transition stations, which could account for some of the
difference.
Diversity (H1) was 1.4 at the STP station compared to the
mean of 1.5 for all other transition stations in the Bay (Table
11-1). However, based on the range of 0.4 to 2.27 for H1 at the
other ten transition stations, the 1.4 value for the STP station
was normal and diversity of the macroinvertebrates was not
reduced.
Industrial Discharge Assemblage
. Three stations represented the area near discharges of two
industrial effluents. Station ACY was near the American Cyanamid
Company discharge and APD and APDN were near the Air Products and
Chemicals, Inc., discharge. These stations were sampled in the
summer of 1974. Physical and chemical characteristics of the
sediments at these stations appeared to be normal for stations at
these depths, distances from shore, and mud content, with two
exceptions. Copper concentrations in the sediments were higher
at 10 and 12 M9/9 than at nearby stations that have equal
sediment characteristics. Aroclor 1254 (PCB) was higher at these
three stations than at nearby stations. Particles of synthetic
matter ranging in size from one mm to three cm were common at
Station ACY.
Based on species-area curves, none of the three stations were
adequately sampled and any conclusions from the data will be
underestimates of the total population of invertebrates near the
discharges. Also, any interpretations of these data should
consider the dates of sampling; that is, ACY, APD, and APDN were
sampled in 1974 and other stations with comparable sediment types
were sampled in 1973.
Dominant species at industry stations ACY, APD, and APDN were
the polycheate worms Laenoreis culveri, Paraprionospio pinnata,
and Parandalia fauveli, while the dominant organisms in sand
stations elsewhere throughout Escambia Bay were Mulinia
11-18
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lateralis, a mollusk, and Grand!dierella bonnieroides, a
crustacean. The dominant specieinthe transition-zone
throughout the bay was Mulinia lateralis. Therefore, there was a
shift in dominance of species from mollusea and Crustacea
throughout the sand and transition stations in the bay to
polychaete worms near the industrial discharges. The ecological
signficance of this shift is that dissolved or suspended
materials from the discharges are such that they act directly as
a food source or secondarily by altering the sediments to favor
the production of polychaete worms. Finer grained and higher
organic sediments are favored by polycheate worms as shown by
worms being the dominant species in mud sediments of Escambia
Bay. Also polychaete worms can tolerate stressed environments
because of physiological adaptations; they often become dominant
in polluted situations.
Transect E, consisting of Stations EA, EB, EC, ED, and EE,
was between ACY and APD and was therefore near the industrial
discharges (Figure 11-1). Sediments at these stations included
primarily mud at EA and EB, the mud plain stations, and also mud
at EC the transition zone station. Sand shelf stations (ED and
EE) consisted of fine sand. Sediments at these E transect
stations appeared normal when compared to other Escambia Bay
stations in Appendix 7-1. Mud stations (EA, EB) had two and four
species per station, respectively, while the other 12 mud plain
stations in the bay averaged 4.7, with a range of two to eight
species per station. The transition zone station (EG) had nine
species while the nine other transition stations averaged 9.9
with a 1 to 19 range. Station ACY was considered a transition
zone station and had 11 species. Sand shelf stations (ED, EE)
had 12 species each and the nine other sand shelf stations
averaged 13.2 with a range of 10 to 22 species per station. If
Station MMD, which was in an oyster bed complex, was excluded
from this sand shelf group, the average would be 12.1 species per
station and would have a range of 10-15 species per station.
Stations APD and APDN were sand shelf stations and had nine and
seven species per station, respectively. The above data suggest
that species per station are slightly reduced around Stations APD
and APDN, which is an area near-shore where Air Products and
Chemicals, Inc. Plant has a waste discharge. It must be
considered, however, that these stations were inadequately
sampled.
Mud stations near the industrial discharges included EA and
EB which had 5.2 and 11.7 number of individuals per m2,
respectively. These values compared with a range of 3.9 to 160.0
and an average for 12 other mud stations of 46.4 individuals per
m2. Transition zone station EC had 144.4 individuals per m2 and
seven other transition stations averaged 106.2 with a range of
9.1 to 239.4. Station AGY was transition and had 239.8
individuals per m2. Sand stations ED and EE had 314.9, and 593.5
individuals per m2 and nine other sand shelf stations averaged
493.2 and had a 61.1 to 1553.2 range. Stations APD and APDN had
sand substrates and 167.6 and 340.6 individuals per m2,
11-19
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respectively. All eight stations near the:industrial discharges
had numbers of individuals per m2 that fell within the range of
values at other like substrates,throughout the bay; therefore,
the: distribution of numbers of individuals near the discharges
appeared normal. Biomass per m2 at mud stations (EA, EB) were
0.01 and 0.03 grams while the average of 12 other mud stations in
the bay was 0.09 and the range was 0.01 to 0.36 grams per m2.
Stations EC and ACY were transition zone stations with biomass
values of 0.16 and 0.48 grams per m2, respectively. These two
values fell within the range (0.02 to 1.84) of nine other
transition zone stations within the bay. Biomass values at sand
Stations ED and EE were 0.30 and 0.34 grams per m2, respectively,
and Stations APD and APDN had values of 0.19 and 0.18 grams per
m2, respectively. The values for APD and APDN appear to be low
when compared to ED and EEr since all four stations had similar
sediments and varied only in distance from the waste discharge.
However, these four values fell within the range (0.03 to 3.05)
of nine other sand shelf stations in other parts of the bay.
The species number, biomass, and numbers of individuals of
benthic macroinvertebrates around the industrial discharges were
altered only in a narrow band parallel to shore in the vicinity
of the discharge from Air Products and Chemical, Inc.
Polinices duplicatus, a mollusk, was collected in the
Pensacola Bay system only at Stations ACY and NES (near an
outfall of a waste treatment plant) and is therefore tolerant of
stressed conditions.
Deep Water Mud Station Assemblage
In order to determine if any difference existed in specie
composition between the mud plain as defined above and the deeper
water mud assemblages, one station was sampled at the mouth of
Escambia Bay (Figure 11-1). This station (ESD) had a sediment
composition of 68 percent clay and a silt content of 30 percent.
Depth of water was 5.6 meters (18.5 ft) at this station. These
samples for macroinvertebrates were taken in January 1974, as
were other deep water samples from East Bay (EBD) and Pensacola
Bay (PBD). Species-area curves indicated ESD was adequately
sampled but PBD and EBD were not adequately sampled. This
problem must be considered in any interpretation of the data.
Eight, species were collected at ESD with the three dominant
species Sthenalais boa, Sigambra bassi, and Oxyurostylis smithi
making up 75 percent of the individuals collected. There were
52.04 individuals per m2.
At EBD in East Bay, the percentage of mud was 97.75, clay
content was 66.66 percent and the classification was clay. Water
depth at this station was 7.0 m (23 ft). The three most dominant
species were Mactra fraqilis, Sigambra bassi, and Paraprionospio
pinnata, which made up 75 percent of the total sample. There
were 81.96 individuals per m2 and 10 species were collected at
this station.
11-20
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The other deep water station (PBD) was in Pensacola Bay south
of the Port in 8.4 meters (27.5 ft) depth. Sediment
classification here was mud with the mud content at 97.47 percent
and clay at 60.05 percent. Dominant species were Oxyurostylis
smithi, Sthenalais boa, and Sternaspis fossor, which comprised 78
percent of the total number of individuals. There were 154.83
individuals per m2 and 12 species at this station.
There were three species in common, between Stations BSD and
PBD. Two of these three species were among the most dominant
species found at both stations. There were six species in common
betweejfi Stations BSD and EBD.
Station PBD was nearer the Gulf Inlet and had higher
salinities than East Bay or Escambia Bay. Two species found at
this station require higher salinities and consequently, these
species, an Ophiuroid and a Hydroid, were not taken riverward in
the estuary.
Although the deep water stations did not have the same specie
assemblages, they did have some dominant species in common.
There was a trend toward more species with an increase in
salinity from Escambia to East to Pensacola Bays.
High Salinity Area Assemblage
The Pensacola estuary has expansive areas where the
macroinvertebrate community is influenced to a large extent by
consistently higher salinity water than Escambia or East Bays.
This study sampled a site at the west end of Santa Rosa Sound to
compare its macroinvertebrate assemblage with the upper estuary.
Three stations were sampled in conjunction with winter 1974
sampling in upper bays. The three stations included a deep water
sand site (SRA), a transitional sand (SRB), and a shallow sand
flat with sparse Halodule wrightii (SRC). All stations consisted
of greater than 97 percent sand. Salinity ranged from 15 to 30
ppt at these stations. All three species-area curves indicated
sampling was not adequate, especially at station SRC. Even
though these three stations had by far the greater number of
species than stations in the Pensacola Bay system, they would
have had even more species with additional sampling.
Macroinvertebrate data for these three stations were compared
with other sand habitats elsewhere in the estuary in table 11-5.
Values for the three stations were higher than any other stations
in the system. The number of species ranged from 67 to 83, while
the highest species per station elsewhere in the bay was only 21.
Individuals per m2 averaged 1748 whereas East Bay averaged 1192
individuals per m2 (Table 11-5). Biomass ranged from 0.61 to
2.95, while the highest value elsewhere was only 0.34 (Table 11-
5). Diversity (H1) ranged from 2.89 to 3.01, which was higher
than any other station throughout the system (Appendix 11-3).
11-21
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Table 11 - 5. llacroinvertebrate data for sand stations sanpled in tha Pensacola Bay systom djcing the "inter of 1971.
Species/station Individuals/a2
Escaobia Bay
East Bay
Elackuater Bay
Santa Posa Sound
2 19 16-21
2 10 8-12
1 21
3 73 67-83
2.6 1060 ' 211-1916 852.2
2.0 1192 ' 789-1596 003.5
HI 3
7.3 1708 1527-1938 170.1
Dean
0.21
0.15
1.30
Bioaass/B2
'range
.08-. 31
.12-. 17
9.1
.61-2.90
Diversity
s.d.- . JS-)
0.13 1.78
0.03 }.36
2.10
0.95 2.97 '
The 1t most dominant species at the Santa Rosa Sound stations
made up 69 percent of the total organisms collected. All
fourteen species were unique to the sound except Polymesoda
caroliniana, which was also found in upper Escambia Bay. Santa
Rosa Sound stations had a total of 133 different species
collected.
The more-stable salinity and improved water quality are
beneficial to the benthic macr©invertebrates and promotes many
species, but not an overabundance of any one species or. group of
species; thus a balanced assemblage persists in Santa Rosa Sound.
Sandy sediments in the Pensacola Bay system produced by far
the most species and individuals compared to a muddy sediment.
Gage (1972) found diversity to be greater in sandy mud than soft
mud. Boesch (1972) found that benthic diversity increased down
the estuary. The Pensacola Bay system also had greatest
diversity down the system toward the Gulf.
Comparison of Diversity Indicies in the Pensacola Bay System
Diversity indicies are useful for comparing one community to
another, and are often used to show changes in a community
structure caused by alterations in that system such as a
pollutional discharge. Since various sediment types are used to
delineate portions of the Pensacola Bay system, diversity
indicies of benthic organisms at these various sediments further
show the relationship of areas in the system*
The Morisita Index was calculated for all possible
combinations of pairing UH stations in Escambia Bay in order to
compare one specie assemblage to another. The Morisita Index
indicated many assemblages throughout Escambia Bay were - related
and therefore, there was no North-South gradient of changes in
assemblage structure. Although there was a salinity gradient in
the North-South direction, assemblage structure did not reflect
this trend. Also, the less saline west side did not differ from
the more saline east side in assemblage structure within
comparable habitats. However, the Morisita Index has serious
limitations in that it reflects only proportions of individuals
11-22
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to species and does not adequately account for the species in
common between the two assemblages. As such, the use of this
index is confined to the above statement and the Shannon-Weaver
formula for diversity is used to further show the assemblages of
benthic macroinvertebrates.
Escambia Bay stations in the mud plain had an average H1
diversity of 1.06. This compares to 1.62 for the transition zone
and 1.65 for. sand shelf stations. The mean for mud stations was
significantly different from the transition zone mean but the
means were not significantly different for the transition and
sand stations. This indicates the mud plain assemblage is likely
different from the transition zone assemblage but the sand shelf
and transition zone assemblages may be similar. The mud plain
had the lowest diversity of benthic macroinvertebrates in
Escambia Bay. Diversity values for all assemblages in Escambia
Bay are shown in Appendix 11-2.
Greatest diversity within Escambia Bay occurred in the oyster
beds at 2.07, with grass bed diversity next highest at 1.93.
Diversities for industrial discharges and the STP discharge
(Table 11-1) were intermediate of the transition zone and mud
plain values. This order of values is reasonable since the
sediments at the discharge sites are intermediate of fine sand
and mud. Since the H1 values at the discharges were higher than
the mud plain H1, the invertebrate assemblages are not impovished
when comparing 1973 data at the transition and mud stations to
197U data for the industrial and domestic discharge stations.
Oyster reef stations had the highest H1 of all assemblages in
Escambia Bay (Appendix 11-3). Stations on the MM transect are at
old established beds, while Station QC represents cultch material
that was planted by man within the last three years. Although
Station QC is not natural, it nevertheless had an index similar
to the natural reefs (Appendix 11-3).
The grass bed of Vallisneria americana in Escambia Bay had an
H1 of 1.93. This compared favorably to the same type of grass
bed in Blackwater Bay with an index of 1.81. There was no
apparent difference in the diversity within like grass beds in
the two bays. The Halodule wriqhtii bed in East Bay, however,
had a somewhat lower diversity at 1.32.
When comparing Escambia Bay to other bays in the system, only
stations on transects G and O that were sampled in February, 1974
were considered, since stations in the other bays were sampled in
197U. The H1 developed from mud plain stations in Escambia Bay
was 2.10. The East Bay value was also 2.10; therefore, diversity
was equal in mud stations for both bays. In the transition zone
stations, the Escambia Bay H1 was 2.12 while East Bay was 2.03.
These values are considered close enough to indicate no
difference in the transition zone between the two bays. Sand
shelf stations in Escambia Bay had an H1 of 1.79 compared to 0.36
11-23
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for similar stations in East Bay. The diversity of sand
stations, unlike the mud and transition stations, were quite
different in the two bays.
The deep water mud station (ESD) had an H* of 1.72 compared
to a deep water station in East Bay (1.79) and Pensacola Bay
(1.76). The depth of the Escambia Bay station was 5.6 m (18.5
ft), East Bay station was 7.0 m (23 ft) deep, and Pensacola Bay
station was 8.4 m (27.5 ft) (Figure 11^1). .All three of these
stations were sampled in the winter of 1974. In comparison, mud
plain stations in Escambia Bay that were sampled at the same time
yielded an H1 of 2.10. East Bay mud plain stations had an H* of
2.10 also. A mud plain station in Blackwater Bay had an H1 of
2.44.
The highest H1 found in the Pensacola Bay system was the
averaged values of Stations SRA, SRB, and SRC in Santa Rosa
Sound. This high salinity area had an H' value of 2.97 during
the winter of 1974 (Table 11-5).
Diversity (H1) values indicate that within like sediments in
Escambia Bay there exists communities of like.: diversity
throughout the bay. The communities in Escambia Bay were similar
to those in East Bay within like sediments. Diversity around the
STP and industrial discharges appeared normal when compared to
similar sediments at other stations. Therefore, according to
diversity values (H1), the macroinvertebrate of Escambia Bay
appear to be normally distributed throughout the bay.
11-24
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Comparison of Diversity Indicies in Gulf of Mexico Coastal
Systems
Holland, et al., (1973) did macroinvertebrate work in
Galveston Bay at mud stations during both the summer and winter.
Calculations made using their data show a mean H1 of 1.62 for
winter samples and 1.31 for summer. Mud stations in Escambia Bay
had seasonal H1 values of 1.98 for winter and 1.06 for summer.
Taylor (1973) studied five different sediment types in
Hillsborough Bay and determined H1 at all stations. From these
data, 12 stations on three of his transects have been selected as
having similar salinities and sediments as Escambia Bay stations.
Eight mud stations in Hillsborough Bay had an average H* value of
2.40 while mud stations in Escambia Bay averaged 1.06. The
numbers of individuals collected in Hillsborough Bay were over
eight times higher than those in Escambia Bay at similar sediment
types. A partial reason for more organisms present in
Hillsborough Bay is that Taylor used a 0.7 mm sieve compared to
1.0 mm in the present study in Escambia Bay. .However, sieve size
alone probably does not account for all the differences in the
two bays. Apparently Escambia Bay has a more stressed ecosystem
from salinity fluctuations, lower dissolved oxygen, greater
turbidity, and more polluted, sediments than the sampled portion
of Hillsborough Bay. Galveston Bay had less diversity than
Escambia Bay in the winter, but a greater diversity than Escambia
Bay in the summer. Therefore, the benthos of Escambia Bay seems
to have H1 values lower than Hillsborough Bay and Galveston Bay
during the critical summer period within comparable mud stations.
Four of Taylor's (1973) sand stations in Hillsborough Bay
gave an average Hf of 2.93 compared to the H*'Of 1.65 for sand
stations in Escambia Bay. Hillsborough Bay diversities were
higher in both sand and mud sediments than values from Escambia
Bay.
Simon (1974) worked on benthic invertebrates in Tampa Bay at
four stations, all with a greater than 70 percent sand
composition. Diversity (H1) calculated from his data (Simon,
1974) indicated a range from 2.03 to 3.21. These values are
similar to Taylor^ (1973) values for Hillsborough Bay (adjacent
to Tampa Bay), but higher than values from Escambia Bay.
s .
Comparing diversity (H1) in the Escambia Bay system to
Hillsborough, Tampa, and Galveston Bays, diversity in Escambia
Bay was lower during the critical summer period.
11-25
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12 - BENTHIC MACROFLORA.
SEAGRASS DISTRIBUTIONS
Introduction
The Pensacola estuary had productive grass beds in all bays
of the system (Figure 12-1) . These plants have true roots, stems
and leaves, and reproduce by means of flowers, fruits, and seeds.
They grow completely submerged with only the lowest tides
exposing some species to the air. Within the northern Gulf of
Mexico Continental Shelf, Humm (1973) listed five abundant
seagrasses (1) Thalassia testudinum, (2) Syringodium f iliforme
(3) Halodule wrightii, (*») Halophila baillonis, and (5) Halophila
engelmanni. These marine plants are continuous from the Florida
Keys to the Mississippi Sound (Humm, 1956) and extend from the
intertidal zone out to depths of several meters (Humm, 1973).
Within the northern Gulf bays and sounds, these plants grow from
the MLHW to depths of about 2.0 m (6.0 ft) (McNulty, et.al.,
1972; Eleuterius, 1973). In the Pensacola Bay system, the three
most abundant species are Thalassia testudinum and Halodale
wrightii, marine to brackish species, and Vallisneria americana,
a fresh to brackish specie. Ruppia maritima is also fairly
common in the fresh to brackish waters of the estuary.
Seagrasses within the estuary are a major component of the
total system and especially important within the role of the
estuary as a nursery ground for commercial finfish and shellfish
of the Gulf. In the Pensacola Bay system the seagrasses provide:
1. oxygen production through basic primary productivity;
2. a food source, either directly or through the
detrital food chain;
3. protection from predators and cover for all ages of-
organisms;
U. a habitat and substrate for both flora and fauna; and
5. a sediment trap which stabilizes the bottom sediments.
Seagrasses, therefore, increase the total diversity and also
enhance sport fishing success through concentration of certain
fishes.
Studies in the Benthic Macroinvertebrate section have shown
the fauna assemblages within these grass beds to have much higher
diversity than areas void of vegetation. Consequently, it is
desirable to reverse the trend of losing vegetation to one of
expanding present beds and revegetating areas that once had
12-1
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KJ
I
NJ
,11 01
Figure 12-1. The Pensacola Bay system and "revegetation sites in
Escambia Bay.
-------
seagrasses. Seagrasses are one of the basic building blocks
necessary for recovery and rejuvenation of an estuary.
An objective of this study was to provide a baseline of the
present vegetation distribution in the system and to review the
changes that have occurred in this distribution over the last 23
years. This study should also provide coastal zone managers with
facts that will enable viable planning in the estuary.
Methods
Photographs obtained from the Florida Department of
Transportation were used to develop maps of the grass beds.
Their file of aerial photographs of Escambia and Santa Rosa
Counties dated back to 19U9. Over-flights of the bays were made
sporadically, and occurred more frequently over areas of greater
highway construction. When a section of shoreline was omitted,
no data was available for that area. Aerial over-flights were
made in 197U by project personnel using hand held 35 mm cameras
with either Plus X black and white film or Kodachrome II color
film. A polorizing filter was used on the camera. The black and
white film permitted prints to be made inexpensively, while the
color exposures gave good color saturation for best grass bed
delineation. Both films penetrated to the depths of all grass
beds and were adequate for interpretation in all cases. All
flights were made at 1,219 meters (M,000 ft) altitude. Anchored
floats were a point of reference which allowed scaling and
determination of a grass bed size.
Results and Discussion
Escambia Bay
A recession and dissappearance of most of the Escambia Bay
grass beds has occurred over the past 25 years (Figure 12-2).
The Escambia River delta area is shown in 1951 and in 197U in
this figure. This shows Vallisneria americana in most shoreline
margins of the delta. Increased water turbidity in the delta
made the photos taken in the late 1950's and 1960's
uninterpretable. Most likely Vallisneria beds were present to
some degree during this period. With this exception, photo
interpretation was not hindered at all due to turbidity. Most
flights were actually made in winter, the time of lowest
turbidity and best visibility. The delta area is the least
altered area in Escambia Bay over the years.
In 1974 V. americana was more abundant than in the last
several years according to bay front residents. In 1975 there
was an even greater abundance of Vallisneria in the delta.area as
warmer weather progressed.
V. americana also inhabited the Macky Bay area north of Laura
Point on the west shore of Escambia Bay. At the present time
there exists only one small bed about one mile north of the point
12-3
-------
1-49
1-51 1-58 10-61 10-65 11-74
1-49
Figure 12-2. Escambia Bay grassbeds 1949-1
974
12-U
-------
in four discontinuous patches. Historically, it has undergone /
recession. However, during the past year, expansion has occurred/
with new growth around each patch. During the summer and fall of
1971, turbidity levels in Escambia Bay were lower than usual, anxd
therefore, beneficial to grass growth.
/'
The Floridatown shoreline, in the northeast corner of /the
bay, had extensive submerged grasses in 1949. Although the
species are unconfirmed, interpretation of the photographs
indicated Vallisneria was dominant. Their greatest extent was
from Basshole Cove south to Fisherman's Point, and also small
patches near Mulatto Bayou. The next record indicated grasses
ceased existence by 1963, concurrently with industries starting
operations nearby on the bay.
Grass beds below Interstate 10 were most likely composed
solely of Halodule wrightii (shoal grass) . It is the most
euryhaline of grasses found in this system. There were no
records of the presence of any other marine species nor are there
other species now present below the 1-10 bridge. Sparse growth
was observed in 1965 along the southwest Magnolia Bluff area. It
extended for 1.6 km (1.0 mi) and was 0.64 km (0.4 mi) wide (van
Breedveld, 1966). A dense bed existed north of Magnolia Bluff
where the Northeast Pensacola STP outfall pipe was laid.
Halodule seems to have flourished best along the lower southeast
shore above Hernandez Point. It extended in discontinuous areas
from the point up to Interstate 10. Ground truth reconnaissance
revealed none in 1974.
Figure 12-2 shows a gradual loss of seagrass over a 17-year
period from 1949 to 1966. By 1970 all of the seagrass had
disappeared. Ground truth searches in 1973-74 revealed no
vegetation along this shoreline.
In summary, Escambia Bay had extensive grass beds along all
shores in 1949, except for sparse areas along the southwest
shore. By 1974 all had disappeared except a small patch of V.
americana along the upper western shore where there was a
significant influence by freshwater flow from the Escambia River.
Pensacola and East Bays
The history of several small beds near the north side of
Pensacola Bay bridge was first recorded in 1951 (Figure 12-3).
The disappearance of these small beds near the port facilities is
likely attributable to dredging. Enlargement of ths Port of
Pensacola (Phase I) involved extensive dredging and filling in
1960. Additional work was done in 1967. Figure 12-3 indicates
the filled areas, before and after the port expansion, and the
related distribution of seagrasses. Other beds were adjacent to
the Pensacola Bay bridge and Bayou Texar. All traces of these
beds were gone by October 1961.
12-5
-------
1-51
11-74
300 m
Figure 12-3. The north shore of Pensacola Bay with ship terminal
and the Pensacola Bay bridge, 1951-1974.
12-6
-------
The south shore of Pensacola Bay west of the bay bridge was
not historically mapped. East of the bridge a nearly continuous
22.5 km (14 mi) grass bed extended to Tom King Bayou (Figure 12-
4). Ground truth in 1966 indicated the species as Thalassia
testudinum beginning in Butcherpen Cove extending eastward one
mile (van Breedveld, 1966). At some point eastward toward Tom
King Bayou, Halodule probably replaced Thalassia as the existent
species. From 1949 to 1966, approximately half of the seagrasses
were gone. From 1966 to 1974, in two year intervals, the record
showed (Figure 12-4) an accelerated lost. Between 1966 and 1968,
well over half of the seagrass was lost. It seems that this loss
may have been primarily Halodule and that the Thalassia was
reduced only slightly. However, over the next two intervals,
Thalassia continued to diminish until 1974 when none was found.
Salinity studies during 1974 indicated a range of 4.0 to 20 ppt
at a nearby station. Thalassia cannot tolerate this low salinity
range over an extended period (Phillips, 1960).
Two records of the northeast area of East Bay are shown in
Figure 12-5. This figure shows a decline in lateral extension;
however, the width of the central area of the bed seems to have
remained fairly constant.
Blackwater Bay
Blackwater Bay has lower salinities than the other bays.
Consequently, the grass beds were composed of Vallisneria
americana for the most part with some Ruppia intersperced.
Records show the beds to occupy virtually the same areas in 1974
as in the early 1950's.
SEAGRASS REVEGETATION
Introduction
There is no question that removal of grass beds from a bay
system will adversely affect its ecology. Several workers have
documented the utilization of seagrasses by vertebrates and
invertebrates (Kikuchi, 1974; Stauffer, 1937; Hoese and Jones,
1963; O'Gower and Wacasey, 1967). This study (Benthic
Macroinvertebrates section) discusses in detail the species,
number of individuals, and biomass within Vallisneria and
Halodule beds. An increase in seagrasses in Escambia Bay would
increase invertebrate diversity. Stauffer (1937) studied the
change in invertebrate population with the loss of Zostera marina
and showed one-third of the species associated with the
seagrasses were eliminated.
The loss of grass beds in Escambia Bay is documented in the
above section. The objective of the present revegetation effort
is to . reintroduce a species to Escambia Bay not presently found
there. No transplanting work was done with Vallisneria since it
currently occupies substantial areas in the delta. Transplanting
of Ruppia martima (Widgeon grass), only sparsely evident in
12-7
-------
Figure 12-4. The south shore of East Bay from the Pensacola Bay
bridge to Tom King Bayou, 1949-1974.
12-8
-------
11-74
1km
Figure 12-5. The northeast shore of East Bay from Tom King Bayou
to Escribano Point, 1949-1974.
12-9
-------
Vallisneria beds in the estuary, was not deemed feasible because
of"~~ lack of plants. Thai ass i a testudinum exists in the more
saline Santa Rosa Sound. It was not transplanted because no
indications were found of prior existence in. Escambia Bay.
Salinity averages in Escambia Bay are believed to be too low for
this species. Halodule wrightii, the most euryhaline species, is
considered to, have the best potential for survival in the bay's
fluctuating salinity regimes. This species is hardy, being able
to inhabit intertidal areas and survive short exposures to air.
It occupies the largest geographical distribution of any seagrass
on the northern Gulf Coast (Humm, 1956). Descriptions of grasses
by long time residents around the bay indicate that vegetation
south of Interstate 10 was Halodule wrightii. Figure 12-1 shows
the pensacola Bay system and the revegetation sites.
Submerged revegetation work is in experimental stages
elsewhere. Viability studies of Thalassia testudinum and
Halodule wrightii in the Tampa Bay area were performed by Fuss
and Kelly in 1966. Twelve months in situ tank culturing
indicated T. testudinum recovered after initial decline following
transplantation (Fuss and Kelly, 1969). Kelly, Fuss, and Hall
(1971) successfully transplanted T. testudinum into Boca Ciega
Bay, Florida. Thalassia revegetation was successful on a larger
scale in lower Biscayne Bay, Florida (Thorhaug, 1974). Here,
seedlings were obtained from mature plants, treated with a growth
stimulator, and planted. Vigorous growth of plantings was
reported. Phillips (1974) reported moderate success on his
transplants of Halodule into Tampa Bay, Florida in 1960.
However, most work to date has been disappointing on Halodule
(Fuss and Kelly, 1969). Eleuterius (personal communication) is
engaged in submerged vegetation work along the Mississippi Coast.
His information that Halodule inhabits low salinity sandy shelf
areas, 0.3 to 1.2 meters deep, compares well with East Bay beds
(0.5 to 1.1m). This species inhabits the Mississippi Sound in
continuous beds with interspersed sandy patches devoid of
seagrass. It also never occurred there in mixed aggregations
with other species of seagrass (Eleuterius, 1973).
Methods
With the help of the Bream Fishermen Association of
Pensacola, transplanting was performed in July 197U and again in
September 1974. Locations of experimental plantings are shown in
Figure 12-1. Two of the sites are known to have had viable beds
in the past. The others were considered to have qualities
conducive to seagrass survival. Transplants were placed at five
depths ranging from 0.3 to 1.0 meter (1.0 to 3.0 ft) MSL at 0.15
meter (0.5 ft) intervals. Ten plugs were planted at each depth
during the two plantings. A total of 100 plugs per site and a00
plugs in all were planted in Escambia Bay.
A plug with a 7.5 cm (3.0 inch) diameter and 12.5 cm (5.0
inch) depth of Halodule wrightii was obtained from the healthy
bed in East Bay, and placed into snug fitting burlap bags. Light
12-10
-------
tight containers were used to transport the plugs, which were
replanted within three hours.
Results
Survival for the July transplants observed in October after
13 weeks in Escambia Bay was 51 percent. Plugs transplanted in
September and observed after being planted six .weeks showed 67
percent survival. Survival would have been higher had mass
mortality not occurred at site 4 where transplanted plugs were
covered with three inches of drifting sand. Excessive sand
transport .occurred along western parts of the shoreline, making
it unsuitable for revegetation. Transplants were observed again
in' "May 1975 after overwintering and data revealed 37 perdent had
green leaves at one site. Two of the" sites were badly covered
with sandr and the third site had less than 10 percent survival.
However, the leaves observed were free of encumberance,
indicating recent new growth. Therefore, it is assumed this is
spring growth and other plugs may yet sprout as the water warms.
Observations should be made later in the spring to determine
fully the results of overwintering.
Discussion
Reestablishment of Halodule wrightii grass beds will be
significant in the recovery of Escambia Bay. The beds would act
as a near-shore sediment stabilizer and tend to retain nutrients
for beneficial utilization by animals. By providing additional
food source and a unique habitat for certain groups of
invertebrates and small fishes, grass beds broaden the lower
segments of the food web, thereby ultimately enhancing the
commercial and recreational fisheries. This study's Benthic
Macroinvertebrate section discusses and exemplifies this point.
The technique of plugging allows the plants within a plug to
be in a desirable sediment for a long period of time after
transplanting to a new location. Thus^ plants within a plug
could conceivably prosper for two years or longer in a location
that has toxic sediments or other undesirable qualities.
Therefore, with plugging, it will take years before a successful
transplant is fully documented.
This transplanting effort was repeated in June 1975. This
earlier-iri-the-year planting took advantage of the spurt of
spring growth that was observed in the field during 1974 and
should increasie the percentage of successful transplants.
12-11
-------
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13-13
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13-15
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14 - APPENDICES
Appendix 1-1. Steering Committee
The Steering committee of the Escambia Bay Recovery Study
consisted of representatives of the Following organizations
outside of USEPA, Region IV:
Florida Department of Natural Resources
Florida Department of Environmental Regulation
Florida Game and Freshwater Fish Commission
Florida State University Marine Laboratory
Monsanto Chemical Company
Northwest Florida Regional Planning Council
Southeastern Fisheries Association, Inc.
University of West Florida
USEPA/ Gulf Breeze Environmental Research Laboratory
14-1
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Appendix 1-2. Recommendations of 1972 Enforcement Conference
(USEPA, 1972e).
To reduce or eliminate the accelerated eutrophication of
Es.cambia Bay and Mulat-Mulatto Bayou, and to provide water
quality suitable for a wide diversity of desirable uses, the
conferees make the following recommendations without prejudice to
the rights of the State of Alabama and Florida to enact more
stringent requirements. These recommendations would be
accomplished by not later than December 31^ 1972, except as
otherwise specified.
1. There shall be reductions of 90 percent 5-day BOD, 94
percent nitrogenous wastes, and 90 percent phosphorus wastes
discharged to Escambia River . and Bay from major sources in
Florida, including American Cyanamid Company, Monsanto Company,
and Air Products, Inc. Due to the distance from Escambia Bay of
Container Corporation of America's plant site, a reduction of 90
percent 5-day BOD waste will be required. These percent
reductions permit the following allowable daily waste effluents.
