Updated Summary Of Status And Trends In indicators Of Nutrient Enrichment In The Gulf Of Mexico


o
United States
Environmental Protection
Agency
                           Off ice Of Water
                           Gulf Of Mexico Program
                           Stennis Space Center, MS 39529
EPA 800-R-92-004
September 1992
An Updated Summary Of
Status And Trends In indicators
Of Nutrient Enrichment In The
Gulf Of Mexico
                             Recycled/Recyclable
                             Printed on paper that contains
                             at least 50% recycled liber

-------
             For sale by the U.S. Government Printing Office
Superintendent of Documents, Mail Stop: SSOP, Washington, DC 20402-9328
                    ISBN 0-16-036279-2

-------
AN UPDATED SUMMARY OF STATUS AND TRENDS

   IN INDICATORS OF NUTRIENT ENRICHMENT

            IN THE GULF OF MEXICO




                       by

                Nancy N. Rabalais
      Louisiana Universities Marine Consortium
                Chauvin,  LA 70344
                   prepared for
              Gulf of Mexico Program
            Technical Steering Committee
          Nutrient Enrichment Subcommittee
           Stennis Space Center, MS  39529
          Publication  No.  EPA/800-R-92-004

         U.S. Environmental Protection Agency
                   Office of Water
               Gulf of Mexico Program
                   September  1992

-------

-------
                                 MEMBERS
                     Nutrient Enrichment Subcommittee
                          Gulf of Mexico Program

Mr. L. Pete Heard, Federal Co-Chair, U.S. Dept. of Agriculture, Soil Conservation
Service, Jackson, Mississippi
Mr. Dugan S. Sabins, State Co-Chair, Louisiana Dept. of Environmental Quality, Baton
Rouge, Louisiana
Ms. Jan R. Boydstun, Louisiana Dept. of Environmental Quality, Baton Rouge, Louisiana

Dr. C. Fred Bryan, Lousiana State University, Baton Rouge, Louisiana

Mr. Charles Demas, U.S. Geological Survey, Baton Rouge, Louisiana

Mr. Mike J. Dowgiallo, National Oceanic and Atmospheric Administration, Coastal Ocean
Program Office, Washington, D.C.
Mr. Daniel Farrow, National Oceanic and Atmospheric Administration, National Ocean
Service, Rockville, Maryland
Dr. David A. Flemer, U.S. Environmental Protection Agency, Environmental Research
Laboratory, Gulf Breeze, Florida
 Mr. Tim Forester, Alabama Dept. of Environmental Management, Montgomery, Alabama

 Mr. Douglas J. Prague, Gulf Coast Fisheries Coordination Office, Ocean Springs,
 Mississippi (Johnny French, alternate)
 Dr. Eddie Funderberg, Louisiana State University Extension Service, Baton Rouge,
 Louisiana
 Mr. Brian Grantham, Citizen's Advisory Committee, Foley, Alabama (James Fogarty,
 alternate)
 Dr. Churchill Grimes, National Oceanic and Atmospheric Administration, National Marine
 Fisheries Service, Panama City, Florida
 Mr.  Vince Guillory, Louisiana Department of Wildlife and Fisheries, Bourg, Louisiana

 Dr. Peter J. Kuch, U.S. Environmental Protection Agency, Washington, D.C.

 Mr.  Ira H. Linville, U.S. Environmental Protection Agency, Region 4, Atlanta, Georgia

 Dr.  Stephen R. Lovejoy, Purdue University, West Lafayette, Indiana
  Gale Martin, Mississippi Soil and Water Conservation Commission, Jackson, Mississippi
  (Mark Gilber, alternate)
  Dr.  David Moffitt, U.S. Dept. of Agriculture, Soil Conservation Service, Fort Worth,
  Texas
                                         111

-------
             : Moore' Texas State Soil and Water Conservation Board, Temple, Texas
 Mr. James Patek, Lower Colorado River Authority, Austin, Texas (Charles Dvorskv
 alternate)                                                                 J '
             Ss]^n>iU'S' Amiy COIPS °f Engineers' Waterways Experiment Station,
 Mr. Dale Rapin, U.S. DepL of Agriculture, Forest Service, Atlanta, Georgia


 Ms. Stephanie Sanzone, U.S. Environmental Protection Agency, Washington, D.C.


 Dr. Alan M. Shffler, Center for Marine Science, University of Southern Mississippi,
 Stenms Space Center, Mississippi


 Dr. Bob Thompson, Jr., Potash & Phosphate Institute, Starkville, Mississippi


          " Whitledge' The University of Texas, Marine Science Institute, Port Aransas,
Dr. John W. Day, Jr., advisor, Louisiana State University, Baton Rouge, Louisiana


Dr. Nancy N. Rabalais, advisor, Louisiana Universities Marine Consortium, Chauvin,
                                     IV

-------
                           ACKNOWLEDGEMENTS















                     have teen incorporated into the final version.
on
                                  DISCLAIMER






STAmfl11992  Given Ae dynamic nature of estuaries, the complex interactions of nature and





 coastal waters.




 endorsement or recommendation for use.
                                CITATION

            1992  An Updated Summary of Status and Trends in Indicators of Nutrient
            the Gulf o 'Mexico. Report to Gulf of Mexico Program, Nument Enrichment
    oee  PuSSorTNo. EPA/800-R-92-004, U.S. Environmental Pi'Otection Agency,
OfficeTwater Gulf of Mexico Program, Stennis Space Center, Mississippi, 421 p.
          N N
              '

-------

-------
                          TABLE OF CONTENTS
                                                                            Page
Executive Summary	•	**

Introduction	,	;•	1

    Impetus for Study	\
    Importance  of  Gulf  Coastal  Waters	^
    Expanded  Information  Bases	•	-4

Perspectives on Nutrient Enrichment and Eutrophication	12

    Definitions	•	\\
    How Much (of What) Is Too Much?	•	-.-J^
    Anthropogenic Factors	•	-	-]*
    Consequences of Nutrient Enrichment	*/
       Altered Trophic Structure	*£
       Oxygen Depletion	27
       Habitat Alteration	~f
    Reversal of Eutrophication	•	^°
    Management Options	•*'
                                                                    ,00
Data  Acquisition	30

    Literature Searches	^
    Data Sources	3y

Estuarine and Coastal Area Units	44

Status Matrix	•	.••••	53

Updated Summary of Status and Trends in
    Indicators of Nutrient Enrichment	63

    Florida	•
    Alabama	:	•
    Mississippi
    Louisiana	•	•
    Texas	•

Appendix A.  Terms and Conversions	260

Appendix B.  Data Bases	263

Appendix C.  Information Resources	-	266

Appendix D.  Bibliographies	272
                                      Vll

-------

-------
                             EXECUTIVE SUMMARY
The Gulf of Mexico region ranks first «»^35      ouge Gu? of
estuarine drainage area an Jm to^wate r«rf ^^^^^J^pected togbe the second
Mexico region is not as densely settled as ^r U .^ °o *mi            F        M    Qf ^
fastest growing coastal region in *e nation (CuUit °* « a£>^'  result 'from human-induced
environmental quality Problems aff ecting Gu^°f ^S iea  These include industrial






particular importance to the Gulf.









 depletion events.

















  all Gulf of Mexico coastal and estuarine areas (presented in Table 1 1).
                                         IX

-------
  various authors, and their results were presented in the review. Still, a vast amount of unanalvzed
  data exists, and some sets may be worthy of a more detailed analysis.        no real data but some indicators that the estuary, or a sub-unit
        estuary, may be on the brink of water quality problems.                      m°-unit

   N - No, there is not a problem.

-------
  7 - There are insufficient data to make a determination, but tailed dam may support a tentative
  inclusion of Yes, No or Potential.
Actuaries in the matrix
these is given in the fi^
"Potential." There are a
conclusions across the Gulf of
short lists, and no state is
enrichment should receive
                           Mexico  The  Yes
single page.  The reader «
                              b^^^^
                                                     ^^ of sufficient data to draw
                                                  potential" categories, however, are not
                                                  ™       p^ems related to nutrient
                                                   SSL in the "?, but No" and "No" lists
                                                   t be complacent about these estuanes




                                   to consmer n                ^ develop man      „,

                                                             problems or causauve  or
contributing factors
                                         XI

-------
Xll

-------
i
-8

•
bo
c3 I

rt O

•a -a

SB*
_t) O

5 *o

1-9
CA -

-------
-------
INTRODUCTION
Impetus for Study

environments, during recent decades me umi nas & for detailed ^

environmental quality. Issues of P^^^f^e because of effects of hypoxia on fisheries
Nutrient enrichment was identified as an yS^_15Sl^S<5SSy have toxic effects on

Producers, and changes in energy .^o^eafp ™
Subcommittee of the Technical Steen^Sfof Sente enterkig the Gulf of Mexico and its
and data base reviews on * Qs?£c^ enSent on the Gulf ecosystem.
tributaries (Purdue Univ., 1991) and 2^etJ"^1f"S tends of Gulf coastal environments with

Adriatic Sea, Stachowitsch, 1984; ^f^^^ T988; North Sea and

1985) Eu^ophication may be manifested in additional ways as detailed later.
-------
identified the following categories into which several Gulf of Mexico estuarine and coastal

areas
Priority Hypoxia Areas - areas that have a demonstrated hypoxia and/or eutrophication problem.

- Perdido Bay
-Tampa Bay
- Mobile Bay
- Louisiana inner continental shelf
- Lake Pontehartrain

Potential Hypoxia Areas - found to be borderline cases where no strong hypoxia was noted but the
conditions for a senous problem occurring were judged to be possible in thefoture.

- Pensacola and Escambia Bays
- Mississippi Sound
- Galveston Bay
- Calcasieu estuary

Areas with Lack of Data but with Potential Dissolved Oxygen Problems.
not identified previously in the 1985 assessments as areas of concern. estuarine basins

Importance of Gulf Coastal Waters

A recent NOAA report (1990a) compiled basic data from the National Estuarine Inventorv fiwn

fSKT y ^ TC (3)' ?Ulf ? Mexico' ** Pacific «*««»• Excerptffrom tMs repoS7NS
-------
Table
1. Summary of selected characteristics of me Nation's estuaries (from NOAA, 1990a).
/£* / -
374 24 ' 41 <1 0 0

14 3 3U -
00 16 4 37 0
5 14 2
436 84 83 45 37 20
250a

500 a

169

648

337
1,904

Note:. All values are rounded. Rank indicates rank among all commercial fisheries in region.
a Values are estimated. .
b Does not include Alaska fisheries values.

Source- NOAA, 1 990f, and unpublished 1 989 statistics .
-------
Although the Gulf of Mexico region is not as densely settled as other regions, it is expected to be
the second fastest growing coastal region in the nation (Culliton et al, 1990- NOAA 1990af

?4lTLtw?en^ld9fi908a0' ^ST^ **? "* m°re *»* 3° percent' «* SeSdS iow by
and2010. Maor ur
4twenl9fi0a ' by
Hntlnn S T,i? and2010. Major urban areas surround port cities such as New Orleans
Houston, and Tampa, and dense populations surround Sarasota Bay, Galveston Bay and Tamoa
Bay. Western Honda has been and will continue to be the most rapidly gWmg aSa' SfceoS?

^rT&rn11 TSff,^ l° 'T ^ by m£6 *** !'5 a£SSm °ver thenlxt twodecades cSffiS
fnrS^i hv}; ! i S-i?e next most raPldly growing state; its coastal population is expected to
increase by over 1.1 million persons during this same period (Culliton et al, 1990).
me 5"vironme"tal Quality problems affecting Gulf coast estuaries result from natural
Thse i rr.'S^ Pi vUtl0n bo* w«hin and uP<"ream of the estuarine drainage ^
«„£ i i? industnal facilities, municipal wastewater treatment plants, power plants
agnculturally applied nutoents and pesticides, and other agricultural waste runoff The Gulf of

V^a^^&Fu** nUmbCn °f *£? «»«« -W8 the regions f
u > ^ rePOIt (see Table 3), as well as 436 power plants (NOAA 1990
the northern Gulf of Mexico is the recipient of the flow of a niSi rim^to
and Atchafalaya Rivers which drains 40 % of the U.S. and ^a^SS
mflow from this nver dwarfs the input from any other Gulfcoast (90 % of GuK Mexico
freshwater inflow) or Atlantic coast system (Figure 3). Mexico
iSfF?011 water qu^ty changes in the Mississippi River have been documented (Walsh et al
1981; Turner and Rabalais, 1991a) (Figure 4). Loadings of the MississSpT River SSe -n
CTurner and Rabalais 1991a) and for the entire Gulf coast (Table 4) (SiS 1987)Sv^Sen

system m the contribution of nutrients to the Gulf coastal systems Mississippi River

The characteristicaUy low tidal energy of the Gulf of Mexico region, high runoff of an aperiodic
nature (bringing nutrients and organic material and resulting in denlity sSificationrhSh
biological Productivity, and warm temperatures places many of the coasti w£S ^bodies 4nfe
bnnk, such that additional organic inputs or enhanced isolation of bottom ^ers?rom
reoxygenation may quickly result in depletion of dissolved oxygen.

Expanded Information Bases
-------
a. Estuarine Drainage Area
b. Estuarine Water Surface Area
•CO
01
CB

W
111
0 2 4 6 8 10 «
Area (thousand square miles)

c. Total Wetlands
to
3
is
0 500 1000 1500 2000 2500
Area (square miles)

d. Urban and Agricultural Land Use
i
UJ
1000 1500 2000 2500 3000 3500
40
EO
80
Area (square miles)
Percentage of EDA

Urban n Agricultural
Notes: Sub-estuaries are not shown separately. All values are in Appendix B. N/D-nodata.
Figure 1. Selected characteristics of Gulf of Mexico estuaries (from NOAA, 1990a). Codes ,0
estuaries listed in Table 3.
-------
03
I
8
0>
0
I
o
O
o

•s
CO

en
43
-------
1800
1900
2000
Year
Figure 2 The drainage basin of the Mississippi River and the annual discharge at Vicksburg,
Mississippi (from Turner and Rabalais, 1991a).
Figure 3. Average annual runoff to ocean in terms of km3/ linear km of coast (from Emery and
Uchupi, 1972).
-------
200
CO
o>
a.
100
CD
0

^s 250

"ro 200

3" 150

*? 100

ra
£ 50

12
8
to

5 4
(p
0
19OO
f
1950
Year
2000
Figure 4. Changes in nitrate silicate and total phosphorus in the lower Mississippi River at St
FrancisviUe (closed.circles) and New Orleans (open circles). Bars are + IsSd
error of the annual average of monthly means (from Turner and RabSaTs 1991a)
-------
180
Table 4. Changes in

delivery of nutrients to coastal areas (modified from Smith el al., 1987).
Change in Load,
1974-1981
Region
Northeast Atlantic Coast
Long Island Sound/New York Bight
Chesapeake Bay
Southeast Atlantic Coast
Albemarle/Pamlico Sound
Gulf Coast
Great Lakes
Pacific Northwest
California
Total
Nitrate
(%)
32
26
29
20
28
46
36
6
-5
Total
Phosphorus
(%)
-20
-1
-0.5
12
0
55
-7
34
-5
-------
oo
-s -s
ss

-
la
D -C

O
II

ft
.S-a
5
w 5-
s.9
10
-------
A?Ss of the TJS Am-cultural Pesticide Use in Estuarine Drainage Areas, draft data summaries on
£H? SourL Discharges irTCoastal Areas of Alabama and Mississippi, the National Estuanne
Point Sourc^iscnarges in v,odiiSs have been inflated in each of these areas for the improved understanding of the status of
the estuary and the processes important in maintaining estuanne health.

All these activities have resulted in expanded data sets for many Gulf of Mexico estuaries and
cSstidlrSs^TOased research and monitoring activities, and several completed studies on
^dS^bSL. Several national programs have focused on the causes and effects of
nutrient enrichment. These include:

- the NOAA/EPA Team on Near Coastal Waters Strategic Assessment of Near Coastal
Waters iftL Ration of Susceptibility and Status of Gulf of Mexico Estuanes to Nutnent
Discharges (NOAA/EPA Team on Near Coastal Waters, 1990),

- the NOAA Coastal Ocean Program Nutrient Enhanced p/stal Ocean Productivity
Droeram which is focusing on the influence of the Mississippi and Atchafalaya Rivers on the
?oJafen?Gdf of Mexico [NECOP Mississippi-Atchafalaya River (MAR) Implementation Plan],

- the NOAA National Ocean Pollution Program Office studies of long-term ttends in water
quality in selected estuaries and its relationship to fishery resources (e.g., Stanley, 1992),

- the NOAA Strategic Environmental Assessments Division National Estuarine
Eutrophication Project (Hinga et al., 1991), and

- NOAA's Coastal Ocean Program Resource Information Delivery component (COP/RID)
which is scheduled to fund, among other synthetic efforts;, aComparative review of tihe problems
stemming from nutrient over-enrichment and harmful algal blooms in U.S. coastal waters.

In summary many Federal and State programs are approaching the study of nutrient enrichment,
ts efS?and mechanisms for control. This report represents one of ™y<*j^£°«* to
synthesize available information on the indicators of nutnent ennchment in the Gulf of Mexico.
11
-------
PERSPECTIVES ON NUTRIENT ENRICHMENT AND EUTROPHICATION

Definitions

The words, "nutrient enrichment," "nutrient over-enrichment" and "eutrophication," are often used
interchangeably but often without similarly intended meanings. For this review the "over-" prefix
will be dropped from the word enrichment, since enrich already means "to increase the proportion
of a valuable or desirable ingredient. v/pviuuu

There has been considerable discussion and usually lack of agreement on the definition of
eutrophication. In many instances it is used interchangeably with "nutrient enrichment " Others
however, chose to limit the meaning of "eutrophication" to a condition resulting from excessive
nutrient loading which stimulates primary production and results in extremely rapid growth and
large standing stocks of phytoplankton. An example of these inconsistencies was obvious in the
m?neL05^/SCiQQnnSM 'SV6061" wo^sh5>Ps f°r the National Estuarine Eutrophication Project
(Hinga et al., 1991). No definition evolved from this group; and, as noted by Garber and Pennock
in the proceedings of the workshop, no clear definition of "eutrophication" evolved from a
S? !?nl- A<:ademy of Science (NAS) symposium on eutrophication in 1967 (NAS, 1969)
Eufrophication" as defined in the NAS (1969) proceedings mearit "a natural or artificial addition of
nutrients to bodies of water and to the effects of added nutrients." This is the definition that will be
loiiowea tor this report.
m ^ ChangC ™ a P°sitive direction. The measurement of this increase thus
requires a data base with adequate temporal resolution. These data are sorely needed or the
analyses of existing data bases are sorely needed, because the examples in the literature wh ch
S™ /°ng;-term °?anges m ?,Utdent supply m limited- NotaWe examples are given™
subsequent sections. Also, not all nutrient increases are detrimental. An adequate supply of
SJSSJ," * J? l6^? -° SUpp0rt food webs' and intentional nutrient additions have been
tw^n J° mcrease fish stodcs in some experimental systems. It is generally perceived, however
that aquatic systems are limited in their assimilative capacities and that the effects of eutrophication
are deleterious.
t0JOCuS °n the i/ldicato?'s of nutrient enrichment. Experimentally or empirically
AK h ? 1PZ *™ C^gGS m "Utrients "^ biolo&cai and/or chemical effects provide
the solid basis for determining how nutrient enrichment effects estuarine and coastal systems
2fc ela?9nshlPs "".not as straightforward, and complex interactions obscure direct lines of
evidence. Many examples are given of the expression of eutrophication effects.

The nutrient inputs and concentrations within an estuarine body or coastal area originate from
sources outside the system (allochthonous) and from within the system (auSthofous) ft£
largely accepted that increased allochthonous loadings of nutrients can lead to TncreasS I SrinwJ
production (Nixon « a/ 1986; Oviatt etal., 1986b; Malone, 1987). The quantification SPSS
relationships and paths of nutrient uptake and regeneration are not, however, adequa ely known
Several studies suggest that recycled nutrients account for a greater percentage of the amS
nutrient concentration than the "new" load entering the system each year (Boynton a al 19S2-
1982J Fher a"d DoAe'.1987)- Chough autochthonous loadings i^ ^essentially
theirC°ntribUti0nS 1S n -derstanlng the effect
th| Purimary ap^opogenic nutrient inputs of concern in coastal
' . considered the most important nutrient in marine and coastal waters-
phosphorus, in freshwater systems. Both nitrogen and phosphorus are important in estuSeT
depending on the season total nutrient loadings, and various physical and chemical condSs'
Silica availability, an indirect consequence of phosphorus loadiig, may strongly influence the
12
-------
occurrence ofdeleteriouse^^
vary down the stem of the estuary,*^ e*'s^u™Sents such as carbon, trace metals,
concentrations will also change. °*°r ^f^^ Stors may also be important in speoflc
(,*., *£ - > afco control
primary production.

How Much (of What) Is Too Much?

Wa,ero«aH,ydaTe.Tr^^
measures are total Kjeldahl j^^Y/j^ "™T which typicaUy transforms organic N to NH3-
includes all forms of N quantifi ^^^^ Sc N TKNcan be for either dissolved or
N. Thus, TKNis the sum of total NH3-N ana organic de ammoma
samples. DIN normally includes mttate P^J^^^ constituent is usually
.

e iSS
uM and ug-at/1 are also common.
Most phosphorus is either dissolved as
suspended in association ^^[^S^ tyin units of mgA, and may represent
Phosphorus may be reported as J^P^^i^gS dissolved phosphorus is in the form
either the dissolved or parttculate fraction or both. .Wg™^ inorganic nitrogen. Silicate, minus

ysts
measured by experimental incorporation of ^^^^^^^oeaia^ of these rates
C/m3/d, or an annual "J^^^J^S^^SKfh^ is usually determined
based on fluorescence and ^S^ m£a^^
fluorometricallyorspectrpphotomemcanyformem^^ water column

pressure liquid chromatography (HPLC).

The concen^ation of dissolved oxygen £ .bottom wj« '^Jejojjja^^
technique to determine die a^^^^^^SSd throughout this report xviU
provides concentrations in units of *&^*^ Bottom water dissolved concentrations of
be mgA. [For conversion, 1 ing/U - « PgJ ^°-^s approSg zero or anoxia are difficult to
<2 mg/1 are considered ^^^.^^S^^tS&aas. but concentrations below
measure (depending on the method) > especially nem ^^s^d column dissolved oxygen

S
estuary (see section on Oxygen Depletion)

Tumidity is often a *"£$%£%%
13
-------
Anthropogenic Factors
14
-------
The Gulf of Mexico region has more point sources of pollution (over 3,700) than any other region
in the U.S. (NOAA, 1990a). Industrial activities are concentrated along the coast and major rivers,
oil and gas production and development activity is high, and the petrochemical industry is large.
Major shipping centers are found in each of the Gulf states. Other industrial activities include
wood and pulping operations and fertilizer mining and processing. With increased demands for
industrialization, urban land use and residential areas, natural resources are impinged upon as
dredge and fill activities alter the landscape.

Agriculture activity accounts for 31 % of the land use in the Gulf of Mexico region (NOAA, 1990a;
see Figure 1). With this land use comes the application of fertilizers. In 1982, application of
fertilizer to agricultural lands in the Gulf of Mexico estuarine drainage areas was the highest among
the regions of the U.S. The greatest applications within the Gulf of Mexico were in the Galveston
Bay, Matagorda Bay, and Lower Laguna Madre estuaries. Fertilizer runoff is a significant nutrient
source [>25 % of the total inputs of either phosphorus or nitrogen in South Ten Thousand Islands,
North Ten Thousand Island, Charlotte Harbor, Suwannee River, Lower Laguna Madre,
Apalachee, Choctawhatchee, Pensacola, Perdido, Matagorda, San Antonio, Aransas and Corpus
Christi Bays (NOAA, 1990a)]. Fertilizer application within the U.S. has increased steadily since
the 1940s, although there has been a leveling-off in recent years (Figure 7). The implications of
these nutrient contributions to rivers, estuarine systems, and coastal waters is a matter for concern
and long-term changes in coastal systems have been documented worldwide where major rivers
deliver nutrient enriched waters to coastal seas (Nehring, 1984; Fransz and Verhagen, 1985;
Rosenberg, 1985; Lancelot et al., 1987; Andersson and Rydberg, 1988; Wulff and Rahm, 1988;
Turner and Rabalais, 199la). (See section G-9.)

An example of water quality changes in the U.S. is represented by the nitrate and silicate
concentrations in the Mississippi River, which drains 40 % of the U.S. and is the dominant
freshwater inflow source into the Gulf of Mexico (Figures 2 and 3). The average annual nitrate-
nitrogen concentration doubled after 1950, and the silicate concentration was reduced by half
(Figure 4) (Turner and Rabalais, 1991a). The average annual nitrate concentration is positively
related to nitrogen fertilizer use; the annual silicate concentration in the river is inversely related to
phosphorus fertilizer use, presumably because phosphorus stimulates diatom growth and diatom
tests sink to lake and reservoir sediments, thus storing silica that would otherwise go into the water
column and downstream (Figure 8) (Turner and Rabalais, 1991a).

The global nitrogen budget for new nitrogen sources from fertilizer applications exceeds by far
contributions from the combustion of fossil fuels (Turner, 1991). World fertilizer consumption
has been increasing since World War n when industrial processes evolved for fixing atmospheric
nitrogen into fertilizers, and mining of P-rich mineral deposits expanded rapidly (Figure 9) (Turner
and Rabalais, 199 Ib). Additional nutrients are released through de-vegetation, farming, soil
erosion, weathering, etc. A linear relationship between fertilizer application and water quality is
not always expected, because of the interaction of various ecosystem components, and subsequent
adjustments by microorganisms, in particular (see e.g., Aber et al., 1989)

Industrially-produced nitrogen is recycled through the atmosphere, and into water supplies. The
worldwide rise in the concentration of nitrogen in rainfall and snowfall is symptomatic of the extent
of these human activities on the environment. The importance of atmospheric inputs of essential
nutrients has only recently been understood, but is clearly important and changing (e.g., Morris,
1991). For example, the inputs from precipitation and river runoff are equal in Chesapeake Bay
(Correll, 1981; Correll and Ford, 1982), an estuarine system often described as eutrophic. The
nitrogen concentration in precipitation has recently increased in the eastern and upper midwest of
the U.S. and in Europe (e.g., Likens and Borman, 1979; Brimblecome and Pitman, 1980; Morris,
1991). These changes are so pervasive as to appear in snowfall in the Antarctic (Mayewski and
Legrand, 1990). Turner (1991) suggests that the precursor for these polar snow deposits could
also be from recently deposited nitrate in fertilizers rather than from fossil fuel sources, as
15
-------
C
O
12
8
4
• N

oP
0-

1990
1920
1940

Year
1960
1980
Figure 7. Nitrogen (as N) and phosphorus (as P2O5 equivalent) fertilizer use this century in the

U.S. up to 1987-1988 (from Turner and Rabalais, 1991a).
C 120
v.
j->
53

3- 80

2
"ro 40
Y=0.0078x-1.65

R2=0.74
4000 8000 12000

N Fertilizer (1000 mt/yr)
-j 200
a

cn ,

n.
>w^

*P
0> 100
4->
co
O

CO
Y=-0.021X+2I2

R2=0.79
3OOO 600O

P Fertilizer (1 000 mt/yr)
Figure 8. The relationship between fertilizer use and water quality at St. Francisville, Louisiana.

Fertilizer forms as in Figure 7, data for nitrogen fertilizer use from 1960 to 1985, data

for phosphorus fertilizer use from 1950 to 1987 (from Turner and Rabalais, 1991a).
16
-------
40
g20
Nitrogen

• Africa
ON. America
• Asia
vEurope
T Oceania
Phosphorus
1970
1990 1950
1970
1990
Figure 9. World and U.S. nitrogen and phosphorus fertilizer consumption since 1950 (Turner and
Rabalais, 1991b).

suggested by Mayewski and Legrand (1990). Most landscapes have been subjected to
significantly increased nitrogen loading this century, and the increase in fertilizer use exceeds the
fossil fuel consumption rate (Turner, 1991). Atmospheric sources of NH4+ may also be generated
from livestock wastes in areas of intensive stockbreeding (Morris, 1991). In addition, the
viewpoint of eutrophication as a local and perhaps point-source problem manageable on a regional
scale is changing to a phenomenon that is the cumulative result of many small actions throughout
the world, and whose scale of management is vastly expanded and more expensive.