Container Corporation: 5-day BOD 4,850 pounds, total
nitrogen not applicable, total phosphorus not applicable.
Monsanto: 5-day BOD 605 pounds, total nitrogen 248 pounds,
total phosphorus 46 pounds.
American Cyanamid: 5-day BOD 425 pounds, total nitrogen 323
pounds, total phosphorus not applicable.
Air Products: 5-day BOD 17 pounds, total nitrogen 477
pounds, total phosphorus 35 pounds.
The foregoing allowable waste loads shall be obtained by
December 31, 1972. If further investigation shows that these
limits are excessive, Monsanto, American Cyanamid, and Air
Products must develop a plan to completely remove their
discharges from the bay.
There shall be maximum feasible reduction of carbonaceous
organic material. All waste dischargers shall monitor effluents
to ensure reductions, conduct feasibility studies, and submit a
plan of .abatement for carbonaceous waste to the conferees by
February 15, 1972.
Container Corporation shall provide further secondary
treatment of bleach plant and woodyard wastes.
The American Cyanamid Company shall immediately cease
discharging acrylonitrile.
2. The Environmental Protection Agency and the State of
Florida technical staffs shall schedule a series of in-plant
14-2
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investigations into treatment techniques and process control of
the Monsanto, American Cyanamid, and Air Products plants to
determine the effectiveness of present: attempts to meet
conference requirements. A report of such investigations shall
be made to the conference as soon as possible, but not later than
May 1, 1972. These investigations' are not in lieu of continued
efforts by the company to effect the results as outlined in
paragraph 1 above. In. addition, any other industrial waste
sources which may discharge into Escambia River and Bay or its
tributaries shall be reported on, with recommendations for
abatement.
The City of Pensacola shall submit to the conferees by May 1,
1972, operating data on the effects of the plant modifications
made to the Northeast Sewage Treatment Plant showing its
compliance with the recommendations of this conference. The City
of Pensacola and the County Commissioners of Escambia shall
report to the conferees by May "T, 1972, the status of the 5-year
master plan developed by the Escambia-Santa Rosa Planning Council
and adopted by the city and county. The status report should
include estimated dates for the implementations of the 5-year
plan.
3. An alternative for accomplishing these objectives is the
construction of a sewer collection system or systems around the
entire bay to intercept wastes from American Cyanamid, Escambia
Chemical, Monsanto and Northeast Sewage Treatment Plant as well
as future and minor present effluents. This is consistent with
the concept of metropolitan planning for waste management. All
domestic and industrial wastes could be treated at a central
facility with discharge away from Escambia Bay after the
recommended carbon, nitrogen, and phosphorus reductions have been
accomplished.
U. The Environmental Protection Agency's Gulf Breeze
Laboratory shall monitor the effluent and adjacent areas of the
Monsanto plant to determine the presence of any polychlorinated
biphenyls and provide monthly reports to the conferees.
5. The conferees recognize the critical situation
concerning the life cycle of Menhaden and are forwarding copies
of the report of the Menhaden Conference to NOAA and the
Southeast Fisheries association urging a plan for protection of
the valuable commercial species.
Because of the additive problems attendant to dead fish
decomposing arid recycling nutrients into 'the bay, as well as
presenting a health hazard, the conferees recommend that the
Governor of the State of Florida take actions as he deems
necessary for the immediate removal of such fish in the future
until such time as corrective measures are completed.
6. Color in the Escambia River at the Alabama-Florida State
line as measured at the Highway H bridge near Century, Florida,
1U-3
-------
shall be reduced to levels meeting Alabama, Florida, and Federal
standards. The conferees require that the Container Corporation
of America shall present a progress report by April 1, 1972, with
its recommendations for color removal.
7. It is recognized the Department of Transportation of the
State of Florida has retained a consultant group to evaluate and
make recommendations concerning the Mulat-Mulatto Bayou and the
1-10 Canal System. The Department of Transportation shall
provide the conferees by March 1, 1972, with their evaluations,
recommendations, and a plan of implementation for corrective
measures as recommended by their consultant. Upon approval or
modification by the conferees, this plan will be, referred to the
Governor of Florida for appropriate action.
8. No further construction dredging shall be permitted ,in
Escambia Bay and Mulat-Mulatto Bayou until the artificial buildup
of organic sediment deposits ceases and stabilizes. Maintenance
dredging of existing channels shall be by hydraulic pipeline or
by hopper dredge. Disposal of all dredged materials from
hydraulic dredging shall be done in a manner and to spoil sites
acceptable to the conferees.
9. The conferees recommend that the Environmental Protection
Agency in cooperation with the University of West Florida and the
State of Florida conduct field studies to determine the effects,
of thermal discharges from Monsanto and Gulf Power Companies on
the biota of Escambia Bay and River and report their findings to
the conferees by September 15, 1972.
10. Century, Florida, and East Brewton, Alabama, shall
install by not later than December 31, 1972, secondary waste
treatment facilities acceptable to their respective State water
pollution control agencies. These municipalities shall report to
their respective State water pollution control agencies on
progress being made beginning March 1, 1972, and each 90 days
thereafter.
11. Because of the many questions which have been brought to
the attention of the conferees regarding the overall ecology and
over-enrichment of Escambia Bay, the conferees recommend that a
recovery study team be organized under the overall direction of
the Environmental Protection Agency. This recovery team shall
include the University of Florida System, working through the
University of West Florida, the Florida Department of
Environmental Regulation, the Environmental Protection Agency,
and any other public or private agency, institution, or industry
with an essential contribution to make. Specific plans for the
recovery study—including staffing, financing, and basic
investigative methods—shall be submitted to the conferees by
April 1, 1972. Independent plans for gathering information in
the next several months that would complement the basic
objectives of the recovery program are encouraged to proceed.
-------
Appendix 5-1. HPDES eftluent liaitations for principal source discharges into Pensacali Bay and its tributaries..
Plant
CONECIJH BIVER,
of Aatirica
ESCAHBIA BIVEB
ESC1HBIA BAY
Horthaast SIP
ChOQ. CO.
Aaerican Cyanaoid Co.
PEUSACOU BAY
Rain Street STP
HAS Punsacola
ELACKBATE8 8IVC5
Hilton, Florida srp
HAS Uniting Field
AppunJi* 5*2. Point
Source
COI1ECUH BIVES
of Aaerica
1. k. nillor
Exxcn Corporation
ESCAr.BIA tiIVZH
Alger-Sullivan Lutsber c
Gulf I'onsr
ESCAKBIA BAV
Air Products and
CncJicjl Co.
Aoecicau CyaniBid Co.
ELACMATER SIVER
MAS WuitiD'l FlelJ
PEtlSOCOLA BAIT
NSS PEHSACOLA
Total
Suspended Total Total
OOD5 Solids Nitrogen Phosphorus
kg/day ppd kg/day ppd kg/day ppd kg/day ppd
Viator 2753 6C6C 11990 11,300 -
Sutnor 2200 0850 1900 11,000 - - -N -
Interia 199 ' 038 156 393 -
Final 53 116 53 116 63 139 15 32
IntociB 150 330 280 625 953 2100 27 60
Final 91 200 281 625 227 500 16 35
InteriB 3083 6796 599 1232 1311 2897
rinal 297 650 511 1120 27U 600
InteriB 1022 2250 1022 2250 -
Final 378 831 378 330 227 5?0 76 168
119 263 119 263
source industrial discharges and plant descriptions.
.
:o. Sawoill Holding ponJ
Electrical Generation Ash Pond
Hty. ot acrylic fibers Neutralization uands and
Spirahoff Cor Jones tic flow
AircLQLt rtaint nuance TciclKio-j filters
Aircraft maintenance Neutralization, chenlcal and
hlolnnlcal treatment and
polishing ponds
3ther Dates effective
kg/Jay ppd
On til Sep. 1978
Until Da?. 1978
Ootil June 1975
June 1975 to June 1977
Until Dae. 1976
Cyanide Jan. 1977 to Sep. 1978
6.8 11.9 OQtil HDf.1975
0.2 O.a Dec.197b to Dec. 1978
Phenols Until Aug. 1976
3.78 8.3 Aug. 1975 to June 1979
N3t issued as of Apr. 1970
Hat issued as of Ape. 1971
Oct. 1974 to nar. 1979
Type of Discharge Beceiviog Streaa
Coaecuh Biver
C3oliag water flurder Creek
Cooling water Little Esca«bia Cr
Lag spray,' lania. ffscaabia Bivec
boiler blowdowa.
Dooestic effluent, Escaibia Bivar
on?e tbrouuh cooling ,
viter. '
surface drainaye
Do Be stic eftlueat, Escaobia Bay
DDBGS tic. affluent,
process water
Domestic effluent
process water
1U-5
-------
Appenlix 5-3, Point source Industrial discharges (loadings in kg/uay).
Source
DOD5
Tatal
Suspended
Solids
Total
Nitrogen
total
Phosphorus
Hemirk
CONEC'JH 81V1SR
Container Corporation
of Aoerica
T. H. Miller
Exxcn Corporation
2200
U990
(3)
Subtotal
2200
4) Final NPDES permit limits.
-------
•e-
I
-j
Design
Flow Process Description
tcmd (4)
Receiving Stream
BODS
kg/day
Total
Suspandel
Solids
kg/lay
Total
Nitrogen
kg/day
Total
Phosphorus
kg/day
Remarks
Appendix 5-U. Point source domestic municipal treatment facilities.
( Henningson, Durham, Bichardson and Hart, 1975).
Source
ESCAKBIA _ CONECUH EIVEK
Andalusia, Alabama
North Side Disposal Plant
Nest Side Treatment Plant
South Side Disposal Plant
Erantley, Alabama STP (3)
Brewton, .Alabama STP
East Branton, Alabama STP
Evergreen, Alabama
Plant No. 1
Plant No. 2
Fort Deposit, Alabama STP
Greenville, Alabama STP
Luverne, Alabama STP
Troy, Alabama
East Side STP
Kest Side SIP
Century, Florida
Dniv. of West Florida
ESC AMBIA BAY
City of Pensacola, Northeast
PENSACOLA BAY
City of Pensacola, Hain St.
Harrington
Pen Haven
2.7
0.4
2.7
0.8
3.8
1. 1
3. a
1.0
9.1
5.7
3.8
5.7
2.3
1.0
1.9
Secondary
Intermediate
Secondary
Secondary
Secondary
Secondary
None
None
Secondary
Secondary
Secondary
Secondary
Secondary
Stabilization Pond
Extended Aeration uith
Polishing Pond
Prestwood 3reek
Collar Hill Cr. trib
Bay Branch
Conacuh River
Murder Creak
Murder Creak
Murder Creak
Murder Creak
Pigaon Creek
Persimmon :r.
Patsalagua Cr.
Walnut Creek
Conecuh ttiver
Escambia River
Escambia Siver
SUBTOTAL
81
12
81
23
11U
34
1 14
25
273
171
11U
425
170
28
57
1722
3.2
3.4. i
7.6
1. 1
Trickling Filter
Activated Sludge
Extended Aeration
Trickling Filter
Escambia Bay 199
Pensacola Bay 1022
Bayou Chico 227
Bayou Chico 95
SUBTOTAL 1344
31
12
91
23
114
34
68'4
255
273
171
10 25
343
136
23
57
3316
155
1J22
227
95
1344
63
9
63
18
89
26
89
19
212
133
89
133
54
22
44
1063
B4
784
176
74
1333
27
'4
27
8
38
11
38
8
91
57
39
57
25
9
19
U58
36
343
76
32
448
(1)
(1)
(1)
(2)
(1)
(2)
(2)
(2)
d>
(1)
(2)
(2)
(2)
(D
(1)
(2)
(2)
(1)
(1)
SANTA BOSA SOUND
Gulf Breeze, Florida 3.4
Pensacola Beach, Florida 1.5
Extended Aeration
Trickling Filter
Santa Rosa Sound 102 132
Santa Rosa Sound 121 182
SUBTOTAL 223 284
79
71
150
34
30
64
(2)
(2)
BLACIUATER BIVER
Hilton, Florida
YELLOW RIVER
Crestvian, Florida
6.4 Trickling Filter
5.7
Secondary
Blaskwatar Bay 193 193
Trammel Crack 170 17D
TOTAL
150
132
64
57
(D
(D
(1)
(2)
(3)
CO
Estimated assuming 30, 30, 23, and 10 mg/1 in the
B3D5 and TSS from interim permit limits; Total
in the effluent.
Proposed plant to be completed June 1975.
thousand cu. meters per day
kg/day 3851 5463 2623 1127
(ppd) 8491 12745 5783 2485
effluent for BODS, TSS, Total Nitrogen and Total Phosphorus..
Nitrogen and Total Phosphorus estimate! assuming 23 and 10 mg/1
-------
Appendix 6-1. Summary of salinity (ppt) data for the Pensacola Bay system
during January throuah September, 197-1.
Sta.
ADGV
ADGV
ADGV
AGJI
AOJI
AGJI
AOJI
AOJI
AGPH
AGPH
AGPH
AOFD
AJPD
AJFD
ALEX
ALEX
ALEX
BFEI
BFEI
BFEI
BJIV
BJIV
BJIV
BNGA
BNGA
BNGA
BREA
BREA
BREA
ECOM
ECGM
ECGM
EEDR
EEDR
EEDR
EEEM
EEEM
EEEM
EEDC
EEDC
EEDC
EEKV
EEKV
EEKV
EGLY
EOLY
EGLY
EGLY
EGLY
EHOD
EHGD
EHOD
EHPK
EHPK
EHPK
EIIL
EIIL
EIIL
EKC
EIKC
EKC
EKLQ
EKLQ
EKLQ
EKMP
EKMP
EKMP
EKMP
Dep.
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
B
C
D
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
5
5
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
8
12
12
11
12
12
12
12
12
12
12
12
12
12
11
12
12
12
12
12
12
12
12
12 '
12
12
12
12
12
Mean
8.1
11.8
18.8
13.1
13.3
11.3
16.2
22.8
13.3
13.9
20.2
12.5
15.5
23.5
13.8
18.7
27.5
0.9
1.7
10.1
1.9
2.8
8.3
3.0
7.0
11.2
5.9
12.2
17.7
0.3
2.9
1.6
0.2
1.3
2.8
0.3
1.1
2.3
1.7
2.1
3.2
3.8
5.2
9.1
1.2
5.1
7.0
U.I
11.2
0.3
5.6
11.1
5.8
6.1
8.2
3.3
1.2
7.8
2.7
1.5
U.8
3.8
1.9
9.0
1.7
6.1
15.1
18.3
Mln.
1.8
2.2
3.3
3.8
1.8
1.9
5.1
7.0
5.1
5.0
•5.5
3.6
3.6
6.2
1.0
6.8
21.1
0.1
0.2
0.2
0.0
0.0
0.0
0.0
0.0
0.2
0.2
0.7
2.8
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.2
0.2
0.3
0.3
0.3
0.0
0.0
0.0
0.3
0.3
0.2
0;0
0.0
0.1
0.0
0.0
0:0
0.1
0.2
0.3
0.2
0.2
0.2
0.2
Max.
11.8
22.7
29.1
18.7
19.5
25.3
26.3
30.3
18.1
21.8
28.9
19.5
26.0
28.8
20.0
27.9
29.9
1.6
3.5
17.3
1.5
9.2
16.8
6.5
19.3
22.0
18.2
23-3
27.2
1.9
15.8
16.0
0.9
13.6
17.3
1.7
11.6
11.9
7.8
12.1
12.1
12.3
13.9
18.8
12.1
13.3
16.8
22.2
25.3
2.0
18.1
22.3
13.6
13.7
18.0
U.I
15.1
20.9
8.8
13.2
20.0
12.0
12.9
18.9
13.6
11.9
21.9
25.6
CV*
18.9
53.5
39.0
38.1
37.7
10.3
37.3
28.3
33.1
39.2
29.9
13.8
16.2
25.7
35.8
36.0
7.5
60.3
68.1
61.3
80.3
96.6
75.0
69.1
90.9
11.6
80.2
57.7
38.9
192.1
191.8
126.5
195.9
300.1
230.9
175.1
293.9
231.1
153.6
171.0
131.2
110.5
106.3
83.0
101.3
90.5
89.0
71.3
53.7
202.8
125.1
89.9
73.3
73.1
67.8
113.7
115.8
91.3
112.3
101.7
66.9
102.7
91.5
65.1
97.1
79.1
53.3
16.9
Sta.
EKMP
EMQC
EMQC
EMQC
ENNB
ENNB
ENNB
ENNB
ENNB
EPLP
" EPLP
EPLP
EPRF
EPRF
EPRF
ERPB
ERPB
ERPB
ERPB
ERPB
ER10
ER10
ER10
ETLQ
ETLQ
ETLQ
ETQE
ETQE
ETQE
PEUE
PEUE
PEUE
P01
P01
P02
P02
P03
P03
P01
P01
P05
P05
P05
P05
P05
P06
P06
P07
P07
P08
P08
P09
P09
P10
P10
PU
'Pll
• • P12
P12
P13
P13
P13
P13
P13
Pll
Pll
P15
P15
Dep.
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C .
E -
A '
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12.
12
9
. 9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
18.2
8.1
12.1 -
17.1
6.2
7.2
15.7
19.3
19.8
7.1
8.9
15-5
9.6
15.0
18.0
9.0
9.8
15.1
21.0
21.6
0.0
0.0
0.0
9-9
11.8
28.1
U.3
12.6
16.8
11.2..
13.3
16.0
21.1
32.6 -
16.8
32.1
19.5
28.3
19.7
27.1
16.7
23.0
29.1
32.0
32.5
15.9
30.7
15.1
29.9
15.5
32.1
16.0
21.7
11.1
31.7
12.5
30.3
11.2
28.2
13.2
11.0
19-5
26.9
30.2
15.3
29.1
13.0
28.3
Mln.
0.3
0.3
0.3
0.'3
0.3
0.2
0.2
0.2
0.2
0;2
0.3
0.3
1.8
1.2
5.8
1.0
1.9
1.9
6.3
10.9
0.0
0.0
0.0
1.1
1.1
21.2
2.5
5.2
6.8
6.0 '
5-9
6.5
9.5-
-29.1
5.6
30.1
6.1
U.5
8.1
15-3
1.1
10.7
18.6
29.6
30.7
1.5
26.0
1.3
25.0
1.1
29.9 .
6.3 "
16.5
1.1
29.0
1.2
26.3
1.2
21.6
1.9
3.7
1.3
15.1
28.2
1.7
26.1
2.8
20.6
Max.
25.9
15.2
21.3
25.1
. 11.2
16.0
23.7
26.9
27.5
16.2
17.5'
25-5
17-5
23-9
27.6
1-7.6
18.1
27.3
28.9
29.5
0.0
0.0
0.0
18.8
26.1
31.0
19.3
23.6
27.1
17.5
21.1
21.0
35-. 5
. 36.0
26.2
31.8
26.1
33.8'
26.1
33.0
25.1
33.1
31.5
35.0
31.8
28.0
-31.8
27.6
31.5
25-9
35.0
21.5'
33.2
21,7
: 22:6
31.3
19.7
33-5
21.1
25.2
32.2
33.5
31.0
23.9
33.0
20.0
32.3
cv*
15.0
.62.9
52.8
16.2
81.2
77.1
56.1
15.0
11.7
72.3
66.5
60.7
55.1
15.6
11.1
65.3
57.0
52.1
36.6
21.5
0.0
0.0
0.0
61.2
19.6
9.3
17.2
15.2
38.9
36.0
32.6
31.7
36.7
6.0
10.5
1.1
31.0
21.7
27.1
18.1
37.3
31.7
16.6
1.6
3.7
18.2
8.5
16.8
8.8
13.2 '
1.7 •
37.5
23.6
15.8
1.9
51.8
6.9
57.1
U.3
19.1
18.7
12.7
19.8
5.9
39.1
7-3
16.3
10.9
1U-8
-------
6 - 2.- Vaciaoles used in calculating the flushing tines of Escaibia Bay during 1973
Variable
Estimated total effective
river discharge
Tidal Range
U. S. Highway 9C bridge
Bean Tids Level
ftOJl BSL
Volume of bay
Su
Si
Cu - outflow
QI - inflow
Flushing Time - T
Volume Displacement Time
Units
m 3/sec
m
0
3
mill, m
ppt
Ppt
m 3 /sec
m /sec
days
days
Appendix 6-2. (cont.) Variables used in
Variable
Estimated total effective
river discharge
Tidal Range'
D. S. Highway 90 bridge
Mean Tide Level
from MSL
Volume of bay
s«
Si
Cu - outflow
C i - inflow
Flushing Time - T
Volume Displacement Time
Dnits
m3 /sec
m
m
mill, m3
ppt
ppt
m 3 /sec
m 3 /sec
days
days
Study I Study II Study III Study IV
1398 630 173 122
0.1 3.6 0.2 0.5
0.0 3.3 -0.1 0.3
217 275 233 -235
0.0 3.0 8.5 18.)
2.0 1.5 ' 26 '.0 25.5
1398 630 257 415
0.0 0.0 84.0 293
•2. 0« 5.3 10.5 6.6
2. OK 5.3 15.6 22.3
calculating the flushing times of Pensacola Bay daring 1973.
Study I Study II Study III Study IV
1697 757 286 238
0.1 0.6 0.2 0.6
0.0 0.3 -0.1 0.0
838 880 817 822
U. 5 11.5 18.5 26.5
32 31 31.5 33
1969 1203 693 1782
272 446 407 157I»
4.9 8.5 13.6 5.3
5.7 13.4 33.1 45.7
14-9
-------
Appendix 6-2. (cent.) Variables used in calculating the flushing times of Pensacola Bay during 1473.
Variable
Estiiatei total effective
river discharge
Tidal Range
U. S. Highway 90 bridge
Mean Tide Level
froai MSL
Voluae o£ bay
su
Si
fiu - outflow
C i " inflow
Flushing rime - T
Volume Displacement Time
Units
n3 /sec
or
in
mill, o
ppt
ppt
n 3 /sec
B /sec
days
days
Study I Study II
1697 757
0.1 3.6
0.0 .0.3
« 3d dBO
i».5 11.5
32 31
1969 1203
272 <»«6
U. -J 8.5
5.7 13. U
Study III
2B6
0.2
-0. 1 ."
817
18.5
31.5
693
U07
13.6
33.1
Study IV
2)3
0.6
• ; o.o
822
26.5
30
1732
157»
5.3
U5.7
-------
Appendix 6-3. Summary of temperature (aeg. C.) data for the Pensacola Bay system durincj
January through Septemoer, 197U (Pensacola 3ay data from the University of West Florida).
Sta.
ADGV
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AGPH
AJFD
AJPD
AJFD
ALEX
ALEX
ALEX
BPEI
HPEI
BFEE
BJIV
BJIV
BJIV
BNGA
BNGA
BNGA
BREA
BREA
BREA
ECGM
EOGM
EO3M
EEDR
EEDR
EEDR
EEEM
EEEM
EEEM
EEDC
E5DC
EEIX
EEKV
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHGD
EHPK
EHPK
EHPK
KIM.
ETTT.
K \ II.
EffiC
EKC
EIKC
EKLQ
EKLQ
EKLQ
EKMP
EKMP
EKMP
EKMP
Dep.
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E .
A
C •
E
A
C
E
A
B
C
D
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
5
5
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
8
12
12
11
12
12
12
12
12
12
12
12
12
12
11
12
12
12
12
12
12
12
12
,12
12
12
12
12
12
Mean
23.0
23.1
23.7
23.3
23.3
23.3
23- 1
23.7
23.3
23.5
23.1
23. 4
23.3
23.4
23.5
23.3
23.7
25.8
26.3
27.8
22.3
22.6
23.4
22.3
23.1
23.6
22.7
23.1
24.0
21.5
21.9
22.2
21.4
21.6
21.7
21.4
21.5
21.7
21.8
21.5
22.2
22.8
22.3
23.3
23-3
23.2
23.2
23.6
23-9
22.1
22.3
22.8
24.3
23.7
24.4
22.9
22.7
22.8
22.7
22.6
23-1
23-5
23.0
22.9
23-3
23.1
23-3
23.6
VOn.
11.1
11.4
13-2
12.0
12.1
12.0
12.1
12.9
12.0
12.2
12.2
12.3
12.2
12.3
12.5
12.8
16.6
23.4
23.5
23.5
U.I
11.1
11.4
U.I
U.3
11.8
U.4
12.1
14.7
11.1
11.0
11.0
11.1
11.2
11.1
11.3
11.3
11.3
U.2
11.2
11.2
12.1
12.3
U.6
12.7
12.4
12.2
11.7
12.0
U.4
U.4
11.8
13.5
13.3
12.2
12.4
12.5
12.2
12.7
12.3
14.0
13.8
13.7
12.0
13.9
13.6
12.0
12.3
Max.
29.3
29.5
29.9
29.8
29.8
29.8
29.9
30.1
29.3
29.5
29.5
30.0
30.0
29.9
30.0
29.7
29.5
27.1
28.8
30.2
29.0
30.4
30.2
28.6
30.0
30.0
29.2
29.6
29.8
29.0
31.1
31.0
29.0
30.1
30.3
28.9
30.8
30.8
29.5
30.2
30.1
30.7
30.5
30.8
30.6
30.7
30.8
31.1
30.9
29.3
30.3
30.2
31.2
31.1
31.0
30.9
30.2
30.5
30.5
30.4
30.5
30.7
30.1
30.5
31.3
30.7
30.7
30.5
.CV*
25.5 '
25.7
24.5
25.6
25.5
25.4
25.1
25.4
26.3
25.3
25.7
25.3
25.6
25.4
25.1
25.4
22.1
5.5
7.2
9.1
25.5
26.3
26.6
25.8
27.1
26.4
25.5
25.7
22.9
26.7
28.8
28.5
26.3
27.0
27.6
26.1
27.4
28.0
26.9
29.6
28.2
27.7
27.7
27.3
26.2
26.1
26.7
27.2
26.0
27.4
28.0
27.2
24.9
25.1
25.1
26.5
25.9
27.0
26.9
27.3 '
25.6
25.5
24.9
26.7
25.6
25.5
27.1
26.3
Sta.
..EKMP
EMQC
EMQC
EMQC
ENNB
ENNB
ENNB
ENNB
ENNB
EPLP
EPLP
EPLP
EPRF
EPRP
EPRF
ERPB
ERPB
ERPB
ERPB
ERPB
ER10
ER10
ER10
ETLQ
EILQ
ETLQ
ETQE
ETQE
ETQE
PEUE
FEUE
PEUE
P01
P01
•P02
P02
P03
P03
P04
P04
P05
P05
P05
P05
P05
P06
P06
P07
P07
P08
P08
P09
P09
P10
P10
PU
PU
P12
P12
P13
P13
P13
P13
P13
P14
P14
P15
P15
Dep.
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
No.
12
12
12
12
12
12
'12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12^
12
12
12
12
12
12
12
12
12
12
Mean
23.6
24.5
24.0
24.1
24.3
23.6
23.5
23.8
23.9
24.3
23.7
23.6
24.0
23.9
23.8
23.7
23.4
23.3
23.5
23.5
21.1
21.2
21.1
23.8
23.1
23.6
23.8
23.7
23.7
26.7
26.0
25.8
22.9
22.7
23.0
22.9
23.3
22.7
23.2
22.9
23.3
22.9
23.1
23.0
22.8
23.2
23.0
23.4
23.1
23.3
22.9
23.1
23.1
23.4
23.0
23-5
23.1
.23.1
23.2
23.5'
23.3
23.2
22.8
23.2
23.6
23.4
23.7
23.2
Mln.
13.0
14.5
13.5
13.3
14.3
13.7
11.9
13.2
14.6
13.9
12.8
12.0
14.9
13-9
13.3
13.6
12.4
12.5
12.8
13.8
10.8
11.1
U.I
13.3
11.9
16.8
14.0
12.8
13.0
16.5
16.5
16.2
13.7
16.3
13.3
16.4
14.1
15-3
13.4
13.7
13.7
13.9
16.8
17.1
16.8
13.1
16.7
13.6
16.5
13.8
16.9
13.9
14.5
13.8
16.8
14.7
16.7
13.9
16.0
13.6 •
13:i
13.2
14.9
16.6
14.1
16.5
13.6
16.5
Max.
30.5
32.1
30.7
30.8
32.9
31.3
30.4
30.4
30.4
31.6
30.9
30.8
30.6
30.1
30.0
30.0
29.8
29.9
29.7
29.7
28.2
28.1
28.0
30.2
30.0
29.4
30.3
29.9
29.9
30.7
29.4
29.2
28.1
28.8
28.5
29.0
29.3
29.0
29.1
29.2
29.5
28.8
29.1
29.0
28.9
29.4
29.2
29.7
29.3
29.2
28.9
29.2
28.8
29.5
29.1
29.8
29.3
29.5
29.4
"29.7
29.4
29.7
29.2
29.3
30.0
29.3
29.6
29.3
CVS!
25.7
25.1
24.8
24.5
26.1
25.5
26.6
25.1
23.5
25.3
26.0
27.4
23.8
24.1
24.8
24.2
25.4
25.6
25.4
25.0
26.3
25.9
25.9
24.4
26.2
21.9
24.2
25.4
24.9
18.2
17.1
17.5
21.5
19.9
23.5
20.6
23.4
22.6
24.2
23.8
23.6
22.6
20.6
19.7
20.4
24.2
20.1
23.6
20.9
23.8
20.4
24.1
23.4
23.4
20.4
23.5
20.7
23.3
21.4
23.8
23.9
24.0
23.8
20.8
23.8
21.3
22.1
22.4
14-11
-------
•C
I.
NJ
w-
-0.4-
lOkm/hr
/
^
f ' f f •» v, • */ ' * ^^\ ' ' * '
05 10 15 20 25 30 35 40 45
i i i ill i i i i
i i i i i i i i i i i i i i ii
1 1
f- w/-'t '
50 55 60 65 70
1 1 It 1
1 1 1 1 1 II
|
/ .* t „ / „
75 80 85 90
ii i i
i i i i i i
1
>^^\ ^ t f
95 hours after
i dump
, , ," , i ,
1
08/06/73
08/07/73
08/08/73
08/09/73
08/10/73
Appendix 6-U. Tide and wind conditions during the August 1973
dye study.
-------
\
• » t\ t /, \ A
MHHHHH HHHHHHHHH H M HHHHH H
8/27/74
8/28/74
8/29/74
8/30/74
t
—V.*
15 km/Mr
9/17/74
9/18/74
9/19/74
9/20/74
9/21/74
9/22/74
9/23/74
I > II ID II >l
9/24/74
Appendix 6-5. Tide and wind conditions during the Air Products
and American Cyanamid dye studies.
14-13
-------
o
z
o
u
4.5 -I
4.0-
3.5-
3.0-
2.5-
2.0-
.8 -
1.0 -
0.5 -
0.0
0.0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 I.S 2.0
Appendix 6-6. Effluent dye concentrations during American
Cyanamid dye study.
4.0-,
3. 5-
2.5-
u
u
>
o
1.5-
1.0-
0. 5-
0.0
-O.I 0.0 O.I 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0 I.I 1.2 1.3
TIME (doys)
Appendix 6-7. Effluent dye concentrations during ths
Products dye study.
Air
11-1U
-------
I
-^
en
'Emonufl 1*1. PtntOCOta Boy
'Emonuel PI ftfiSOCOlO Boy
Appendix 7—1* Location o£ sediment
sampling stations in the Pensacola
Bay system during 1973-1974.
Appendix 7-1 (cont• ) Location of
sediment sampling stations in the
Pensacola Bay system during 19734974*
-------
II 01
Appendix 7-1 (cont. ) Location of sediment sampling stations In the
Pensacola Bay system during 1973-1974.
-------
Appendix 7-2. Sediment sample stations and their
habitat type in the Pensacola Bay system.
Sand Shelf
Transitation Zone
Mud Plain
> ED
•'/, EE.
"GD
IE
KE
MC
MD
MMD
OD
QD
QE
SD
GC2
OC2
BWC
EBWC
SRA
SRC
EBED
EBEE
EC • .