Consequences of Nutrient Enrichment

The potential and observed consequences of nutrient enrichment for coastal habitats are often
documented in bold newsprint that announces a major fish kill, dead zones, red tides, catastrophic
decline of seagrass beds, or reduced fisheries landings. Few such reports, however, have
specifically linked increases in nutrient supplies to subsequent eutrophication, low dissolved
oxygen levels, algal blooms, long-term changes in community structure, or altered habitat
biodiversity. Many anthropogenic factors, as mentioned above and not to exclude overfishing,
dredging and filling, industrial pollutants, and population expansion, can contribute to reduction in
coastal water quality and changes in natural resources. Climatic factors and long-term global
changes may also be implicated in subtle changes in resources.

There are several major categories of ways that nutrient enrichment may affect coastal habitats:
through changes in food source quantity, food source quality, habitat suitability, alterations of
predator-prey relationships, catastrophic events, ecosystem predictability, and intraspecific
competition. A National Estuarine Eutrophication Project Workshop was convened in January
1990 to specify the potential range of eutrophication effects and associated factors which influence
estuarine environments (Hinga et al., 1991). A table listing effects attributed to eutrophication was
presented to the workshop participants and modified following their discussions and input. The
resultant table is shown in Table 5. The table lists effects attributed to eutrophication, appropriate
measures of each effect, and factors that may potentially influence the expression of the effects.
The table also lists the relationships to be tested between nutrient loading and effects, and the
factors controlling them. Some general examples of the effects of nutrient enrichment are given in
17
-------
i
i
o
I
I
03
O
s
I
s
•s
I

I
ID
-3

I
I
I
I

0
lothesized Relationshi
Li
^

to
7J
co

^
a
u
fi
J]
1

-•••* ~'
V \
tO (Q
JE S
— go
r** C ^ .^^
i C £ ">^
*W S "g'ni
s | -§5
CO = O*.
to CO CD'S,
CD > > .E3
o co rt -J
E Q.' ol oL
z z, zz^
II II II II
0 0 00
to
CD
•5
Loading rate: N, P, & Si by spei
Temporal Pattern of loadings
Concentration of N or P
Light and light penetration
Temperature
Salinity
Stratification
Phytoplankton assembledge
Bordering Wetlands

3
r— T— CD ^
nT nT P 2 ^
Q Q o> CD T3
"fc 'P >•__ c
c to co o
CD D5 Q r" (n
E E J^ ^C C/J

i/r
to
s

o«^>
c
o
'•5
C 3
o -D
2 S

0 CO
i-i
CLQl

5
i-i
2 E
D. •*=
0 0;
|i
§g
rn
z

55
o3 CD
a-'-l
CD CD
D>£
c ,_
S -2
to .E
II
Itf
« 0
s^ CL
11 5<
•"^ Q)
o^
0)
S s 1
o J? -=
Loading rate: N, P, & Si by spe
Temporal Pattern of loadings
Concentration of N or P
Seasonal variability in loading i
Depth
Stratification
Grazing
Turbidity
Water residence time
Temporal distribution of vertica
energy
Abundance of grazers

JO
75
=3
co evi o
'E 'E 75 " ^
re| a\_ c t
S ±2 0 0
O o 2 °> o>
CD
o

CO
TJ
C
3
JJ
C
j2
2
CO
O.
_o
^
^

;
D
I
3 10
= co

= •- 0
- 2 S
- "o>«
5 !£ "O
i c§
igellates become dom
oadings
ift to smaller species i
sioning of water for "g
J2 — .c o
U- CO Q.

N:Si ratio in sewage effluent
P:Si ratio in sewage effluent
Succcession
Bad water (modification)
o
to
E
o
75 g

« ll S
2 c? »
s 5= ®
O O)
o S 5
•^ O CD
CO «- S;
CC <
CD
o>
CO
JD

m ® -»».
to 75 50
to = .2
CO CD o
c i? S
.2== w
2 co —
c S «
JO p '5
g- § —""5
'Si" ~ _N m
a.— — —
18
-------
•8
• 3
I

n
g
H
CD
DC
-o
CD
.N
0>
Q.
X

Factors

1
t/
CT
Q

^
p
x

1
*c
UJ
0
•o
.2

>•»
CD
Jj;
•5)
O
E
—
'S
o .
••— * •
rt fe

.2 '*

n) CD
|E
_D
B

E
w> ^
Oj "o ®
E 8 -2:
Horizontally distinct water i
A vertically stratified water
Warm weather conditions
High photosynthetically acl
radiation

tn o
E 2
CQ -Q
d) "x o
jg:£ .-
CD Q) Q)
Jj "O "x
SR °
£5 15
•^^ k.
JE <.
I
8
CO
05
"5 r?
•«- o

G> ^
c rt
g -2>
« jo^
Q_"X
< o

o • « !2 ^
0 E ® N -C ° ~
S> o .2 E 5 o t3
o -£ •£ S •=.>».« 52"o-£ <"
HlSff?i||sSi8fil
c c c.-8 •— ' CD C" ro^ rt ° CD ^ « =
iS uj < co«coir »cro

U5
o
— *S CD
co i2 o
•s '•= 5
o —2
c ^ CEJ
.2 "S S.
rt § Q.
= CD W
Q CC

o
S
(0
Q.
O
1^
£ ,
^"—^
o 2
±: n)
w're
£5
52 o> °?

8 "O s=
C « CD
"S «- 13
5 ffl ?
J3 'C «j
^ "5 -^*
c c -2*
~ o> — i
H 1
b 1 V
Q ?-

• c
_o
f-
Nutrient concentration
Turbidity, light color
Phytoplankton abundance
Epiphyte abundance
Bottom substrate, Sedimei
Depth, pigment type
Water flow rates, mixing
Mechanical disturbance
Wave action
1 I
0 CO
8 1
^_ CD
O >
1 I

")< *
»_ to
o -g
O O)^— ^,

c > w
"O :§
-------
CD
CD
coQ CD
CO
LL
CO
o>
0>
rt
CO
£
ff

8
CD
CD
.2
i 2
s>
co "5 -c w 0>
S> Q Q. c ft
£-.£.£« CD
15 CL .3 C '- O3
ia=l.i^

I
C
CO
o
I
CO
8.
CD
.
C O !
CO
•^ CO WC
O
O.LL. I-O
0)
ll
ll
§1
(551
20
-------

8
:
2
5
5
0
0
•o
D
n
D

I
J
C

12
1
How Measured 1

•5
I
L

^^
-5]
CO
i
2.
H-,
O

"to
;j
ST
CO
8
c
to

c
i

"c
Primary production
Depth
Organic carbon input
Grazing rates (top down contr
No. macrofauna nr2
Gr. macrofauna rrr2
Bioturbation

o
'.c
c
2
"o
8 co-~
C C 1
< o^
"c"
g
I
"c
8
i
1
0,
H^
O
*-
to
3
o-
CD
CO
8
c
(0
•o
c
1

~o
Oxygen concentrations
Sediment quality
Grazing rates (top down contf
No. macrofauna m"2
Gr. macrofauna rrr2
Bioturbation

o
Ic
c
2
"5
llf
(0 co (0
11 §
li1!

^»
"5.
Q.
3
CO
c
o
1
•2-
2

O"
.52
c
.2
*55
o
Q
E
o
O

Primary production
Oxygen concentrations
Food Quality
Sediment quality
Organic carbon input
Salinity variability
Diversity indicies
Presence of "desirable"
species
Bioturbation
o

1
a.
E
o
CO

1 E-
Inorganic sediment inputs, rui
Sediment resuspension
Storm events
Phytoplankton abundance
DOC concentration and adso
Light extinction
coefficient
mg suspen. matter 1 -1

^
"O
e

D)
^
increased populations respon
increased organic matter
Glucose or amino acid
metabolism
Thymidine uptake

;>.
;i
1
to
Si
1

m
>
£
3
CO
Altered conditions promoting
of pathogens
Altered conditions reducing
resistance of organisms
i Reports of diseased
organisms
c
(0
E
o

w
E
CO
<0
cfc
8 1
-------
Table 6 (Turner and Rabalais, 1991b), with some brief examples provided to illustrate the major
points. We know more about what is on these lists, which is seemingly all-encompassing, than of
the scientific understanding of the subtle interactions.

Table 6. Examples of coastal eutrophication and its effects (after Turner and Rabalais, 199 Ib).
Adriatic Sea
Baltic Sea, incl.
Kattegat and
Skagerrak
Bayou Texar, FL

Chesapeake Bay

Great South Bay,
Long Island, NY

Lac de Tunis,
Tunis, Tunisia
Mississippi River
Delta Bight, U.S.

Southern Bight
of the North Sea
Tampa Bay, FL
Probable or Observed Effect1

ox.; turb.; food chain
ex. al.; food chain; ox.,
macrophyt. gain; incr.
sec. prod.
ox., food chain, health, nox.

food chain, incr. prod., ox.

ex. al.
ex. al.; ox.; macrophyt. loss;
macrophyte gain; food chain

changes in area and extent of
hypoxia

ex. al.; incr. prod., food chain;
nox.; incr. sec. prod.
macrophyt. loss; turb; healt.;
ox.; nox.; food chain
Reference •

Krstulovic and Solic, 1990;
Justic, 1991; Faganeli, 1985;
Stachowitsch, 1986

Rosenberg, 1985,1986; Rosenberg
and Loo, 1988; Cederwall and
Elmgren, 1980; Andersson and
Rydberg 1988; Ankar 1980

Moshiri etal., 1981

Seliger etal., 1985

Ryther, 1954

Kelly and Naguib, 1984

Rabalais et al., 1991
van Bennekom et al., 1975;
Beukema and Cadee 1986;
Westernhagen and Dethlefson, 1983;
Lancelot etal, 1987

Johansson and Lewis, 1991
Santos and Simon, 1980
*Key to abbreviations:
ex. al. = excessive algal growth (including filamentous and attached)
food chain = food chain alterations affecting important fisheries species,
including fish kills, loss of benthic organisms
incr. al. prod. = increased primary productivity
incr. sec. prod. = increased secondary productivity, including benthos
nox. = noxious algal blooms
healt. = health problems with seafood consumption
macrophyt. loss = loss of important macrophytes
macrophyt. gain = gain of macrophytes
macrophyt. inv. = invasion of undesirable macrophytes
ox. = low oxygen levels
turb. = increased turbidity from phytoplankton growth
22
-------
Altered Trophic Structure

Nitrogen and phosphorus are the primary anthropogenic nutrient inputs of concern in coastal
waters. Nitrogen is considered the most important nutrient in marine and coastal waters;
phosphorus, in freshwater systems. Both nitrogen and phosphorus are important in estuaries,
depending on the season, total nutrient loadings, and various physical and chemical conditions.
Other chemical constituents such as silica, carbon, trace metals and chelators may also be important
in specific systems and under certain conditions. Many factors interact to influence changes in
primary producer and consumer populations, including the supply, relative availability, and timing
of nutrient inputs, and various physical characteristics of the estuary or coastal water body such as
temperature, turbidity, currents and water column stratification.

Increased phytoplankton production and biomass is the likely result in an otherwise nitrogen-
limited coastal food web (the current paradigm for many coastal systems) (Harris, 1986; Valiela,
1984). Although there are no phytoplankton indicator species of incipient or advanced stages of
coastal eutrophication presently identifiable, Smayda (1983, 1989, 1990, 1991) and others
(Richardson, 1989; Cherfas, 1990; Cadee, 1990) have identified a significant shift in
phytoplankton community structure at the phylogenetic level occurring globally in response to
coastal nutrient enrichment. Smayda (1991) further notes that this phylogenetic shift has been
towards increased abundance and seasonal dominance of flagellates and non-motile,
nannoplankton chrysophytes and, in some cases, N-fixing blue-green algae. Many of these
species may be noxious, harmful, or toxic in increased concentrations, and their sinking and
decomposition in the water column or at the seabed may contribute to increased hypoxic/anoxic
episodes.

Diatoms are thought to provide the primary energy source for traditional food webs that support
teleosts as top predators. The abundance of coastal diatoms is influenced by the silicon supplies,
whose Si:N atomic ratio is about 1:1 (the Redfield ratio). Diatoms out-compete other algae in a
stable and illuminated water column of favorable silicate concentration. Anthropogenic enrichment
of N and P, leading to long-term increases in these nutrient loadings, has also lead to long-term
declines in the Si:N (Figure 10a,b) (Turner and Rabalais, 1991a,b) and Si:P ratios. When nitrogen
increases and silicate decreases, flagellates may increase in abundance (Officer and Ryther, 1980).
The decline in the Si:P and Si:N ratios has particularly favored non-diatom blooms and is a key
factor associated with the global epidemic of novel toxic and harmful phytoplankton blooms and
phylogenetic shifts in phytoplankton biomass predominance in coastal seas (Smayda 1989, 1990,
1991); similar shifts may be occurring in the waters adjacent to the Mississippi River (Dortch and
Whitledge, 1992). In particular, noxious blooms of flagellates are becoming increasingly common
in coastal systems, according to Smayda; and there is evidence for an ongoing global increase in
the frequency, number of occurrences, and dynamics of toxic and harmful phytoplankton blooms
(Siddall, 1987; Dundas et al, 1989; Richardson, 1989; Cherfas, 1990; Cadee, 1990; Smayda,
1990, 1991). Evidence comes from the Baltic Sea, Kattegat, Skagerrak, Dutch Wadden Sea,
Black Sea, Tolo Harbour (Hong Kong, Korea, Seto Inland Sea, and northeastern coastal waters of
the United States). (See also Table 7 and many more examples in Shumway, 1990; Shumway et
al., 1990).

Less dramatic evidence for shifts in phytoplankton community composition comes from the work
of others who have documented species present in the plume of the Mississippi River during the
last few years (1989-1991) (Q. Dortch, personal communication) compared to earlier surveys
(Thomas and Simmons, 1959). Melosira distans which used to be a dominant phytoplankton
species in the waters adjacent to the Mississippi River delta (Thomas and Simmons, 1959) have
not been found in any recent surveys (Q. Dortch, personal communication). The Si:N ratio of the
river inflow to the coastal Gulf of Mexico has decreased from 4:1 to approximately 1:1 over the
same period (Turner and Rabalais, 199la).
23
-------
(U
2
o
E
o
•i-i
z
<1>
4->
CO
a_
*f\
U)
5;
4'
.
•
3:
•
2-
1
"
«
1;

0 V
o • »
\s ^&
A? ^^p|Q
Qv vD
• o^«
ft. ^
o^ta^^ f\
^^B>^ Jit
^J fmfff^flf
-^B
1900 1920 1940 1960 1980
. Changes in the atomic ratio of silicatemitrate-nitrogen this century at twc
the lower Mississippi River (St. Francisville = closed circles; New Orleans = open
circles) (adapted from Turner and Rabalais, 199 la).
160
I
60
1986

o
• St. Francisville, La.
o -New Orleans, La.
•o D —1905
9
120 180
Silicate pg at/I
240
Figure lOb. Average annual nitrate and silicate concentration in the lower Mississippi River
(adapted from Turner and Rabalais, 199 Ib).
24
-------
Table 7. Examples of the appearance of noxious blooms in coastal waters (after Turner and
Rabalais, 1991b).
Species

East coast of Florida Synechoccus sp.