GC
1C
ID
KC
KD
MB
OB
OC
OB
OC
SC
GB2
OB 2
BWB
EBWB
EBEB
EA
EB
GA
GB
IA
IB
KA
KB
MA
OA
QA
QB
SA
SB
GA2
OA2
BWA
SB
14-17
-------
eiy.
g j
[2
CO
£5
C6
[7
td
C9
C1C
C11
1 12
1 1
£0
17
E8
Gt
G2
G3
GO
G5
G6
G7
G8
11
12
10
15
16
7
8
1
2
3
0
5
6
7
8
9
10
1 1
Appendix
Station
111
«2
S3
no
us
ft
B7
HB
n*
mo
01
C2
03
04
05
06
C7
ce
09
010
Cl
02
C3
C3A
c.4
cs
C6
C7
ca
C9
CIO
51
52
53
SO
55
56
SI
58
59
S10
Sll
CHI 2
CH7
CU1C
CHI 9
CH16
CHI5
anil Pana
""ft
5. 12
5.82
2.65
0.67
0.60
2. 16
2.0U
2. JO
2.0 1
2.22
0.70
1.70
2.01
2.32
1.65
1.06
0.85
1.52
1.30
2.65
2.96
1.25
1.22
0.76
0.76
1.95
2.22
-
3.63
2.63
2.32
1.71
0.79
1.25
1.52
3.02
3.93
2.62
2.62
2.5)
2.56
0.55
0.33
7-3|
Depth
<•>
0.79
1.01
2.83
2.77
2.77
2.70
2.70
2.68
1.28
0.37
0.61
1.98
2.71
2.99
-
3.26
3.08
-
1.07
0.06
0.58
1.19
-
-
-
-
-
-
-
-
-
0.60
0.90
3.80
9.05
0.08
0.18
4.18
3.90
3.47
1.07
0.76
-
-
-
-
-
-
•d City Bays
Total
C.36
_
_
-
_
.
.
_
_
-
.
-
0.21
0.10
0.04
0.01
-
-
-
0.23
0.27
-
-
-
-
0.30
0.10
-
0.16
0.20
-
-
-
-
0.36
0.12
0.53
0.02
0.03
0.25
0.00
-
-
Organic
1.00
-
-
-
-
-
-
-
.
.
-
-
-
1.31
0.52
0.20
0.37
-
-
-
1.56
1.51
-
-
-
-
1.02
0.63
-
0.97
1.50
-
-
~
-
0.09
1.39
2.30
1.59
0.00
1.95
0.33
-
-
Phosphorus
(•9/01
0.19
-
-
0.31
0.25
C.27
6.29
0.31
0.20
0.02
-
0.10
0.29
0.15
-
C.33
0.19
-
-
-
-
-
0.30
-
0.36
-
-
0.28
-
~
~
0.01
.
-
0.35
C.38
0.36
C.36
0.20
-
-
-
t.28
0.37
0.29
0.33
0.27
0.91
Hitrogon
(B9/9I
0.11
-
.
2.60
.39
.36
.65
.63
.31
. 17
.
.63
.51
.13
-
1.63
0.69
-
-
-
-
-
i.ae
-
1.83
-
-
1. 54
-
-
-
0.06
-
1.81
2.72
2.01
1.81
1.37
-
-
-
1.47
2.41
1.54
2.65
2.08
2.70
percent
12.7
10.5
1 J.I
0. 8
o.n
0.7
5.3
6.2
3.3
3.3
a.O
0.3
5.6
6.5
6.0
1.6
2.2
1.3
6.3
u.8
9.9
9.0
0.8
1.2
1.2
0.7
a. 3
10.2
12.7
12.7
11.6
1.6
C.9
0.6
0.5
0.6
13.2
12.
10.
li .
7.
3.
0.
0.
3rganlco
(»l
0.0
0.3
3.3
17.6
8.1
11.9
13.0
15.9
7.2
0.6,
0.1
10.5
10.9
13.1
10.0
10.0
10.7
-
0.5
1.0
0.0
0.3
13.2
-
11.7
10.9
10.3
9.2
0.3
0.7
0.5
0.3
0.3
15.7
10.2
21.0
13.5
12.7
7.7
2.6
0.4
0.6
14.2
12.1
10.9
12.8
9.1
13. C
Organic
1.4/91
05.9
-
-
-
-
-
-
-
-
-
-
-
-
20.5
19. C
6.7
9.3
-
-
-
36.3
26.0
-
-
-
-
31.7
20.6
-
30.9
29.9
-
-
-
-
1.6
02.1
39.3
30. a
16.0
23.0
13.2
-
-
Carbon
("9/91
2.1
-
_
30.0
24.9
31.7
33.2
35.1
25.8
0.6
-
37.2
36.11
28.8
-
35.7
29.9
-
-
-
-
-
30.3
-
36.3
-
-
27.9
-
-
-
1.7
_
-
30.7
30.3
35.9
23.1
20.9
-
-
-
90.2
37.0
37.2
"2.3
16.3
06.6
P 9
Scdlnont
Type
Saniy Silt
Sandy Silt
oilty Sand
SJnd
Sand
Sand
Sand
Silty Sand
Silty Sand
Silty Sand
silty Sand
Sand
SLlty sand
Silty Sanil
Silty Sand
Sand
Sand
Sand
Sand
Sand
Silty Sand
Silty Sand
sand
Sand
sand
sa nd
Silty Sand
Sand-Silt-Clay
Sandy silt
Sandy Silt
Sand-Silt-Clay
Sand
Sand
Sand
Sand
Sand
Sandy Silt
Sandy Silt
Sand-Silt-Clay
Silty Sand
Silty Sand
Silty Sand
Sand
Sand
Typo
Sand
Sand
silty Sand
Silty Sand
Sandy Silt
Sand-Silt-Clay
Sand-Silt-Clay
Silty Sand
Silty sand
Sand
sand
Sand-Silt-Clay
silty Sand
silty sand
silty Sand
Silty sand
silty Sand
Silty sand
sand
Sand
Sand
sand
Sand-Silt-Clay
-
Silty Sand
Sand-Silt-Clay
Silty sand
Silty sand
Silty Sand
Sand
Sand
Sand
Sand
clayey Silt
Clayey Silt
clayey Silt
Clayey Silt
Clayey Silt
Sand-Sllt-Clny
sand
Sand
sand
Clayey Silt
Silt
Clayey Silt
Sandy silt
Sand-Silt-Clay
Sandy silt
Clay
10.9
14.7
7.9
1.2
1.2
1.3
8.0
10.1
10.3
9.0
8.5
0.6
11.6
16.5
11.6
3.7
0.0
2.5
7.4
1.0
15.9
15.8
1.4
2.0
0.6
1.5
15.3
20.6
18.0
13.0
21.6
5.2
1.5
1.1
0.6
1. 1
10.3
9.9
27.6
10.9
16.3
7.4
0.8
1.6
=Uy
0.3
1.7
10.0
19.8
16.9
25.3
20.5
19.1
12.5
1.3
1.3
26.2
15.
18.
17.
14.
13.
10.
1.6
1.3
0.8
0.8
23.2
23.2
17.9
20.7
13.6
16.5
10.8
2.2
0.6
C.4
C-.3
2.9
34.5
25.9
28.7
31.6
22.4
6.7
C.6
C.B
39.6
18.3
15.8
15.7
26.1
16.6
Silt sand Bill Grain Sin
• 50.
47.
29.
1.
1.
3.
15.
32.
26.
30.
23.
0.
31.
3o.
23.
a.
7.
6.
17.
3.
30.
29.
1.
0.
8.
3.
02.
35.
01.
55.
35.
10.
2.
1.
1.
1.
61.
69.
43.
21.
29.
18.
9.
1.
9 30.3 65.8 1.
1 38.1 61.7 0.
9 61.2 36.8 3.
5 ' 97.3 2.7 1.
8 97.0 3.0 2.
6 95.1 9.9 2.
3 76. a 23.2 3.
1 57. a 92.2 3.
9 63.3 36.7 3.
0 60.6 39.4 3.
I 67. a 32.2 3.
9 98.6 1.4 1.
6 56.9 93.2 1.
2 09.3 50.7 3.
3 65.2 39.9 3.
7 87.5 12.5 2.
3 88. 11.9 2.
3 91. a. 9 2.
1 75. 20.5 3.
J 96. 9.3 1.
» 51. 46.3 3.
3 59. 45.1 3.
9 96. 3.3 2.
0 93. 6.1 2.
2 87. 12.8 2.
7 90. 5.2 1.
1 02. 57. »
3 45. 55.0 4.
3 40. 59.2 9.
9 31. 63.3 9.
9 42. 57.5 9.
1 84. 15.3 2.
3 95. 4.3 2.
6 97. 2.7 1.
8 97. 2.6 1.
1 97. 2.5 1.
2 24. 76.0 4.
1 21. 79.} 0.
5 28. 71.2 4.
4 67. 32.4 1.
-
'
•'
4 95. 95.7 1.3
1 79. 25.7 3.9
9 93. 1.6 1.9
9 96. 1.9 1.7
(»)
0.
•2.
18.
39.
61.
16.
01.
16.
10
1.
1.
27
36
30.
31.
29
29
18
1.
2.
1
0.
02.
92
36
39
10.
28.
17.
1.
1.
0.
0.
6
57
53.
16
57
38.
12.
0.
1.
53.
75.
53.
90.
98.
55.
(» (II
98.1 1.7 1.9
95.4 4.S 2.1
71.9 28.1 1.1
90.3 59.
21.7 78.
38.0 62.
38.1 61.
99.0 55.
56.6 93.
96.9 3.
97.6 2.
5 06.2 53.
9 98.0 52.
3 97.1 52.
3 51.6 98.
7 55.9 90.
1 57.3 92.
5 71.0 28.
9 96.5 3.
1 96.7 3.
2 98.0 2.
6 90.6 1.
3 39.6 65.
2 31.6 65.
7 45.4 54.
: 00.2 59.
3 07.1 52.
0 55.5 44.
2 72.0 28.
4 96.4 3.
1 98.3 1.
6 99.0 1.
3 99.0 0.
9 7.2 92.
2 a. 3 91.
) 20.2 79.
7 9.6 90.
6 1C. 8 89.
9 39.2 60.
2 81.1 la.
B 98.6 1.
2 98.1 1.
7 6.8 93.
3 5.9 9t.
i 11.1 aa.
a 39. 5 60.
5 25.4 79.
7 27.7 72.
0.1
9.4
9.1
9.3
9.0
1.6
2.1
2.2
1.4
1.1
1.4
3.5
3.1
1.0
1.1
2.1
1.1
1.0
1.7
1.9
1.9
3.3
3.6
3.6
3.2
1.9
2.1
1.7
1.2
1.7
9.8
9. 8
4.6
4.e
9.8
9.1
3.0
2.0
2.0
5.0
4.6
4.9
9.1
4.5
5.4
m-18
-------
Appendii 7-3 (rant) . Physj.
Bay, and Pana aa city Bays.
IIOLH
110
ERIV
EB21
IBM
EB20
BID1
SEBV
EB16
EB19
BEB
EA
EC
ED
EE '
ESC 1
ESC 2
GA .
GB
GC
CD
IA
IB
1C
ID
IE
KA
ItB
KC
KD
KE
A
B
C
D
HA
HB
BBC
OA
OB
OC
OD
7)" ph°.,%tus
0.10
0.13
-
0.02
.
-
_
-
0.10
-
-
2.19
2.13
K3U
0.78
-
-
2.19
1.77
1.35
1.08
2.35
1.19
1.81
1.08
0.91
2.12
2.11
1.89
1.73
0.77
2.73
2.08
1.11
0.90
2.81
2. 15
2.15
1.56
3.20
2.02
1.51
1.23
0 ' P t
2.62 12.7
2.01 12.3
-
0.06 0.1
.
-
.
-
2.17 10.0
.
0.7
0.5
17
5.7
0.2
0.1
0. 1
0.1
2.9
1.9
3.7
1.6
9.7
8.0
6.5
1.8
0.6
9.2
6.6
0.7
0.1
0.2
9.8
6.6
0.6
0.6
9.0
3.6
0.8
0.3
- , '•'
5.6
2.7
0.6
10.3 clayey Silt
39.3 Clayey Silt
-
Sand
-
-
.
-
02.7 Silty sand
Sand
(Grav) Bud and S
Sandy nud
sandy nud (r,. SH
Fine sand
Pine Sand
Fine Sand (G, U)
Fine Sand (G,Q)
Sandy nud(G,5H)
nuddy V F Sand(
Fine Sand(G,5H)
nuddy P Sand (3 ,
Sandy nod
Sandy nud(G.SH)
Sandy nud
nuddy ? sand
fled Sand (G.SII.
Sandy nud
Sandy flud(G,Sll)
Buddy F Sand
Pine Sand (G.SII)
Fine sand (G, Q)
.fud(G,SH)
Sandy nud(G,SH)
Pine Sand (G,SH|
Pine sand(G,SH)
Fine sand(G, SH
Fine Sand
Hud
Sandy Hud(G,SH)
nuddy F Sand .
Pine Sand (G, SH
(11
26. 1
22.8
0.5
C. 1
C.6
0.0
I'.O
1.6
8.6
0.1
7.5
25.1
28.7
1.7
0.7
0.1
0. 1
17.0
10.2
2.7
a. 9
15.2
11.2
33.6
1.9
1.3
19.5
35.0
3.8
. 2.1
0.3
59.5
32.3
1 .8
1.3
21.8
19.1
3.0
0.7
61.0
20.9
8.1
1.5
01
61. S
67.1
1.1
C.O
1.3
0.7
1.9
2.3
36.9
tl. 1
1.6
19.5
56.7
1.5
0.6
0.6
0.1
33.7
23.1
1.2
15.7
03.7
01.0
12.7
9.3
1.2
39.5
10.2
7.1
3.5
0.3
35.3
36.9
1. 1
0.1
11. S
10.0"
0.6
35.7
15.3
10.9
1. 1
(HI
12.0
10. 1
98. 1
99.9
98.2
99.3
99 9
97.1
95.7
50.7
99.8
87.5
25. 1
11.6
96. 8
98.7
99.3
96.8
08.7
66. 7
93. 1
75.0
11. 1
15.2
• 23.7
86.2
97.2
10.9
20. 1
89.1
90.3
99.3
0.2
30.7
97. 1
98.2
30.5
35. 8 '
98.7
2.9
30.0
81.0
97.3
01
87.7
89.9
1.9
0.1
1.8
0.7
0.1
2.9
1.3
05.
0.
12.
71.
85.3
3.2
1.3
0.7
0.5
51.3
33.3
6.9
20.5
88.9
82.7
76.3
13.8
2.5
89.1
75.1
10.9
5.5
0.6
95.5
69.2
2.8
1.7
33.6
29.1
1.3
97.1
66.1
19.0
2.7
0.7
0.7
1.8
0.9
1.3
1.1
1.2
1.6
0.5
3.6
2.0
1.7
3. II
2.6
2.8
2.0
2.3
2.3
2.0
3.2
3.0
2.7
2.9
3.2
3.0
1.0
2.2
1.9
3.1
2.9
2.3
2.3
2.2
3.1
2.9
2.0
2.3
2.0
1*0
2.0
3.1
3.0
2.5
2.S
Appendix 7-3 (contl . Physical and chonical data froa core sa.plina stations in the Pen9acola Bay syste., choctavhatchee
Bay, and Panana city Bays.
Station
OA
OB
CC
CD
CE
SA
SB
SC
SD
sin 1
sin 2
lEXAH
i
GA(70
GB(71|
GC(70)
OA(70|
OB(70)
OC(70|
EUA
EUB
BUG
EBUA
EBUB
ESD
EBD
CBD
SBA
SBB
SBC
LXH-1
LNM-2
LMH-3
LNH-1
LHN-5
LI. 11 -6
LNS-1
LNS-2
LKS-3
IHS-1
LNS-5
LHS-6
Depth
CI
3.20
2.95
2.25
1.12
1.25
0.82
3.75
3.31
1.50
2.11
5.18
2.00
0.57
2.00
1.10
0.50
2.70
1.20
o.ao
2.60
1.1C
C.90
2.3C
1.50
5.60
7.00
8.10
5.80
1.70
1.2C
1.30
2.10
2.10
2.30
2. 10
1.50
1.30
2.00
2.23
2. 10
2. 10
1.30
Total
Phosphorus
(19/91
_
.
-
-
-
- "
-
-
-
-
-
-
-
0.13
0.06
0.01
C.37
0.11
C.03
0.09
0.00
0.03
0.28
0.32
0.05
0.10
0.07
0.05
0.03
0.03
0.03
C.28
0.28
0.17
0.20
0.03
0.03
0.27
0.35
3.33
0.51
0.09
Or anic
H itrogon
(au/g)
.
-
.
-
-
-
-
-
-
-
-
-
-
0.39
0. 16
0. 16
0.72
0.36
0.08
0.69
0. 11
0.01
0.17
0.21
0.72
0.78
0.71
0.12
0. 16
0.30
0.00
0.63
0.56
0.66
0.51
0.02
0. 12
0.53
0.69
0.65
0.65
0.05
Qrganics
HI
0.0
3.7
0.5
0.3
0.2
11.9
13.2
8.7
0.0
0.5
0.3
8.5
0.5
3.5
1.3
1.0'
20.3
3.5
0.5
13.8
1.1
1.0
5.0
2.0
26.0
21.1
25.3
1 .2
0.7
1.8
0.5
11.7
9.7
11.3
3.1
1.1
1.3
7.1
12.5
13.9
10.9
5.d
0
Carbon
(»u/9l
.
-
-
-
-
-
-
-
.
-
-
-
-
17.3
6.0
20.3
36.1
13.5
2.0
05.5
5.7
' -tl.1
21.8
8.5
33.5
36.1
35.1
2.5
1 . 1
6.C
1.5
45.9
36.5
38.2
31.9
u.5
5.7
28.1*
39.5
3H.C
42.7
20.7
Type Clay Silt Sand flu3 Grain Site
(K) <*) (lj (ft)
Nuddy Floe Sand 21.6 14.1 64.3 35.7 2.8
nuddy Fine Sand 27.1 22.1 53.8 19.2 3.0
Silty Fine Sand 2.2 15.2 82.6 17. U 2.$
Silty Pine Sand 0.8 0.4 98.8 1.2 2.5
Fine Sand(G,SH) 0.5 0.3 99.1 O.B 2.3
Clay 67.5 30.3 2.5 97.5 2.5
Clay 69.2 25.4 2. 4 97.6 3.0
Hud Ned Sand(G, 22.0 12.1 45.2 34.1 1.9
Pine Sand 0.5 0.2 99.3 0.7 2.0
Ned Sand(G.Q) 1.4 1.3 97.6 2.4 1.6
Ned Saod(G.a) 0.5 0.4 98.8 0.8 1.2
Sand Nud(G, SH) 59.7 27.8 12. Q 87.5 2.0
aediua Sand 3.7 2.3 94.0 6.0 1.7
--.,-.
-
-
_
.
. • _
_'__,-
_
______
- _
_ - _
_,_"... - .
'- -•:..-.-
- •- .__•_.- »
' - - ,- '
: -•-'•-.•-
- . _ •
..'_._
-____'
--_...
-___._
_
-
___»-'•
--_..-•
- - ...
_
_
_
14-19
-------
Silt
ID
1-1
1-3
1-5
1-7
1-10
1-19
1-15
B-1
e-5
S-6
E-7
[-9
B-11
I-I1C
EU1
eva
EiC
BIC
EIO
CAT
CB-I
CB-2
CB-2
CB-2
CB-3
CB-«
CB-5
CB-5
CB-5
CB-6 1
EBV1
IB«B
EBWC
ISO
01
CB
GC
01
OB
OC
PC-1
PC- 2
PC-
PC-
PC-
PC-
K- 1
PC-
PC- <
PE»
TCI
>C-I
1C- 2
C-1S
1BE-1
EBB-B
1B8-D
EBI-E
EBE-C
C.O
C.O
0.9
1.3 0.1
.0 C.O
.6 0.3
.90' 0.3
0.0
C.2
0.2
0.2
e.o
.70 0.3
0.9
.60 0.2
.10 C.O
.90 0.0
.80 0.2
.10 0.21
0.0
.10 O.lf
.70 0.3
.00 0.9
.00 C.5
.10 0.3<
.90 0.3
.SC 0.3*
.00
.00
.79 0.2
.30 C.O!
.70 C.O
.90 0.0
.60 0.01
.00 0.1
.90 0.0
.S3 0.0
.90 0.3
.20
.SO 0.0<
.10 0.3
.20 0.<
.60 0.1!
.30 0.9f
.70 0.6
.10 0.36
.10 0.62
.20 0.6
.20 O.ie
.50 o.o:
.WO 0.2
.30 0.16
.go o.u
0.25
.70 0.7'
,«0 0.0<
.20 0.03
.go o.o
.30
0.01
0.01
0.09
0.6B
0.0
0.53
0.15
0.39
0.73
0.60
0.13
0.22
0.15
0.9S
.50
.32
. 19
.65
.S3
0.39
1.33
0.03
o.ts
0.00
2.53
0.83
1.58
1.03
o.as
2.53
0.03
0.2«
0.31
0.83
0.33
0.32
0. 18
0.53
_
0. 37
1.23
1. 10
1.«3
1.60
1.35
0.50
1.38
1.93
0.60
8:M
0.98
0.60
1.C4
1.26
0.75
0.11
0.23
-
0.1
0.1
3.2
6.8
2.3
16.5
13.8
9 .9
17.1
27.7
10.3
1.3
12.7
25.3
12.3
1.9
0.8
10.0
16.3
1.5
19.8
22.1
11.6
8. a
22.7
21.5
17.3
15.2
13.9
20.2
.0
.1
.9
1 .9
.2
.8
.2
2 .8
[3
1 .0
1 .1
13.9
16.1
13.9
«.8
15.1
25.7
9.9
,2:o-
5.8
6. a
12.3
12.0
2.1
0.3
0.5
-
0
'3
0
19
10
36
33
33
20
-------
Appendix 7 - i». Pesticides concentrations in the sediments of the Pensacala
Cay system daring 1973 through 1974.
Eesticida
Aldrin
Lintiane
Chlordane
ChlorobenziLate
EDO
CDE
CCT
Eieldrin
Endrin
HeptdChlor ilpoxide
Heptachlor
Hethoxchlor
Toxapliene
Eiazinon
Guthion
Methyl r-arathion
Farathion
Halatniou
Ethion
Trithion
Hire*
Approximate 'liniraun Detection Limit
(py/Xq)
0.
0.
2.
25.
•^
0.
1.
0.
1.
-'•
:.
5.
15.
10.
25.
1.
2.
u.
u.
2.
1 .
25
1C
50
00
50
5"
00
5-:
0"
57
25
•) ij
CO
j C
00
)0
00
OS
•°
00
00
Appendix 7-5. Nutrients (m-j) ^resent in the reictor v.itec by lay numoec in tne
sedioaat nutrient release study.
EGLV
Day
>D N UQibt? C
,
3
6
9
12
16
20
24
33
41 '
46
54
6C
65
67
C
4
6
11
17
26
32
3B
40
42
45
Total
Phosphorus
1.1 2d
0.674
0.387
0.293
C.24B
0.247
0.613
C.613
1. 24 1
• C.410
C.68U
0.344
C.577
0.704
0.4*6
C.230
0.23C
C.233
C.274
C.230
C.2JO
0.231
0.317
-
C.660
0.3SO
Nitrate-
Nitrite
<«>9>
1.52'i
•? . 5 2 **
0.435
: . 52-*
3.52H
* . 4do
0.48-1
3.4HO
0.4BP
D.361
0.262
1.262
'0.262
3.262
0.262
3.23,-
1.70"
1.415
1.C1?
C.654
0.258
3.434
3.26?
-
0.26C
0.261
TKi.'
7.2:
12.99
15. 12
22. 8U
29.63
29. Oa
-
166.49
-
140. 1»
*
61.95
45.71
44.73
47.90
4. 14
4.99
2.79
4.42
-
3. 18
3.02
2.83
-
1.93
1.3:
Total
sitro jen
7. 73
13.52
15.55
23.41
30. 16
29.56
-
166.92
-
1-4C. 55
<
b2.21
45.97
48.99
48. 12
4.37
6.69
4.21
5.43
-
3. 44
3.45
3. 14
-
2. 19
1.56
Dissolved
Oxycfaa
(•y/l)
7.7
.
R.I
8.0
8. £>
6.4
9.9
5.8
'
4.7
9.3
.
8.6
7.5
8. 1
7.4
_
8.8
_
.
-
8.2
7.4
7.8
1U-21
-------
Appendix 7-5 (cant) . Nutrients (mcj) present in tho reactor water by >iay number in the
sedimsnt nutrient release study.
Station
EIIL
EKHP
Day
Number
0
3
6
9
12
16
20
24
33
41
46
54
60
65
67
0
4
6
11
17
26
32
30
40
12
15
Total
Phosphorus
(mg)
C.338
0.256
0.256
0.256
0.256
0.256
0.782
C.501
0.866
O.H42
0.732
0.256
1.032
0.106
0.362
0.290
0.293
0.294
0.291
0.247
0.247
0.240
0.568
-
0.34C
C.341
Nitrate-
Nitrite
0.312
0.564
1.657
1.859
2.034
3.026
4.256
5.106
6. 122
-
-
11.569
12.36B
13.381
13.375
0.242
0.385
0.603
0.508
0.381
0.7811
1.275
1.411
-
-
1.942
TKN
(og)
8.53
7. 94
0. 96
15. C1
12.25
20.93
24.62
10.49
13.21
25.82
22.77
17.93
-
15.06
4. 39
2. 66
6.72
3.88
4. 28
2.85
10.01
8.65
7.34
-
.
8.59
Total
Nitrogen
(mg)
8.89
6.50
10.62
16.87
14.28
23. 96
28. 88 '
15.60
26. 33
-
.
29. 50
-
28. 44
17. 76
2. 90
7. 61
4. 43
4. 79
3.73
10. 80
9.93
8. 75 ,
'
_
10.53
Dissolved
Oxygan
(Bg/1)
_
3.6
_
8.8
3.6
8.6
7.5
8.6
7.2
-
7. 1
-
8.7
_
8.7
7.8
7.3
9.4
_
7.3
-
-
-
7.3
7.7
9. 1
Appendix 7-5 (ront) . Nutrients (my) present, in the reactor water by day number in the
sediment nutrient release study.
Day
Station Number
EPL? 0
3
6
9
12
16
20
24
33
•41
46
54
60
65
67
EhPB C
4
6
11
17
2o
32
38
40
42
45
Total
Phosphorus
0.812
0.225
0.477
0.366
0.232
0.230
0.450
0.385
1.301
0.457
0.333
1.290
C.903
0.903
C.766
0.4C8
0.455
0.437
0 .409
0.247
C.246
C.515
C.626
-
C . J4 1
O.u71
Nitrate-
Nitrite
(mg)
0.232
S.227
0.225
') . 4 C 1
0.401
0.444
0.552
0.552
0.445
0.40?
2.234
7.781
11.014
6.670
4.860
0.240
0.832
0.308
0.763
1 .433
1 . y35
4.39C.
y . 1 :l 3
-
11.412
11.400
TKN
(mg)
6.26
9.60
16.56
14.33
23.36
26.63
23.83
23.31
30. 19
31.22
31.77
24.63
15.99
17.36
17.53
6. 36
4. 10
4. 59
1 <3 . C 4
-
ID . 27
16. 94
9. 17
-
6.11
-------
6 E
E 6
1U
X
tu
o
O.5
f / ~
18.3 km/hr.
KEY
Sompling Periods
I—I KH H
5 67
H
a
10
i_
i
I
0600 1200 1800 2400 0600 1200 1800 2400 0600 1200 1800 2400
SEPT 23 SEPT 24 SEPT 25
1969
^ u^.
0.3
0.2
O.I
7 0
I -O.I
o
r -0.2
UJ
- -0.3
10 km/ hr.
HHHHHHHH
I 2 3 4 5 6 7 8
KEY
Sampling Period
I
I I
I
I
03 6 9 12 IS 18 21 0 3 6 9 12 IS 18 21 0 3 6 9 12 15 18 21 0 3 6 9 12 IS IB 21 0
APRIL 12 APRIL 13 APRIL 14 APRIL 15
1973
-------
\\V\\\ \\*0^
-------
1.0
i i»/ /
0.5
X
o
LU 0
X
LU
Q
-0.5
-1.0
w
18.5 km/hr (
S
I I I I I I I I
3 6 9 12 15 18 21
10/4/73
1.0
0.5
-0.5
7//*///'/
I 1 I i I i I I
3 6 9 12 15 18 21
12/5/73
14-25
-------
t _ x x / / \ t
— •• K -e *'
,\ //\v
> -
UJ
o
0.2
O.I
_i
in 0
O.I
sampling
period
5/29/74
I I I I I I I
3 6 9 12 15 18 21
7/30/74 data
not available •
0.2
~ O.I
E
_i
UJ
-O.I
-0.2
-0.3
N
I8.5km/hr
••E
0.2
6/18/74
I I I I I I
>
UJ
u>0
-O.I
3 6 9 12 1518 21
* \ i~ *»+-
A
AT
UJ
0-0.2
8/20/74
I I I I I I I
3 6 9 12 15 18 21
14-26
//
0.2
~ O.I
_l
-------
Appendix 3-2. Location, Storet retrieval information, and parameters
sampled for all sampling stations occupied by US-EPA and University
of west Florida during the Escambia Day Recovery Study.
PAGE PARAMETER
00006
00010
00070
00077
00300
00301
00343
00400
00480
00600
00605
00610
00625
00630
00665
00671
"00680
31505
31615
32230
32231
32232
70507
00003
2 00530
28 00608
28 00631
28 00681
98 00094
98 00690
98 70305
105 70990
142 00299
DESCRIPTION
NUMBER USED IN SAMPLE ACCOUNTING PROCEDURE
TEMPERATURE. WATER (DEGREES CENTIGRADE)
TURBIDITY, (JACKSON CANDLE UNITS)
TRANSPARENCY, SECCHI DISC {INCHES)
OXVGEN, DISSOLVED (MG/L)
OXYGEN, DISSOLVED (PERCENT of SATURATION)
OXYGEN DEMAND, TOTAL (MG/L)
PH (STANDARD UNITS)
SALINITY - PARTS PER THOUSAND
NITROGEN, TOTAL (MS/L AS N)
NITROGEN, ORGANIC, TOTAL (HG/L AS N)
NITROGEN, AMMONIA, TOTAL (MG/L AS N)
NITROGEN, KJELDAHL, TOTAL, (MG/L AS N)
NITRITE PLUS NITRATE, TOTAL 1 DET. (MG/L AS N)
PHOSPHORUS, TOTAL IMG/L AS P)
PHOSPHORUS, DISSOLVED ORTHOPHOSPHATE IMG/L AS P>
CARBON, TOTAL ORGANIC (MG/L AS C)
COLIFORM,TOT.MPN,CONFIRMED TEST.3SC (TUBE 31506)
FECAL'.COLIFORM,MPN,EC MED.44.5C (TUBE 31614)
CHLOROPHYLL A (MG/L)
CHLOROPHYLL'S IMS/D
CHLOROPHYLL c IMG/L)
PHOSPHORUS,IN TOTAL ORTHOPHOSPHATE (MG/L AS P)
DEPTH IN FEET ' . -
RESIDUE, TOTAL NONFILTRABLE (MG/L)
NITROGEN, AMMONIA,, DISSOLVED (MG/L AS N)
NITRITE PLUS NITRATE* DISS. 1 DET. (MG/L AS N)
CARBON, DISSOLVED ORGANIC (MG/L AS C)
SPECIFIC CONDUCTANCE,FIELD (UMHOS/CM 9 25C)
CARBON, TOTAL (MG/L AS C)
SALINITY BASED ON CONDUCTIVITY
PHYTOPLANKTON PRODUCTION.c-14 METHOD IC-G/MS/HR)
OXYGEN, DISSOLVED (ELECTRODE) (MG/L)
Appendix 0-2. (cont.).
AGENCY PRIMARY STATION SECONDARY
1113TOTO 1203*5 BjIV
130375 EPRF
120660
120665
120670
120855
120850
120845
120770
120775
120780
120785
120790
1Z0795
120765
120760
120753
120725
120730
120720
120880
120075
120840
120800
120605
120810
120750
120745
120740
120885
120890
120695
120900
120835
120630
120825
120815
120820
120735
120075
120310
120365
120360
120305
120300
120070
12006S
-Oil
-012
-013
-021
-022
-023
-031
-032
-033
-041
-042
-043
-051
-052'
-053
-061
-062
-063
-071
-072
-073
-08)
-082
-083
-091
-092
-093
-101
-102
-103
-104 '
-111
-112
-113
-121
-122
-123 -
OGV •
FSX
OJI . ',' '
GPH
GTA'
GUF
JFD
KAA -
120370 ALEX
120385 8FEI
120350 BNGA J .
120355 BREA
120700 E-Olli
120705 E-012
120710 E-013 -
120695 E-021 *
STATION LOCATION
CHANNEL HARKER 30
NEAR OYSTER PLANTING S OF. TROUTB
1/2 HI 270 DEGREES U OF 021 . ~
3/5 HI 270 DEGREES U OF 022
2/3 HI 270 DECREES U OF 023
CHANNEL HARKER R "16"
CHANNEL HARKER R "12"
CHANNEL HARKER R "8"
1 HI 91 DEGREES E OF 021
1/2 HI 180 DEGREES S OF 031
1/2 HI 180 DEGREES S OF 032
1/2 Hi 180 DEGREES S OF 033
1/2 HI 180 DEGREES S OF 041
1/2 HI 180 DEGREES S OF 042
3/5 HI T N OF 052
3/5 HI T N OF 053
3/5 HI T N OF 091
4 HI 84' DEGREES E OF 023
1 HI 180 DEGREES S OF 061
4 3/4 MI 91 DEGREES E OF 023
1 1/4 HI 227 DEGREES Sir OF 023
1 1/4 HI 206 DEGREES SU OF 023
1 1/3 HI 190 DEGREES SU OF 023
1/2 HI 180 DEGREES S OF 043
1/2 HI 180 DEGREES S OF 061
3/5 HI 180 DEGREES S OF 062
3/5 T N OF 092
3/5 HI T N OF 093
1/2 HI T N OF 123
2 Hi 247 DEGREES SU OF 023
4/5 HI 192 DEGREES SU OF 101
3/4 HI 192 DEGREES SU OF 102
2/3 HI 192 DEGREES SU OF 103
1 4/5 HI 180 DEGREES S OF 023
2 1/2 HI 180 DEGREES S OF 023
3 1/5 MI 160 DEGREES S OF 023
3/5 HI 163 DEGREES S OF 083
3/5 HI 180 DEGREES S OF 121
3 1/2 HI 129 DEGREES SE OF 023
• EAST BAY
MILLER PT VEST OF PUR CABELS
CENTER OF EAST BAY
3000 YDS UEST OF POUER LINES
HILLER PT AT POUER CABLES
KILLER PT. EAST OF PUR CABLES S
EAST BAY :
EAST BAY
•REDFISH COVE IN LINE UITH CHNL
BUOY 40 IN BLACKUATER RIVER '
CHANNEL HARKER 24 ' "-
CHANNEL HARKER IB
1 MI 288. DEGREES NU OF 021
1 1/3 MI 280 DEGREES NU OF 022
5/8 HI EAST OF STATION 023
'2/3 HI NORTH OF STATION 022
.STATE
FLORIDA
FLORIDA
•FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
'FLORIDA
' r FLORIDA ,
FLORIDA
FLORIDA
FLORIDA
FLORIDA
• FLORIDA
FLORIDA
FLORIDA.