Laguna Madre, TX "brown" tide

Long Island bays brown tide

Narraganset Bay, RI Aureococcus

North Carolina Ptychodiscus brevis
Swedish west coast
Texas coast
Prorocentrum minimum
and Gyrodinium aureolwn

Gymnodinium
splendens, Pthycho-
discus brevis
Norway

West coast of Florida Gymnodinium breve
Chrysochromulina
polyepis
Yearfs) Reference

1972,73 Mitsui era/.,, 1989

1990 Stockwell and Bus-
key, pers. comm.

1985,86 Cosper etal, 1987

1985 Tracey, 1988

1987 Summerson and
Peterson, 1990

since Grandli et aL,
1980 1986

1955, Riley etal., 1989;
1984, 86 Harper and Guillen,
1989

1988 Cherfas, 1990
common Eng-Wilmont and
Martin, 1977
Phylogenetic shifts within phytoplankton communities may alter the food supply available to
herbivorous organisms. Evidence suggests that smaller, "less desirable" flagellate- and
cyanobacterial-dominated communities are less acceptable as food for grazers (Smayda, 1983).
Zooplankton, the main consumers of whole diatoms and a staple of juvenile fish, are thus affected
by these nutrient changes in a cascading series of interactions. Alternatively, changes in type and
distribution of higher trophic-level herbivores and predators may have a cascading effect down the
food web to primary producers.

The widespread occurrence of changes in nutrient loading to coastal zones has also changed the
annual and seasonal variability of nutrient concentrations. Fertilizers, a major contributor to the
nitrogen and phosphorus budget, are usually applied in the spring, just before or during the
planting period. An example is shown for the lower Mississippi River at St. Francisville and New
Orleans, Louisiana (Figure 11) (Turner and Rabalais, 1991a) where a spring rise in nitrate
concentration is now evident. [N.B., A previous seasonal signal in silicate concentration is no
longer evident.]

A change in the timing of the spring bloom that supports fish entering estuaries to feed during
critical recruitment periods may also be an important consequence of eutrophication. Townsend
and Cammen (1988) point out that the timing of the spring plankton bloom in high latitudes is
important to the benthic-pelagic couplings upon which fisheries recruitment is dependent. The
timing of a bloom, is often very sensitive to light conditions, but declines from nutrient depletion.
25
-------
to
-
E
1601
120
80
40
200
KJ
en
CJ
•»->
o
o
100
a
•Cf>
CL
15
j-j
o
0
121
8
•5 4
11975-1985
a 1905-1906
«1955-1959

• 1933-1935
11905-1906
a 1955-1959
a 1975-1985
51975-1985
J FMAMJJAS
Month
0 N D AH
Months
Figure 11. Monthly average nitrate, silicate, and total phosphorus for 1905-1906 and 1933-1935
from the New Orleans water plant at Carrollton and for 1955-1959 and 1975-1985
• from St. Francisville, Louisiana. The bars are ± 1 standard error of the monthly
averages (from Turner and Rabalais, 1991a).
26
-------
Changes in the nutrient loading, and timing, could affect recruitment success through a mis-match
of larval recruitment and food supply, as well as an altered food chain. Early blooms with a
greater sedimentation to the benthos could positively affect demersal fishes, but late blooms
positively affect pelagic fisheries through a zooplankton food chain. Zooplankton graze on
diatoms extensively, so that changes in nutrient loading and the ratio of nutrients could affect the
balance and timing of the demersal and pelagic food webs.

Supportive evidence of this benthic-pelagic coupling is the work of Cederwall and Elmgren (1980)
who demonstrated a rise in macrobenthos around the Baltic islands of Gotland and Oland, which
they attributed to eutrophication, a known event (Nehring, 1984). Other examples of increased
benthic production are in Ankar (1980) (Tables 5 and 6). In other instances, nutrient enrichment
may be linked to decreased secondary benthic production (see section below on habitat suitability).

Oxygen Depletion

Oxygen-depleted waters are obvious manifestations of nutrient enrichment Where eutrophication
occurs, oxygen depletion often follows presumably as a consequence of the increase in organic
loading which is stimulated by increased nutrients. Excessive production of organic material in
surface waters may sink to the bottom, either directly, as grazed material, or advected.
Decomposition of these materials may lead to oxygen depletion, especially in stratified water
columns where the rate of depletion of oxygen is greater than the reaeration of the water column
from surface oxygen production or diffusion.

A good discussion of the chemical, geological and biological terminology of oxygen deficient
environments is given in Tyson and Pearson (1991). The term "hypoxic" has long been used by
physiologists to describe conditions or responses produced by stressful levels of oxygen
deficiency. The application of "hypoxic" ("hypoxia") to oxygen deficient environments began to
be common in the late 1970s, especially by those working in the Gulf of Mexico, and it is now in
widespread use by marine biologists and ecologists (Tyson and Pearson, 1991). Based on
laboratory and/or field observations on oxygen stress responses in invertebrate and fish faunas,
hypoxic has been variously defined as corresponding to dissolved oxygen levels lower than a
range of 3.0-0.2 ml/1, with the consensus being in favor of 2 mg/1 (=1.4 ml/1) (Tyson and Pearson,
1991).

The largest, most severe and most persistent zone of hypoxia (operationally defined by dissolved
oxygen levels <2 mg/1, or 1.4 ml/1, based on effects on local biota; see below) in the United States
coastal waters is found in the northern Gulf of Mexico on the continental shelf off Louisiana
(Figure 12). Equal to or larger than similar but less frequent phenomena off the northeastern coast
of the United States (Garside and Malone, 1978; Swanson and Sindermann, 1979; Falkowski et
al., 1980; Swanson and Parker, 1988; Welsh, 1991), these hypoxic zones occur at the terminus of
the largest river in North America and amidst the Nation's richest and most extensive fishing
grounds.

For the NOAA/OAD Nationwide Review project (Rabalais et al, 1985; Whitledge, 1985;
Windsor, 1985), a dissolved oxygen concentration of <4 mg/1 (2.8 ml/1) was determined as the
minimum level acceptable for coastal waters. In that review, estuaries or coastal areas were
categorized as having marginal and/or deteriorating water quality with respect to this level of
dissolved oxygen concentration. For 55 estuaries categorized by Rabalais et al. (1985) and
Windsor (1985), 37 were listed as experiencing hypoxia (< 4 mg/1) in part or all of the area for any
records. Within the 36 estuaries categorized by Rabalais et al. (1985) for Alabama, Mississippi,
Louisiana, and Texas, 12 were categorized with severe or regularly occurring hypoxia in part or all
the estuary. A similar category was not provided by Windsor (1985); instead, he listed seven of
19 estuaries as having potential problems or deteriorating water quality. For both studies, a little
over half (56 %) of the estuaries were categorized as having adequate data for evaluation.
27
-------
29'
94'
93*
92'
91'
1985
90*
91*
I
94'
1986
93"
92'
91'
90'
90'
i
1989
29'
29
1987
93*
92'
90"
1990
93*
92'
90'
Figure 12. Distribution of hypoxic bottom waters on the Louisiana continental shelf in mid-
summer for the years indicated. Shaded areas are <2 mg/1 dissolved oxygen.
Note, figures differ in station coverage and scale, longitude provides relative
distance (adapted from Rabalais et al., unpublished data).
28
-------
(

MSo wS Vduefbetow this are associated with reduced benthic macromfauna, and values
below oTmSl (or 7 % oxygen saturation) are associated with severely reduced numbers of
Snthic infS (Figure 13). Trawling for demersal species and not catching anything when the
nfaulbelow 2 mg/1 is not proof that fish and shrimp are absent because of the low
rations- however, tiiese relationships have been consistently observed (Figure 14
1 Pavel^Tet al, 1983; Leming and Stuntz, 1984; Renaud, 1986b). Experimen al
(i986a) indicated that white shrimp (Penaeus setiferus) detected and sigmficantiy
intiding water containing < 1.5 ppm dissolved oxygen and brown shrimp^naeus
) were more sensitive and avoided water of dissolved oxygen concentrations < 20 ppm.
For this revSwT a value of 2 mg/1 has been set as the limit that characterizes
oxygen-deficient waters (or hypoxia).

It should be pointed out that not all oxygen depletion results from nutrient enrichment Where
ncreased mJrients contribute to organic loading and subsequent decomposition of material and
on of oxygen, these features are usually coupled with a physical phenomenon of a stratified
Column Ss density stratification/controlled by temperate or salinity differences,
riaeration of the bottom waters at a rate sufficient to offset the depletion of oxygen
reSn In many deep channels, this density stratification may occur and oxygen may
delleted without increased organic inputs. Very often, however, the oxygen demand in the
tottoSwSeTsokeeper channels, especially near industrialized and urbanized areas, may be
relaSd to chemical oxygen demand or organic loading from sewage outfalls. Other deep channels
S toSgraphSy lowe? features may be consistently hypoxic in the bottom waters just because of
SeTyS structure and lack of mixing of the water column. In submerged aquatic vegetation
bedF (e7 seajass meadows or heavily vegetated creeks and bayous), a normal diel cycle of
oxygen concentration will produce low oxygen levels in the early morning hours following
exSve respkation of the vegetation during the dark cycle. In other instances, the movement of
SaUy stagnant swamp waters into other bodies of water following a flushing event may
contribute temporarily to a low oxygen condition.

The oxygen concentrations of surface waters may also be a key to the eutrophication status of a
water body Nutrient enrichment which stimulates phytoplankton growth may result m the
TupeVsaSon of oxygen in surface waters. Values of oxygen saturation >100 % are common y
fS in Louisiana colstal waters when high chlorophyll at biomass is ^oincid^ustlfa^9i)f
documented long-term trends in dissolved oxygen content of both the surface and bottom layers of
^Sern Adriatic Sea for the period 1911-1984 (Figure 15). An increase m the surface layer
and a decrease in the bottom layer were observed in all seasons except winter (Justic, 1991). The
presence of an oxygen minimum zone with depth, particularly above a pycnoclme, may also
indicate high respiration rates in the water column. These conditions are prevalent on the Louisiana
shelf.

A word of caution should be given regarding the use of dissolved oxygen data in water quality
monitoring data sets. Continuous oxygen measurements [e.g., Longley, 1992 (see Figure T13),
Summers and Engle (1992)] indicate diel variability in dissolved oxygen levels in most
environments. Water quality monitoring conducted primarily during daylight hours may skew
distributions of dissolved oxygen measurements.
29
-------
R-squared: 0.428
0)
o
o
0)
Q.

"5
0>
n.
W

**•!
o

E
3
C
CO
0)

E
.1
.15
•25 .3 .35

bottom oxygen (mg/l)
.4
T

.45
R-squared: 0.273
•2 .25 .3 .35

bottom water oxygen (mg/l)
.4
.45
-I
.5
Figure 13. Relationship of mean number of individuals per core and mean number of species per
core for benthic macroinfauna for bottom water oxygen concentrations <0 5 me/1 at a
station in 20 m water depth off Terrebonne Bay that is consistently subjected tolow
oxygen concentrations through the warmer months of the year (Rabalais et al
unpublished data).
30
-------
D.
1 •
0
123456789
Bottom Oxygen (mg/l)
300
I
100
0 • 1 23456789
Bottom Oxygen (mg/l)
4.0i-
2.0,-
tc

Ui
z
£2.0
o
5
X
OT
O
O
2.O 4.0
BOTTOM WATER DISSOLVED OXYGEN
CONCENTRATION (PPM)
6.O
O.O
y=a-U>Logx
r=0.56
_L
_L
2.0 4.0
BOTTOM WATER DISSOLVED OXYGEN
CONCENTRATION (PPM)
6.O
Figure 14. Upper panel: Shrimp and finfish catch rates plotted against bottom oxygen
concentration at trawl stations for June 1982 (from Leming and Stuntz, 1984).
Lower panel: Offshore shrimp abundance and fish biomass in relation to bottom
water dissolved oxygen concentration for trawl samples collected between 1972
and 1983 (from Renaud, 1986a).
3.1
-------
9

8h
c
0>

c
O 7
o
c
o
o>
>» e
X 5
O
t •
e

e «' «•«**

*•*. '
-HWP V* I

S o e e e •
i i • i i i
5 *:!
^ * o ^
. i
i
* '
30
20
2 10
u
o
o
(0
1911-13 29-33
37-43
55 65-66
72-84 Year
Figure 15. Oxygen content of the water column during August-September and Secchi disk
visibility during April-May, in the northern Adriatic Sea from 1911 to 1984; a:
surface layer, b: 2 m above the bottom; symbols refer to eastern, northern and
western subareas (from Justic, 1991).
32
-------
Habitat Alteration

Excessive nutrient loading can cause accelerated eutrophication; the resultant increase in planktonic
biomass decreases the distance that light can penetrate through the water column. Reduced light
penetration has been shown to inhibit photosynthesis in deeper waters of some eutrophic estuaries
(Pennock, 1986; Pennock and Sharp, 1987) and to affect photosynthetic microorganisms as well
as submerged aquatic vegetation (Short, 1987, 1991; Johansson and Lewis, 1991). Excessive
nutrient loading in an estuary can eliminate an eelgrass system in three ways according to Short
(1991): 1) change to a plankton-dominated ecosystem, 2) change to a macroalgal-dominated
ecosystem, and 3) change to a system with excessive amounts of epiphytic algal growth. All three
possible changes have been observed in the field and have been directly associated with
documented eelgrass declines (Short, 1987,1991). The loss of seagrass beds following decreased
water clarity is often observed (Cambridge and McComb, 1984; Cambridge et al., 1986;
Johansson and Lewis, 1991). It is also well established that certain coastal fisheries species seem
to require a physical structure to escape from predators while young. Where the area of estuarine
macrophytes declines or improves, fisheries harvest is observed to respond proportionally (e.g.,
Turner and Boesch, 1987). In this manner, nutrient enrichment and eutrophication can contribute
to the loss of emergent and submerged macrophytes that limit fisheries species during critical
recruitment periods, leading one to conclude that the potential harvest of dependent fisheries will
probably decline too. Such subtle changes are difficult to detect without substantial amounts of
long-term data (two examples are in Turner and Boesch, 1987).