FLORIDA:
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA.
FLORIDA'
FLORIDA ,
FLORIDA
FLORIDA
FLORIDA .
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA '
FLORIDA
FLORIDA '
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
' FLORIDA. .'.
FLORIDA '
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
HINOR BASIN
BLACKUATER BAY
ESCAHBIA BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST 'BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY. CHANNEL AT BUOY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY
EAST BAY CHANNEL AT BUOY
EAST BAY AT BUOY 1, 1 MI
EAST BAY
BLACKUATER RIVER
BLACKUATER BAY
BLACKUATER BAY
ESCAHBIA BAY
ESCAHBIA BAY
ESCAMBIA BAY
ESCAHBIA BAY.
12
4
S
14-27
-------
,\ Hin«"lx 8-2 (cont.l-
AGENCY PRIMARY S
1113*070 120690
120665
120660
120655
120650
120715
12066S
1206*5
120680
1206TS
120670
120640
12062S
120620
120635
120630
120615
120605
120600
120610
120595
120590
120580
120575
120570
120585
120565
1205*5
120560
120SSS
120550
120540
Appendix ft
AGENCY
1113T070
.
'flIHARV
20020
20230
20290
20160
20215
20220
20260
20235
20015
20115
20150
20255
20165
20240
20155
20000
20185
20250
20245
20330
20040
20030
20035
20335
20045
20050
20055
20175
20010
20025
20060
20170
20005
20380
20080
20085
20095
0090
0100
0105
0110
0265
0275
0270
0475
0455
0460
04*5
20485
20470
20450
20480
20490
204*0
20*65
20420
20*25
20*35
20*10
20415
20430
20315
20320
20405
20395
20390
20325
20400
120515
120520
120525
120510
120505
120500
120125
120200
120195
120205
120135
1201*0
120210
120130
120280
120285
120225
120180
120120
1201*5
120190
- 2. (cont.
STATION SEC
EEI
EEK
EEK
EEK
EEL
EEL
EFK
EFL
EFL
E6E
EOH
EGL
EGL
EGM
EOH
EHG
EMI
EHL
EMM
EHP
EII
CIK
EIM
EKL
EKK
EMO
ENN
EPL
EH-
ERP
ETL
ETQ
GULF
PEUE
PHZt
PIVF
PJPC
PJR
POOf
PPJ
POJC
RSDE
RSD
RSD,
VIM
YIV»
YKRt
YK71
YLG>
YLNS
YLZE
YNKF
YOF1
Y09
YPOC
ZHQ
ZIM
ZJE
ZJV
ZLOE
ZNH
ZOJC
ZOK
ZOWl
Z02l
Z06
ZPK
ZR2k
ATION SECONDARY STATION LOCATION
£-032 1 Hi WNW OF N "1*"
E-033 1/2 MI MNW OF N "1*"
£-0*1 BE RAF "18"
E-0*2 C "15"
E-043 N "1*"
E-051 1 1/2 Ml FROM C15LONLINE MULL»TO
E-052 1 HI FROM C1510NLINE MULLATO BYU
£-061 1/2 HI FROM CHANNEL
E-O i MIO CHANNEL ONLINE BTWN no i RR
E-O 2 N "12"
E-O 3 N "10"
£-0 1 100 TROS OFF STAKES DUE SOUTH
e-0 2 2 1/2 HI FROM C"7"IONL1NE INDN B
E-O 3 1 HI FROM STAKES ONLINE RA REF 2
E-O * 2 MI FROH C"T"tONLiNE INDIAN BYU
E-O 5 1 HI FROH C«7"10NLINE INDIAN BYU
E-O 1 I/* HI £ OF 0R STK&ONLINE N"*-
E-O 2 1 I/* HI W OF N'<*»tONLlNE 60 SIR
E-O 3 3/« HI W N"4»40NLINE OR1CK STACK
E-l 1 C "7"
£-1 2 N "*"
E-l 3 N "12" RA REF
E-l 1 3/* HI E OF N »*"
E-l 12 2 HI FROM C"T" ONLINE WITH IND B
E-121 2 HI OFF N "l2"iONLINE AERO BN
E-l 32 3/4 HI S OF 13113 H] EN£ AERO BN
E-l 33 3/4 HI S OF 132i3 HI £ OF AEROBN
E-U1 3/4 HI N OF 1*2
E-142 3/4 Ml N OF 1*3
E-143 * HI E AREO BN/2 HI H OARCON PT
EAOO WHITE R. 3 HI ABOVE NQUTH
EAOT WHITE HIV AT HEAD or SIMPSON RIV
EBFO SIKPSOH RIV AT WOODBINE BAYOU
ECGM SIMPSON R 1.3 Hi ABOVE US-90 BR
EDFE BENNY BAYOU AND DEAD RIV.-CONFLU
EDIP SIMPSON RIV MOUTH ABV US- 90 BR.
ED IV SIMPSON RIV. BELOW US-90 BRIDGE
EOJL UPPER BAY NEAR FLORIDATOWN
EOLU ESC. BAY .6HI NW OF AIR PROD OSCG
EEOO ESC. RIV AT BUOY N32 CNTR CHAN.
EEOR ESCAHBIA R UPS IN S CNFLU WHITE R
EEEH LITTLE WHITE R 1.75 HI ABV NTH
EEHF LIT. WHITE R. .1HI FH BENNY BAYOU
1 .
NOARV STATION LOCATION STATE
ESC. SAY .7*1 £. OF AIR PROD DSCO
UPPER BAY NEAR FLORIOATOWN
o.6H s. OF FLORIOATOWN
ESC. BAY .2H1 FH AIR PROD OSCHG
ESC. BAY ,8MI NW OF AH.CYN. BOIL
ESC. BAY .SMI S. OF AIR PROO OSCG
ESCAHBIA BAY
ESC.RIV.DWNSTH GULF P DISCHARGE
EAST RIV 1 HI UPSTH FROH MOUTH
ESC. BAY .SHI WSW OF AH.CYN BOIL
0.*H S.W OF F I SHERMANS POINT
ESCAMBIA RIVER
ESC. BAY .6HI sw OF AH.CYN. BOIL
500 YDS S.E. OF RR BRIDGE
ESCAM8IA BAY
ESCAMSIA BAY
0.3HI FH W SHORE JUST ABV RR BR.
ESCAHBIA BAY
ESCAMBIA BAY
ESCAMBIA BAY
0.2H SE OF CHIMNEY STACK
0 ESCAHBIA RIVER
E5CAM8IA BAY
ESCAMBIA BAY
0.3 H WEST OF HERNANDEZ PT.
GULF OF MEXICO
0.6MI ABV US-90 BR.CNTR OF BAYOU
PENS AC OLA BAY
PENSACOLA BAY
PENSACOLA BAY
PENSACOLA BAY
PENSACOL A BAY
PENSACOLA BAY
*
MOUTH OF SOLDIERS CREEK
MOUTH OF SOLDIERS CREEK
AT MOUTH OF SOLDIERS OREEK
.5 HI S.E. OF BEN'S LAKE
MOWY BTWN WHITE 1 BUCCAROO PT
MDWY 8TWN COBBS i BUCCAROO PT.
I.C.W. HILE 237
MOUTH OF GARNIER BAYOU
1.8 HI. EAST OF BLACK POINT
1.* HI S.S.W. OF WHITE POINT
1. HI SOUTH OF SLACK POINT
MOUTH OF NARROWS* ICW MARKER 4
.2 HI N. OF US-Q6 BR. AT OESTIN
l HI s.w. NTH. OF ALAQUA BAYOU
.75 MI N. OF I.C.W. HARKER *T
MDWY BTWN HAMMOCK i FOURHILE PT
-. 1 HI S.W. OF MTH LA GRANGE BAYOU
HARKER 1 IN LA GRANGE BYU CHNL
.7 HI N. OF HEWETT BAYOU
HOGTOWN BAYOU
HOGTOWN BAYOU
.3MI N. CNTR SPAN OF 331 BRIDGE
HOUTH OF CHOCTAWHATCHEE RIVER
3.0 HI FH HOUTH OF CHOC* RIV
HOGTOWN BAYOU
BUOY i IN i.c.w. EAST SIDE
STATE
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLOS IDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA
FLORIDA -
FLORIDA
FLORIDA
FLORIDA
LORIDA
LORIDA
LORIDA
LORIDA
LOR I DA.
LORIDA
LORIOA
LORIOA
LORIOA
LORIDA
FLORIDA ESCAHSIA BAY
FLORIDA ESCAMBIA BAY
FLORIDA ESCAMBIA BAY
FLORIDA ESCAMBIA BAY
FLORIDA ESCAMBIA BAY
FLORIDA ESCAMBIA BAY
FLORIDA ESCAMBI
FLORIDA ESCAMBI
FLORIDA ESCAMBI
FLORIDA ESCAMBI
FLORIDA ESCAHBI
FLORIDA ESCAMBI
FLORIDA • ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAMBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHSI
FLORIDA ESCAHSI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
FLORIDA ESCAHBI
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
BAY
FLORIDA ESCAHBIA BAY
FLORIDA ESCAHBIA BAY
ESCAHB
E5CAHB
ESCAH8
E SCANS
ESCAHB
* ESCAHB
ESCAHB
ESCAHB
ESCAHB
ESCAHB
. ESCAHB
ESCAM8
ESCAMB
ESCAHB
ESCAHB
ESCAHB
ESCAHB
ESCAHS
ESCAH E
ESCAMB
ESCAHB
ESCAH E
ESCAH E
ESCAMB
ESCAHB
ESCAHB
ESCAMB
ESCAH E
ESCAMB
PENS Eh
PENSACC
PENSACC
PENSACC
PENSACC
PENSACC
PENSACC
PENSACC
PERDIDC
PERDIOC
PERDIDC
CHOC T A
CHOC T At
CHOC T At
CHOCTAk
CHOCTAk
CHOCT h
CHOCT k
CHOCT k
CHOCT h
CHOCT k
CHOCT k
'. CHOCT I
CHOCT i
CHOCT k
CHOCT k
CHOCT k
CHOCT k
CHOCT k
CHOCT k
CHOCT
CHOCT k
CHOCT k
CHOCT k
CHOCT k
BA NEAR HOUTH OF
BA
BA
BA
BA
BA
BA
BA
BA ONE MI NW OF F
BA
BA
BA
BAY
RIVER AT H6WV 90
BAY
BAY
BAY
BAYtHULATTO BAYOU
Y HALF HI NE OF ELL
BAY CHANNEL AT BUO
BAY
CHAN BETWEEN 1-10 A
O.T5 HI W OF MOUTH
BAY CHANNEL AT BUO
BAY
R AT UPPER BLUFFS
BAY CHANNEL AT BUO
Y ONE HI NE OF MAGN
BAY
CHAN AT BUOY 2 IN
LA BAYiBAVOU TEXAR
LA BAY 2.3 MI NQ-EAS
LA BAY AT BAY BRIDGE
LA BAY CHA
LA BAY CHA
LA BAY CHA
LA INLET A
BAY
BAY
BAY
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE 6A
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
HATCHEE BA
4NEL AT BU
4NEL BTW B
*NEL AT BU
r BUOY 10
r
r
14-28
-------
Appendix 8-3. Summary of bottom sampling depths (meters) for Study I (ftpcil 13 - 15, 1973) and
Study II (April 19 to 21, 1973).
Station
AOGV
AJFD
AKAA
EEIX
EFLU
EIIL
EIKC
EIRE
EKNF
EHQC
ENNB
EBPB
EB10
ETLQ
GOLF
PHZH
EIVP
PJPD
PJRT
EOOH
PPJV
PQJQ
N
7
7
7
8
8
8
8
8
8
8
8
8
8
8
7
7
7
7
7
7
7
7
Study
dean
2.7
3.0
3.2
1.0
2.0
1.7
3.3
1.9
2.1
1.7
1.9
2.6
4.6
3.3
12.8
4.9
8.1
4.5
10.9
11.2
11.6
11.7
I
Lou
2.4
2.7
2.7
0.6
.8
.5
.7
.5
.5
.5
1.5
1.5
3. a
2.7
9.1
4.6
7.6
3.0
9.1
9.1
9.1
4.6
Stud; II
High
2.7
3.0
3.4
1.2
2.1
1.8
4.3
2.4
3.4
1.8
2.4
3.0
6. 1
3.7
14.9
5.5
8.3
3.0
13.4
11.9
13.4
15.2
C.
4
5
7
21
8
9
18
16
28
9
18
18
29
7
15
6
5
24
14
9
13
39
V.X
.3
.0
.4
.8
.2
.7
.0
.6
.6
.2
.4
.0
.2
.7
.7
.6
.3
.1
.8
.1
.8
.1
Station
&DGV
AJPD
AKAA
EEIX
EFLU
EIIL
EIKC
EIHE
EKHP
ENQC
ENNB
ERPB
EB10
ETLQ
GOLF
PHZH
PIVP
PJPD
PJHT
POOH
PPJV
PQJQ
N
7
7
7
8
9
8
8
8
8
8
8
7
8
7
2
7
7
5
5
5
5
6
Mean
2.8
2.9
3.4
1. 1
2.1
1.8
3.5
2. 1
2.8
2.4
2.9
3.3
4.9
3.9
13.3
4.7
9. 3
5.2
10.0
11.3
9.0
10.6
Lou
2.7
2.4
2.7
0.9
1.5
1.5
2.7
1.8
2.4
2.1
2.4
3.0
4.0
3.0
13.1
4.6
8.8
4.0
9.4
11.0
4.6
1.5
High
3.0
3.0
3.7
1.5
2.4
2.1
4.3
2.4
3.4
2.7
3.7
3.7
5.8
4.6
13.4
4.9
9.8
6.7
11.9
11.9
12.2
14.9
C. V.X
5.3
8.2
13.5
20.5
12.4
12.3
12.3
13.8
13.7
9.1
17.0
7.1
23.6
13.0
1.6
3.4
3.2
21.6
13.6
3.5
38.6
51.6
Appendix 8-3 (cont) . Summary of bottom sampling depths (meters) for Study III (August 16 - 17,
1973) , and Study IV (August 23 - 25, 1973) .
Station
Station
ADGV
AJFD
AKAA
EEIX
EEKV
EGLY
EIIL
EIKC
EIHE
EKNP
EHQC
ENNB
EPLP
ERPB
EB10
ETLQ
ETQE
GULF
PHZH
PIVP
PJPD
PJRT
POOH
PQJQ
N
d
8
8
7
7
7
7
7
7
7
7
7
7
7
7
7
7
7
8
8
8
8
8'
8
Stud]
Mean
2.9
3.2
3.6
0.9
1.4
2. 1
1.6
3.7
1.8
3. 1
2.1
3.2
2.2
3.3
3. 1
4.0
1.7
12.7
5.0
8.1
4.9
9.9
10.8
12.2
! Ill
LOU
2.7
3.0
3.0
0.6
1.2
2.1
1.5
3. a
1.5
2. 1
1.8
2.7
2. 1
3.0
2.7
4.0
1.5
11.9
4.6
7.9
4.fi
8.8
10. 4
11.9
High.
3.0
3.4
4.3
1.2
1.8
2.1
1.8
4.0
•1.8
4.3
2.4
3.7
2. 4
3.7
3.7
1.3
1.8
14. 3
5.5
8. 8
6.4
11.3
12. 5
12.2
C.V.*
5.4
5.0
11.4
19.2
17.2
0.0
9.2
8.3
6.5
24. 3
10.1
10.9
6.7
6.4
10.8
2.9
9.8
7.7
5.6
4.0
12.6
11.2
6.7
0.9
ADGV
AJFD
AKAA
EEIX
EEKV
EGLT
EIIL
EIKC
EIHE
. EKHP
EHQC
ENNB
EPLP
EBPB
ER10
ETLQ
ETQE
GOLF
PHZH
PIVP
PJPD
PJRT
POOH
PQJQ
8
8
8
8
8
8
8
8
8
8
8
8
8
8
7
8
8
6
a
8
8
8
8
7
Study
(lean
2.6
3.1
3.4
0.9
1.3
2.1
1.6
3.5
1.6 '
3.7
2.3
2.8
2.1
3.3
3.0
3.9
1.6
13.0
5.0
8.0
5.3
9.1
10.6
11.9
IV
Lou
1.5
2.7
2.7
0.6
0.9
1.8
1.2
2.4
1.5
3.0
2.1
2. 1
1.8
2.7
2.4
3.7
1.2
12.2
4.6
7.3
3.7
8.8
10.1
9.4
High
3.0~
3.4
4.C
1.2
1.5
2.4
1.8
4.3
1.8
4.3
2.7
3.4
2.4
3.7
4.0
4.3
1.8
13.4
5.5
8.8
7.0
9.4
11.3
13.1
c.v.s
19.5
8.2
12. 3
30. 9
15.5
10. 5
16. 3
18.2
9.6
12.0
10. 1
16. 1
12. 1
11.9
16.3
6.5
17.0
3.5
5.6
6.4
27.5
3. 3
3.6
9.6
U-29
-------
pendix 8-1. Summary of depth (meters) data for the ?ensacola Bay system during
January through September, 1974 (Pencacola Bay data from the Univarsity of West Florida).
Sta.
ADGV
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGP II
AGPH
AGPli
AJFD
AJFD
AJFD
ALEX
ALEX
ALEX
EFEI
EFEI
EFEI
EJIV
EJIV
EJIV
ENGA
BNGA
BNGA
EREA
EFEA
EREA
ECGK
ECGM
ECGH
EEDR
EEDR
EEDR
EEEM
EEEM
EEEM
EEIX
EEIX
EEIX
EEKV
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHGD
EHPK
EHPK
EHPK
UIL
EIIL
EIIL
EIKC
EIKC
EIKC
EKLQ
EKLg
EKL^I
EKHP
EKMP
EKHF
EKNP
liep.
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
C
E
A
C
E
A
C
£
A
B
C
D
No.
12
12
12
12
12
12
12
12
1^
12
12
12
12
12
12
12
12
5
5
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
3
12
12
11
12
12
12
12
12
12
12
12
12
12
1 1
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Moan
0.3
1 .4
2.6
0.3
0. S
1 .6
2.3
3.0
0.3
1.4
2.7
0.3
1 .6
3. 1
0.3
2.2
4. 2
0.3
1 .7
3.3
0.3
1. 1
2. 1
0. 3
1.1
2. 1
C.3
1 .1
2.7
0.3
2.2
1.1
0.3
2. 1
1.0
0.3
1 .2
2.1
0.3
C.6
0.9
0.3
0.8
1 .1
0.3
0.7
1.1
1 .6
2.0
0.3
2.6
5.0
0.3
0. 6
1 . 3
C.3
1.0
1. 6
C.3
1 .2
2.2
0.3
1.0
1 .7
C.3
1 . 1
1.9
2.7
Man.
0.3
1.2
2.3
C.3
0.8
1.1
2.0
2.7
C.3
1.2
2.4
C.3
1.4
2.7
0.3
1.5
3.0
0.3
1.7
3.0
?. 3
0.8
1.7
0.3
0.9
1.8
C.3
1.2
2.4
0.3
1.4
2. 1
C.3
1.8
3.4
0.3
0.8
1.5
0.3
C.5
J.6
0.3
0.5
0.9
C.3
0.5
C.8
1.1
1.8
0.3
2.3
1.6
0.3
6*9
0. 3
0.6
1.2
C.3
0.9
1.5
C.3
0.6.
1.5
0.3
0.5
1. 1
1.6
Max.
0.3
1.7
2.9
0.3
1. 1
1.3
2.7
3.4
0.3
1.7
3.C
0.3
1.0
3.4
0.3
2.1
1.6
0.3
2.0
3.7
0.3
1.3
2.1
0.3
1.4
2.4
0.3
1.7
2.9
0.3
3.4
6.1
0.3
2.6
4.6
0.3
1.5
2.4
J.3
0.6
1.2
0.3
1, 3
2.3
C.3
C.8
1.4
1.9
2.1
0.3
2.9
5.5
0.3
3.9
1.5
0.3
1 . 3
2.0
0.3
1.S
3.3
0.3
1.2
1.8
3.3
1.4
2.4
3.5
CV% '
0.0
11.0
7. 1
O.C
1-1.3
9.5
3.7
6.7
0.0
11.8
7.0
0.0
10.8
8.4
0.0
1 1 .6
9.9
0.0
7.8
7.7
0.0
13.7
11.8
C.3
16.7
10.8
C.O
10.9
6.7
0.0
23.3
25.1
O.C
12. C
11.8
0.0
16.9
15.2
3.0
16.9
23.6
0.0
31 .8
32.3
0.0
11.5
11.8
3.6
9.2
0.0
7.0
6.2
:• . o
15.7
18. 7
3.0
20.1
11.8
3 .0
21.9
33.7
3.3
15.5
9.5
0.0
20.9
18.0
17.5
Sta.
SKMP
*HfK)C
Edge
EHQC
ENNB
ENNB
ENNB
ENNB
EN Mb
EPLP
EPLP
EPLP
Epnp
EPSF
EPRF
E3Pb
ERPB
ERPB
F.RPB
ERPB
EH10
EH1 3
ES10
ETLQ
ETLQ
ETLQ
ETQE
2TQE
ETQ2
PEUS
PEUE
PHtlE
P31
P01
P02
P02
P03
P03
POl
P04
P05
P05
P05
P05
P05
P36
P06
P07
F07
POS
P03
P09
F09
P10
P10
F11
?1 1
PI 2
P12
P13
P13
P13
P13
?1 3
t>14
P1U
P15
F15
Dep.
V
A
C
E
A
B
C
D
E
A
C
E
A
C
E
A
B
V.
D
2
A
C
E
A
C
E
A
C
E
A
C
=
A
E
A
E
A
E
A
E
A
B
C
D
E
A
2
A
;
A
A
£
A
i?
A
E
A
r
A
3
C
D
£
A
T?
A
E
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
3.5
0.3
1.3
2.2
0.3
1.0
1.8
2.5
3.3
0. 3
1.2
2. 1
0.3
1.3
2. 3
0.3
1.0
1.7
2.5
3.2
0.3
2. 1
3.9
0.3
2. 1
1.0
0. 3
1.1
2. 1
0.3
1. 1
2. 1
0.4
17.6
0.4
10.8
0. 3
7.3
0.3
6.2
0.4
2.9
5.5
7.8
10.2
0. 3
6.4
0.3
5.5
0.3
10.1
0.4
3.7
0. 3
8. 4
0.3
5.3
0.3
5. 1
0.3
1. 7
3.0
4.3
5. 5
0. 3
5.4
0. 3
6.8
nin.
2. 1
0.3
1.1
1.8
0.3
0.6
1.2
1.8
2.4
0.3
1.1
1.8
0.3
1. 1
2.0
0.3
O.b
1. 4
2.1
2. 7
0.3
1.8
3. 1
0.3
2.0
3.7
0.3
0.8
1. 5
0.3
0.9
1.8
0.3
15.2
0.3
9. 8
0.3
5.5
C.3
5.5
0.3
2.1
1.6
6. 1
7.6
0.3
6. 1
0.3
4.6
3.3
6. 1
0.3
3.0
Q.3.
o!3
4.3
3.3
4.6
0. 3
1.5
2.4
3.7
4.9
0.3
4.3
0.3
6. 1
Max.
4.6
0.3
1.4
2.4
0.3
1.2
2.1
3.0
4.0
0.3
1.2
2.1
0.3
1.5
2.6
C.3
1.1
2.0
2.7
3.7
0.3
3.0
5.8
0.3
2.3
4.3
0.3
1.4
2.4
0.3
1.2
2. 1
0.9
19.2
0.9
11.6
0.6
8.2
0.6
7.3
1.2
3.7
7.6
9.1
1 1.6
0.6
7.0
0.6
6.1
0.6
11.6
0.6
4.6
g .6
9.8
0.6
6.1
0.6
' 5.3
C.6
1.8
3.4
4.9
6.1
0.6
6. 1
C.6
7.3
CVS
17.6
G.O
9. 1
8.5
O.C
16.3
13.6
13.5
13.0
0.0
5.8
5.8
0.0
12.3
8.4
0.0
12. 1
10.5
8.2
7.5
0.0
17.3
18.7
0.0
6.0
5.0
3.0
15.7
13.5
0.0
9.8
5.4
49.5
7.6
49.5
4. 1
26.6
9.3
26.6
7. 1
59.3
14.5
13.8
12. 1
9.8
26. S
5.7
26.6
9.7
26.6
14. 1
32.0
15.6
26.6
8.3
26.6
8.6
26.6
7.5
26.6
9.5
9.5
9.0
7. 3
26.6
8. 1
26.6
5.5
14-30
-------
Appendix 8-5.—Water Quality Methods.
SAMPLE COLLECTION AND PRESERVATION
Surface samples for all water quality parameters except
dissolved oxygen were collected by rapidly dipping the sample
container one foot beneath the surface. Surface D.O. samples
were collected using an APHA "dissolved oxygen dunker." All
subsurface samples from depths less than 4.9 m (16 ft) were
collected using a pump system. The pump system was thoroughly
flushed with a diluted hydrochloric acid solution and tapwater
before each study. In addition, the pump system was tested
before each study to insure that it was not aerating the water
samples. The pump was allowed to flush for one minute before the
sample was collected. A Kemmerer-type sampler was used for
samples from depths greater than 4.9 m (16 ft). Water samples
for carbon, nitrogen, phosphorus, and turbidity were collected in
500 ml. nalgene bottles; samples for long-term BOD were collected
in half-gallon plastic bottles; and samples for dissolved oxygen
were collected in 300 ml BOD incubation bottles.
For preservation of dissolved oxygen samples, two ml of
manganous sulfate and two ml of alkaline iodide-azide solution
were added .to each sample, and the sample was shaken. The D.O.
samples were then kept at ambient temperature in the dark and
analyzed within three hours after collection. Samples for all
other parameters were kept on ice in coolers while being returned
to the laboratory. In the laboratory, they were kept in a
refrigerator at 5°C until they were analyzed. Any samples which
could not be analyzed within one day of collection were preserved
with sulfuric acid. This was only necessary with total organic
carbon and total Kjeldahl nitrogen. Sufficient sulfuric acid was
added to these samples to bring the pH below 2.
ANALYTICAL PROCEDURES
Dissolved Oxygen
Dissolved oxygen was analyzed by the modified Winkler with
full-bottle technique (USEPA, 1974).
Nitrogen
Ammonia
Ammonia was analyzed by the Automated Colorimetric Phenate
Method (USEPA,. 1974) . .
Nitrate-Nitrite
Nitrate-Nitrite was analyzed by the Automated Cadmium
Reduction Method (USEPA, 1974).
14-31
-------
Total Kleldahl Nitrogen (TKN)
Kjeldahl nitrogen was analyzed by a combination of a manual
TKN digestion (USEPA, 1974), and analysis of the digestate by the
Automated Colorimetric Phenate Method (USEPA, 1974).
Phosphorus
Total Phosphorus
For the analysis of total phosphorus, sulfuric acid and
ammonium persulfate were added to an aliquot of each sample,
which was autoclaved at 15 psi and 120°C for 30 minutes. The
digested samples were analyzed by the Automated Colorimetric
Ascorbic Acid Reduction Method (USEPA, 1974).
Total Orthophosphorus
Total Orthophosphorus was analyzed by the Automated
Colorimetric Ascorbic Acid Reduction Method (USEPA, 1974).
Dissolved Orthophosphorus
Dissolved Orthophosphorus was determined by filtering an
aliquot of each sample through a 0.45 jj membrane filter. The
filtered samples were analyzed by the Automated Colorimetric
Ascorbic Acid Reduction Method (USEPA, 1974).
Carbon
Total Organic Carbon (TOC)
Total organic carbon was determined by first purging the
acidified samples with nitrogen gas to remove inorganic carbon,
then analyzing the purged samples by the Total Organic Carbon
Method (USEPA, 1974). The instrument used for analysis was a
Beckman Model No. 915 TOC analyzer.
Turbidity
Turbidity was determined by the USEPA Turbidity Method. The
instrument used was a Hach Model No. 2100 Turbidimeter.
Biochemical Oxygen Demand
Long-term BOD was determined with no dilution or
seeding (USEPA, 1971). Duplicate BOD incubation bottles were set
up for each sample. Initial D.O. concentration and D. O.
concentrations at intervals of several days for a total of 50
days were read on a Y.S.I. Model 51-A Oxygen Meter.
Long-term BOD data were modeled using a computer program
based on Marquardt's Compromise Method (Barnwell, 1970), which
used non-linear techniques to estimate first order carbonaceous
14-32
-------
and nitrogenous BOD parameters. The first order BOD model is
represented by the following expressions: ;
when t < t^ ...••:•
when
t > t,
-kct
- e
1 - e
). ..8-:
where
y
L
time in days
time that nitrogenous demand starts to be exerted
(in days)
BOD (mg/1) exerted at time, t
ultimate carbonaceous BOD (mg/1)
ultimate nitrogenous BOD (mg/1)
carbonaceous rate constant (per day, base e)
kn = nitrogenous rate constant (per day, base e.)
Equation 8-1 represents just the carbonaceous demand, and
Equation 8-2 represents the carbonaceous and nitrogenous demands.
The computer program of the model provided values of the
parameters tn , Lc , Ln , kc , and kn that meet the statistic
criteria of the computer program. As an additional check,
.calculated BOD values using Equations 8-1 and 8-2 were plotted
against the actual values to examine the fit of the model by eye.
Visually, the model provided an excellent fit of the actual data.
Total and Fecal Coliform Bacteria
Intensive water quality surveys were conducted during the
months of April and August, 1973, and every three weeks beginning
in January and ending in September, 1971. Sampling stations were
located in Escambia River, Escambia Bay, Blackwater River,
Blackwater Bay, East Bay, Bayou Texar, and Pensacola Bay (Figure
8-45) .
14-33
-------
Surface water samples were collected by grab technique at 0.3
m (1.0 ft) below the surface, and bottom samples were collected
with a pump from 0.3 m (1.0 ft) above the bottom. The pump was
submerged at bottom depth and allowed to pump for one minute
before collecting the sample. Water samples were collected in
sterile, wide mouth, glass bottles (250 ml) with ground glass
stoppers. Samples were placed on ice until analysis. All
samples were analyzed within four hours after collection.
Samples were analyzed by the Most Probable Number (MPN)
multiple dilution tube fermentation test, using five tubes each
for three dilutions, according to American Public Health
Associaton (1971). Lauryl tryptose broth medium was used for the
presumptive test. After 24 and 48 hours incubation at 35°C
(+0.5°C) all positive tubes with gas production were transferred
to brilliant green bile broth and EC Medium. Positive tubes with
gas produced in brilliant green bile broth in 24 and 48 hours at
35°C (_*0.5°C) were recorded as confirmed total coliforms. Fecal
coliforms were determined by growth accompanied by gas production
in 24 hours at 44.5°C (+0.5°C) in EC medium.
14-34
-------
Appendix 8-6.—Florida Standards for Class II and Class III
waters.
17-3.08 Criteria: Class II Waters - shellfish harvesting;..'
"The following criteria are for classification of waters in
areas which either actually or potentially have the
.capability of supporting recreational or commercial shellfish
propagation and-harvesting. Harvesting may only occur in
areas approved by the Division of Health, Florida Department
of Health and ..Rehabilitative Services.,
(1) Bacteriological Quality, Coliform Group - areas
classified for shellfish harvesting, the median coliform MPN
(Most Probable Number) of water cannot exceed seventy (70 per
hundred.(100) ml, and not more than ten (10) percent of the
samples ordinarily exceed an MPN of two hundred and thirty
(230) per one hundred (100) ml in those portions of areas
most probably exposed to fecal contamination during most
unfavorable hydrographic and pollutional conditions.
(2) Sewage, Industrial Wastes, or Other Wastes - any
industrial wastes or other wastes shall be effectively
treated by the latest modern technological advances as
approved by the regulatory agency.
(3) pH - of receiving waters shall not be caused to vary more
than one (1.0) unit above or below normal pH of the waters;
and lower value shall be not less than six. (6.0) and upper
value not more than eight and one-half (8.5) . In cases where
pH may be, due to natural background or causes, outside
limits stated above, approval of the regulatory agency shall
be secured prior to introducing such material in waters of
the state. • .
(4) Dissolved Oxygen - The concentration in all surface
waters shall not average less than 5 mg/1 in a 24-hour period
and never less than 4 mg/1. Normal daily and seasonal
fluctuations above these levels shall be maintained.
Dissolved oxygen concentrations in estuaries and tidal
tributaries shall not be less than 4.0 mg/1 except in natural
dystrophic waters. In those cases where background
information indicates prior existence under unpolluted
conditions of lower values than required above, lower limits
may be utilized after approval by the regulatory authority.
Sampling shall be performed according to the methods approved
by the Florida Pollution Control Board.
(5) Toxic Substances - free from substances attributable to
municipal, industrial, agricultural or other discharges in
concentrations or combinations which are toxic or harmful to
humans, animal or aquatic life. .
14-35
-------
(6) Odor - threshold odor number not to exceed 24 at 60°C as
a daily average."
General Authority 403.061 FS. Law Implemented 403.021, 403.031,
403.061, 403.101 FS. History-Formerly 28-5.08, Amended 6/10/72,
8/30/72, 7/3/73.
17-3.09 Criteria: Class III waters - recreation
propagation and management of fish and wildlife.
"The following criteria are for classification of waters to
be used for recreational purposes, including such body
contact activities as swimming and water skiing; and for the
maintenance of a well-balanced fish and wildlife population.
All surface waters within and coastal waters contiguous to
these basins, including off-shore waters, not otherwise
classified shall be classified as Class III; however, waters
of the open ocean shall be maintained at a dissolved oxygen
of not less than five (5.0) ml/1, streams specifically
listed in Section 17.3.21 by a separate listing designated as
"Special Stream Classification" shall similarly be maintained
at a minimum dissolved oxygen level of five (5.0) ml/1.
(1) Sewage, industrial wastes, or other wastes - any
industrial waste or other wastes shall be effectively treated
by the latest modern technological advances as approved by
the regulatory agency.
(2) pH - of receiving waters shall not be caused to vary more
than one (1.0) unit above or below normal pH of the waters;
and lower value shall be not less than six (6.0), and upper
value not more than eight and one-half (8.5). In cases where
pH may be, due to natural background or causes outside limits
stated above, approval of the regulatory agency shall be
secured prior to introducing such material in waters of the
state.
(3) Dissolved Oxygen - the concentration in all surface
waters shall not average less than 5.0 mg/1 in a 24-hour
period and never less than 4.0 mg/1. Normal daily and
seasonal fluctuations above these levels shall be maintained.
Dissolved oxygen concentrations in estuaries and tidal
tributaries shall not be less than 4.0 mg/1 except in
naturally dystrophic waters. In those cases where background
information indicates prior existence under unpolluted
conditions of lower values than required above, lower limits
may be utilized after approval by the regulatory authority.
Sampling shall be performed according to the methods approved
by the Florida Pollution Control Board.
(4) Bacteriological - in those waters designated for body
contact recreation, fecal coliform shall not exceed a monthly
14-36
-------
average of 200 per 100 ml of sample, nor exceed 100 fecal
coliform per 100 ml of sample in 10 percent of the samples,
nor exceed 800 fecal coliform on any one day, nor exceed a
total coliform count of 1,000 per 100 ml as a monthly
average, nor exceed a total coliform count of 1,000 per 100
ml in more than 20 percent of the samples examined during any
month; nor exceed 2,400 per 100 ml on any day. In those
waters not normally used for body contact recreation, fecal
coliform shall not exceed a monthly average of 500 per 100 ml
of sample, nor exceed 750 fecal coliform per 100'ml of sample
in 10 percent of the samples. Monthly averages shall be
expressed as geometric means based on a minimum of 100
samples taken over a 30 day period. MPN or MF counts may be
utilized.
(5) Toxic substances - free from substances attributable to
municipal, industrial, agricultural or other discharges in
concentrations or combinations which are toxic or harmful to
humans, animal or aquatic life.
(6) Deleterious - free from material attributable to
municipal, industrial, agricultural or other discharges
producing color, odor or other conditions in such degree as
to create a nuisance.
(7) Turbidity - shall not exceed fifty (50) Jackson units as
related to standard candle turbidimeter above background."
General Authority 403.061 FS. Law Implemented 403.021, 403.031,
403,061, 403.101 FS. History-Formerly 28-5.09, Amended 6/10/72,
8/30/72, 7/3/73.
14-37
-------
Appendix 8-7. Summary of total organic carbon (nig/1 as C) data foe the Pensacola Bay system during
January throuqh September, 1974 (Pensacola Bay data from the University of West Florida) .
Sta.
ADGV
AOGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFD
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BNGA
BNGA
BSEA
BREA
ECGM
ECGM
EEDR
EEDR
EEEM
BE EH
EEIX
EEIX
EEK-V
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHPK
EHPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLQ
EKMP
EKflP
EKHP
EKMP
EKNP
EHQC
EHQC
EHNB
ENNB
ENNB
Dep.
A
E
A
B
C
0
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
p
A
E
A
E
A
E
A
B
C
0
E
A
E
A
S
A
E
A
E
A
E
A
B
C
D
E
A
E
A
B
C
No
12
12
12
12
12
12
1 1
12
12
12
12
12
12
5
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
11
12
12
11
12
12
12
12
12
12
12
12
12
12
11
11
12
12
12
12
12
1 1
. Neau
4.8
3.fl
4.2
3.7
4.2
4.1
3.7
4.3
3.6
3.9
3.6
3.9
3.6
6. 1
6.8
4.6
4.7
5.4
4.1
5.3
5.0
6.7
5.9
5.6
5.6
5.7
6.U
5.9
5.6
6.7
5.4
5.7
5.4
5.6
5.6
5.5
5.5
5.5
6.6
6.2
5.3
5.1
5.3
5.1
4.9
4.2
5.2
4.9
4.0
3.9
4.0
4.4
3.6
5.5
5.4
4.2
Min.
1.0
1.0
1.0
1.C
2.0
1.0
1.0
•1.0
1.C
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
.1.C
1.0
1.0
1.0
1.0
3.0
2.5
1.0
'1.0
1.0
4.0
2.5
3.2
2.5
1.0
1.C
1.0
2.5
1. 7
1.0
1.0
3.5
1.0
1.0
1.0
1.0
1.0
1.0
1.0
2.C
1.0
1.6
1.0
1.0
1.8
1.C
1.6
1.6
2.0
flax.
11.0
7.0
10.0
7.0
6. 1
8.5
7. 5
11.7
6.5
8.0
9. 2
5.7
8.0
14.4
17.0
15.2
1U. 3
15.8
9.5
1U.O
1C. 5
20.0
12.5
11.1
12.0
14. 9
16.3
13.0
10.7
17.2
10. 5
9.0
1C. 6
12. 1
14.0
9. 5
13. 1
15. 1
10.5
13.0
11.0
10.0
12.5
14.0
11.5
>9. 3
11.5
9.3
5.5
9.0
7.5
6.5
6.2
10.0
9.0
9.0
CVX
56. 3
51.3
56.it
48.0
35. U
51. 1
55. 9
65.6
13.0
52.8
67.6
37.6
62.8
81. 1
97.0
84.6
79.8
75.2
6H. 6
73. U
54. 8
89. fl
45.0
49.4
62. a
68.4
58.7
43.0
46.5
62.7
40.8
37.8
43.2
57.0
57.6
53.8
66. 3
74. 9
28.0
46.4
51.7
55.8
61.0
68.7
54.4
52. U
50.1
44.3
33.4
54.9
46.5
34.6
43.4
49. 1
45.0
44. 3
Sta.
EHNB
ENNB
EPLP
EPLP
EPRF
EPRF
EBPB
ERPB
ERPB
ERPB
ERPB
EH 10
ER10
ETLQ
ETLQ
ETQE
ETQE
PEOE
PEUE
P01
P01
P02
PC 2
P03
P03
P04
P04
P05
PC 5
P05
P05
PCS
P06
P06
P07
P07
P08
P08
P09
P09
P10
P10
P11
P11
P12
P12
P13
PI 3
P13
P13
P13
P14
PI 4
P15
P15
Dep.
D
E
A
E
A
E
A
B
C
D
E
&
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
NO.
12
12
12
IP
12
12
12
12
12
12
12
12
12
12
1 1
12
11
9
9
10
10
11
11
11
11
9
10
11
11
9
10
1C
11
10
1C
9
11
1 1
10
11
10
11
11
10
11
11
9
10
10
11
10
10
9
10
11
Hean
3.3
3.7
5. 3
4.4
5.6
5.9
6.0
5.5
4.9
4. 4
4.2
6.5
6. 8
4.9
3. 9
4.1
5.5
5.2
4.9
3.2
3.1
2.7
3.0
2.6
3. 1
2.6
2.6
2.5
2.9
2. 8
2.6
3.2
3.9
4.5
5.4
4.6
4. 8
4. 4
3.5
3.0
3.9
4.0
4. 9
5.0
4.0
4.2
3.7
4.0
3.6
3. 5
3.9
3.8
3.9
4.0
4.3
din.
1.0
1.0
1.6
1.0
1.0
1.0
1.5
3.0
2.5
1.5
2.5
1.0
2. 5
2.5
2.2
1.0
3.5
1.5
2.5
1.0
1.5
0.5
.0
.5
.5
.0
. 5
.0
.5
2.0
1.0
1.5
2.0
1.5
3.0
0.0
3.0
2.0
1.5
1.0
1.5
2.0
2.5
3.0
1.0
1.5
2.0
2.0
2.0
1.0
1.5
1.0
2.5
1.5
2.0
Max.
7.5
7.5
10.5
9.0
12.2
24.0
13.5
9.0
7.5
9.0
8.5
11.0
10.5
9.5
8.7
7.2
9.0
7.5
7.7
7.5
4.5
5.0
6.0
3.5
5.0
6.0
6.5
4.5
4.0
4.0
3.5
5.0
7.0
8.5
7.5
7.0
7.0
8.0
6.0
6.0
7.0
9.5
7.5
8.0
8.0
9.5
6.5
7.5
6.0
5.0
6-.0
5.0
6.5
6.0
8.0
CV*
55.9
55.4
49.0
51.9
52.8
98.7
52.5
33.9
30.2
50.7
43. 1
46.6
37.9
44.6
49.6
47.1
30.1
36.5
31.5
60.4
30.4
48. 1
53.7
27.0
32.2
69.5
82.9
42.5
31.3
31.3
29.8
46.1
40.0
49.5
30.5
44.4
31.2
33.6
44.0
51.6
.42.6
56.7
32.2
33.8
64.6
51.9
43.7
40.7
38.6
29.3
30.7
37.8
37.7
39.5
42.8
14-38
-------
Appendix 8 -,fl. Summary of ammonia (rag/1 as N) data for the Pensacola Bay system during
January through September, 197U (Pensacola Bay data from the University of Hest Florida).
Sta.
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFU
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BNGA
BNGA
BREA
BREA
ECGN
ECGM
EEDR
EEDR
EEEH
BEEN
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EUGD
EHPK
EHPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLQ
EKHP
EKHP
EKHP
EKHP
EKHP
KHQC
EHQC
ENNB
ENNB
ENNB
Dep.
A
E
A '
B
C
D
E
A
•-E
A
E
A
E
A
E
A
E
A
E
A
•E
A
E
A
E
A
E
A
: E
A
. E
A
- B
C
D
E
A
E
A
E
A
E
A
E
.A
E
A
B
C
D
2
A
E
A
B
C
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
5
<*
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
1 1
12
12
12
12
12
12
12
12
12
12' •
12
12
12
12
12
12
12
12
Mean
0.027
0.072
0.028
C.025
0.02<*
C.051
0.077
0.032
C . 0 5 3
0.027
0.062
O.C21
0.087
O.OU1
0.099
C.C25
C.OUt*
O.C2U
C.06U
C.02H
0.092
0.035
0.105
C.036
C. 073
0.031
C.0'66
0.057
C.039
C.G51
0.091
0.061*
0.097
O.C93
0.083
0 . 2 1 8
0.038
0.096
0.066
0.075
0.037
0.069
0.01*6
0.113
0.035
0.080
C.038
0.039
0.079
O.C96
0.11U
O.OU8
0.067
C.036
0.038
0.090
Kin.
0.010
0.010
C . 0 1 C
0.010
0.010
O.OK
0.010
O.OK
0.010
0.010
0.010
0.010
0.010
0.02C
0.050
O.OK
0.010
0.010
0.010
o . - 1 o
0 .010
0.012
0.012
0.012
0.012
0.01'
0.015
0.010
0.010
0.010
0.010
0.018
0.012
0.010
0.010
0.012
0.012
0.012
0 . 0 1 C
0.010
0.010
0.010
0.012
0.010
0.010
0.010
0.010
0.010
0.0 1C
0.010
0.022
0.010
O.OK
0.010
O.C10
0.01C
Max.
0.080
0. 226
0.116
0.080
0.075
0. 282
C . 2 fc 2
f. 152
0.170
0.075
0.177
C.C5H
C. 197
0. 058
C.225
0.075
0.105
0.05B
0. 170
0.075
0.282
0.090
0. 312
0.090
0.275
0.09?
0.259
0. 277
C.090
C. 172
0.530
0. 11*5
0. 308
0. 325
0.278
1. 350
0.090
0. 250
?. 182
0. 180
0. 103
0. 198
0.111
C. 3«2
0.090
0.2U2
0.098
0. 125
0. 270
0. UD2
0. l*i»2
0. 130
0.276
0. 130
0. 130
0. 335
CVS
87.1*36
101.055
109. 957
81. 162
82.219
151.369
103.691
128. 091
91*. 092
76.069
86. 121
71*. 010
72.637
33.1*52
85.U66
79.UR9
81*. 608
62.3U3
92.U83
82.112
97.271
60.5U8
92.102
56.536
103. 116
69.060
121. 1*36
129. 015
67.998
95. 9U8
160. 73U
56. 195
99. 753
104. 568
1?2. 82«
170.769
52.801
83.959
95.059
96. 31*5
69.991
9H.2HB
55.769
89.205
67.271
89.791
6S.U77
86. 127
118. 63C
121.1*36
93.1*51*
101 .868
120.305
106.695
103.205
120. 110
Sta.
ENNB
ENNB
EPLP
EPLP
EPRF
F.PHF
ERPB
EPPB
ERPB
ERPB
ERPB
EB10
ER10
ETLQ
ETLQ
ETQE
ETQE
PEUE
PEUE
P01
P01
P02
P02
PC 3
Pi? 3
poi*
pot*
P05
PCS
PC 5
PC 5
PC 5
P06
PC 6
PC 7
P07
PC 8
POH
P09
P09
.P10
P10
P1 1
P11
P12
P12
PI 3
P13
P13
P13
P13
P1i»
P1U
P15
PI 5
Dep.
D
- E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
p
A
E
A
C|
A
E
A
B
C
[)
E
A
E
A
E
A
2
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
11
11
11
11
1 1
1 1
1 1
11
11
11
1 1
10,
11
11
11
11
11
1 1
11
11
11
11
11
11
11
1 1
11
11
11
1 1
11
11
11
11
11
11
Mean
0.079
0.09U
0.03 U
0. 060
O.C39
0. 057
O.OU2
0.039
O.OU3
0.050
C. 08«
0. 03U
C.031
0. 03U
C.093
0.03U
0. 058
0.022
0. 037
C. 022
0.017
C.022
0.028
C.031
C.037
0. 035
0.0,39
0.03U
&.022
0.032
0.036
0.056
0.033
0.076-
0.035
0.085
0. 031*
0 . 05'8
C.029 -
0.030
C.026
0.057
0.036
0. 10«
0.038
0.088
0.032
0.022
0.031*
0.052
0.078
0. 020
0.070
0.031
O.C96
Min.
0.010
0.012
0.010
0.010
0.010
0.010
3.010
0.010
0.010
O.OK
0.010
0.010
0.010
0.010
0.015
O.CK
0.010
0.010
0.010
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
n.0"5
0.005
0.005
0.006
0.009
".?05
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.006
0.006
0.005
0.005
0.005
0.006
0.006
0.005
0.005
0.005
0.005
0.005
0.005
flax.
0.272
0. 292
0. 130
0.265
0.111
0.182
0. 170
0. 1U8
0. 170
0.202
0.230
0.080
0.080
0. 1«8
0. 180
0.103
0. 1U5
0.075
0.215
0.0i»9
O.OU1
0.060
0.069
0. 173
0. 11U
0.128
0. 113
0. 151*
0.080
0.092
0. 121
3. 128
0. 111
0.202
0. 105
0.205
0.08U
0.235
0.076
0.063
0.088
0. 163
0. 111*
0.335
0. 11*7
0.2«l»
0.071
0.050
0.077
0. 168
0.238
O.OU5
0.199
0. 135
0.275
CV*
95.221
8«. 523
103.886
122. 1«7
95.939
100.376
115.9U6
108.515
113. 302
119.U36
86.127
55.072
63.548
117.1*21
57.539
92.920
90.363
97.607
179.51*9
76.196
81.81*3
88.396
88.775
158. 326
101.037
110.668
89.1*71*
132.588
111. 177
106.727
105.356
79.506
97.1*63
77. 331*
9U. 806
76.502
89.603
111*. 257
86.716
67.7U6
108.01*9
78. 1*55
100. 630
101*. 517
111.683
76.861*
90.639
73. 528
77.915
96.195
90.686
71.2.H*
98.323
120.058
93.51*9
14-39
-------
Appendix b - 9. Summary at nitrate nitrite (mg/1 - N) data for the Pensacola Bay system during
January through September, 1S74 (Pensacola Bay data from the University of West Florida).
Sta.
SDGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGP II
AJFD
AJFD
ALEX
ALEX
BIE1
EI'EI
EJIV
EJIV
ENGA
ENGA
EPEA
EBEA
ECGM
£CGM
EiDh
lEDh
EEEPI
EEEM
EEIX
JEIJt
EEKV
EEKV
HGLY
EGLV
EGLY
EGLY
EGLY
EHGD
EI1GD
EHPK
EHPK
EIIL
EIIL
EIKC
EIKC
EKL^
EKLQ
EKMP
EKMP
EKHP
EKMP
EKMP
EMOC
EMQC
ENNB
ENNB
ENNB
Dep.
A
£
A
B
C
D
p
A
5
A
2
A
E
A
E
A
£
A
E
A
E
A
E
A
E
A
E
A
£
A
E
A
B
C
D
T?
A
E
A
2
A
E
A
E .
A
•s
A
B
C
D
E
A
E
A
B
C
MO.
12
12
12
12
12
12
12
12
12
12
12
12
12
5
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
0.030
0.029
3.321
0. 320
0.018
C.320
0. 321
C.020
0.022'
C.023.
0.02«
0.021 '
0.028
O.C93
C . C it C
0.065
0.-016
0.055
0.032
0.036
0.028
0.132
C . 1 C 1
0..119
O.V26
0. 136
0.1 15
0. 103
C.095
0.089
O.C76
0.086
0.090
0.092
0.073
0.080
0.1*49
0 . C 6 8
0.071*
0.075
0.099
C.070
0.108
0.061
o.oes
O.C67
O.C80
0.066
0.018
0.010
0.038
O.C63
0.011
0 . C 5 9
0.055
O.G19
Min.
0.010
0.010
0.010
0.010
0.010
0.010
0.010
C.010
0.01 0
O.C10
0.010
O.C10
0.010
O..C30
0.029
0.022
0.010
0.021
0.010
C.010
C-;010
0.050
0.030
0.052
0. C35
0.05U
0.011
O.C53
0.022
0.010
0.010
O.C10
0.0 1C
0.01 0
0 . C 1 0
O.C10
0.051*
0.020
0 . 0 10
0.010
0.017
0.016
0.071
O.C19
0.010
0.022
0.010
0.010
0.010
0.010
0.010
G.010
O.C10
0. 01C
0.010
0.010
Max.
0.080
0.070
0.065
0.060
0.052
0.052
0.052
0.060
0.050
0.055
0.055
0.055
0.076
0. 121
0.070
0.095
0.105
0. 100
0.100
0.085
0.060
0.210
0. 159
0.237
C.237
0.225
0.213
0.159
0. 155
C . 1 10
0. 130
O.ilO
0.210
0.225
C.220
0.335
0.252
0. 110
0.3CO
0.315
C. 11*5
0. 135
0. 165
0. 135
0. 1i*0
0. 135
C. 130
0.130
0.135
0. 135
0.120
0.182
0. 1 10
0. 130
0. 130
C.I 30
CV*
77;196
72.957
86.338
80. 126
85. 179
80.507
71. 918
81.227
70.121*
73.307
77. 310
72.087
7d.39U
39.2U8
1*2.537
3U. 020
59.790
10.977
79. U 09
67.777
67. 107
31.163
42.271
38.663
50. 313
35.677
51.813
31.311
1*1*. 298
1*8. 61*3
53. 7HO
67. 3HO
71.1*19
81.171
89.679
123.666
36.770
58.2 17
113.U95
129.251*
3o.003
57.653
25.615
59.751
1*2.1*85
53.303
50.175
69.531
82.316
95.231
91.51.9
87.721
88.679
71.077
81.153
38. 261
Sta.
J:NNB
ENNB
EPLP
EPLP
EPR?
3 par
S3PB
3BPB
2UPU
2SP3
B3PB
3R10
2R10
3TLU
ETLoa
• poa
P09
PO'J
pi:
P10-
pn
pii
P12
P12
P13
P13
P13
P13
P13
P11
Pii
?15
P15
Dep.
D
' E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
2
A
E
A
T:
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
u
A
7?
A
B
C
D
E
A
E
A
£
No.
12
12
12
12
12
12
12
11
12
12
12
12
12
12
12
12
12
9
9
11
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
(lean
0.011
0.013
0.051
0.018
0.019
3.03d
0.051
0.050
0.012
O.OJ1
O.C29
0. 135
0.111
0.015
0 .031
3.058
0.032
0.029
0.020
0.033
0.013
0.015
0.016
0.012
0.011
0.011
0.010
0.013
0.017
0.013
0.010
0.011
0.018
0.031
0. 107
0.012
0.0 2'J
0 . 0 1 U
0.022
0.015
0.021 '
0.021
0.030
0.032
0.029
0.035
0.027
0.025
0.021
0.017
3.021
0.021
O.C21 •
0.022
0.029.
Min.
0. 010
0.010
0.010
C.010
0.010
0.010
0.010
0.010
0. 010
0. 010
0. 010
0. 039
0. 015
0.010
0. 010
0.010
0. 010
C.010
0.010
0.009
C. 005
0.005
0. 305
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.010
0.009
0.005
0.005
0.005
0.005
0.005
C. 005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0. 005
0. 005
0. 005
0.005
0.005
C.005 "
0.005
(lax.
0.125
0. 125
0.115
0.115
0. 125
0.095
0.120
0. 125
0.100
0.087
0.077
0.220
0.235
0. 1 16
0.070
0.212
0.087
0.080
0.050
0. 156
0.011
0.060
0.016
0.053
0.020
0.0«9
0.321
0.063
0.011
0.031
0.017.
0.-029
0.066
0.092
0.670
0.210
0.070
0.058
0.051
0.050
0.067
C.086
0.076
0.091
0.076
0.110
0.081
0. 101
0.086
0.018
0.071
0.059
0.059
". 060
6.071
CVS
87.135
83.086
79.891
82.329
83.857
81.140
83. 291
89.666
79.109
85.053
79.663
10. 174
10.786
91.310
57.551
113.82U
78.922
100.511
78.950
126.683
76.299
108.926
89.758
109. 192
17.515
97.662
49.837
122.226
.'77.071
62.639
31.192
• 50.. 782
•95. 112
73.688
181.056
129,283
85.676
76.693
90.536
85. 71 '4
99.829
98.077
90.253
86.208
91.969
89.252
102.873
125.121
110. 26'3
69.616
87.297
81.389
85. 183
93.116
78. 159
14-40
-------
Appendix 8 -1C. Summary of organic nitroqen (mg/1 as N) data 'for the Pensacola Bay system daring
January through September, 1971 (Pensacola Bay data from the University of Rest Florida).
Sta.
ADGV
ADGV
&GJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFD
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BHGA
BNGA
BREA
BREA
ECGM
ECGH
EEDR
EEDR
EEEH
EEEM
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGU
EHGD
EHPK
EHPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLQ
EKHP
EKMP
EKMP
EKMP
EKMP
EHQC
ENQC
ENN3
ENN3
ENUB
Dep.
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
- A-
E
- A
: E
A
•E
A
- :E-
''A
E
A
E
A
B
C
D
E
A
' E
A
E
A
E
A
E
A
E
A
B
C
D
E-'.
A
E''
A
B
C .
Mo.
12
12
12
12
12
12
12
12
12
12
12
12
12
5
1
12
12
12
1 1
12
1 1
12
12
12
12
12
12
12 '
12
12
12
12
12
12
12
1 1
12
1 1
12
12
12
12
12
12
12
12
12
12
1 1
12
12
12
12
12
12
12
Mean
0.209
0.238
G.199
C.2C6
0.206
0.189
C. 256
C. 196
0.231
0.237
^.217
0.283
0.263
0.311
0.159
C.153
C. 195
C. 1U8
0.218
0. 176
C.261
0.210
C.281
r. 358
0.317
C.202
0.239
0.-222
0.267
0.336
0.106 •
r.360
0.386
C.167
0.310
0.393
C.233
0.300
0.125
0.366
C.217
C . 295
C.217
C. 316
0.202
0 . 3 1 U
C.292
0.317
0.309
0.313
0.297
0.308
0.250
0.26C
0.307
C.359
Hin.
0.029
0.025
0.052
O.C10
0.025
0.025
0.013
0.02C
O.C80
0.062
0.060
0. 120
0.085
0.003
0. 115
0.029
0.065
0.035
0.015
0.0
0.013
0.007
0.022
0.027
0.025
0.010-
0 . C 1 C
0.036
0.023'
0.130
0.090
0.055
0. 125
0.075
0.0
0.083
C.M5
0.070
0.285
0. 117
O.C95
C.085
0. 115
0.010
0.065
0.001
0. 103
0.052
0.055
0.012
0.075'
0.060
0.018
0.063
C. 1UC
.0.175
Max .
C. 170
0. D88
0.570
0.550
C.510
0. 320
0.695
0.700
0. 610
0.610
0.67C
C. 61?
0.780
1. 138
0. 185
0.350
'0.190
0.310'
O.U55
0. 355
C.700
0. 119
<0.662
1. 375
1.008
0. 360
0. 115
0.160
0.520
0.618
1.169
C.668
0.898
1.058
0.555
0.728
0.118
0. 128
0.680
0.518
0.315
0. 510
0.363
0.628
0.1C3
0.598
0.590
C.HO
0.520
0.610
0.600
C.175
0.125
0.370
C. 530
0. 615
CV*
62.8
50.7
70.1
63.3
61.1
35.6
90.3
92.0
67.3
58.3
70.2
19.6
67. 1
151. 1
20.1
73.1
61.8
67.2
Sfl.1
59.7
85.8
57.7
72.5
97. 1
71.6
52.5
15. 1
55.7
17.8
50.8
68.3
15.7
56.5
66.5
19.2
51.6
63.6
36.1
23.6
35.6
32.1
13.9
31. 1
52.0
39.1
18. 1
16. 3
32.0
17. 1
53. 3
56.5
37.1
U2.9
38.9
38.6
13.3
Sta.
ENHB
ENHB
EPLP
EPLP
EPRF
EPRF
ERPB
EBPB
ERPB
ERPB
ERPB
ER1C
ER10
ETLQ
ETLQ
ETQE
ETQE
PEI1E
PEUE
PC1
PCI
PC 2
PC 2
P03
PC 3
P01
PCI
PCS
P05
P05
PC 5
PC 5
PC 6
P06
P07
P07
PC' 3
P08
PC 9
PC 9
P10
P10
P11
PI 1
P12
P12
P13
P13
PI 3
P13
P13
P11
P11
PI 5
P15 •
Dep.
D
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
g •
A
E
A
E
A
E
A
E
A
E
A
E
K
E
A
B
C
D
E
A
E
A
E
HO.
•12
12
12
10
12
12
11
12
12
12
1 1
12
12
12
12
12
11
9
8
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
0 . 35 1
0.301
0.286
P. 297
0. 271
C. 229
C.291
0.301
0.263
C.232
C.260
C . 2 1 3
0. 207
0.262
C.288
0. 257
0.219
0.357
0. 110
C. 158
0.213
0.208
0. 223
0.2C6
C . 3 1 1
0. 182
C.222
0. 212
0. 216
0. 113
0. 193
C. 117
C . 18C
C. 211
C. 186
C. 118
0. 163
C. 192
0. 185
0.232
0. 151
0.208
C . 2 1 8
r . 1 5 1
0. 171
C. 211
C. 201
r. 231
0. 253
0.175
0.258
0;258
C.256
0.237
C. 265
Hin.
R.077
0.022
0.067
0. 15fl
0.117
0.010
0.036
0.063
0.022
0.022
0.0
0.085
0.018
0.090
0.010
0.097
0.027
0.085
0.060
0.03C
0.082
O.C78
0.010
•0.013
O.C70
0.0
0.0
0.063
0.035
0.0
0.031
P. 036
• 0.0
0.052
0.0
0.0
0.006
•0.038
0.026
0.013
0.0
0.0
0.0
0.0
0.0
o.c
0.013
0.056
0.0
0.027
O.C
0.033
•0.0
0.020
0.0
nax.
0.665
0.565
0.110
0.150
0.110
0.118
0.510
0.510
0.615
0.118
C.520
0.380
0.390
0.170
0.563
0.110
0.190
0.690
1.060
C. 396
0.617
0.385
0.961
0.185
1.026
0.153
0.126
0.591
0.615
0.385
0.199
f.157
0.382
0.885
0.130
0.175
C.12C
1.639
0.525
0.521
0.133
0.882
0.800
0.111
0.379
0.803
0.122
0.721
0.193
0.112
0.192
0.735
0.736
0.785
0.703
- CV*
52.3
51.3
39.5
31.6
29.0
53.1
15.7
10.7
55.6
51.8
59.1
19.0
58.2
11.5
51.3
36.3
51.8
56.2
72.1
67.1
69.5
51.7
118.5
73.5
81.0
80.0
65.8
70.9
81.1
75.2
77.0
83.2
68.7
111.8
79.0
95.5
78.2
93.5
90.9
80.2
88.0
135.6
101.8
93.7
70.0
111.0
60.7
93. 1
65.7
77.2
55.8
73.0
97.1
99.7
95.1
-------
Appendix 8-11. Summary of total nitrogen (mg/1 as N) data for the Pensacola Bay system daring
January throuqh September, 1971 (Fensacola Bay data from the University of Vest Florida).
Sta.
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPM
AGPH
AJFD
AJFD
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BNGA
BNGA
BRKA
BBEA
ECG:1
ECG.'I
BED 3
EEDR
EEEH
EEEM
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHPK
EHPK
SIIL
EIIL
EIKC
EIKC
EKLU
EKLO
EKNy
EKKP
EKKP
EKHP
EKMP
EHQC
ENQC
ENN3
ENHB
EHND
Dep.
A
E
A
3
~
D
E
A
E
A
E
A
E
A
E
A
p
A
2
A
u
A
E
A
E
A
E
A
E
A
E
A
B
C
D
•y
A
E
A
E
A'
E
A
£
A
E
A
U
c
D
:?
A
E
A
3
C
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
5
U
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
1 1
12
1 1
12
12
12
12
12
12
12
12
12
12
1 1
12
12
12
12
12
12
12
Mea'n
C.267
0. 339
0.218
f .251
C.2U8
C.259
C.357
0.2U8
0.306
C.287
r;.33«
0. 325
0.378
r.445
C.256
0.2U3
0.284
C.226
0.291*
0.236
C. 356
C.l»07
C.U9C
0.5411
0.517
0.370
0 . 4 2 f
0. 361
C.UC1
C.476
r.573
0.511
0.573
C .652
C.U93
C.565
f . U 2 0
0.465
0.564
^.516
C. 383
0.434
0.«C1
r . u 9 1
0.405
C .161
".410
C. 424
C .430
-? . 11 u 9
0. 4U9
C .u 19
C.35H
r. 356
C .40 1
r . 4 <• 9
Hin.
0.06C
0.060
0.080
0-. 060
O.C6C-
0.060
O.G9C
0.060
0. 100
0. 100
•1.131
0. 1UG
0.201
0. 157-
0. 120
0. 100
0. 170
0.071
? . 0 60
0.025
C.C6C
0.245
0.289
0.275
0.295
0 . 2 0 D
?. 257
0. 192
0. 2«5
0.268
D.258
1. 115
0. 175
0. 128
0. 102
0. 1U7
0.202
C.32".