Long-term changes in the turbidity of the water column as measured by changes in Secchi disk
depth have been documented for the northern Adriatic Sea (Justic, 1991). These long-term
changes are related to nutrient enrichment of the Adriatic from the Po River and a coincident long-
term decline in the oxygen concentration of the water column (see Figure 18). Other long-term
changes in the turbidity of the water column in coastal systems may be related to the reduction of
the suspended sediment load of a major freshwater source. This appears to be the case in the
waters adjacent to the Mississippi River, where a long-term increase in the Secchi disk depth is
perhaps related to increased water clarity as a result of the reduction of the suspended sediment
load and/or changes in phytoplankton community composition (Meade and Parker, 1985; Turner et
al., 1987; Turner et al., unpublished data). Increased water clarity adjacent to the Mississippi
River delta may have implications for increased phytoplankton production and biomass in a system
where turbidity is a factor limiting phytoplankton growth at various levels of light intensity.

There are numerous examples of the impacts of low oxygen conditions on reduced benthic fauna,
in terms of fewer species, lower abundance, or both (Rosenberg, 1977; Gaston, 1985; Gaston et
al., 1985; Rosenberg and Loo, 1988; Stachowitsch, 1984, 1986; Westernhagen et al., 1976;
Harper et al., 1991; Boesch and Rabalais, 1991; Rabalais et al., unpublished data). The level of
effect depends on the level or organic enrichment and/or concentration of dissolved oxygen in the
overlying waters and whether hydrogen sulfide is generated from the sediments during anoxic
events (Boesch and Rabalais, 1991; Harper et al., 1991; Rabalais et al., unpublished data). A
reduction in the benthic fauna is a habitat alteration that may have an indirect impact on other parts
of the food web, e.g., reduction in adequate food supplies for other species, such as demersal fish
and shrimp.

Areas impacted by low oxygen are a concern with respect to fisheries resources. For example, the
largest, most severe zone of hypoxia in the U.S. occurs at the terminus of the Mississippi River
and amidst the Nation's richest and most extensive fishing grounds. The area impacted by and
duration of hypoxia on the Louisiana shelf is important since Louisiana fisheries landings are 28 %
of the U.S. total. Trawl samples indicate that the demersal catch is reduced or virtually zero when
the bottom water dissolved oxygen levels fall below 2 mg/1 (see Figure 14). The processes
involved—direct mortalities, avoidance by bottom-dwelling shrimp and finfish, altered migration
(Renaud, 1986a), reduction in available habitat, changes in food resources, or increased
33
-------
susceptibility to predation-are not known. Although dead or decaying fish have been pulled up in
trawls where hypoxia occurs (Pavela et al., 1983), the trawls are usually empty under reduced
bottom water oxygen. These organisms move out of the area or up into the water column
(Rabalais and Harper, unpublished data). In either case, the area of suitable habitat is reduced and
the individuals may be more susceptible to predation. In addition, the stress incurred by fish,
from, for example, experiencing low oxygen tensions or starvation following oxygen depletion is
believed to be a contributing factor to the development of disease in fish; the areas off the Danish
west coast that experience oxygen depletion in the early 1980s are regions where high disease
frequencies have been observed compared to regions where oxygen depletion has not been
recorded (Nielsen and MeUargaard, 1989).

Less motile invertebrates are stressed by low oxygen conditions and either adapt behaviorally or
are killed. Dead and decaying invertebrates have been observed on the seabed where oxygen levels
are severely reduced (Stachowitsch, 1984; Faganeli et al., 1985; Rabalais and Harper, unpublished
data). Behavior modifications include movement to the sediment surface, extending body parts
above the sediment surface, or finding topographically higher locations (Rabalais and Harper,
unpublished data), all of which expose the typically infaunal organisms to increased predation
pressure.

The potentially enormous consequences of oxygen depletion to living resources in the northern
Gulf of Mexico are a regional and national concern. The potential exists for certain life stages of
penaeid shrimp to be affected by hypoxic bottom waters (Figure 16). Critical periods in the life
history of both brown and white shrimp occur during May through September when hypoxia is
present Figure 16 illustrates the temporal and spatial overlap of hypoxic bottom waters with major
spawning, larval recruitment and emigration events for brown and white shrimp. The effects of
hypoxia on shrimp populations are not clear but can be predicted based on the results of other
studies. Renaud (1986a) suggested that decline in the shrimp catch of Louisiana could be related to
hypoxic events, particularly those recorded from May 1983 to May 1984 and in 1982. He also
pointed out, based on a shrimp mark-release study, that hypoxic bottom water could act as a
physical barrier to juvenile shrimp emigration offshore and to postlarval migration into estuaries.
He further stated that the presence of hypoxia during critical periods in the development of
penaeids implicate it as a source of variation in annual shrimp yields.

Habitat suitability is the result of several interacting conditions, including oxygen. Low oxygen
levels in the water column, typically below 2 mg/1, are generally not satisfactory fish habitat.
Because nutrient enrichment and eutrophication frequently leads to low oxygen levels, an indirect
effect of eutrophication may be the contraction of suitable habitat necessary for reproduction and
growth. A recent example of this interaction is provided by Coutant and Benson (1991). They
examined the summer habitat conditions of the striped bass, Morone saxatilis, an important
commercial and recreational fisheries species in Chesapeake Bay, where the frequency and
duration of low oxygen events appears to be increasing (Officer et al., 1984; Seliger et al, 1985).
They estimated habitat suitability as the thickness of the July water column that had temperature
and oxygen conditions suitable for striped bass (for the central basin); they then compared the
changes in the habitat to an empirically-derived estimate of juveniles. Among the annual variations
usually attributable to climatic influences is a coincidental decline in both parameters (Figure 17).
In effect, the decline in suitable upper water column thickness appears to have compromised the
habitat suitable for juvenile reproduction. Without the long-term surveys of juvenile abundance,
the relationships might have gone unnoticed, because the adults are harvested over a much larger
area.
34
-------
100m-
DISTANCE (km)

20 40 60 80 100
DISTANCE (km)

20 40 60 80
100
m
UJ
li-

ar
a:
a.
—3

o
a.
LU
o
o
o
o
LJ
O
100m-
spa wiling
DEPTH
DEPTH
Penaeus

aztecus
Penaeus

sefif e rus
Figure 16. Major events in the life cycle of the brown shrimp (left panel) and the white shrimp

(right panel) through a year and in reference to the location on the continental shelf.

The shaded area represents the occurrence of hypoxia in bottom waters along a

transect across the shelf offshore of Terrebonne Bay through time. (Rabalais,

unpublished.)
35
-------
o Maryland Juvenile index
• Habitat thickness (18=max)
1950
1990
Figure 17. Decline in habitat suitability and the abundance of juvenile striped bass in Chesapeake
Bay from 1954 to 1988 (from data in Table 1 of Coutant and Benson, 1991). The
maximum value for the area of suitable habitat is 18 m, and is based on the water
column with a temperature below 25"C and dissolved oxygen above 2 mg/1 during
July. The juvenile index is based on summer-time beach seining surveys of 100 day-
old striped bass at standard locations (adapted from Turner and Rabalais, 1991b).

Reversal of Eutrophication

There are a few examples of what happens when eutrophication is reversed. Four are discussed
here: 1) Bayou Texar, Florida, 2) Tampa Bay, Florida, 3) Seto Inland Sea of Japan and 4)
Kaneohe Bay, Hawaii.

The eutrophication of Bayou Texar, near Pensacola, Florida was studied by Moshiri et al. (1981)
to determine the causes and remedies for extensive fish kills (up to five weeks), closure to
recreational use, dinoflagellate blooms (primarily Ceratium sp. and Gymnodinium sp.),
chrysophytes (primarily from the genera Chrysochromulina and Chromulina), diatoms (Navicula
and Cyclotella), and high algal biomass which contributed to low dissolved oxygen levels. In
1974, a retention reservoir and weirs in the upstream channels were built, and sewage plants
repaired. The authors reported an almost total reduction in fish kills, a 90 % reduction in
phytoplankton primary production, and a virtual elimination of algal blooms. Fish kills in recent
years (1988-1990) indicate that the problem has not disappeared (D. Flemer, personal
communication).

Johansson and Lewis (1991) documented a decline in water quality and then restoration in
Hillsborough Bay, near Tampa Bay, Florida. Tampa Bay was "grossly polluted" from cannery
wastes and poorly treated municipal wastewater discharges in the 1960s. A principal concern was
the loss of submerged macrophytes (Halodule wrightii), presumably because of increased turbidity
following eutrophication. Anoxia and high coliform counts were additional concerns. Following
improved sewage treatment, the nitrogen loading to Hillsborough Bay was reduced 30 %,
primarily between 1979 and 1980. It was not until four years later that the ambient chlorophyll a
concentration decreased substantially, which was coincident with the decline in a nuisance
planktonic blue-green alga, Schizothrix calcicola sensu Drouet. Turbidity decreased.
36
-------
A major change in seagrasses, reduced to 20 % of the area! coverage of 100 years ago, occurred
following improvements in water quality around 1984. The areal coverage of seagrasses in
Hillsborough Bay and Middle Tampa Bay doubled from 1986 to 1989. Seagrasses in most
shallow areas, however, have not yet recovered and high concentrations of chlorophyll a persist.
Major sources of nitrogen and phosphorus remain in the fertilizer plants and storage facilities, as
well as leakage at loading terminals. This partial recovery has followed partial reduction of nutrient
loads, but the system was still responding after five years of the initial nutrient load reduction.

The third example is a report by Cherfas (1990) of a summary by Smetacek. The annual incidence
of red tides in the Seto Inland Sea of Japan increased from 40 to more than 300 annually, from
1965 to 1972, as nutrient loading increased. In 1972 nutrient loading was reduced in half, and the
frequency of red tides peaked in 1975 and has been declining ever since.

Smith (1981), described the impacts of nutrient loading and restoration in Kaneohe Bay, Hawaii, a
subtropical coral reef/estuary complex. Effluent from a large sewage treatment plant provided 80-
90 % of the inorganic nitrogen and phosphorus loading to the bay before being diverted to an
ocean outfall in 1977-1978. The initial sewage addition resulted in enhanced plankton biomass
near the outfall (frequently a bloom developed), with only small increases in nutrient concentration,
but a significant increase in benthic biomass. Following the diversion to the outfall, the plankton
biomass dropped quickly, but the benthic biomass dropped more slowly. The authors explain the
different response times as being a function of the washout characteristics of the two
compartments: the phytoplankton have low storage of nutrients, high nutrient turnover, and a fast
washout time. In contrast, the benthic community has a slower nutrient recycling rate of the larger
nutrient storage pool, hence the biomass remained nearly the same as before the diversion after
three years.

These four studies, particularly the discussion by Smith (1981), illuminates the obvious
possibilities for recovery following a reduction in nutrient loading. When the causes of
eutrophication are reversed, the symptoms may be reversed. But recovery varies with the cycling
rate of various stored nutrients, and the flushing rate of the estuary. Seagrasses, at least those that
are inhibited by the reduced light penetration that often accompanies eutrophication, may recover,
but only over a decade or more.

Management Options

Most aspects of the policy implications of eutrophication are well stated in other places and the
basis for numerous legislation. Some less obvious issues, however, are related to the
interrelationship of the national policy of nutrient control in freshwater and the impact, or lack of
impact, on coastal systems. Management of eutrophication on a national scale has not sufficiently
integrated freshwater and estuarine systems. The national freshwater policy is to control
phosphorus, and is based on the numerous excellent laboratory and field studies of the stimulatory
effect of phosphorus on freshwater ecosystems. Coastal systems, however, are usually thought to
be nitrogen limited.

A national policy in common to both freshwater and coastal systems is sewerage treatment, in
general. But as is shown for the Mississippi river (Turner and Rabalais, 199la), the terrestrial
system is very leaky, and treatment does not mean a reduction of loading to the estuary via water
and precipitation. A second understated issue, therefore, is that sewerage treatment upstream does
not necessary equate to controlling nutrient loading to downstream estuaries. The minimization
and mitigation of uses seems a less prudent management policy than an outright reduction in use.
The ecosystem is simply too leaky to control all flows of important nutrients from use to arrival in
the estuary. Of course, getting people to accept that reduction in use is another issue.
37
-------
The Clean Water Act of 1972 dictates efforts to restore the quality of the Nation's water. Many of
these w.aters, however, remain heavily polluted. The EPA estimates that nonpoint sources of water
pollution account for more than half of the pollutants entering national waters. Pollution from
nonpoint sources, such as feedlots, landfills, and agriculture, are five to six times the pollution
load from municipal and industrial point sources (testimony, U.S. House of Representatives,
Subcommittee on Oversight and Review, Committee on Public Works and Transportation, July
17, 1979). Historically, Congress has been reluctant to deal directly with nonpoint source
pollution (EOS, June 25,1991). The Water Quality Act of 1987 expanded EPA's role but leaves
primary responsibility for nonpoint pollution with the state because the problem is considered a
local issue. Development of methods for monitoring and control of nonpoint sources of pollution,
however, appears to be a national need when multi-state sources contribute to the nutrient loading
of an estuary or coastal system. Cooperative programs are not insurmountable. A major goal of
the multi-state Chesapeake Bay Program is to reduce inputs of phosphorus and nitrogen 40 % by
the year 2000. The U.S. EPA and states of New York and Connecticut are developing plans to
guarantee that the level of nutrients does not increase in Long Island Sound where there is an
oxygen depletion problem. Cooperative initiatives can also be international, for example, the
Agreement on Conservation of the Marine Environment of the Gulf of Maine drawn between the
Canadian provinces of Nova Scotia and New Brunswick and the states of Maine, Massachusetts
and New Hampshire. The Gulf of Maine initiative began at the local level, in lieu of no national or
international policy, to respond to recognized needs for action to protect a shared environment

DATA ACQUISITION

.•The data for this review were obtained from several sources. Initial literature searches were
facilitated by the works conducted during the NOAA/OAD Nationwide Review (Rabalais et al.,
1985; Windsor, 1985) and supplemented by new computer searches. Many of the data sources
identified during these previous reviews were reassessed and supplemented with others. In
addition, as mentioned above, many new and ongoing programs have been completed or are in
progress in many of the Gulf states.