0.330
7.215
C. 22C
1. 197
0.238
0.218
0. 161
0.22"
0. 130
0.090
0.10 f.
C. OHO
0. 195
•:•. irr
Q. 1-"-5
0. lug
.?. 1SO
0.290
Max.
• 0.580
0.510
0.590
0.570
0.560
C.5CO
0. 784
0.720
0.680
0.630
0.715
0.660
0.825
1. 30 4
0. 37?
C. 487
0.530
0.367
0. U91
<\456
0.720
0. 630
0.773
1. 585
1.150
0. 485
0.555
0.588
".562
0. 960
1. 281
0.880
1.262
1.510
0.94<-
1.055
0.642
0.603
0. 890
0.995
O.U91
C. 657
0.505
0.917
0.56-)
0.7U2
0. 730
0.602
0. 857
C.9U2
0. 797
0.672
0. 516
C.562
0.677
, 1. 088
CVX
53. 1
3tt.7
55. «
52.8
55.8
U3.1
59. 1
71.7
50.9
1*9.3
55. 9
UU. 6
UU. 8
108.7
UO. 5
U7.5
1*0.0
1*7.0
«5. 1
55.1
51*. 3
31. 1
32.9
61. U
U0.8
21*. 7
20.1*
31. 1
23.5
39. 3
U8.0
12. 1
U6.5
66. 1
5". 9
1*6. 9
33.5
19.7
26.9
37. 1
21.U
29.. 1
21.3
UO. 9
27.2
28. 3
39.0
30.7
1*9.2
M7.6
39.8
38. 1
36. 2
29.5
36.6
1*3. 7
Sta.
ENNB
ENHB
EPLP
EPLP
EPBF
EPRF
ERPB
EfiPB
ERPB
ERPB
ERPB
ER10
EE10
ETLQ
ETLQ
ETQE
ETQE
PEUE
PEUE
P01
P?1
P02
PC 2
P03
PC 3
POU
PC«
P05
P05
PCS
PC1 5
P05
P06
P"6
P07
PC' 7
pra
PC 8
PC 9
P09
P10
P10
P11
P11
P12
Pi 2
P13
P13
P13
P13
PI 3
P1H
Pit*
P15
P15
Dep.
D
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
F.
A
g
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
2
A
E
A
B
C
D
E
A
E
A
E
No.
12
12
12
10
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
0.472
O.U39
0.371
C.380
C.363
0.325
0.358
0.385
0.3U8
C.313
0.351
0.382
0.379
C.3U1
0. U15
0. 350
r . 3 1 8
C. U07
O.l»l»7
0. 209
0.271
''.2U3
0. 261*
0.2U7
0.359
0. 225
C.265
0.286
0. 252
0.179
.".. 233
0.212
0. 228
0.312
0. 323
C. 258
C.222
0. 261*
0. 23U
0.275
0.197
0.282
0.279
0.275
0.232
0. 351*
C.257
0.27S
0.308
0.239
0. 351
0.298
0 . 3U2
0. 288
0.377
Bin.
0.157
0.110
0.107
0.218
0.175
0.062
0.060
0.095
O.C69
0.060
0.120
0.225
0.227
3.125
0.120
0. 125
1.065
0.135
0.105
0.089
0.095
0.090
0.059
0.090
0.089
0.010
O.C95
0.075
O.C90
1.031
O.C69
3. 080
0.089
0.096
0.085
0.070
C.C9C
O.C72
0.095
O.C92
0.080
0.067
0.080
1. 110
0.080
0.070
0.103
0.089
0.089
0.069
0.1 1C
0.095
0.08U
0.096
C.085
Has.
0.778
0.67U
0.598
0.500
0.585
0.«75
0.630
0.662
0.717
0.505
0.567
0.502
0.500
0.522
0.655
0.5U5
0.587
0.710
1.080
O.H20
0.6UC
0.1*30
1.0UO
?.512
1.1UO
P. 536
O.i»69
0.693
0.675
O.UOO
0.530
0.601*
O.i»39
1. 102
0.760
0.770
3.1*61*
0.709
0.537
0.580
O.i»i»5
0.969
0.826
0.1*87
0.506
0.972
O.U35
0.781
0.560
n.(*75
0.687
0.927
C.909
0.98C
0.955
C7*
37.8
32.1
39.0
23.1
3Q.1
13.2
50.0
M3.5
1*7.1*
50.9
1*11.1*
23. 1
25.7
39.7
3U.1*
33.7
1*7.7
1*6.3
69.0
50.2
61.7
1*9.8
103.4
58.9
81.1
69.2
5U. 3
64.7
73.5
61.7
61.5
72.8
1*9.0
91.2
62. 1
79.7
56.8
72.2
65.9
65.1
62.1
106.5
77.2
53.9
55.7
78.4
41*. 1
76.5
54.3
61.3
51.5
66.4
77.1
92.7
70.9
14-42
-------
Appendix 8 - 12. Summary of total phosphorus (rog/1 as P) data for the Pensapola Bay system during
January through September, 1971 (Pensacola Hay data from the University of West Florida) .
Sta.
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFD
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BHGA
BNGA
BREA
BHEA
ECGN
ECGH
EEDR
EEDH
EEEM
EEEM
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHPK
EHPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLQ
EKMP
EKHP
EKMP
EKHP
EKHP
ENQC
EHQC
ENNB
ENNB
Dep.
A
E
A
B
C
D
E
A
E
A
E
A
E
A
£
A
E
A
E
A
E
' A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
B
No.
12
12
12
12
11
12
12
12
12
12
12
12
12
5
5
12
12
12
1.1
12
12
12
12
12
12
12
1-2
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
11
12
12
12
12
12
12
12
12
12
12
11
Mean
0.011
0.022
P . C 1 3
C . 0 1 3
0.012
O.C1U
0.019
0.013
0.018
0.013
C.021
0 . C 1 8
0.021
O.C18
0.021
0 . C 1 9
0.026
0 . C 1 7
n.?2T
0.016
0.022
0.033
0.035
0.010
O.C38
0.033
0.011
0.033
0.036
0.03C
0.033
0.027
0.031
C.031
0.03U
0.033
0.037
O.OU3
C..031
0.03«
0.031
0.030
0.028
C.016
O.C25
0.031
C.028
0.028
0.027
0.033
0.031
0.022
0.022
0.023
0.028
Min.
0.010
0.010
0.010
0.010
0.010
0 . i" 1 0
0.010
0.010
0 . C 1 C
0.010
0.010
C.01C
0.010
0.010
0. 019
0.011
0.010
0.010
0.011
0.010
0.013
0.019
0.017
O.C20
0.023
0.022
0.025
0.018
0.022
0.018
0.020
0.015
O.C17
O.C16
0.011
0.011
0 . " 2 0
o!o25
0.010
0.011
0.019
0.011
0.01U
O.C1«
0.011
0.016
0.013
0.011
0.013
0.016
O.P19
0 . 0-1 0
0.010
. 0.013
0.011
Max.
O.C30
0.051
0.027
0.030
0.023
0.031
o.ruo
0.021
0.036
0.019
0 . C 3 1
0. 083
O.C12
0.026
C.C29
0.030
0.065
0.021
0.027
O.C32
0.052
0.072
0.056
0.068
0.075
C.070
C. 120
C.C60
0.057
0.055
0.053
C . 0 1» 8
C.C55
0.066
O.C62
0.060
0.070
0. 112
0.059
.0.066
O.C61
0.0 1'7
0.055
0. 160
0.055
0.060
0.052
0.050
0 . 0 1'1
0.070
0.055
0.051
0.037
•0.051
0.070
CVS
12. 9
63.1
39. 3
U3.6
32.7
«t). «
11.8
26.3
10.6
21.2
35. 1
111. 2
39.6
36.5
18.2
27. 1
53. 7
29.9
25.1
19. 1
19.0
12.5
10.2
37.6
31.9
39.3
63. 1
35.8
27.1
35.0
31.5
36.8
39.8
15. 9
18. 1
16.6
3fl. 1
72.7
15.2
10. 1
39.8
38.9
10.9
88.3
16.5
38.1
50.3
11.5
11.0
18. 1
32.2
50. 1
38.7
51.7
67.9
Sta.
ENNB
ENNB
EPLP
EPLP
EPRF
EPRF
ERPB
ERPB
EHPB
ERPB
ERPB
ER10
ER10
ETLQ
ETLQ
ETQE
ETOE
PEU'E
PEUE
PD1
P01
P02
PC 2
P03
PC 3
P01
pnu
P05
PC 5
P05
P05
PP5
P06
P06
PC 7
P07
P08
PC 8
PC 9
-P09
P10
P10
P11
P11
P12
P12
P13
PI 3
P13
P13
P13
P11
P11
P15
P15
Dep.
D
E
A
5;
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
p
A
g
A
E
A
E
A
V
A
E
A
E
A
E
A
B
C
D
E
A
E
A
g
NO.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
11
Mean
0.012
0.039
0.027
0.03C
0.018
0.021
0. 019
0.021
0.018
0. CIS
0.028
O.C1C
0.01C
0.023
0.039
0.016
0.018
0.026
0.030
C . 01 7
0.021
0.022
0.020
0.020
0. 010
0.022
0.028
0. 021
0.017
0.017
0.018
0.029
0. 022
C. 027
0.077
0.037
0.021
O.C36
O.C18
0.018
0.016
C.031
0.025
0.030
0.021
0.032
0.016
0.016
0.017
0.020
0.036
0.016
0.030
O.C20
0.026
Hin.
0.016
0.011
0.013
0.010
0.010
0 . C 1 C
0.010
0.010
0.010
0.010
0.010
0.021
0.027
0 . C 1 0
0.010
0.011
0.012
0.016
0.021
.0.010
0.006
0.007
0.010
0.006
0.005
O.C05
O.C06
0.007
0.007
0.006
0.005
0.007
0.007
O.CQ6
0.006
0.010
0.006
0.005
0.005
0.005
0.007
0.005
0.005
O.C05
0.005
O.C05
0.006
O.OC5
0.005
O.C05
0.006
0.006
0.005
0.005
0.005
Max.
0.118
0. 088
0.019
0.051
0.031
0.037
0.015
0.037
0.027
0.029
0.018
0.055
0.070
0.067
0. 139
0.028
0.010
0.037
0.052
0.260
O.OU1
0.063
0.058
0.080
0.230
0.056
0.015
0.071
0.031
0.037
0.015
0.059
0.081
0.060
C.600
0.085
0.037
0.080
0.039
0.031
0.026
0.075
0.017
0.056
0.066
0.071
0.035
0.032
0.039
0.012
0. 116
0.032
0.081
0.075
0.017
CVS
67.9
53.0
11.5
52.9
39.6
11.6
51.9
51.2
36.1
35.7
18. 1
22.1
30.5
70.0
90.6
10.5
13.8
28.fi
33.1
116.1
52.1
72.9
67.8
101.3
151.8
71.0
17.1
88.0
52.1
73. 1
67.1
61.0
91.0
61.1
215.7
51.9
51.8
59.0
62.6
55.3
11.1
65.9
52.3
53.0
79.1
69.0,
51.8
61.9
62.1
65.1
105.5
58.1
79.5
98.2
50.3
-------
Appendix 3 - 13- Summary of dissolved orthophosphorus (mq/1 as P) data for thp Pensacola Bay system
during January through September, 197U (Pensacola Pay data from the University of West Florida).
Sta.
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFD
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BNGA
BNGA
BREA
BREA
ECGM
ECGM
EEDR
EEDR
EEEM
EEEM
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHPK
EHPK
EIIL
EIIL
EIKC
EIKC
EKLy
EKLQ
EKMP
EKBP
EKMP
EKMP
EKMP
EMgc
EHQC
ENNB
ENN8
ENN3
Dep.
A
E
A
B
C
D
£
A
p
A
p
A
E
A
E
A
p
A
E
A
E
A
E
A
p
A
E
A
E
A
p
' A
B
C
D
E
A
T?
A
E
A
E
A
p
A
E
A
B
C
D
E
A
E
A
B
C
No.
12
12
12
12
12
12
12
12
12
12
12
12
12
5
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
C.C10
0.010
C.01?
C . 0 1 J
: . o i o
f .0 K
O.IK
r: . C 1 1
f . 0 1 0
C.010
0 . 1 1 C
C.01 •:•
C.010
0.01 c
o . o r?
0.011
o.on
C.010
C.010
C . r< 1 0
C.010
C.010
0.010
0.011
C.010
0.011
C.010
0.010
0 . C 1 0
0.010
0.010
r.cio
0.010
0.010
C.OK
0.010
O.C10
6.010
0.010
0.010
0.01"
r . o 1 o
0.013
0.01 0
0.011
0.010
0 .010
C.010
0.010
0 .010
0 . C 1 0
0.01 0
0.010
C . 0 1 C
"I . 1 1 0
C . C 1 0
Min.
O.C1
1.01
C.01
0.01
C . 0 1 C
0.01C
0.01 r-
0 . 0 1 C
0.010
0 . 0 1 C
0.010
0.01 0
0.010
0.010
0.010
0.010
0.010
0.010
0.010
O.OK
0:010
0 . C 1 C
0.010
0.011"
0.010
O.OK
0.010
0.010
0.010
0.010
C.010
0.010
3.01 0
0.01 0
0.01"
0.010
0.010
0.010
0.010
0.01 0
6.010
O.OK
0.010
0.01 C
0.01 0
0.010
o . o 1 r-
O.OK
0.010
0 . r K
0.010
O.CK
0.010
o . o 1 r
O.T10
0.010
flax.
0.010
o . : i o
C.C10
0 . C 1 ?
r . o i :•
C.010
0.012
0.010
0.010
C.010
0.010
0.012
0. 010
C.010
0.010
0.010
0.010
0.010
0.010
0 . C 1 0
0.012
0.01 0
0.010
O.OI1.
C.012
C. 023
0.010
o . c i ;•
0.010
r . 0 1 O
0.010
0.01"'
0.010
O.OK'
0.010
C.01 0
0.015
0.012
0.010
0.010
0.010
0.011
0 . C 1 1
0.010
G . 0 1 1
O.C10
0.01 0
0.01 0
0.010
0.010
O.OK
0.010
0.010
O.C10
0 . C 10
r, . c 1 2
cvt
0. 0
,1 1
0.0
0.0
0.0
0.0
5.7
0.0
0.0
0.0
0.0
5. 7
0.0
0.0
0.0
0.0
0.0
-, _ n
o!i
0. 0
5.7
0. 1
0.0
lit. 2
7. 5
33.3
0. 0
0 . 0
0. 0
0. 0
•"1 ("'
o!c
0.0
0.0
0.0
1. 0
13.9
5. 7
0.0
1.0
1.0
2.9
0. 0
0. 0
2. 9
0.0
0. 0
0.0
0. 0
0 . 0
0.0
0.0
" . 0
0.0
0.0
5.7
Sta.
ENNB
ENNB
• EPLP
EPLP
EP3F
EPRF
ERPB
EEPB
ERPB
ERPI3
ERPB
ER10
ER10
ETLQ
ETLQ
ETQE
ETQE
PEUE
PEtJE
P01
P01
P02
P02
pr.3
P03
PCM
PC'U
p05
PT5
P05
PC 5
P05
PC 6
PC 6
P07
P07
PC 3
PCS
PC 9
P09
P10
P10
P1 1
P11
P12
P12
P13
P13
P13
P13
P13
P1«
P1«
PI 5
P15
Dep.
D
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
u
A
E
A
p
A
B
C
D
E
A
E
A
R
A
p
A
E
A
E
A
E
A
E
A
B
C
D
V
A
T?
A
E
Mo.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
C.010
0.010
0.010
0.010
0.010
0.010
c . c 1 r
0.010
O.C1C
0.010
0.010
0.011
0.011
<• .010
C . 0 1 C
C . C 1 C
0.01 0
C.01-"1
o . r- 1 c
0 . 0 C 5
0.005
0.005
C .005
0 . 0 1 5
0 .005
C. 005
0. 005
0.005
0.005
0.005
0. 005
0.005
0.005
0.005
0.007
C nnc
0. 005
0.005
C. 005
0.005
o. or 5
".005
C .005
C. 005
0.005
0. 005
0.005
O.OC5
C.0"5
0.005
0.005
0.005
0.0'- 5
r .005
0.005
Min.
O.C1C
0.010
0.011
0.010'
r . c; i f
0.010
0.010
0.010
0.010
0.010
C.010
0.010
0.010
0.010
0.010
0.010
O.OK
0.010
0 . C 1 C
r.OC5
0.005
0.005
o.or.5
0.005
0 . C 0 5
0.005
0.005
0.005
0.005
O.OC5
O.CC5
7.005
0.005
0-. 005
0.3*5
i 0-">5
P.Of-5
0.005
0.005
0.005
O.OP5
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
Max.
0.010
0.01C
n.oio
0.010
0.010
0.010
0.010
f . 0 1 0
0.010
n.om
0.010
0.016
0.018
O.OK
0 .010
0.010
0.010
•-M1C
0. 01C
0.005
0.005
0.005
0.005
0. 005
0.035
0.005
0.005
0.005
0.005
0.105
0.005
0.005
0.005
0.005
0.030
0. O1* 1
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
0.005
C. ?05
1.005
0.005
0.005
0.005
O.C05
0.005
0.005
0.005
CVS
0.0
0.0
.0.0
0.0
0.0
0.0
0.0
0 . 0
0.0
11.2
0.0
19.7
23.5
0.1
0.0
0.1
0.0
0.0
0.0
0.1
c.o
0.1
1 .1
0.0
0.0
0.1
0.0
o.r
0.0
".p
0.0
0.0
0.0
0.1
101.9
118.7
n.o
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0 .0
^ n
0.0
0 .0
0.0
o.n
0.0
0.0
0.0
0 ."*
0.0
14-44
-------
Appendix H - 14. Sumaiary of orthophosphorus
January throuqh September, 1974.
(m 4
0 . 117
0 .053
0.056
0.056
0.050
0.05 0
0.047
0 .054
CV
31
63
40
40
19
r,
49
17
23
14
22
•T
24
12
23
46
27
49
49
39
53
47
49
44
53
52
59
,. 53
45
1">2
51
60
51
55
47
52
48
'I
.6
. 1
.8
.8
. 1
"I
.9
.8
.8
.2
.8
, 0
.5
. 9
.6
.6
, o
.2
ft
r.
.6
. 3
.2
. 3
.8
. 0
.4
.4
.6
% %
.3
.4
.6
.6
.9
.2
.2
Sta.
EHGD
EH PK
EHPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLQ
EKMP
EKSP
EKIIP
EKMP
EKMP
F.MQC
EMQC
ENNB
EKNB
EN IP,
ENNB
ENND
EPLP
EPLP
Et>RF
EPSF
TUKPB
EKPn
ERPB
EEPB
EfiPB
ER10
ER10
ETLQ
ETLQ
ETQE
ETQE
Dep.
p;
A
E
A
E
A
E
A
5
A
3
C
D
E
A
t-i
A
E
C
D
£
A
E
A
' E
A
D
C
D
IT
A
V
A
E
A
E
NO.
12
12
12
12
12
12
11
12
12
12
12
12
12
12
12
12
12
1 1
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
M ean
"• 02 "3
0. "22
'"• .024
C .021
0 . •" 2 n
0.022
0.023
0 . C 2 1
0.02 0
r. 021
0.021
r . o 1 6
r-- . 0 1 S
0. 02 C
0.016
C . 014
^.020
0 . 0 1 6
0 .019
0. 022
C . 0 2 C
0.017
0.017
0.012
0 . 0 1 2
0 .014
0.014
r .012
0.011
C .014
0.034
0.034
r . o 1 1
0. 018
'••.011
0.011
Min.
0.010
o . o n
0.010
0.011
O.C 11
0.012
0.01 0
C . 0 1 0
0.010
0.010
0 . r 1 0
0.010
0.010
0.01 0
0.01 0
0 . C 1 0
0 . 0 1 •*
0.010
0 . C 1 0
0.013
0.01 0
n B f\ 1 n
0.010
0.010
' 0 . 0 1 0
0.010
0 . C 1 0
0.010
0.010
0.^10
o . r- 1 8
0 . C 1 7
0.010
0 . C 1 0
0.01 0
0.010
^
0
0
A
- f\
0
0
0
0
^
•.;
n
0
0
0
0
3
0
o
f\
3
f\
^
I_l
0
n
o
o
0
0
0
n
p.
A
\J
o
0
0
.-I
Max.
.080
.049
.045
.057
.042
.047
.042
.053
.041
.047
. 0 50
.042
.042
.047
.030
.030
.041
.039
.047
.035
.032
.037
.037
.024
.016
.032
.037
.022
.016
.021
.054
.059
.022
.042
.015
.0-17
CV,
66.7
49.5
43. 1
57.8
44 . 1
58.6
38.0
70.3
43.3
58.0
60.2
56.3
48.4
49.9
39.8
41. 5
47.7
55.6
61.9
37.6
39.1
44.9
52. 3
36. 1
21.6
45.4
55.4
30.4
18.2
32. 1
34.2
40.2
31.5
63.9
15.1
22.9
I
*r
Ul
-------
Appendix 3 - 15. Data uase for calculation of initial PHI values.
Eescription
Date
Agency Code
Station Numbers
P.eiua rks
I
f:
data collected by the
Escambia Bay Recovery Study
Univ. of West Fla. Sea Grant
data for Escambia and East Bays
Univ. of West Fla. Sea Grant data
for Psnsacola BAY
Eata from FWPCA Study of
Escambia Bay
Data fron USEPA study of
Perdilo Bay
Data rrom USEPA study of
Mississippi Gulf coast
Data from USEPA study of
Escambia River
1973 to 1971
1973
197U
1969
1972
1972
1971
1113T070 12DCOO - 120490
1113TC7C 120500 - 120900
PG1 - P15
EC1 - E27
11135003 017030 - 017012
6UOC75 - 6UC1 11
HQ-:>1 - HQ-05
HQ-20,WQ-21,WQ-55,Hy-56
S1 - R14
Primary station number
Primary station number
Unpublished data
(not in STORET)
Not in STORE! after
USDI, 1970
After USEPA, 1972
Unpublished data
Unpublished data
-------
Appendix 8 - 16. Summary of dissolved oxygen (ag/1) data foe the Pensacola Bay system during
January thcougd September, 1971 (Pensacola Bay data from the University of (Jest Florida).
Sta.
JDGV
ADGV
AGJI
AGJI
AGJI
AGO I
AGJI
AGPH
AGPH
AJFD
ftJFC
ALEX
ALEX
EFEI
EFEI
EJIV
EJIV
EHGA
ENGA
EBEA
EREA
ECGM
ECGM
EEDR
•EECE
EEEP1
•EEEM
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
EHPK
EhPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLC
EKKP
EKHP
EKHF
EKflP
EKHP
E«yc
EMOC
ENNB
ENNB
ENNB
ENNE
Dep.
A
E
A
a
c
0
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
t
A
E
A
E
A
B
C
D
E
A
E
A
B
C
D
No.
12
12
12
12
12
12
11
12
12
12
12
12
12
5
<*
12
1 1
12
11
12
1 1
12
12
12
12
12
12
12
12
12
12
12
10
12
VI
11
12
1 1
12
12
1 1
12
1 1
12
12
11
12
12
12
12
11
12
12
12
12
12
1 1
dean
7.9
5.2
8.1
8.0
8.0
7.9
a. 7
7.8
5.3
8.0
5.1
8.1
i;i
5.9
2.2
7.5
5.5
7.5
5.7
7.5
1.9
6.8
5.2
6.9
6. 1
7.1
6.0
7. 1
7.0
8.0
5.7
7.9
8.2
7.6
6.2
1.3
6.8
4 .'6
7.9
6.9
7.5
6.1
7.3
1.7
7.9
5.6
8. 1
8.3
5.9
i*.tt
3.9
8.0
5.7
8.2
8.2
6.1
U.2
din.
6.2
2.1
6.2
5.7
6.0
6.1
1.0
5.7
2.1
6.8
3.3
7.0
0.7
1.9
0.0
1.5
1.C
1.5
2.9
5.0
2.0
1.7
0.6
5.1
0.2
5.3
o.i
5.1
5.2
5.8
0.8
' 5.H
6.7
5.6
J.3
2.1
5.3
0.0
5.8
3.6
1.8
2.2
1.8
O.C
1.9
C.6
5.1
a. 8
2.3
0.0
0.0
5.9
2.5
5.3
1.9
1.5
0.0
Max.
9.6
9.0
1C. 1
10.1
10.5
9.7
9.8
10.0
9.9
9.7
9.6
10.0
6.7
6.5
1.7
9. 1
8.7
9.1
9.l»
8.9
8.U
9.3
9.1
9.0
9.2
9. 1
9.3
9.2
9.2
9. 1
8.9
'9. 1
9.8
9. 1
9.0
8.9
9.3
9.3
10.0
10. 1
9. 1
9.2
5.9
8.5
9.2
9.3
9.6
9.5
9.6
9. 1
7.9
9.6
9.O.,
9.3
9.2
9.4
9,5
CVS
14. l(
13. 9
13.9
15.5
17.8
11*. 8
56.1
16.6
10.3
12.5
32.2
11.9
33.5
10.5
89.9
16.1
28.8
18.1
36.3
15.8
37.9
22.6
56.7
17.1*
15.1
19. 1
17.2
17.8
17.8
11.5
17. 7
12.7
1C. 1
13.2
33.7
56.7
20.5
71 .8
12.6
27.0
17.5
U2.9
17.9
51.9
13.8
52.9
!«.(*
15.1
U2.7
60.1
62.1
13.8
38.0
12.7
11.0
11.3
67.0
Sta.
ENNB
ENNB
EPLP
EPLP
EPHF
EPRF
EHPB
ERPB
EBPB
ERPB
EHPB
ER10
EH 10
ETLQ
E7LQ
ETQE
ETQ2
PSUE
PSUE
P01
P01
P02
P02
P03
P03
P?i*
P01
P05
P05
P05
P75
PC 5
P06
P06
P07
P07
PJ8
P08
P09
P09
P10
P10
P11
P11
P12
P12
?13
P13
P13
P13
P13
' P11
P11
P15
P15
Dep.
D
E
A
E
A
E
A
B
C
D
'E
A
t?
A
w
A
£
A
E
A
E
A
E
A
E
A
g
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
2
A
E
No.
11
12
12
12
12
12
12
12
12
12
12
11
12
11
12
12
12
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
\\.
Mean
1.2
1.3
8.3
6.1
8.1
6.2
8. 1
8.0
7.1
6.3
1.3
6.9
6.9
8.2
3.1
8.3
7.0
9.0
6.5
6.7
6.8
7.6
6.0
7. 1
5.9
7.1
5.5
7.2
6.7
5.9
5.1
5.2
7.3
1.9
7. 1
1.0
7. 1
5.0
7.2
6.2
7.3
1.7
7. 1
3.7
7.0
3.5
7.0
7.0
6.6
5.1
3.5
7.0
1. 1
7.3
3.8
Bin.
0.0
0.6
6.3
1.5
7.2
1.0
6.7
6. 2
3.8
3.9
1.5
5.1
5.2
7.0
1.1
7.0
3.8
8.1
3.5
2.1
2.1
2.2
2.2
2.1
2.3
2.2
2.0
2.3
2.5
2.1
2.1
2.1
2.1
2.1
2.3
1.7
2.3
2.0
2.0
1.3
1.8
1.7
1.9
.1
.9
.3
.9
.8
.8
.2
.5
.7
.5
1:1
Max.
9.5
8.7
9.3
9.5
10.1
9.5
9.7
9.1
9.7
10.0
9.2
9.2
9.8
9.9
5.3
10.8
9.9
11.1
10.7
10.7
10.8
11.8
9.1
12.6
11.3
12.1
9.3
12.7
10.5
8.8
8.1
8.1
12.8
7. 1
11.0
6.1
11.6
7.8
12.1
9.7
11.9
7.0
11.1
5.3
10.3
5.3
11.5
11.2
11.2
a.i
5.1
11.6
6.1
18.-1
:vz
57.0
5U.3
10.9
'46.7
12.0
11.1
12.2
13.0
21.3
36.9
16.9
15.7
16.1
11.6
35.5
13.8
21.8
10.8
33.9
10.1
38.9
37.2
38.2
11.0
11.2
11.6
12.2
10.9
11.5
10. 1
11.5
39.7
11.7
35.2
11.9
10.5
11. 1
37.1
12.6
10.1
12.2
38.8
12.9
10.3
39.9
11.0
13.2
41.5
13.7
17.6
36.3
15.1
11.1
\l:\
14-U7
-------
Appendix 3 - 17. Summary of dissolved oxygen percent saturation. (*) data for the Pensacola Bay
system duriny January throuyh September, 1974 (Pensacila Bay data trom the University of West Florida),
Sta.
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFD
ALEX
ALEX
EFEI
EFEI
EJIV
EJIV
ENGA
EHGA
BREfi
EBEA
ECGH
ECGH
EEDB
IEDH
EEEM
EEEfl
IEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EBGD
EHGD
EHPK
JRPK
EIIL
EIIL
EIKC
EIKC
EKLQ
EKLQ
EKHP
EKHP
EKRP
EKHP
EKHP
EMQC
EMOC
ENNB
ENNB
ENNB
Dep.
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
e
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
B
C
No.
12
12
12
12
12
12
1 1
12
12
12
12
12
12
5
4
12
11
12
1 1
12
11
12
12
12
12
12
12
12
12
12
12
12
10
12
12
11
12
11
12
12
11
12
1 1
12
12
11
12
12
12
12
11
12
12
12
12
12
Mean
95.3
67. 1
101.9
100. 1
100.9
102. 1
63.0
96.9
68.7
100.9
71. 1
102.9
60.5
74.3
2H. 7
87.3
67.4
87.2
70.9
89.6
65.0
76.0
57.4
77.3
66.8
79.3
65.9
81.3
81.6
95.3
68.6
96.1
99.0
92.9
76. 1
52.4
77.7
46.7
98.2
85.6
87.8
72.0
85.0
57.5
94.7
65.6
98. 1
97.1
73.4
54.5
47.5
100.6
73.4
101.9
100.6
76.7
Win.
80.1
30.3
91.7
84.3
88.8
67.8
15.1
80.9
26.8
89.7
41.8
96.1
10.6
58.1
0.0
54.3
43.3
54.7
33.1
62.4
27.5
55.5
8.6
63.5
3.0
62.5
5.9
62.0
63.2
72.8
10.8
67.5
83.2
68.3
48.4
31.0
62.5
0.0
76.7
46.7
57.5
32.9
58.0
0.0
63.8
9.0
66.8
59.5
34.4
0.0
0.0
77.4
35.9
68.4
61.6
22.8
Max.
106.7
106.5
124.2
114.0
115.4
129.7
105.2
106.3
99.2
112.2
103.7
115.5
103.2
81.3
'- 55.9
108.7
91.2
108.3
98.5
108.2
90.8
96.2
90.0
85.9
88.3
101.2
86.7
103.0
101.3
123.5
109.5
123.5
123.3
108.0
107.8
95.7
87.7
86.2
112.9
109.4
99.6
1-11.3
107.9
88.5
107.3
105.5
126.4
117.8
133.9
89.2
83.5
115.1
110.3
119.4
118.9
113.8
'cv*
7.8
38.4
7.9
8.2
8.6
14.3
52.0
. 6.6
36.3
5.8
25.3
5.2
37.2
12.6
83.1
16.6
20.4
14.8
29.2
12.2
33.8
14. 1
49.3
7.7
40.2
12.3
42.7
13.4
13.0
17.9
44.8
16.9
14.2
11.8
27.6
42.2
9.8
58.2
12.2
23.2
13.6
38.3
16.4
48.0
13.4
50.0
18.0
17.1
38.2
49.7
50.6
10.7
31.6
14.8
16.3
36.9
Sta.
ENNB
ENNB
SPLP
EPLP
EPilF
EPHF
ESPB
EHP8
2BPB
ERPB
EBPB
EH10
ER10
ETLQ
ETLQ
ETQE
ETQE
PEUE
PEUE
P01
P01
P02
P02
P03
P03
P04
P04
P05
P05
P05
?05
P05
P06
P06
P07
P07
P08
P08
P09
P09
P10
P10
P11
P11
P12
P12
P13
P13
P13
P13
P13
P14
P14
Dep.
n
s:
A
17
A
E
A
B
C
D
E
A
E
A
. E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
B
C
D
E
A
E
A
E
No.
11
12
12
12
12
12
12
12
12
12
12
11
12
11
12
12
12
9
9
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
.12
j2
12
Mean
53. 1
50. 1
103. 1
74.7
104.8
73.3
103. 7
99.5
93.6
82.2
57.4
78. 1
77.3
103. 1
47.2
103.6
90. 3
120.3
85.5
36.9
93.8
94.9
83.2
90.3
78.3
89. 1
72. 1
90.1
85.4
78.8
73.9
70.9
89.9
67. 1
87. 1
53.9
87.7
69. 1
88. 1
80.5
89. 1
64.4
86.8
50.4
85.2
47.8
85.9
86.0
82.6
65.8
47.8
86.2
55.6
sor 1
.lin.