Literature Searches

A large body of literature, both published and "gray," exists on the many Gulf of Mexico estuarine
systems and coastal areas. Some of these documents proved useful in the assessments of
eutrophication status of the water body, while others were useful in providing the descriptive
information for an estuary within which to assess the status. Other literature was relevant to Gulf
coast estuaries but provided no directly useful information for assessing the status and trends of
eutrophication. In addition, many worthwhile references on nutrient cycling, eutrophication,
oxygen deficient waters, noxious and toxic algal blooms, and long-term changes in coastal water
quality were relevant to this report. Most of the relevant and useful pieces of literature that were
identified are included in the two bibliographies in Appendix D.

Initial literature searches were guided by the bibliographies developed in the Rabalais et al. (1985)
and Windsor (1985) sections for the Nationwide Review of Oxygen Depletion and Eutrophication
in Estuarine and Coastal Waters (Whitledge, 1985). Several other bibliographies proved useful:
Dennis et al. (9184), Renaud (1985), Schroeder et aL (1988) and a personal bibliographic
reference manager (J. Hand, 1990, Florida Department of Environmental Regulation, M.
Freidm^nn, personal communication).

Computerized data bases were searched through DIALOG (1950 to present), GEOREF (1987
through September 1990), ASFA (Aquatic Sciences and Fisheries Abstracts, 1987 through
February 1991), and the Louisiana Database, Coastal Information Repository, Center for Wetland
Resources, Louisiana State University, Baton Rouge, Louisiana. Libraries, federal agencies, state
agencies for fish and wildlife, natural resources, and water quality, and university-affiliated marine
38
-------
laboratories were sources of information. The libraries of the Louisiana Universities Marine
Consortium (LUMCON) Marine Genter, Cocodrie; Coastal Information Repository, Center for
Wetland Resources, Louisiana State University (LSU), Baton Rouge; The University of Texas
Marine Science Institute, Port Aransas Marine Laboratory; Marine Environmental Sciences
Consortium, Dauphin Island Sea Lab; and Gulf Coast Research Laboratory, Ocean Springs,
Mississippi, were used to locate obscure manuscripts and reports. Copies of most literature and
reports are retained within the libraries of the Louisiana Universities Marine Consortium, the
Coastal Information Repository at LSU, or the personal collection of the principal investigator,
N.N. Rabalais at LUMCON. Other literature was obtained through Interlibrary Loan services.

The references listed in Bibliography I (Appendix D) were used to develop the status and trends
reported in this volume. These references are annotated with a short abstract describing the
contents of the volume and/or results. Details of the manuscript, especially where relevant to
identification of eutrophication indicators, are included in the text of this volume. The references
are coded to identify the estuary or coastal area of concern. References identified as "not in hand"
were listed in either Rabalais et al (1985) or Windsor (1985), but could not be located for further
examination for this report.

Data Sources

Computerized literature searches were useful, but much of the data that would indicate conditions
of eutrophication (e.g., nutrient concentrations, turbidity, dissolved oxygen levels) are not reported
in the scientific literature and much of it does not even occur in government or contractor project
reports. Most data reside with state and federal agencies and research laboratories, and are nor
fully accessible. It was necessary to conduct telephone and personal interviews with agency
representatives and regional experts to determine what data sets existed and which were available
for examination (see Appendices B and C). Our experience indicates that it was more efficient and
the data were quality-controlled in a better fashion if we accessed data directly from an agency
(e.g., Louisiana Department of Environmental Quality or the U.S. Geological Survey) rather than
by obtaining it from the EPA STORET data base.

Our efforts in examining data bases were hampered by the nature of the data collected. Many
studies or monitoring programs have a specific limited purpose and are not sufficient in their
resolution or duration to indicate trends in increasing or decreasing water quality. The link
between any observable trends are also difficult to attribute to anthropogenic activities Some data
bases have already been examined by various authors, and their results are presented in this
review. Still a vast amount of unanalyzed data exists (see Appendix B), and some sets mav be
worthy of a more detailed analysis. .

A general description of the data sets obtained for this review are given in Appendix B Where a
data set was examined for frequency, duration and severity of oxygen depletion, a discussion of
those data follows.

Water quality data for Florida are maintained by several agencies including the various Water
Management Districts; county agencies, such as the Hillsborough County Environmental
Protection Commission; and the Florida Department of Environmental Regulation. Site specific
studies have been conducted by these state agencies; federal agencies, such as NOAA and EPA-
and university collaborators. The most extensive studies have been conducted in the Tampk Bav
estuary, Apalachicola Bay, Pensacola and Escambia Bays, and Perdido Bay.

The Marine Resources Division of the Alabama Department of Conservation and Natural
Resources has been collecting hydrographic data in conjunction with its fisheries assessment and
monitoring program since October 1980 (S. Heath, personal communication). Sixty-six stations
have been established in the State's coastal waters for trawl, seine, surface plankton and benthic
39
-------
plankton samples. A suite of stations is sampled monthly. Some stations have been sampled for
{^duration of the program; others have ben discontinued or added as fisheries management
MorSon nee^ have changed. From 1977 to 1980, a brown shrimp survey was conducted
fffCa tough October It various stations throughout the State's coastal waters These
Storing&£sets have been computerized and are managed by the departmental its Gulf Shores
SteSHSSski. personal communication). Data from field reports of the Alabama Deparmient
SrEnvironmentalManagement were provided by J.C. Carlton (personal communication).
Additional data for Alabama were available from literature and technical reports based on studies
conduced by researchers at the Dauphin Island Sea Lab, Dauphin Island, Alabama (W.W.
Schroeder, T.S. Hopkins, G.F. Crozier, M. Dardeau, J. Pennock, personal communications).

Information for Mississippi was obtained primarily from personnel of the Gulf Coast Research
Laboratory, Ocean Springs. The most extensive data base was provided by the Fisheries
Monitoring and Assessment project (F.C. Saner, T. Warren personal communications) This
group has been collecting hydrographic data with its trawl and seine samples at 36 stations in Ae
Soastal waters and Mississippi Sound since 1973. Some stations have been sampled for the
dSon of the program; otihers have been discontinued or added as fisheries^management
information needs have changed. Additional hydro^aphic data have been collected with various
research programs conducted by scientists at the laboratory (e.g., Mississippi Sea Grant Projec
R/LR-11 K Stuck, personal communication; Eleuterius and Beaugez, 1979; H. Perry, personal
communication). Hydrographic data were also obtained from the Mississippi Department of
Natural Resources, Bureau of Pollution Control, in the form of technical reports (R.H. Seyfarth,
personal communication).

Information on water quality in Louisiana was obtained from initial literature searches in BIOSIS
id the Louisiana Database of the Coastal Information Repository, Center for Wetlmid Resources
Louisiana State University, Baton Rouge. Computerized data, field reports, and 305(b) reports
were obtained from the Louisiana Department of Environmental Quality (M.H. Schurtz, J.
Boydstun, S. Braden, personal communications). Additional hydrographic data for various
Louisiana estuaries were provided by G. Gaston, R.E. Turner, and Q. Dortch (personal
communications).

The maiority of the data for the coastal waters of Texas was obtained from the Texas Water
Development Board (G. PoweU, personal communication). The Coastal Data System is based on a
State and Federal (USGS) cooperative program started in the late 1960s. In addition to the data
collected statewide, the TWDB has conducted a series of species studies in a number of Texas
estuaries (see Appendix C, Univ. of Texas Marine Science Inst.). The TWDB also maintains a
data set the Statewide Monitoring Network, which contains water quality data from collections
since January 1968 in or near waste outfall areas and channels and harbors. The data base contains
both hvdrographic and biological data; samples may be taken at several depths in the water column
and possibly more than once a dat. These data sets are managed by the Texas Natural Resources
Information System. Additional long-term, automated hydrographic monitoring data were
obtained from draft reports by G. Powell (personal communication). The Texas Parks and
Wildlife Department collects hydrographic data with some fisheries data. Data prior to 1976 are
reported in Martinez (1969-1970 etseq.). Data collected since 1975 are recorded on standardized
forms submitted to the Austin headquarters, and have now been computerized (M. Osborn,
personal communication). Since 1975 monthly shrimp trawl samples have been taken in all major
bay systems and are accompanied by bottom water samples. Monthly bag seme samples and
seasonal gill net samples are accompanied by surface to mid-depth water samples in 0.2 to 1m of
water. The types of collections and station locations are outlined in Texas Parks and Wildlife
Department publications (e.g., Benefield et al, 1983; Hegen, 1983).

Several unpublished and agency reports were available from the University of Texas Marine
Science Institute, Port Aransas Marine Laboratory library. Additional raw data and reports with
40
-------
hydrographic data for the inner continental shelf were provided by D.E. Harper, Jr. (pers.
comm.).

One of the data bases analyzed for indicators of nutrient enrichment was NOAA's Inventory of
Fish Kills in Coastal Waters, 1980-1989 (draft data base, March 1991; Lowe et al, 1991). The
information contained in the fish kill inventory may be useful as indicators of coastal waters that
are currently degraded or that are beginning to show symptoms of decline. Fish kills are a clear
sign of acute stress; however, the source of the stress may be anthropogenic or natural, or a
complex combination of natural and man-induced factors. The fish kill inventory data are useful in
that many states compile the information and there is a potential to evaluate changes in the water
quality of an estuary where the data set is adequate.

The data examined for fish kill reports were from all Gulf states for all counties within the estuarine
drainage basins as outlined in Figure 18 (taken from NOAA, 1990a). Only the data for counties
which directly bordered an estuary were used; this was to avoid the preponderance of freshwater
systems in the upper drainage area of the estuary. Even within the counties to which the analysis
was limited, there are a number of freshwater streams. It was beyond the limitations of this study,
however, to precisely identify the water body and its salinity characteristics. We tabulated all fish
kills for an estuary by determining where the majority of the county occurred geographically. We
then noted the number of fish kills attributed to causes outlined by the inventory as: 1 - low
dissolved oxygen, 4 - eutrophication, 18 - nutrients, either from applied ammonia or septic tank
leachate 22 - red tide, 88 - unknown, and 99 - unspecified. Other causes that were listed in the
data base are given in Table 10 and were not attributable to nutrient enrichment either directly or
indirectly. A data base is only as worthwhile as the quality of the data entered; we are cautious in
applying too much emphasis to this analysis. The percentages of fish kills that can be attributed to
the causes most directly linked to nutrient enrichment can provide some measure of the status of the
estuary.
41
-------
Gull of Mexico Counties (Eastern)'
FkxMa
Bay
Calhoun
Charlotte
Collier
Columbia
Dado
Do Solo
Onto
Escambia
10 Franklin
11 Gadsden
12 Gitehtist
13 Glades
14 Gull
IS Haidce
16 Hendry
17 Highlands
18 Hillsborough
19 Holmos
•C«v*tl cwnckicty Of p
20
21
22
23
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
40
~.en«^™° —— —
Jackson Georgia
Jellerson
Lafayette 41 Brooks
Lee 42 Decatur
Leon 43 Grady
Levy 44 Thomas
Liberty
Madison
Manatee
Monroe
Okaloosa
Pasco
Pinellas
Polk
Santa Rosa
Sarasola
Suwannee
Taytor
Wakulla
Walton
Washington
Alabama

45
46
47
48
49
50
51
52
53
54
55
56
57
58

Baldwin
Choctaw
Clarke
Coffee
Conecuh
Covington
Crenshaw
Escambia
Geneva
Houston
Mobile
Monroe
Washington
Wilcox

Mississiooi

59
60
61
62
63
64
65
66
67
68
69
70
71
72
73
74
75

Amite
Franklin
George
Greene
Hancock
Harrison
Jackson
Lamar
Lincoln
Marion
Pearl River
Perry
Pike
Stone
Walthall
Wayne
Wilkinson

Gulf of Mexico Counties (Western)*
(.ou/si.ina

1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
-------
I
rt
.a
§

c/j

a
T3
CO
..E S-
:&Ei
•2"S!
s"6 ^
.1 • If
p
el

11
s H!
SBrt geofi-gn •=•£
iff, iiip!. is
111 It

p Ifllj lit
III Jll

Iliflll
Hli pi! i
. s 1 £ » I'JHc. g
nlH lia*
It! IIJO ill Hi
g

•£ ^
HI
ll|

ail
1
E?

il-- it
\w is
H*« II
'So
i|li
•is 5 eg
Is-ll
lilt
-»s» I
81 S " 11 «

i 111] 1
*51lll H
jjjpl. f?

I'as
La
!!
U '" fl g JS
•s S z &a *
Iinil

trill1
-I 3|
1* Is
tl
•Si

ii
•5 i
Ill
T)
.g
1
;E
.?
.s

I
1
s

1
»

o
E
o
S258 H888S!
43
-------
ESTUARY AND COASTAL AREA UNITS

The 1985 Nationwide Review conducted for NOAA Ocean Assessments Division (NOAA/OAD)
provided for the division of the Gulf of Mexico estuaries and coastal regions into standard
hydrographic units for Florida (Windsor, 1985) and the remaining Gulf states (Rabalais et al.,
1985). These codes were expanded where necessary (in Rabalais et al., 1985, and this report) to
accommodate additional hydrographic units. The codes from the previous reports were retained
for the current work, even though other coding structures have since been developed by NOAA for
various data compilations. The codes used in this report are listed in Table 9 and illustrated in the
accompanying maps (Figures 22-26). The site specific summaries and literature annotations refer
to these codes. Literature and hydrographic data sets for 59 coastal areas (Table 9) in the five-state
region (western Florida, Alabama, Mississippi, Louisiana, and Texas) were examined. Areas of
concern were limited to inner shelf offshore waters, coastal and estuarine waters, and the tidal
reaches of freshwater streams, bayous and rivers. A cross-listing of the various codes in current
use is given in Table 10.