0.0
9.2
34. 7
22.7
94.9
15. 1
84.2
85.2
52.6
54.0
21.9
67.8
61. 1
93.0
17.0
93.0
44.5
104.6
48.8
32.0
31. 4
32.0
33.2
34.6
35.9
32.5
29.7
32.2
38.3
37. 1
31.9
35.6
33.4
31.9
32. 1
26.9
31.9
29.4
28.7
27.2
25.7
25.8
27.0
21.7
23.3
20.9
25.7
25.7
25.8
18.5
21.9
24.3
23.9
11. 9
Max.
103.1
96.1
118.0
108.9
123.7
121.6
111.9
110.5
118.9
143.7
94.4
85.8
37.2
110.2
71.8
109.5
119.9
131.2
124.8
123.9
169.6
134.9
130.8
147.9
126.3
142.9
97.6
149.1
124.0
113.5
109.8
101.7
146.2
96.7
129.1
85.1
132.8
97.9
137.7
118.9
136.6
97.2
128.7
71.9
114.6
71.4
130.6
126.2
115.0
93.9
71.4
134.7
90.0
135.5
93.7
cvS
54.4
42.3
9.7
3U. 1
7.3
38.8
8.D
9.2
19.2
30. 3
40.7
7.5
9.3
6. 1
34. 1
4.4
21.4
6.6
25. 1
31.5
39.0
31.7
34.9
32.9
32.0
33.0
32.6
33.4
33.7
33. 1
39.4
34.0
33.7
31.2
33.8
34.9
33.2
32.4
34.3
33.3
35.0
34.5
33.9
36.7
32.8
38.2
34.2
35.8
33.1
39.6
34.1
36.4
38.8
36. 5
51^4
14-U8
-------
Appendix 8-18. Mean dissolved oxygen concentrations and percent
dissolved oxygen saturation during the 1973 diel water
quality surveys.
1U-49
-------
14-50
-------
14-51
-------
1U-52
-------
Appendix 6 - 19. ultimate biochemical oxyqen demand data for Station ES1 G surfa-e and bottom by date.
DATS
1/23/71
2/12/71
3/05/71
3/27/71
1/16/71
5/07/71
5/29/71
6/18/71
7/09/71
7/30/71
8/20/71
9/11/71
averaqe
Appendix
Date
1/23/71
2/12/71
3/05/71
3/27/71
1/16/71
5/07/71
5/29/71
6/18/71
7/09/71
7/30/71
8/20/71
9/11/71
averaqe
Lu
5.9
5.7
1.2
1.9
3.8
3.3
3.9
11. '6
3.3
3.1
3-2
1C. 9
5.6
Lc
(mc;/l)
1.3
3.7
2.1
1.3
3.1
1.0
2.1
2.1
2.1
3. 1
0.8
10.9
3.1
8-19 (cont) .
Lu
(fflq/D
5.8.
11.9
. 9.8
5.9
5.5
5.5
8.5
8.8
9.7
8.7
5.5
10.9
8.0
Lc
(mq/1)
2.0
1.7
7.2
1.5
5.2
2.5
5.1
5.5
9.3
6.8
2.2
3.8
1.1
ERIf
- S
Ln tn kc kn
(mq/1) (days) (dayl) (day-1 )
1.6
2.:
1.8
3.6
0.7
2.3 .
1.5
12.5
0.9
-
2.1
-
2.9
Ultimate
2GLY
Ln '
3.8
10.2
2.6
u u
1.3
3.0
3.1
3.3
C.I
1.9
3.3
7.1
3.6
30.1
28.7
19.9
7. 1
36.5
8.0 •
17. 1
27.1
27.0
-
18.5
-
21.0
O.C97 C.
0.012 0.
0.056 0.
0.757 0.
C.060 0.
0.300 . 0.
0.321" 0.
0.100 0.
0.051 0.
0.030
1.890 0.
0.015
0.310 0.
biochemical oxyqen
- S
tn
(days)
16.0
10.0
31.3
9.2
36.9
11.2
1 7. 6
26.0
27.-
38.5
18. C
21.5
22.6
(day'1) (
0..183
0.157
0.056
0.501
0.017
0. 170
0.205
0. 120
0.017
0. 117
0.707
0.085
0.225
117
"31
325
037
389
010
123
001
035
-
088
-
C90
demand
kn
day -1)
0.019
0.009
0.001
0.039
0.139
0.060
0.112
0.091 •
0.097
0.35C
0.111
0.021
0.115
Lu Lc
(mq/1) (mg/1)
5. 1
7. 1
1.2
5.7
16. 1
3.3
1. 1
7.7
3. 3 v
2. 7
3.8
..7.0
5.9
data for
Lu
23.6
7. 0
8.0
1.5
1.2
6. 7
6. 3
8.9
7. 1
8.1
8. 3
11 . 7
11.5
3.5
2.3
2.6
1.1
2.2
2.9
2.7
2.6
3.3
2.7
1.0
1.7
2.7
Station
Lc
1 (mq/1)
10.1
3.2
7.3
1.2
3.5
2.5
1.1
5.9
1.1
3.1
3.6
11.7
o 7;9
ER10 - B
Ln tn
(mg/1) (days)
1.6 29.1
1.8 20.5
1.6 19.0
1.3 6.6
13.9 15.0
0.9 13.2
1.1 18.1
5.1 29.0
-
-
2.8 11.7
2.3 21.0
3.9 22.0
SGLY surface and
EGLK - B
Ln tn
(og/1) (days)
13.5 32.2
3.8 16.7
0.7 31.0
3.3 9.2
C.7 15.0
' 1.2 12.0
1.9 17.8
3.0 25.6
3.0 21.1
5.0 25.0
1.7 15.8
- '
1.0 20.1
kc
(lay"1)
0.093
0.089
0.011
0.715
0.122
0.050
0. 195
0.090
0.028
0.038
2.250
0.012
3.313
bottom
kci
(day'1)
0.101
0. 158
0.035
0.315
0.056
0. 150
0.163
0.110
0.113
0. 103
0.225
0.006
0. 130
kn
(day'1)
O.C89
0.017
C.G17
0.029
0.001
0.030
0.082
O.C13
-
-
O.C5C
0.022
0.010
by date.
kn
(day'1)
0.062
O.P19
0.069
0.056
0. 136
0. 010
0. 161
0.069
0.090
0.033
o.oti
-
O.C78
1U-53
-------
19 (cont). Ultimate biochemical oxygen demand data for Station EKMP surface and bottom hy date.
Date
1/23/71
2/12/7U
3/05/71
3/27/71
1/16/71
5/07/7U
5/29/71
6/18/71
7/C9/7I4
7/30/71
8/20/71
9/11/71
average
Appendix
Date
1/23/71
2/12/7U
3/C5/71
3/27/71
1/16/7U
5/07/71
5/29/71
6/18/71
7/09/714
7/30/71
8/20/71
9/11/71
average
Lu Lc
(ng/1) (mg/1)
5." 2.5
8.1 2.6
6.2 3.2
6.7 1.5
51.7 2.1
5.3 1.8
5.6 3.7
8.C 5.3
1.1 3.1
8.8 1.9
5.1 1.7
5.6 3.1
10.1 3.3
8-19 (cont) .
Lu Lc
5.6 1.1
1.2 2.1
12.1 1.5
17.3 2.9
16.1 16.1
5.3 5.2
6.5 3.6
6.1 14.2
8.1 6.8
-
6.1 2.3
11.6 3.3
12.1 5.0
SKKP
Ln
(mq/1)
2.5
5.8
3."
5. 2
19. 3
0.5
1.9
2.7
1.C
3.9
3.1
2.2
6.8
Ultimate
ENNB
I.n
(aq/1)
1.5
2.1
7.9
11. 1
-
0.1
2.9
1.9
1.6
-
1. 1
141.2
7.1
- S
tn
(days)
27.0
2C.C-
20. C
9.8
21."
38.1
18.3
26.9
26.5
29.3
16.9
30.1
23.7
EKHP - B
kc
(day"1)
C. 163
0. 181
0.081
0. 28?.
n. 059
0.050
0. 211
0. 100
0.098
0. 122
0.630
0.070
0. 173
kn
(day'1 )
0.018
0.0 16
;.oi5
n.023
0.001
0.150
0. 181
0.092
0.268
0.019
0.057
0.071
0.081
biochemical oxygen demand
- S
tn
(days)
30.5
19.1
20.0
21.7
-
1U.9
16.2
26.5
27.0
-
15.1
23.1
21.1
kc
0. 117
0. 131
0.061
0. 112
0.008
0.050
0.237
0. 120
0.038
-
0.51U
0.070
0. 117
kn
(day^)
0. 135
0.010
0.003
0.003
-
0. 110
0.061
0. 112
0.113
-
0.052
0.002
0.072
Lu
1. '?
6. 1
5. 8
3.9
3.7
15.7
6. 1
8. 7
-
6.0
6.1
22.3
6. 5
data for
Lu
(mg/1)
9.5
11. 7
5.3
1.C
1.6
5. 3
7. 3
7. 1
1. 1
7.8
7.3
7. 3
6. 7
Lc
(mg/1)
2. 6
2.3
5.8
• 1.1
2.3
1 .1
1.5
5.6
-
1.5
1.6
19.7
5.0
Station
Lc
(og/1)
2.8
1.9
5.3
1.5
U.6
1.9
1. 1
5.5
3.5
6.6
7.3
1.2
1. 1
Ln
(mg/1)
1.1
3.8
-
2. '5
1.1
11.3
1.9
3. 1
-
1.5
14.8
2.6
3.1
tn
(days)
30.0
19. 2
-
10.0
15.0
31.9
18.2
20.0
-
38.6
15. 3
20.6
20. 1
ENNB surface and
ENNB
Ln
(mg/1)
6.7
9.8
-
2.5
-
0.1
3.2
1.6
0.9
1.2
-
6. 1
3.5
- B
tn
(days)
18. 7
16. 8
-
10.1
-
38.3
16.9
32.9
35. 6
17.0
-
13.6
22.2
kc
0. 15U
0.201
0.026
0.228
0. 102
0.060
0. 138
0. 110
-
0.010
0.576
0.006
0. 158
bottom
kc
(day1 )
0.200
0.200
0.021
0. 287
0.003
0.060
0. 197
0.080
0.065
0.039
0.031
0. 116
0.118
kn
(dayl)
0. 196
0.030
-
0.067
0.061
0.002
0.181
0. 058
-
0.261
n.esa
0. 103
3.089
by date.
kn
(dayl)
0.008
0.010
-
r.C69
-
O.C90
0. 100
C.073
-
0.058
-
0 . P 30
0.055
14-5U
-------
Appendix 8 - 19 (cont). Ultimate biochemical oxygen demand data for Station EBPB surface and bottom by date.
Date
1/23/71
2/12/71
3/05/71
3/27/71
1/16/71
5/07/71
5/29/71
6/18/71
7/09/71
7/30/71
8/20/71
9/11/71
average
Appendix
Date
1/23/71
2/12/71
3/05/71
3/27/71
1/16/71
5/07/71
5/29/71
6/18/71
7/09/71
7/30/71
8/20/71
9/11/71
average
Lu Lc
(mg/1) (mg/1)
5.2 3.8
6.7 1.9
5.1 1.2
- 3.5 2.7
9.6 9.8
6.3 2.3
5.9 1.0
9.1 1.1
1.5 3.2
.16.5 7.2
5.2 2.3
5.1 2.5
1.1 1.0
8-19 (cont).
Lu Lc
(mq/1) (mg/1)
3.3 2.3
5.6 1.6
3.8 2.1
1.7 3.3
1.6 1.6
9.6 1.6
1.3 2.6
1.3 3.1
1.C 2.8
5.5 1.6
7.1 2.3
5.3 2.8
5.1 3.1
ERPB
Ln
(mq/1)
1.1
1.8
0.9
0.8
-
.1.0
1.9
5.0
1.3
9.3
2.9
2.6
3.2
Ultimate
AGJI
Ln
(tnq/1)
1.0
1.0
1. 7
1.1
-
5.0
1.7
1.2
1.2
0.9
5.1
2. 5
2.3
- S
tn
(days)
28.8
11.3
13.1
31.8
-
10.0
27.1
30.3
27.0
13.0
18.0
19.2
23.9
kc
(day-1)
0. 122
0.315
0.068
0.010
0.017
0.210
0. 283
0. 120
0.079
0.022
0. 361
0.131
0. 153
kn
(day'1)
0.095
D.032
0.257
0.130
-
0.032
0.. 166
0.037
0 . 1 56
-
0.095
0.065
0.137
biochemical oxygen demand
- S
tn
(days)
10.0
21.2
19.0
31.1
-
33.7
27. 1
29.0
27.0
37.1
13.5
27.8
28.2
kc
(day'1)
0. 191
0. 130
1. 127
0. 1 18
0.039
0.060
0.278
0. 110
0.058
0.032
0.329
0. 111
0. 117
kn
(Jay'1)
0.317
0.020
0.065
0. 120
-
0.001
0.116
0.093
0. 128
0.109
D.019
0.011
0.086
Lu
(mq/1)
-
6. 2
1..8
5.0
3.9
1. 2
6.0
6.0
35. 1
13.0
5.0
6.1
8.5
data for
Lu
(mq/1)
7.P
3.6
3.8
3. 3
6.9
3.7
-
5.6
19. 3
19. 8
6.6
3.3
?.5
Lc
(mg/1)
-
1.6
1.8
2.0
2.1
1.2
1.1
3.1
3.3
13.0
1 .1
6.1
1.3
Station
Lc
(mg/1)
3.0
2.3
1 .9
2.5
6.9
3.7
-
3.7
2.6
19.8
1.9
2.0
1.6
ERPB
Ln
(mg/1)
-
1.6
-
3.0
1.5
-
1.6
2.6
31.8
-
3.6
-
7.0
- B
tn
(days)
-
20.5
.-
25.7
18.9
-
18.1
27. 1
25.1
-
17. 3
-
21.9
A3JI surface and
AGJI
Ln
(mq/1)
1.0
1.3
1.9
0.8
-
-
-
1.9
16.7
-
1.7
1.3
1.1
- B
tn
(days)
21.5
31.1
28.3
31.5
-
-
-
28.3
23.7
-
17.8
29.8
27.2
kc
(day -1)
-
0.173
0.033
0.065
0.099
0.010
0.111
0. 130
0.061
0.008
0.211
0.028
0.108
bottom
kci
(day'1 )
0. 188
0.059
0.093
0.079
0.029
0.050
-
0.110
0.061
0.007
0.253
0.098
0.093
kn
(day'1)
-
0.015
-
0.018
o. ins
-
0.161
0.086
0.003
-
0.066
-
0.065
by date.
kn
(day'1)
0.021
0.081
0.231
0.293
- ,
-
- -
0.113
0.003
-
0.086
0.112
0. 119
14-55
-------
dix 8-19 (cont). Ultimate biochemical oxygen demand data for Station BFEI surface and bottom by date.
BFSI - S
n.f« Lu Lc Ln tn kc kn
(mq/1) (mg/1) (mg/1) (days) (day'1) (day ^
1/23/70 -
2/12/70 - - - * ' - . ,
3/05/70
3/27/70 - - - . . * ' *
0/16/70 - - - ".'"."
5/07/70 - -
5/29/70 - - -
6/18/70 -
7/09/70 2.0 1.9 0.5 27.0 0.062 0.9UO
7/30/70 -
8/20/70 3.8 1.1 2.7 22.0 0.215 0.022
9/11/70 8.0 7.2 0.8 00.5 0.027 0.050
average 0.7 3.0 1.3 31.2 0.1C1 0.338
BPEI - B
Lu Lc Ln tn kc kn
(mg/1) (mg/1) (og/1) (days) (day'1) (dayl)
-.:..- -:•..- •,:• - .;^-;
-.,-.-..- . - ••. -
— ' — — — — —
-
•- - - ' - - -
----- -
3.0 2.0 1.0 29.0 0.080 0.020
6.9 2.6 0.3 26.1 0.083 0.023
- - - - -
0.3 1.1 3.2 18.0 0.1S9 0.093
6.3 ».9 1.0 29.8 0.008 0.070
6.5 2.8 2.5 25.8 0.082 0.152
Appendix 8-19 (cont). Ultimate biochemical oxygen demand data for statian PEUE surface and botton by date.
Date
1/23/70
2/12/70
3/05/70
3/27/70
0/16/70
5/07/70
5/29/70
6/18/70
7/09/70
7/30/70
8/20/70
9/11/70
average
PEUE - s
Lu Lc Ln tn kc kn
(mg/1) (nig/1) (mg/l| (days), (day'1) (day'1)
-
. - -
....
•-
-
-
-
9.7 7.0 2.3 32.3 0.106 3.101
9.3 6.5 2.8 25.8 0.090 C.079
11.1 11.1 - - 0.000
9.8 6.5 3.3 21.8 0.080 0.052
10.0 -5.it 5.0 20.6 0.100 0.099
10. 1 7.0 3.0 ' 26.1 0.086 0.093
PEtlE - B
Lu Lc Ln tn kc
(rng/1) (mg/1) (mg/1) (days) (day1 )
- - -
-
-
.
-
-
-
8.3 6.0 2.3 26.2 0.090
8.5 7.8 0.7 27.0 0.037
5.5 0.1 1.0 37.0 0.055
11.2. 6.0 5.2 20.0 0.111
7.2 3.0 4.2 11.3 0.106
8.2 5.0 2.8 25.3 0.087
kn
(dayl)
-
-
-
-
-
-
-
0.050
3.700
0. 155
O.C63
0.009
0.800
14-56
-------
Appendix 8 - 20. Summary of turbidity (JTH) data for the Pensacola Bay system
January throuqh September, 1971.
Sta.
ADGV
ADGV
AGJI
AGJI
AGJI
AGJI
AGJI
AGPH
AGPH
AJFD
AJFD
ALEX
ALEX
BFEI
BFEI
BJIV
BJIV
BNGA
BNGA
BREA
BBEA
ECGH
ECGH
EEDR
EEDR
EEEH
EEEM
EEIX
EEIX
EEKV
EEKV
EGLY
EGLY
EGLY
EGLY
EGLY
EHGD
EHGD
Dep.
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
E
A
.E
A -
• E
A
"E
A
E-
A
B
C
0
E
A
E
No.
12
12
12 .
12
12
12
12
12
12
12
12
12
12
•>'
5
12
12
12
12
12
12
12
12
12.
12
12 -
12
12
12
12
12
12
12
12
12
12
12
12
Mean
0.6
6.0
2.9
.. 2.8
2.6.
2.5
s;7
3.0
0.8
3.2
5.3
2.1
u.7
4. U
5.5
5.9
6.1
7.0
6.3
5.2
9.1
16.7
15.6
17.8
18.9
18.5
20.2
15.1
m.8
12.3
10.2
11.6
11.2
1C. 9
10.5
10.6
17.6
15.9
Mi
1.
1.
0.
0.
0.
0.
• o.
• o-.
1.
C .
0.
0.
2.
2.
2.
1.
2.
1.
1.
1.
1.
0.
5.
5.
it.
5.
6.
0.
3.
3.
. '3.
3.
3.
2.
2.
3.
5.
3.
n.
1
0
5
7
6
5'
9
9
6
7
5
5
0 •
3
3
2
3
9
7
2
9
9
1
U
5
5
6
7
8
2
5 '
3
3
6
3
2
9
3
Max.
15.0
10.0
15.0
10.0
8.0
7.7
9.8
7.5
9.1
10.0
10.0
U. 8
10. -0
8,9
15.0
16.0
1U.O
20.5
21.5
21. ?
39.0
37.0
rOO.O
03.0
05.0
01.0
52.0
30. 0
30.0
30.0
30.5
30. 0
31.0
30.0
27.5
27.5
03.0
57.0
CV%
95.3
82.7
138.2
131.5
90.0
8U.8
07.5
79.0
50.1
86.3
55.7
63.0
50.2
61.0
97.0
71.9
65. 1
78.8
89.7
106.6
110.7
56.2
73.6
57. U
60.1
61.9
63.6
63.9
65.1
69.6
83.0
85.6
81.9
89.9
71.0
67.8
61.5
99.3
Sta.
EHPK
• EHPK
El IL
EIIL
EIKC
EIKC
EKLQ
ETLQ
EKHP
EKHP
EKHP
EKHP
EKHP
EHQC
EHQC
ENNB
EHNB
ENNB
ENNB
ENNB
EPLP
EPLP
EP8F
EPRF
ERPB
ERPB
ERPB
EBPB
ERPB
EB10
ER10
ETLQ
ETLQ
ETQE
ETQE
PEUE
PEIJE
Dep.
A
E
A
E
A
E
A
E
A
B
C
D
B
A
E
A
B
C
D
E
A
E
A
E
A
B
C
D
E
A
E
A
E
A
E
A
E
NO.
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
9
9
(lean
9.1
9.9
13.6
1 1.0
10.5
17.0
12.8
10.8
12.9
12.0
10.0
11.0
10.7
7.5
7.5
11.2
10.8
12.3
13. 2
10.1
8.9
8.5
5.0
5.3
7.2
6.3
6. 8
0.6
7. 0
19.7
20.8
6.0
10.7
0.2
0.1
6.2
5.8
Bin.
2.8
3.5
3.5
3.8
3.. 2
3.2
3.2
2.1
2.3
2.8
2.7
3. 7
0. 1
1.6
1.9
1.8
1.5
1.0
5.3
6.6
1.5
2.1
1.3
1.2
1.0
1.0
0.6
1.0
2.8
8.1
12.0
0.6
2.0
0.9
0.7
2.0
2.9
Max.
22.0
20.5
36.0
28.5
37.0
09.0
33.0
27.0
30.0
30.0
30.5
29.0
30.0
21.5
15.0
33.0
30.0
33.0
22.5
29.0
26.0
23.0
16.0
10.0
22.5
20.0
27.0
10.0
18.0
39. C
39.0
20.5
26.0
13.0
12.5
16.0
8.9
cv%
58.8
58.. 0
75.1
66.3
71.6
80.7
73.9
70.0
86.9
87.3
86.5
70.9
66.9
98.3
50.6
101.5
99.3
87.9
08.1
58.1
90.9
80.8
87.1
09.8
103.3
112.0
113.6
63.7
59.5
03.0
38.1
107.3
71.1
93.5
90.5
77.0
38.1
Appendix 8 - 21. Locations of sampling stations during August 15 aad
November 2.0. 1970 turbidity studies.
Station
E-1
E-2
E-3
E-o:
E-5
E-6
E-7
1-8
E-9
E-10
i-11
E-1
B-2
E-3
E-0 • •
E-5 •
E-6
Y-1
Y-2
X-3
Y-0
Y-5
fioad
U.S. -90
F1.-18U
Fl.-O
U.S. -29
F1.-01
F1.-01
U.S.-29
U.S. -80
U.S. -29
(dirt)
U.S. -80 •
U.S. -90
(dirt)
Fl.-O
Fl. -191
Fl.-O
Fl.-U
F1.-B7
"U.S. -9?
- F1.-2
F1..-85
F1.-285
Kiver
Escambia River
Escambia hiver
Escambia River
Big Escambia Creek
Conecub River
Murder Creek
Conecuh Biver
Conecuh River
Conecub River
Patsaliga Creek
rigeon Creek :
Blacktiater Biver
Blacknater Biver
Blackuater River
Coldwater Creek
Coldwater Creek
Colduater Creek
Yellow aiver
Yellou aiver
Yellow River
Shoal Hiv«r
Shoul River
Location
6 km. south of Pace, Florida
8 km. northeast of Cantonment, Florida
5 km. east of Century, Florida
2 km. north of Flomaton, Alabama
3 km. south of East Breuton
2 km. east of Breuton, Alabama
27 km. cast of Brenton, Alabama
3 km. vest of Andalusia, Alabama
3 km. north of Andalusia, Alabama
6 km. uest of Santt, Alabama
19 km. uest of Andalusia. Alabama
1 km. vest of Milton, Florida
2 km. . northwest of Harold, Florida
6 km. uprthuest of Baker, Florida
. IV km. northeast of Hilton, Florida
10 km. west of nunson, Florida
5 Km. .east of Jay, Florida
16 km. north of Holley, Florida
5 km. west of Crestviea, Florida,
8 kia. east of Blackman, Florida >
8 km. south of Crestview, Florida
8 km. north of Mossy Head, Florida
1U-57
-------
Appendix 8 - 22. Turbidities in the Escambia, Blackwater and Yellow Rivers
during Auqust 15, 197U and November 20, 1974.
Station
B1
84
35
B6
B3
Y2
Y3
Y5
Y4
B2
Y1
Turbidity
Auqust 15
11.0
10.0
11.0
3.1
3.7
4.0
2.8
3.2
2.0
5.3
5.3
4.7
3.7
3.3
4.2
12.0
12.0
6.8
19.0
22.0
21.0
U.2
4.2
4.3
6.4
6.3
6.0
5.0
5.4
4.6
5.7
5.8
5.4
(JTU)
/ November 20
2.2
2.3
2.8
1.8
1.5
1.7
1.0
1.5
1.5
2.8
2.8
2.5
2.3
2. 3
2.5
4.2
4.5
4.0
6.0
5.3
5.3
6.0
5.8
7.0
5.0
5.0
5.5
4.5
4.5
4.5
6.5
6.0
6.C
Station
E1
E2
E3
E4
E6
E5
E7
E9
E10
E8
E11
E12
Turbidity (
August 15
10.0
10.0
10.0
15.0
15.0
15.0
36.0
34.0
38.0
21.0
22.0
23.0
10.0
10.0
10.0
42.0
39.0
40.0
28.0
29.0
30.0
13.0
12.0
12.0
42.0
40.0
43.0
24.0
24.0
25.0
20.0
18.0
20.0
33.0
37.0
33.0
;JTH)
November 20
5.0
5.0
4.8
6.3
8.0
8.5
15.0
13. C
13.0
7.0
7.5
6. 3
58. C
70.0
60.0
10.0
10.0
12.0
10.2
10.0
9.2
5.8
5.2
5.5
33.0
32.0
35.0
9.8
8.8
9.8
25.0
27.0
25.0
13.0
18.0
20.0
14-58
-------
Appendix 9-1. Summary of chlorophyll _a_ (mg/1) data for the Pensac.ola Bay system
January through September, 1974.
Sta.
ADGV
AGJI
AGPH
AJFD
ALEX
EFEI
BJIV
BNGA
8PEA
ECGM
EEDR
EEEM
EEIX
EEKV
EGLY
EHGD
EHPK
EIIL
EIKC
EKLQ
EKMP
EMQC
ENNB
Dep.
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
No.
12
12
12
11
12
5
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
Mean
0.0039
O.C034
C.0035
0.0038
0.0032
0.0036
G.OC45
0.0046
0.0044
0.0041
0.0049
0.0051
0.0056
O.CO&4
C.C081
0.0038
0*0.161
0.0056
C.0051
0.0068
C.OC71
0.0057
G . 0066
Min.
0.0022
0.0017
0 . C 0 1 4
0.0011
0 . C 0 1 6
0.0003
0.0017
0.0017
0.0012
0.0016
0.0019
0.0016
0.0015
0.0007
0.0027
0.0014
0.0066
0.0023
0.0006
0.0019
" 0.0033
0.0028
0.0026
flax.
0.0100
0.0082
O.OG86
0.0110
C.OC65
0.0062
C . C 1 1 1
O.OC93
0.0160
O.OC73
0.0121
C.OC86
0.0108
0.0170
0.0137
C.0088
C.0410
C . 0 1 C G
0.0131
C.0102
C.0'179
- 'C.0087
0.0106
CV*
54.4
54.3
5.3.4
69.4
40.5
67.6
66.7
51.0
- 90.8
46.2
59.1
44.6
55.3
65.0
48.5
59.6
68.1
43.2
73.0
33.1
. 54.0
29.7
39.5
Sta.
EPLP
EPRF
ERPB
3R10
ETLQ
£Tv2E
PEUE
P01
P02
P03
P04
PC5
P06
P07
P08
P09
PIG
P11
P12
P13
P14
P15
Dep.
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
NO.
12
12
12
11
12
12
8
12
12
12
12
12
12
12
12
12
12
12
12
12
12
11
Mean
0.0073
0.0056
0.0058
O.CC53
0.0048
0.0043
0.0121
0.0026
0.0042
0.0035
0.0035
0.0033
0.0044
0.0040
0.0033
0.0033
0.0032
0.0065
0.0033
0.0032
0.0032
0.0038
Min.
:<.:o39
o!c028
0.0028
".0013
C.0020
C .0013
0 .0061
0.0 OC4
0.0010
0.0011
C . 0 0 1 0
0.0010
o.:oi5
0 . C 02 2
0.0012
O.C011
0.0013
0.0013
0.0017
0.0012
C.0012
0.0013
Max.
0.0143
0.0107
0.0113
0.0096
0.0118
0.0067
0.0239
0.0126
0.0138
0.0096
0.0094
0.0100
0.0111
0.0095
0.0116
C.OC90
0.0047
0.0376
0.0051
0.0092
0.0095
0.0080
c«
50.6
41.8
52.5
56.9
53.5
42.9
52.6
135. 1
99.3
36.6
67.6
34.2
73.8
53.5
35.7
71.9
37.4
155.8
34.6
68.8
55.7
64.4
-------
Appendix 10 - 1. Bimonthly distribution of otter trawl samples b'y area and by station*
* Number of trawl samples
ea Station Oct.
II 2
III 2
V 2
VI 2
VII 2
VIII 2
I .0
IV 1
IX 2
X 2
XI 0
Dec.
2
2
2
. 2
2
2
1
2
3
2
2 .
Feb.
2
2
2
2
2
2
2
2
1
2
2
Apr.
2
2
2
2
2
2
2
2
2
2 . .
2
June
2
2
2
2
2
2
2
2
2
. 2
2
Aug.
2
2
2
2
2
2
2
2 .
."' 2 -
2
2
Total
12
12
12
12
12
12
9
11
9
12
10
Total
17
19
21
22
22
22
123
-------
Appendix 1C- - 2. Spatial distribution of fishes collected by otter trawl in Rscambia Bay,
during 1973 through 1974. Areas are illustrated in Figure 10 - 1.
Species
tasyatis sabina
Dasyatis sayi
Lepisosteus osseus
Elops saurus
Brevoortia patron us
Harer.gula pensacolae
Eorosoma petenese
Anchoa hapsetus
Anchoa mitchilli
Synodus t'octens
Ictalurus punctatus
Arius falis
Eagre marinus
Opsanus beta
Menidia beryllina
Synynathus louisianae
Synqtiathus scovelli
Caranx hippos
Chloroscombrus cbrysurus
Oligoplites saurus
Selene vomer
Eucinostouus argenteus
Archosarjus probatocephalus
Lagodon rhoohoides
Bairdiella chrysura
Cyncscion arenarius
Cynoscion nebulosus
Leiostoums xanthurus
Henticirch us americanus
Henticirrhus litteralis
Hicropogon undulatus
Cbaetodipterus faber
flugil cephalus
Polydactylus octonemus
Gobioides btoussonneti
Gobionellus hastatus
Gobioncllus shufeldti
Trichiurus lepturus
Sccmberomor us maculatus
Peprilus alepidotus
Prionotus tribulus
Citharicthys spilopterus
Etropus crossotus
Earalichthys lethostigma
Irinectes maculatus
Synphurus plagfusa
SphoeroiJes parvus
Chilcmycterus sciioepfi
Total
Area 1
^
2tt
0
0
2U
2
1,570
0
10
173
5,522
0
0
3
C
0
1
0
0
10
9
2
0
1
0
0
2
172
0
2,828
n
0
1,«93
0
0
131
0
0
1
3
0
a
0
1
0
0
1
0
0
0
11 ,963
Area 2
1
2U
r
*
1
1
270
'1
."J
1,27.3
5,690
5
0
30
1
1
0
Q
0
1
181
C
0
0
7'
0
16
157
2
2,387
2
0
1,363
1
0
1l»5
0
0
0
3
3
5
0
2
3 •*
A
i;
0
z\
ff
n
11,551
Area 3
Number of
2tt
.•)
1
\J
,T
255
13
0
1,670
3,60 1
2
£t
27
0
**,
0
1
n
0
-------
Appendix 10 - 3. Bimonthly distribution of fishes collected by otter travl iu Escambia Bay, 1973-74.
June
Oct.
Dec. Feb. Ape.
Number of trawl samples
Aug.
Species
Easyatis sabina
Dasyatis sayi
Lepisosteus osseus
Elofs saucus
Brevoortia patronus
Harengula pensacolae
Corofsona petenese
Anchoa hepsetus
Anchoa mitchilli
Synodus foetens
Ictalurus punctatus
Arius, felis
Eagre marinas
Opsauus beta
Menidia baryllina
Syngnathus louisianae
Syngnathus scovelli
Caranx hippos
Chlcroscombrus chrysurus
Oligoplites saurus
Selene vomer
Eucinostomus arqenteus
Archosargus probatocephalus
Lagodon rhouboides
Eairdiella chrysura
Cyncscion arenarius
Cyncr.cion nebulosus
Leiostomus xanthurus
(lenticirrhus americanus
denticirrhus litteralis
Hicropogon undulatus
Chaetodipterus faber
tlugil cephalus
Eolyddctylus octonemus
Gooioides broussonneti
Gobionellus hastatus
Gobionellus shufeldti
Trichiurus lepturus
SccmberoDorus naculatus
Peprilus alepidotus
Fricnotus tribulus
Citharicthys spilqpterus
Itropus crossotus . .