Table 9. List of codes for Gulf of Mexico coastal areas (after Rabalais et al., 1985; Windsor,
1985).
CODE

F-9
F-10
F-ll
F-12
F-13
F-14
F-15
F-15.1 _
F-16
F-17
F-18
F-19
F-20
F-21
F-22
F-23
F-23.5_
F-24
F-24.1 _
F-25
F-26
F-27
F-28&G-1
G-2
G-2.1
G-2.2
G-2.3
G-3
G-4
G-5
G-5.1
ESTUARY OR COASTAL AREA

.Whitewater Bay
_Big Lostman's Bay
.Chatham Bay/River
_ Caloosahatchee River
_ Charlotte Harbor/Peace/Myakka Rivers
_SarasotaBay
_Tampa/Old Tampa/Hillsborough Bays
_ Florida inner continental shelf (sw)
_ Crystal Bay/River
_ Withlacoochee River
_WaccasassaBay
_Suwannee River/Sound
_Deadmans Bay/Steinhatchee River
_Aucilla River
_ Apalachee Bay/St. Marks River
.OchlockoneeBay
St. George Sound
_ Apalachicola Bay/River/East Bay
.Florida inner continental shelf (panhandle)
.St. Andrew/West/North/East Bays
.Choctawhatchee Bay
.Pensacola/East/Escambia Bays
.Perdido Bay/River
.Mobile Bay/River/Tensaw River
.Alabama inner continental shelf
.East Mississippi Sound
.Mississippi Sound, Gulf Islands area and mid-Sound
.Pascagoula Bay/River/Escatawpa River
.Biloxi/BackBays
rSt. Louis Bay/Wolf/Jourdan Rivers
.Mississippi inner continental shelf (outside Gulf Islands)
44
-------
Table 9. Continued
CODE
G-6
G-7
G-7.1
G-8
G-8.1
G-9_
G-10
G-ll
G-ll.
G-12
G-13
G-14
G-15
G-16
G-17

G-18

G-19
G-20
G-21

G-22.

G-23 .

G-24
1
G-25
G-26
G-26.:
G-26.:

G-26.:
G-27
ESTUARY OR COASTAL AREA

_Pearl River
_ Lakes Pontchartrain/Maurepas
_ Louisiana inner continental shelf
_LakeBorgne
_Breton/Chandeleur Sounds
_ Mississippi River
_BaratariaBay
_ Terrebonne/Timbalier Bays
_ Caillou Bay
_ Atehafalaya Bay/River
_ Vermilion/West Cote Blanche/East Cote Blanche Bays
_ Mermentau River/Grand/White Lakes
_Calcasieu River/Lake/Pass
_Sabine Lake/Pass (Sabine-Neches Estuary, includes Sabine Lake, Sabine Pass)
_ Galveston/East/West Bays (Trinity-San Jacinto Estuary, includes Galveston East
West, and Trinity Bays, Bolivar Pass, GIWW)
_ Brazos River (Brazos River Estuary, includes Brazos River, San Bernard River,
Freeport Ship Channel)
_ East Matagorda Bay
_ Colorado River (Colorado Estuary)
_ Matagorda/Lavaca Bays (Lavaca-Tres Palacios Estuary, includes Lavaca, Matagorda
and Tres Palacios Bays)
_San Antonio/Espiritu Santo Bays (Guadalupe Estuary, includes San Antonio, Espiritu
Santo and Mesquite Bays)
_ Aransas/Copano Bays (Mission-Aransas Estuary, includes Mission, Aransas Copano
and Redfish (part) Bays and Aransas Pass)
.Corpus Christi/Nueces Bays (Nueces Estuary, includes Nueces, Corpus Christi and
Redfish (part) Bays and Aransas Pass)
.Baffin Bay
.Laguna Madre
_ Upper Laguna Madre
.Lower Laguna Madre (includes Arroyo Colorado, South Bay, Brownsville Ship
Channel and Brazos Santiago Pass)
.Rio Grande Tidal
.Texas inner continental shelf
45
-------
Table 10. Cross-listing of codes used in this report with other coding structures of NOAA and
EPA. ,
This
study

_.
F-9

F-10
F-ll
——
F-12
F-13
* •* *r
F-14
F-15
F-15.1
F-16
F-17
F-18
F-19
F-20
F-21
F-22
F-23
F-23.5
F-24
F-24.1
F-25
F-26
F-27
F-28&G-1
G-2
G:2.1
G-2.2
G-2.3
G-3
G-4
G-5
G-5.1
G-6
G-7
G-8
G-8.1
G-9
G-10
G-ll
G-ll.l
G-12
System Name
Florida Bay
Ten Thousand Islands
Whitewater bay
South Ten Thousand Islands
Big Lostman's Bay
Chatham Bay
North Ten Thousand Islands
Rookery Bay
Caloosahatchee River
Charlotte Harbor
Sarasota Bay
Tampa Bay
SW Florida Shelf
Crystal Bay/River
Withlacoochee River
Waccasassa Bay
Suwannee River
Deadmans Bay/Steinhatchee R.
Aucilla River
ApalacheeBay
Ochlockonee Bay
St. George Sound
Apalachicola Bay
Florida Panhandle Shelf
St. Andrew Bay
Choctawhatchee Bay
Pensacola Bay
Perdido Bay
Mobile Bay
Alabama Shelf
East Mississippi Sound
Mississippi Sound
Pascagoula Bay
Biloxi Bay
St. Louis Bay
Mississippi Shelf
Pearl River
Lake Pontchartrain
Lake Borgne
Breton/Chandeleur Sounds
Mississippi River
Barataria Bay
Terrebonne/Timbalier Bays
Caillou Bay
Atchafalaya River/Bay
NOAAa
NEI
__
3.01
—
—
—
__
—
3.02
3.24
3.03
—
—
—
3.04
~
—
3.05
—
3.06
~
3.07
3.10
3.08
3.09
3.11
~
3.12
3.12
3.12
3.12
3.12
—
—
3.12b
3.12a
3.25
3.13
3.26
3.27
3.14
NOAA/OADb NOAA/EPA0
1990 Abbreviation
G010

X™1 /\S\f\
G020
—
G030
G040
/~*f\Ef\*
GOSOa
G050
G060
G070
—
—
~~
G080
—
--
G090
—
G100
—
G110
G120
G130
G140
G150
~
G160
G160
G160
G160
G160
--
~
G160b
G160a
G170
G180
G190
G200
G210

Til

CHR
TAM

SUW

AEE

APA

AND
CHO
PEN
PER
MOB

MSS
MSS
MSS
MSS
MSS

MIS

AN
46
-------
Table 10. Continued
This
study
System Name
NOAAa
NEI
NOAA/OADb NOAA/EPA0
1990 Abbreviation
G-13
G-14
G-15
G-16
G-17
G-18
G-19
G-20
G-21
G-22
G-23
G-24
G-25
G-26
G-26.1
G-26.2
G-26.3
G-27
Vermilion/Cote Blanche Bays
Mermentau/GrandAVhite
Calcasieu Lake
Sabine Lake
Galveston Bay
Brazos River
East Matagorda Bay
Colorado River
Matagorda Bay
San Antonio Bay
Aransas Bay
Corpus Christi Bay
Baffin Bay
Laguna Madre
Upper Laguna Madre
Lower Laguna Madre
Rio Grande Tidal
Texas Shelf
3.14
_.
3.15
3.16
3.17
3.18
—
__
3.19
3.20
3.21
3.22
3.23a
3.23
—
—
__
—
G210
__
G220
G230
G240
G250
—
__
G260
G270
G280
G290
G300a
- __
G300
G310
._
«
A/V

CAL
SAB
GAL
BRZ

MAT
ANT
ARA
COR

LAG

aNOAA (1985).
bNOAA (1990a).
CNOAA/EPA Team on Near Coastal Waters (1990), uses the same code as the NOAA (1985) NEI.
47
-------
48
-------
oo
49
-------
oo
ON
s
en
O
4?
at
E-
50
-------
>n
oo
•a
I
O
bo
1
o
1
03
I

-------
Location mop
I G-16
Sjabine
Lake/Pass
G-17 Calves toi^4.
/East/West Bays
\ HARRIS _Pc,t H'^v^

\ f V~""\ SJ CHAMBERS JEFFERSON \^
-18 Brazos River
East Matagorda B
G-20 Colorado River n
21? Matagorda/Lavaca
-22 San Antonio/Espiritu Santo "[Bays

G-23 Aransas/Copano Bays

-24 Corpus Christi/Nueces Bays
G-26 Laguna Madre
-G-26.1 Upper Laguna Madre
G-25 Baffin Bay ° "> J0 30 40M1LES
G-27 Inner Continental Shelf
-G-26.2 Lower Laguna Madre
-G-26.3 Rio Grande tidal
Figure 23. Coastal areas of Texas with codes as indicated (G-16 through G-27) [after Rabalais et
al. (1985)].
52
-------
STATUS MATRIX
The 1985 Nationwide Review of Oxygen Depletion and Eutrophication (Rabalais et aL, 1985;
Whitledge, 1985; Windsor, 1985) developed a matrix which identified the status of the individual
estuarine basins and coastal areas of the Gulf of Mexico with regards to dissolved oxygen
concentrations of bottom waters. The critical level (as defined by NOAA/OAD as 4 mg/1) was used
to establish priority hypoxia areas with a demonstrated hypoxia and/or eutrophication problem,
potential hypoxia areas which were borderline cases where no strong hypoxia was noted but where
conditions for a serious problem occurring were judged to be possible in the future, and areas with
lack of sufficient data to make a determination (some of which were also classified as "potential").

Also, as mentioned earlier, the critical level of 4 mg/1 may not be appropriate for Gulf coast
estuaries, and other indicators of nutrient enrichment may be evident in a system. On the other
hand, additional factors affect the water quality of an estuary and may not be related to nutrient
enrichment. [E.g., chemical contamination may be a problem within an estuary, whereas there are
no indicators of nutrient enrichment] A matrix has been developed based on the previous reviews
which incorporates:

1) information obtained in the previous reviews related to nutrient enrichment but not considered in
the categories based on oxygen levels,

2) a more appropriate oxygen level of 2 mg/1,

3) additional indicators of nutrient enrichment as outlined in the section on perspectives,

4) new literature or information obtained between the previous reviews (data circa 1984) and this
document.

The matrix is presented in Table 11. Each estuary or coastal area is listed along the left margin
with its code which is keyed to a map in Figures 19-23. (More detailed names of each estuary
and/or other coding options are listed in Tables 9 and 10.) All water bodies within an estuary are
included in the assessment for the estuary. An indicator of nutrient enrichment may affect only part
of the estuary and may not be representative of the whole estuary. The status of indicators,
however, shown in the matrix may target part of the estuary rather than summarize data for the
whole basin. For example, low dissolved oxygen levels may be present in a secondary bay but not
in the primary bay. The status for that estuary under the heading of "Oxygen Depletion" would
indicate the presence of that indicator.

Across the top of the matrix are several indicators of nutrient enrichment as outlined earlier in the
"Perspectives" section. The categories are broad, because there is usually not sufficient detail
within any single water body to provide a status for all indicators. Other categories not listed may
be detailed in the text of an individual estuary.
j,
The codes chosen to indicate the status of an estuary with regards to a particular indicator are:

Y - Yes, there is evidence of the particular indicator in the estuary, or a sub-unit of the estuary.

P - There are indications of a potential problem with regards to the indicator but no strong support
from long-term data sets; some indicators that the estuary, or a sub-unit of the estuary, may be on
the brink of water quality problems.

N - No, there is no evidence of the particular indicator in the estuary, or sub-unit of the estuary,
where the data or literature exist that would identify such indicators if present.
53
-------
? - There are insufficient data to determine whether an indicator of nutrient enrichment is present in
the estuary, or sub-unit of the estuary. Insufficiency of data includes lack of recent data (e.g.,
circa 1985 to present).

The last column of the matrix is a summary of the previous indicators. This column, coded the
same as the others, indicates whether there is a problem with regards to the condition of the estuary
based on the indicators of nutrient enrichment as defined earlier. The categories are:

Y - Yes, there is a problem in estuarine condition due to nutrient enrichment

P - There is a potential problem, no real data but some indicators that the estuary, or a sub-unit of
the estuary, may be on the brink of water quality problems.

N - No, there is not a problem.

? - There are insufficient data to make a determination, but limited data may support a tentative
conclusion of Yes, No or Potential.

Few data sets within the Gulf of Mexico study area are temporally or spatially adequate to draw
definitive conclusions on the various indicators of nutrient enrichment (notable exceptions are
detailed in the appropriate sections). The results of literature and data searches are synthesized for
each estuarine area. The data and/or information are assumed to be of uniform quality. The details
of any estuary are provided in the subsequent area-by-area descriptions where citations to
literature, data bases, or individuals are given.

The matrix was developed from the available literature and analyzed data. A more thorough
knowledge of the conditions or status of any of the estuaries may reside with several authorities in
any area. A single individual, however, reviewed all literature for all estuariess as a basis for the
categorizations. The classifications of each estuary by indicators of nutrient enrichment were
treated as uniformly as possible based upon the synthesis of similar types of information. As
additional data or information become available, the matrix should be revised. A graphic
representation of three indicator categories and the summary for the estuarine areas are shown in
Figures 24-27.