Paralichthys lethostigma
Trinectes naculatus
Symphurus playfusa
SpboeroiJas parvus
Chilcmycterus schoepfi
Total
17
C
0
16
0
3
1
0
1,517
7,092
0
0
17
0
0
0
0
0
1
254
0
2
0
2
2
0
20
0
1,593
1
A
181
0
C
1C
1
/;
0
0
3
5
. 0
C
o
0
0
0
1
0
1C, 722
19
1
r
2
0
5
p
8
2.U35
11,591
5
0
0
0
C
0
1
0
9
2
3
0
11 1
2
-\
g
55
8
U1 1
7
H
79
1
3
r
• C
•1
0
r.
0
r\
2
0
n
n
0
1
1
1
11,767
21
1
0
1
r
5,305
C
7
C
3,532
0
2
0
0
C
6
0
1
ri
2
C
0
2
1
1
1U
6
1
1,821
4
i*
V.
398
0
12
C
A
•;; 3
•1
/•
r
r.
0
1
r
0
1
0
0
,-
11,123
22
0
3
6
7
2,3iy
0
J
3
979
1
0
13
1
1
0
0
0
3
0
0
0
}
u
0
1
116
D
2,911
5
1
2,171
,1
6
13
0
13
0
6
0 .
1
0
' 3
a
2
3
V
3
C-
S,5iJ6
22
0
2
1
C
1,640
0
0
2U
2,938
0
3
10
0
0
0
0
0
5
0
0
0
0
0
10
37
1,1 OU
2
6,151
0
y
U, 103
C
3
379
0
1
0
19
3
1
n
2
0 • .
3
2
0
2
'"'
16,552
22
0
D
3
1
33
254
0
717
1,U3U
5
D
U3
3
T
D
3
3
3
367
3
2
3
2
12
23
286
3
939
3
D
9C3
3
3
65
0
0
3
3
3
13
3
A
3
1 -
2
3
2
D
8, 126
i ota j.
catch
2
2
29
a
9,305
255
15
1,693
30,566
11
5
123
1
1
6
1
1
23
625
3
4
1 13
11
25
84
1,587
11
13,826
12
5
7,915
1
24
467
1
17
1
25
3
20
2
12
10
6
8
1
9
1
69,376
1U-62
-------
Appendix 10 - 4. bimonthly distribution of fisher, collected by seins in Escambia Bay, 1973-7'4.
I
ON
Species
Oct. Dec. Feb. Apr.
Number of seine hauls
June
Aug.
Total
3,278
92
119
3,325
2,110
572
Total
F.IOJS saurus
firevoortia patronus
Harenjula pensacolae
Ancnoa hepsetus
Anchoa mitchi_Lii
Synodus foetens
Arius felis
Strougylura marina
Cyprinodon .variegatus
Fundulus grandis
Fundulus similis
Lucania parva
Menidia beryllina
Micropterus salmoides
Chlcroscombrus chrysurus
Oligoplites saurus
Lut janus yriseus
Eucinostomus argenteus
Lagodon rhoraboides
Cyncscion arenarius
Cyncscion nebulosus
Leiostomus xanthurus
Menticirrhus americanus
Micropogon undulates
Mugil cephalus
Polydactylus octonemus
Gobiosoma bosci
Gobiosoma robustura
Gobionellus shufeldti
Cit har icthys npilopterus
Etropus croasotus
Trinectes maculatus
Sphoeroides parvus
4
0
2b69
5
;**,
155
0
0
o
o
0
5
2
384
0
0
3
1
33
1
1
1
7
C
4
0
0
1
0
n
0
1
0
>j
4
0
12
0
n
33
0
0
•J
5
0
1
o
6
0
}
0
1
5
0
8
1
4
D
3
13
0
0
n
o
0
0
0
0
4
0
8
0
r
n
r
0
r>
,"•
0
0
0
18
^*>
r:
r.
0
0
1
C
Q
33
0
n
57
0
0
1
1
?
0
0
/-,
4
2
2807
0
Q
22
4
0
0
1
21
0
0
43
Q
0
C
0
U
20
22
0
28
0
109
237
0
Q
0
0
n
0
0
0
a
0
3
0
2
1231
0
1
3
0
49
4
0
403
2
1
0
0
0
35
2
0
97
1
251
10
10
0
0
0
1
0
1
3
'4
0
0
15
0
7
*\
1
0
0
0
0
0
83
0
296
2
0
14
7
0
0
2
0
121
r
\j
0
o
0
o
C
G
,••1
22
udcun
2
5499
20
2
1448
4
2
3
6
70
10
2
942
2
299
5
2
61
64
33
2
171
1
488
317
10
1
1
1
1
1
1
25
9,496
-------
Appendix 10 - 5. Spatial distribution of fishes collected by seine in Sscarabia Day
during 1973 through 1974.
I
<*
•e
Species
Hops, saur us
Erevoortia patronus
Hare.ng.ula pensacolae
Anchoa hapsetus
Anchoa nnit.chilli
Syncdus tcetens .
Arius felis
Strongylura marina
Cyprindon varieyatus
Fundulus grandis
Fundulus similis
Lucania parva
Menidia baryllina
Micropterus salmoides
Chloroscombrus, chrysurus
Oligoplites saurus
Lutjanus griseus
Eucinostomus argenteus
Lagodon rhonboides
Cyncscion arenarius
Cyncscion nebulosus
Leicstomus xanthurus
Menticirrhus americanus
Micropogon undulates
flugil cephalus
Polydactylus cctouemus
Gobiosooa bosci
Gcbiosoma robustuia
Gobionellus shufeldti
Cit haricthys spilopterus
Etropus crossotus
Trinectes maculatus
Sphoeroides parvus
Total
Area 1
6
1
4706
0
1
329
0
2
1
0
0
G
0
138
o
c
2
0
33
18
7
0
56
0
371
2
0
0
0
0
b
0
1
0
5,668
Area 2
Number of
6
1
760
0
0
17
a
3
0
0
1
0
0
336
n
5
2
0
0
0
2
Q
7
1
6
1.1
C
p
r.
0
f,
'*J
0
O
3
1,160
Area 3
seine haul
6
0
a
20
0
1046
r>
A
1
o
n
1
0
73
/\
29U
1
o
12
u
2U
2
3U
0
15
57
0
0
0
0
0
1
0
22
1,615
Area U
s
6
•}
25
0
1
56
G
D
1
6
69
9
2
395
2
0
0
2
16
U2
' G
f\
74
0
94
245
10
1
1
1
1
r\
-i
±t
0
1,053 .
Total
r* a 4- /-• K
C at. Ca
2
5U99
20
2
1448
4
2
3
6
70
10
2
942
O
299
5
2
61
64
33
2
171
1
488
317
10
1
1
1
1
1
1
25
. 9,,496
-------
Appendix 10 - 6. Spatial <
Escambia Bay during 1971
Species
Eenaeus setiferus
Pcnaeus aztecus
Penaeus' iuocarum
Total
Jistribution of shrimps (penaeus spp. ) collected by otter trawl in
3 and 197U. Areas arc illustrated in Figure 1C - 1.
Area 1 Area 2 Area 3 Area U Area 5
Number or trawl samples Total
2U 2U 21* 29 22
1 11 1 50 1U 83
59 51 U2 153 57 362
0 7 26 0 i» 37
63 69 72 2C3 75 082
Appendix 10 - 7. Bimonthly distribution of shrimps (Peiideus spp.) collected by otter trawl in
Escambia Bay during 1973 and VJ7I*.
Species
\
Fenaeus setiferus
Fenaeus aztecus
Fenaeus duorarum
Total
Oct. Dec. Feb. Apr. Juno Aug.
Number of trawl samples Total
17 19 21 22 22 22
B 19 U 1 1 50 B3
25 25 27 U9 226 10 362
2 0 35 0 0 0 37
35 4U 66 5C 227 60 162
Appendix 10 - b. Commercial landings of shrimp (E'enaeur, spp.) from Escamljia Bay from 196'4 to 1973.
1
196U
1965
1966
1967
1968
1969
1970
1971
1972
1973
Annual average
five-year average
(196U-1963)
Five-year average
(1969-1973)
lumber
182
2U1
63
U1S
14 10
U29
59
2
0
2
180
262
98
Broun
0
16,701
C
59,21«
53,093
1,955
73
11C
0
G
13,115
25,802
K28
Catch (Ibs)
Pink
/*,
571
\
r\
333
1.16?
11,999
853
20
0
98
1.8U7
U99
3, 1'JU
White
29.37U
18,567
3,553
5,818
7,740
8, 180
1,700
0
;
C
7.U96
13,016
1,976
Total
(Ibs)
29,37U
35,789
3,56 j
65,665
61,993
25, 13U
2,626
130
0
98
22,1157
39, 317
5,598
Dollar
13,763
15,391*
2,623
30.181
35.561
18,327
1,663
151
5
96
11.826
19,601*
1*, JU7
Average
(Ibs)
161. u
118. 5
56.6
158.7
151.2
58.6
<*"». 5
65.0
0.0
19. C
• 12U. 6
150.0
56.9
14-65
-------
Appendix 10 - 9. Commercial landings of shrimp (penaeus spp.) from East Bay from 196U to 1973..
Year
1964
1965
1966
1967
1968
1969
1970
1971
1972
1973
Annual average
five-year average
(1964-1963)
Five-year average
(1969-1973)
Appendix 10 - 1C.
Hear
1964
1965
1966
1967
1968
1969
1970
1971
1972
1973
Annual average
Five-year average
(1964-1968)
Five-year average
(1969-1973)
Number
of trips
84
068
58
60
493
103
0
0
0
69
133
233
34
Broun
C
100,"»06
4
8,613
41,876
8,278
0
0
0
0
15,917
30,180
1,655
Commercial landings
Number
of trips
2.224
2,016
3,950
3,816
U.2C7
2,417
924
5U5
766
1,52U
2,302
3,368
1,235
Brown
182,152
365,802
448,716
337,903
702,030
120,022
6,484
15,356
1,320
117
217,990
407,321
28,660 .
Catch (Ibs)
Pink
0
0
64
632
3,170
1,102
C
o
0
2,341
731
773
689
White
6,796
20,675
4,744
0
12,274
371
0
0
0
0
4,449
8,898
74
of shrimp (Penaeus spp.)
Catch (Ibs)
Pink
67,403
98,436
135,581
168,856
166,757
83,730
34,497
1,609
55,372
121,584
93,383
127,407
59,358
White
44,208
72,058
10, 124
16,334
33,534
32,020
11,043
186
2,042
542
25,734
35,251
16,217
Total
catch
(Ibs)
6,796
121,081
4,814
9,245
57,320
9,751
0
0
0
2,34 1
22,749
39,451
2,418
from Pensacola
Total
catch
(Ibs)
293,763
536,296
594,421
523,093
902,321
235,772
52,024
17, 151
58,734
122,243
333,582
569,979
97,185
Dollar
value
3,519
49,315
3.638
4,325
37,113
4,901
0
0
0
2,605
10,542
19,582
1,501
Bay from 1964
Dollar
value
113,285
242,874
344,255
325,610
490,044
162,503
41,552
15,968
48,662
150,334
193,509
303,213
83,804
Average
catch/trip
(Ibs)
80.9
258. 7
83.0
154. 1
116.3
94.7
0.0
0.0
0.0
33.9
170.4
169.6
70.2
to 1973.
Average
catch/trip
(Ibs)
132. 1
202.7
150.5
137. 1
214.5
97.5
56.3
31.5
76.7
80.2
144.9
169.2
78.7
14-66
-------
Appendix 10 - 11. Commercial landings or shrimp (Penaeus spp.) from Choctavhatchee Bay from 1964 to 1973.
Number
¥ear of trips
1964
1965
1966
1967
1968
1969
1970
1971
1972
1973
Annual average
live-year average
(1964-1968)
Five-year average
247
267
795
807
611
315
298
259
525
419
454
543
363
Brown
10,843
35,537
49,739
30,966
33,302
452
5,072
1 1,084
61,451
0
23,844
' 32,077
15,612
Catch (Ibs)
Pink
1,434
'1,082
21,226
31,449
24,334
17,387
24,493
9,418
13,600
31,334
17,626
15,905
19,346
White
6,521
20,789
28,921
14,571
8,823
8,44?
16,610
10,395
1,647
o
11,671
15,925
7,418
Total
catch
(Ibs)
18,798
57,408
99,886
76,986
66,459
26,279
46, 175
30,897
76,698
31,834
53, 142
63,937
42,377
Dollar Average
value catch/trip
(Ibs)
9,205 ".,
31,917
83,761
63,247
60,261
21,156
32,994
27,950
106,874
43,256
48,062
49,678
46,446 ,
76. 1
215. C
125. b
95.4
108.8
83.4
154.9
119.3
146. 1
76. C
117. 1
117.7
116.7
(1969-1973)
-------
Appendix 10 - 12. Monthly distribution of fish kills in the Pensacola Day
system from 1970 through 1974.
.p
I
00
Month
January
February
March
April
Hay
June
July
August
September
October
November
December
Total
1970
0
0
0
1
0
3
15
13
19
5
0
0
56
1971
0
Q
A
0
0
2
6
8
20
6
0
0
42
1972
1
0
2
2
U
2
4
6
5
8
0
1
35
1973
0
0
1
o
1
1
2
3
4
2
n
'j
19
1974
0
0 :
0
4
3
3
0
0
4
0
r\
w
0
14
Total
1
0
f .
3
7
8
11
27
35
52
21
0
1
166
-------
Appendix 1C -13. Listing of the time, place and estimated size of the fish kills
in the Pensacola Bay system during 19700
Date
April 21
June 21
June 29
June 29
July 1
July 1
July 3
July 3
July 5-7
July 8
July 9
July 12-13
July 13
July 25,27
July 27
July 27
July 27
July 29
July 30
August 5
August 6
August 7
August 17
August 18-25
August 24
August 25
August 25
August 25
Location
Bayou Chico
Mulat Bayou
Mulatto Bayou
Trout Bayou
Hulat Bayou
Bayou Grande
Bass Hole Cove
Trout Bayou
Mulat Bayou
Bayou Chico
Dead River
Mulat Bayou
Bayou Chico
Trout Bayou
Bass Hole Cove
Mulat Bayou
Racoon Bayou
Bayou Chico
Trout Bayou
Escambia Bay
Indian Bayou
Racoon Bayou
Bayou Chico
Bayou Texar
Trout Bayou
Bayou Chico
Bayou Texar
Mullatto Rayou
Estimated number
of individuals
3.500
250,000
750,000
1,000,000+
2,000
50.
11,000,000+
1,000,000+
11,000,000+
8,000
10,000,000+
10,000+
20*000
1,000,000+
750,000
1,000,000
millions
1,000*
10,000
hundreds
5,000
15,000
1,000+
U,000+
500
5,000+
3,000+
700
-------
in tha
-13(cont). Listing of the time, place and estimated siza of the fish Kills
f:
I
1C -13(cont) . Listing of the time
Pensacola Bay system during 1970.
Eatc
August 26-31
August 27
August 27 J
August 31
September 1
September 2-3
September 2
September 2
September 2-4
September 3
September 3
September 4
September 4
September 3
September 1C-22
September 18
September 18
September 18
September 23
September '24
September 24-25
September 24
September 28
October 12
October 12
October 26-27
October 27
October 27
Location
Escambia Bay
Woodland Bayou
Indian Bayou
Trout Bayou
Hoffman Bayou
Bayou Texar
Escambia Bay
Racoon Bayou
Bayou Grande
Woodland Bayou
Gilmore Bayou
Thompson Bayou
Mulatto Bayou
Trout Bayou
Bayou Texar
Bayou Chico
Escambia Bay
Woodland Bayou
Escambia Bay
Bayou Grande
Escambia Bay
Hoffman Bayou
Mulatto Bayou
Mulat Bayou
Escambia Bay
Bayou Chico
Escambia Bay
Judge's Bayou
Estimated number
of individuals
10,000,000
5
10,000,000
3,000
100
300
millions
thousands
150+
100
50
no estimate
no estimate
500
200 +
20,000
a,ooo
300
45
25+
2,000+
200
1,000,000
200,000
3,000
10,000
3,000
300,000
-------
Appendix 10 - 15. Total.- length frequency of Atlantic bumper,
Chloroscombrus chysurus, from Escambia Bay during 1973-1974.
Hidclass
(mm)
17
22
27
32
27
42
U7
52
57
62
67
72
77
82
87
92
97
Total
Oct. Dec. Feb.
1
54
68
8 1
4 1:
4 1
3 1
8
1
1
152 2 2
Apr. June Aug.
1 2
2
3
8
23
31
19
6
5
13
24
31
U5
22
11
i*
0 1 249
Appendix 10 - 14. Total - length frequency of Gulf menhaden,
Brevoortia patronus, from Sscambii Bay rrow 1973-197*4.
Hidclass
22
27.
32
37
42
47
52
57
62
67
72
77
82
87
92
97
1C2
107
112
117
122
127
132
137
Total
ss Oct.
1
6
22
53
62
38
1C
7
199
Dec. Feb. Apr.,
343
.9 43 81
106 77
21 32
1 16
12
5
9
ft
3
1
5
14
10
3
7
7
3
2 2
2
1
17 175 296
June
14
26
20
36
21
9
17
21
12
14
14
5
1
1
192
Aug.
2
1
3
1
1
1
6
b
y
1
33
14-71
-------
Appendix 10 -
arenari us,
Hidclass
(mm)
27
32
37
U2
t»7
52
57
62
67
72
77
82
87
92
97
102
107
112
117
122
127
132
137
1i*2
1U7
152
157
162
167
172
177
182
187
192
197
202
207
212
217
122
227
232
237
242
2U7
257
282
292
297
327
332
337
Total
16. Total-length freyuency or sand seatrout,
from Escarabia Bay during 1973 - 197U.
Oct. Dec. Feb. Apr. . June
7
1 5
2 23 2
U 173
3 9 17
1 1 27
5 52
1 2 45
11 1 35
19
1 24
5 6
8 6
6 1 5
10 1 5
8 11
7 2 9
1 U 2 6
2 6
9
1 5
2 -2
2
1
2
2
1
... 3
1
1
1
1
3
5
2
3
1
2
2
21 53 6 82 318
Cynosian
Aug.
-'
1
1
1
3 .
6
3
21
U
21
19
21
IB
29
3<*
11
11
4
3
2
2
2
2
2
3
1
3
2
2
2
6
2,
2
2
1
1
1 .
1
1 :
1
1
:r
263
14-72
-------
Appendix 10 - 17. Total - length frequency of spot, Leiostomus
xanthurus, from Escambia Bay during 1973 - 197U.
Midclass
(mm)
17
22
27
32
37
42
1*7
52
57
62
67
72
77
82
87
92
97
102
107
112
117
122
127
132
137
142
147
152
157
162
167
172
177
182
187
192
197
202
207
212
217
222
227
232
237
242
247
252
257
262
267
272
Total
Oct.
1
3 ,
9
21
147
29
10
11
4
1
4
1
1
1
1
1
2
1
148
Dec.
.
5
3
2 .
7
23
43
48
54
39
30
23
18
18
6
15
5
2
3
4
1
2
1
1
1
1
1
356
Feb.
21
82
205
165
64
8
3
1
2
6
13
10
8
13
11
9
3
4
1
1
1
3
2
2
1
1
640
Apr.
2
25
43
15
11
29
48
33
20
9
5
2
2
1
3
5
5
6
5
4
7
4
2
5
3
1
1
2
1
1
1
1
302
June
9
16
17
18
27
47
30
33
39
26
14
11
8
1
2
4
1
1
1
3
5
4
4
1
1
2
2
1
1
1
5
2
5
5
1
3
1
3
3
1
359
Aug.
8
19
42
39
46
50
40
31
18
16
6
6
4
2
3
3
4
6
10
7
4
1
2
1
2
1
1
2
2
4
4
2
1
1
2
3
1
3
2
399
1U-73
-------
Appendix 10 - 18. Total - length frequency of Atlantic croker, Micropo^on
undulatus, £1:00 Escatnbia Bay during 1973 - 1974.
Hidclass
(mm)
12
17
22
27
32
37
42
U7
52
57
62
67
72
77
82
87
92
97
102
107
112
117
122
127
132
137
142
147
152
157
162
167
172
177
Oct.
1
1
1
1
7
U
10
1<4
1U
15
10
7
5
3
Dec.
2
1
1
3
1
3
2
1
2
1
1
2
4
6
7
9
5
7
1
3
Feb.
1
6
19
47
42
42
34
25
23
17
5
3
4
3
7
5
2
2
1
1
2
4
4
6
2
Apr.
1
7
14
29
12
14
16
22
22
23
20
18
11
12
U
2
1
1
1
1
June
1
9
9
14
27
31
34
24
25
12
17
19
10
10
5
6
4
2
Aug.
a
10
14
27
28
38
34
49
31
28
24
23
16
17
13
13
8
13
11
6
5
14-74
-------
Appendix 10 - Ib(cont). Total - length frequency of Atlantic croker,
Kicropogon undulatus, from Escambia Bay during 1973 - 1974.
Bidclass Oct.
(mm)
182 2
187
192
197
2C2 2
207
212 2
217 2
222
227
232
237 2
242
247
252
257
262
267
272
282
267
292
297
202
207
212
217
222
327
247
252
402
Dec.
1
•2
2
3
2
2
1
2
1
2
1
Feb.
2
2
1
4
8
7
4
4
4
2
2
2
1
1
1
1
Apr.
1
5
1
5
6
5
1
4
1
3
1
1
1
2
1
1
2
June
3
3
5
6
13
1C
11
15
6
9
6
4
1
6
1
1
1
1
1
Aug.
3
'3
2
1
3
8
9
•5
6
6
7
7
5
4
.5.
2
3
5
6
7
1
2
2
1
1
1
1
2
Total ' 103 83 362 272 362 520
m-75
-------
Appendix 11-1. B*3iitiiie macroinvertebrate sampliiuj dates and stations
in the Pensacola Bay system.
July - August, 1973
January, 197
April, 197U
August, 1974
EA, EB, SC, 2D, ±~1, GA, GB, GC, GD, IA, IB,
1C, ID, IE, KA, KJ, KC, KD, KE, MA, MB, M3,
HD, HH-\, KMU, ilf'iC, Mi'lD, OA, 03, OC, OD, QA, '
yB, QC, QS, SA, 5B, SC, SD
GA, GB, GD, OA, 03, OD, BWA, 3MB, BHC, SBWA,
E5KB, EBWC, LSD, EBD, PBD, SRA, SRB, SRC
EBEA, EilSB, Eii EC, EHSn, EBEE
ACY, APD, APJN, BWG, j;SG, NES
14-76
-------
Appendix 11-2.—Benthic Macro-fauna from the Pensacola Estuary.
(E = Escambia Bay; A = East and Blackwater Bays; S = Santa
Rosa Sound)
Arthropoda
Insecta
Chironomid (Midge) E
Crustacea
Amphipoda
Ampelisca vadorum EAS
Ampelisca sp. (nr. verrilli) S
Ampelisca abida S
Monoculodes edwardsi EAS
Monoculodes sp. B. EA
Haustorius sp. EAS
Photis pugnator ES
Listriella sp. (nr. barnardi) AS
Rudilemboides nageli S
Grandidierella bonnieroides EAS
Gammarus mucronatus EA
Elasmopus levis S
Melita nitida EA
Batea catharinensis S
Cymadusa compta S
Corophium sp. (nr. acuturn) EA
Paracaprella pusilla S
Isopoda
Edotea sp. EAS
Cyathura sp. AS
Erichsonella filiformis : AS
Tanaidacea
Leptochelia sp. A
Apseudes sp. S
Cumacea
Oxyurostylis smithi EAS
Mysidacea
Mysidopsis biqelowi EAS
Praunus sp. EA
Decapoda
Penaeus setiferus EA
Penaeus aztecus EA .
Trachypeneus constricta S
Palaemonetes puqio EA
Palaemonetes sp. EA
. Hippolyte pleuracantha S
Periclimenes lonqicaudatus S
Family: Processidae . . S
Sicyonia brevirostris ' S
Shrimp sp. A. E
Pinnixa sayana EAS
Pinnixa chaetopterana S
14-77
-------
Callianassa jamaicense louisianensis EA
Pagurus longicarpus S
Micropanope sp. A
Eurypanopeus depressus EA
Neopanope texana texana EAS
Callinectes sapidus EA
Callinectes ornatus EA
Zanthid juveniles ES
Portunid -juveniles E
Unidentified larval crustacean ES
Mollusca
Pelecypoda -
Mysella planulata EA
Nuculana acuta S
Mercenaria campechiensis EAS
Tellina versicolor ES
Tellina sp. B. S
Cyclinella tenuis EAS
Macoma mitchelli EA
Ensis minor EAS
Mactra fraqilis EAS
Mulinia lateralis EA
Polymesoda caroliniana EAS
Rangia cuneata E
Amyqdalum papyria EA
Taqelus plebeius EAS
Anomalocardia cuneimeris E
Brachidontes recurvus EA
Crassostrea virqinica EAS
Brachidontes exustus EAS
Abra aequalis S
Lyonsia hyalina floridana S
Crassinella lunata S
Anadara transversa S
Martesia cuneiformis A
Martesia smithi A
Lucina multilineata S
Lucina amiantus S
Laevicardium mortoni S
Dinocardium robustrum S
Ma'coma tenta . S
Cuminqia antillarum S
Musculus lateralis S
Gastropoda
Nassarius vibex ES
Crepidula maculosa S
Crepidula fornicata S
Crepidula plana EA
Retusa canaliculata EAS
Olivella pusilla S
Kurtziella limonitella . S
Natica pusilla S
Anachis simplicata S
14-78
-------
Mitrella lunata S
Granulina(Bullata) ovuliformis S
Thais haemastoma S
Thais sp. B. S
Manqelia stellata S
Urosalpinx cinera S
Eupleura sulcidentata S
Nudibranchs EAS
Prunum apicinum S
Turbonilla conradi S
Odostomia sp. A. EA
Odostomia sp. B. EA
Bulla occidentalis ES
Epitonium rupicola ES
Polinices duplicata EA
Neritina reclivata EA
Polychaetes
Polynoidae
Ant.inoiella sarsi S
Eunoe nodpsa S
Harmothoe lunulata S
Sigalionidae
Sthenelais boa EAS
Amphinomidae
Amphinome rostrata S
Phy11odoci dae
Anaitides maculata ES
Eteone heteropoda ES
Nereiphyla fraqilis . S
Phyllodoce (Genetyllis) castanea S
Pilargidae
. Ancistrosyllis hamata . .•, ; EA
Cabira incerta S
Parandalia fauveli EA
Sigambra bassi EA
Hesionidae
Gyptis capensis EAS
Podarke obscura E
Nereidae
Laeonereis culveri EA
Leptonereis laeyis S
Neanthes succjnea EAS
Nereis pelagica occidentalis S
Platynereis dumerili S
Nephtyidae
Aglaophamus inermis S
Glyceridae
Glycera oxycephala AS
Goniadidae
Glycinde solitaria EA
Eunicidae
Marphysa sanguinea E
Onuphidae
14-79
-------
Diopatra c. cuprea EAS
Lumbrineridae
Ninoe nigripes gracilis E
Lumbrineris pallida S
Arabellidae
Drilonereis cylindrica EA
Spionidae
Microspio pigmentata : S
Paraprionospio pinnata EAS
Polydora caeca '....-.. • EAS
Polydora socialis S
Polydora websteri EA
Prionospio pygmaea S
Scolelepis squamata EAS
Spiophanes bombyx S
Spio pettiboneae S
Magelonidae
Magelona alleni S
Poecilochaetidae
Poecilochaetus johnsoni S
Cirratulidae
Cirratulus cirratus S
Cossura longocirrata S
Orbiniidae
Haploscoloplos fragilis EAS
Paraonidae
Aricidea suecica S
Opheliidae
Polyophthalmus pictus S
Trayisia forbesii S
Capitellidae
Heteromastus filiformis EAS
Maldanidae
Axiothella mucosa S
Gravierella sp. , A
Isocirrias lonqiceps A
Sternaspidae
Sternaspis fossor S
Pectinariidae
Pectenaria gouldii EAS
Ampharetidae
Amphicteis gunneri floridus EA
Melinna maculata . . S
Terebellidae
Lanice conchileqa S
Pista cristat.a , S
Terebellides stroemi S
Sabellidae
Chone duneri S
Potamilla reniformis S
Serpulidae
Hydroides uncinata S
Hirudinia
14-80
-------
Species E
Hemichordate
Species EA
Nemertean
Species Cerebratulus lacteus (Leidy) EAS
Phoronida
Phoronis architecta S
Platyhelminthes
Species EAS
Echinoderms
Ophiuroids
Amphioplus coniortodes S
Amphibdia at.ru S
Holothuroids
Synaptula hydriformis EAS
Pentatnera pulcherrima S
Echinoid , '
Lyttiecinus var iegatus S
Coelenterates
Hydroid forms S
Medusoid forms S
Anemones S
Chordates
Branchiostoma caribaeum S
Vertebrates
Gobiosoma sp, A
Trinectes maculatus ES
Microdesmus lonqipinnis E
Microqobius qulosus E
Gobioides sp; E
Myrophis puntatus E
Gobiosoma bosci E
Pipefish S
v
Priapulida
Species S
14-81
-------
appendix 11 - 3. Shannon - Heaver (H1) diversity index values for all benthic macro-fauna
stations in the Pensacola Bay system.
Station
ACY
APD
APDN
EBA
EBB
EBC
EBG
£A
EB
EBD
EBEA
EBEB
EBEC
EBED
EBEE
EBHA
EBHB
EBEC
EC
ED
EE
ESD
ESG
GA
GA2
GB
GB2
GC
GC2
GD
IA
IB
1C
ID
IE
KA
KB
KC
KP
KE
HA
HB
BC
HD
HHA
HHB
BBC
HMD
NES
OA
OAD2
OA2
OB
OB 2
OC
OC2
OD
EBD
CA
CB
QC
CE
SA
SB
SC
SD
SDP
NHS
SRA
SRB
SRC
Total Species/Station
11
9
7
18
21
21
24
2
4
10
1C
13
25
8
26
19
23
12
9
12
12
8
23
7
13
6
22
8
16
11
4
2
3
1 1
13
5
3
17
19
13
5
2
1 1
13
19
21
18
22
23
4
13
16
9
17
12
21
15
12
5
3
18
1 1
4
3
9
10
15
25
67
68
83
Total Indi viduals/o
239.8
167.7
340.6 .
286.2
348.7
412.9
704.8
5.2
11.7
82.0
55.9
150.6
4271.7
1595.7
1527.0
239.4
244.3
788.7
144.4
314.9
593.5
52.0
924.2
160.0
264.1
83.3
822.3
140.5
1916.2
90.3
10.4
3.9
9.1
239.4
1553.2
36.4
42.9
85.9
171.7
203.2
20.8
9. 1
571.2
1114.5
361.7
651.9
135.3
193.6
774.2
63.8
200.3
197.3
37.7
264. 1
104. 1
211.3
593.9
154. '4
5«,6
62.5
257.6
67.7
9.1
9.1
51. 3
61.1
145.7
77ii. 1
1781 .4
1937.5
1525.0
Diversity (H1)
1.634
1.732
0.831
2.439 '
2.483
2.111
1.813
0.562
1. 149
1. 787
1.748
1.722
0.955
C.219
1.316
2.452
2.516
0.504
1. 393
1. 486
1.275
1.724
1.933
0.779
2.056
1.263
1.858
1.233
1.206
1.871
1.255
C.637
0.796
1.333
1.507
1.251
1.680
2.250
2.269
1.931
1.160
0.410
1.259
1.075
1.879
1.969
2.404
2.357
1.347
1. 134
2.313
2. 147
1.868
2. 196
1.783
2.357
1.634
1.760
0.833
0.830
2.323
2.123
1.277
0.956
1.731
1.600
2.389
1.376
3.005
2.892
3.012
Biomass (gr./o2 )
0.48 . .
0.19 ••"
. 0.. 18
0.92
0.25
0.13
5.16
0.01
0.03
0.06
. . ..0.19
0.02
4.64
0.17
0.28
1. 17
0.13
0.12
0. 16
0.30
0.34
0.03
5.45
0.04
0.23
0.12
0.63
0.25
0.34
1.62
0.04
0.01
0.11
1.84
3.05
0.02
0.27
0.12
0.25
0.09
0.02
0.32
0.46
0.85
228. 11
107.10
2.40
0.09
0.43
0.36
1.47
3.38
0.07
8: if
0.08
0.25
0.12
0.07
0.03
0.98
0.03
0.05
0.01
0.14
0.05
- 0. 15
0.43
1.85
2.94
0.61
------- |