Area-by-area descriptions follow the status matrix. Literature citations specific to an estuary are
listed within each estuary. General references which cover an entire state, or sub-unit such as the
eastern Gulf of Mexico, are not repeated within each area description but are listed at the end of the
general introduction for the state and before the beginning of the area-by-area descriptions.
Parameter units are presented as given in the literature source. Equivalents and conversion tables
are listed in Appendix A, along with definitions of terms. Information concerning data bases and
individuals familiar with particular geographic areas or issues are provided in Appendices B and C.
Bibliographies are located in Appendix D.
54
-------

li
pa
. £-3
'i?
c -a *2
O O •*-» CO
C S OJ
U ^ 00
'C* C C
fi o §
55 I U
00
o
•a
CQ co
C4 ^
§ §
1 S
Z
en M

S CO g
h °° 2
^11
S o
z u

Area Name

(U
•o
o

Whitewater Bay

Big Lostman's Bay

o
ti

Chatham Bay

<— i
ti

>-(

4«l
><"

I
^

Caloosahatchee River

Charlotte Harbor

en
ti

Sarasota Bay

•^
fi

Tampa Bay

•o
ti

>-<

ft-
Florida Inner Shelf (S

v>
ti

&
>->

i
>

I
^

Crystal River/Bay

\o
ti

Withlacoochee River

r-
ti

Waccasassa Bay

00
ti

1
*

Suwanee River

o\
ti

i
>«

a
«8
Deadmans Bay/Steinh

o
ti

>-i

Aucilla River

T-H
ti

>-<

Apalachee Bay

CN
ti

>-r

Ochlockonee Bay

en
ti

St. George Sound

en
ti

>->

1-7-

Apalachicola Bay

•*
ti

03
Inner Shelf (Panhandl

S
ti

>-!

i
>H"

I
^

5?
PQ
CO
oo

•o
ti

1
>;

Choctawhatchee Bay

C)
ti

Pensacola Bay

r~-
li
i
o.
>^

i
>H"

>«

5?
PQ
1

f°
ti
.S
6
>H"

PQ
1

Alabama Inner Shelf

^"
•

•o
East Mississippi Soun

«N
i
a

K*1

Mississippi Sound

Pascagoula Bay

en
6

>-
o-

•rf
3

f>
z"

cd
CO
5

'O
6

g
>*"

>H
**

>
c~:

"i
Mississippi Inner She

o
55
-------
J

00
o w
.~+ G
||
w «
.H ^>
^<
«J 1
O 0 o «
^ H 00 O C
&£:ll 1
|j» S -0 "§ .oi
** 'I • |
&1 yj
'S a S
u c3 oo
•5 § §
£ S3 fi

00
o
•a
2 oo
QJ ^
'S CJ
CO M
S M •
c |1
*^ CO 5?
•PI
5 U
2

Area Name
"I
CJ

Pearl River

S
c

Lake Pontchartrain

"S
;s!
C--

^
C^^

Louisiana Inner Shell

• i
6

Lake Borgne

c—

TJ
e
3
Breton/Chandeleur S(

Mississippi River

SH
K"

Barataria Bay

o
6

cu
^
2"

^
*^-i

Terrebonne Bay

<-l
6

OJ
m
9
•a
u

<-<
6

s
r
£
2
.s
c
OH"

^
**

k<
Atchafalaya Bay/Rivt

1-
1
'

Galveston Bay

r~
6

Brazos River

oo
6

East Matagorda Bay

o\
6

Colorado River

o
6

o>
!>•

Matagorda Bay

>-c
6

O.
i~..

San Antonio Bay

C-4
6

>-i

Aransas Bay

en
6

m
•a
6
Cfl
I
u

rj-
6

rt
m
c

>/•>
6

Laguna Madre

\o
6

&*"1

11
0)
1
I
T-H
VO
CD

>-i

-•

^
e
'

Texas Inner Shelf

t~
6
56
-------
!
•r»
&
to
3
57
-------
•s
58
-------
59
-------

<4-l
03
Oro
•t->

i CO
•8
•3^8
0^73
«n
cs
oo

ffi
60
-------
61
-------
62
-------
UPDATED SUMMARY OF STATUS AND TRENDS IN
INDICATORS OF NUTRIENT ENRICHMENT
FLORIDA

The length (770 statute miles) and biological diversity of the Florida Gulf coast exceed those of any
ouTer Gulf state (McNulty et al, 1972). The climate varies from subtropical to temperate Tidal
swamps and marshes fringe the coast and submerged vegetation covers the seabed of most
shallow-water bottoms. The mangrove swamps of the southern and central coasts are gradually
replaced by tidal marshes north of Cedar Key (Figure Fl) (McNulty et al., 1972).

The activities which impact Florida's estuaries are many (Estevez et al, 1984). The Port of Tampa
is the seventh largest port in the U.S. and largest on Florida's west coast. The impacts of maritime
transportation and industry include dredge and fill activities, retention, structure failure, long-term
overall effects of increased turbidity, ^suspension of contaminants, and filling of intertidal areas.
Fisheries declines have been attributed to pollution, overfishing and habitat loss. Other habitat
alterations result from dredging activities for fill material, either sand or oyster shell, and thermal
effluents from power generating facilities.

Several estuarine areas of Florida are receiving major flows of pollutants (Figure F2) (McNulty et
al 1972) Industrial pollution from wood processing and phosphate processing plants are
prevalent dong the western panhandle and southwest Florida coasts, respectively. Activities from
phosphate extraction are expected to increase in Manatee and Sarasota Counties and may begin near
Charlotte Harbor (Estevez et al., 1984). The 1972 (McNulty et al, 1972) status outlined high
levels of domestic pollution in Tampa Bay, eutrophication, increased primary production and algal
growth decreased species richness of mollusks, and evidence of eutrophication in Boca Ciega
Bay The Fenholloway River carries heavy loads of paper mill wastes to the Gulf at Apalachee
Bav The St Marks River is subject to domestic sewage pollution and occasional oil spills.
Industrial pollutants have altered the water quality and biota of St. Joseph Bay. Fish kills and
other evidence of pollution have been documented in Pensacola and Escambia Bays, and the upper
section of Escambia Bay is in a state of accelerated eutrophication. Heavy pollution has been
documented in the northern part of Perdido Bay (McNulty et al, 1972). Several of the Florida
embayments have recorded fish kills attributed to low oxygen levels, eutrophication or nutrients
(Table Fl).

The 1988 Florida Water Quality Inventory for EPA 305(b) reporting requirements (Hand et al,
1988a-o) were particularly helpful in assessing the status of the water quality of Florida
embayments. Where not available, the assessments provided in Windsor (1985) were used; these
were based on the Hand and Jackman (1984) reports.
GENERAL REFERENCES: FLORIDA

ASIWPCA (1984)
Basta and Bower (1985)
Burrage (1989)
Culliton and Blackwell (1989)
Delfino (1989)
Ehler and Basta (1985)
EPA (1974, 1978)
Femald (1981)
Flor. Bd. of Conservation (1966, 1975)
Friedemann and Hand (1989)
Handera/. (1988o)
Jones etal (1973)
Keys(1975)
Mahadevan et al. (1984)
Main etal. (1987)
McNulty etal (1972)
NOAA/EPA Team (1990)
Pechmann et al. (1986)
Steidinger and Joyce (1973)
63
-------
sand beaches and
low dunes on Gulf;
tidal marshes and
low pinelands an bays
Figure Fl. The major coastal types of the west coast of Florida (from McNulty et al, 1972).

Ten Thousand Islands Area

It is difficult to distinguish separate embayments along the extensive barrier island system of the
southwestern Florida coast. The area is generally referred to as the Ten Thousand Islands.
Various sources of literature divide the area into South and North Ten Thousand Islands. Within
these areas fall several designated water quality units: Whitewater Bay, Big Lostman's Bay
Catham Bay and River, and Rookery Bay. The area receives, drainage from the Florida
Everglades, Everglades National Park, Cypress National Preserve, and Corkscrew Swamp
Sanctuary (Figure F3). The construction of freshwater control structures, canals and channels has
significantly altered the landscape of the area. The first significant river north of this area is the
Caloosahatchee River which flows past Ft. Meyers and into San Carlos Bay.
64
-------
3 <
lift
?¥§

-------
Table Fl. Summary of NOAA Fish Kill Inventory Data for Florida (draft data base, 1991; J.A.
Lowe, personal communication; see section on Data Sources).
AREA Records
County per County
TEN THOUSAND ISLANDS
Monroe 11
ROOKERY BAY
Colu'er
93
CHARLOTTE HARBOR
Charlotte 18
Lee 22
SARASOTA
Sarasota
WACCASASSA
Levy
SUWANEE
Dixie
TAMPA
Hillsborough
Manatee
Pinellas
APALACHEE
Jefferson
Taylor
Wakulla
APALACfflCOLA
Franklin
Gulf
ST. ANDREW
Bay
CHOCTAWATCHEE
Walton
PENSACOLA
Okaloosa
Santa Rosa
13
7
0
30
7
25
0
6
0
7
10
11
13
17
30
Cause
Low DO
7
70
12
12
10
0
0
12
7
20
0
0
0
1
0
0
1
11
1
Cause Cause
Eutrophication Red Tide
0
13
0
4
0
0
0
3
0
0
0
0
0
0
0
0
0
0
5
0
0
0
0
0
0
0
0
0
0
0
0
,0
0
0
1
0
0
0
Cause
Nutrient
0
3
0
0
0
0
0
0
0
0
0
0
0
0
0
2
5
1
0
Cause
Unknown or
Unspecified
0
4
0
0
3
0
0
4
0
3
0
0
0
0
1
2
4
1
2
66
-------
Figure F3. Map of Everglades west coast area (adapted from Schomer and Drew, 1988).

F-9 Whitewater Bay

Whitewater Bay receives drainage from the Lower Everglades (Schomer and Drew, 1982), a broad
expanse of sawgrass marsh studded with occasional tree islands, or hummocks (Figure F4). A
definite fresh to brackish to marine environment has prevailed along the northeast/southwest axis
of the bay for the past 5000 years (Schomer and Drew, 1982). The timing of the wet and dry
seasons in Whitewater Bay, as reflected in minimum and maximum salinities, has been shown to
be approximately 3 mo out of phase with flow from the Tamiami Canal to the north. Extreme
losses to evapotranspiration often lead to salinities greater than in open sea water.

Population in the area is very low (<1000 inhabitants), and no sewage treatment facilities or
industries discharge their effluents into these waters (Windsor, 1985). No dissolved oxygen
violations were noted during 1982-1983 (Hand and Jackman, 1984, cited in Windsor, 1985), but
there are very few water quality data available. Water flow in the drainage basin is sluggish'and
typically low in dissolved oxygen, but this occurrence is considered to be a natural process
throughout most of the Everglades drainage basin (Windsor, 1985).
REFERENCES: F-9

Dragovich et al. (1961)
Finucane (1964)
Schomer and Drew (1982)
Williams etal (1990)
67
-------
Coastal Swamps
& Lagoons
Broad River/
Lostman's River

Drainage
Cape Sable
Figure F4. Map of lower Everglades physiographic zones (from Schomer and Drew, 1988).
F-10 Big Lostman's Bay

This area coincides with the North Ten Thousand Islands area (see Figure F4 in Section F-9), and
partially within the Everglades West Coast Basin 305(b) reporting area of Hand et al. (1988f). The
area is considered to be unpopulated and has no discharges from sewage treatment plants or
industry affecting the water quality. No dissolved oxygen violations were noted during 1982-1983
(Hand and Jackman, 1984, cited in Windsor, 1985), but there are limited water quality data. The
area between Rookery Bay and South Ten Thousand Islands was designated as good overall water
quality (limited 1970-1987 STORET data) (see Figure F5 in Section F-l 1).
REFERENCES: F-10

Dragovich et al (1961)
Finucane (1964)
Handera/. (1988f)
Schomer and Drew (1982)
68
-------
F-ll Chatham Bay/River

The Chatham River estuarine system lies within the Everglades National Park. Population is low
(<1000) and no industries or sewage treatment plants are present in the drainage basin. The area
north of Everglades National Park, however, is experiencing rapid growth characteristic of much
of southwest Florida.

The Rookery Bay area has been designated a National Estuarine Research Reserve and has been
the focus of comprehensive environmental and water quality monitoring studies, resulting in a land
use plan which called for an extensive preservation system. A baseline water quality monitoring
study began in 1980 and will be used to establish the characteristics of a nearly pristine estuary
(Florida Dept. of Natural Resources, program in progress, as cited in Delfino et al., 1984). Other
water quality studies are being performed in Naples Bay to determine the pollutant loadings to the
Bay from various land use categories during storm events to monitor changes occurring in the Bay
as a result of land use and sewage disposal practices.

This area coincides partially within the Everglades West Coast Basin 305(b) reporting area of Hand
et al (1988f). The basin has a very limited STORET water quality data set. The areas of Rookery
Bay and Naples Bay were designated as good overall water quality (1970-1987 STORET data)
(Figure F5), but the water quality of the Tamiami Canal and Gordon River which empty into
Naples Bay were rated as fair. Representative water quality data for Naples Bay and Estero Bay
are shown in Figures F6 and F7, respectively. The Hand et al. (1988f) report indicates that the
wastewater treatment plant for the City of Naples has been upgraded and is due to go entirely to
spray irrigation. Land use in the area, however, is scheduled for extensive water control structure
construction, and the potential to disturb the character and productivity of Rookery Bay, Naples
Bay and Faka Union Bay is great. The previous 305(b) report (Hand and Jackman, 1984)
indicated poor water quality for the Gordon River based on very low historic dissolved oxygen
values (Windsor, 1985). Windsor (1985) also indicated low dissolved oxygen levels in Naples
Bay, but had little water quality data available for a thorough analysis.

Work of Thayer et al. (1985) in Faka Union Bay has focused on the effects of excessive
freshwater inflow. During 1982, the salinity of the bay was lower than adjacent bays to the east
and west, and salinity changes in the bay in response to rainfall patterns were slower. There has
been a decrease in the extent of seagrasses in Faka Union Bay since the early 1970s (Carter et al.,
1973, cited in Thayer et al., 1985).
REFERENCES: F-ll

Dragovich et al. (1961)
Finucane (1964)
Sheridan (1992)

F-12 Caloosahatchee River
Thayer etal. (1985)
Williams etal. (1990)
The major surface water draining this area is the Caloosahatchee River which flows past Ft.
Meyers and into San Carlos Bay. The upper-end system is Lake Okeechobee. Flow in the
Caloosahatchee River has been altered since the late 1800s with locks and dams, and its basin is a
maze of canals and ditches (LaRose and McPherson, 1983). Land use in the basin is dominated by
rangeland with some agriculture, particularly in the upper basin.

Severe algal blooms occur periodically in the river and pose a particular threat to drinking water
supplies, and lush growth of aquatic plants limits light penetration and contributes to severe
oxygen depletion (LaRose and McPherson, 1983). An assessment of the Caloosahatchee River
(LaRose and McPherson, 1983) indicates that the contributions of nitrate plus nitrate,
69
-------
TRA^FFORD
BONITA SPRINGS
xSUNNILAND
&5 COCOHATCHEE RIVER CANAL
GOLDEN GATE
CANAL
4.55
HENDERSON CREEK
CANAL
BARRON RIVER v
CANAL
BIG

CYPRESS

SWAMP
EVERGLADES
CITY
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA
RIVERS/STREAMS LAKES/ESTUARIES

GOOD f~
--» 1X^15
FLORIDA TROPHIC
Figure F5. Everglades West Coast basin [from 305(b) report of Hand et al. (1988f)].
70
-------
DM
QIMVOMO 10NVh3Q N30AXO 0
X30NI OUOIfl

•S
X
•5

"1 ^>/'
B
I
S

X
X
a

i
R
,..
I
X
•8
g
*1
fi
it ;
a
£
s
X
E
8
eg
R
s _-- """
R
S 1. .1. .Jinn,..,
2
X
S
.g
si
s
* <^"
R "^
fi ,,,,., i,,.i
S
X
8
g
*0 {
3
s <:
H ^~~-
(9 in i mi
8
X
3
SK
$
R
•ft
s
P
d3UlS
MUOJOOO J. I/OH SrtHOHdSOHd

J
/
I

4
:
3
g
R
j*
R '
2
t
X
-3
-i '
B ^^
* xxX^
B
£ .....nil II
I
t
a
!g
R
•s
fi
•g I.-..I I.....
t
t
a
!| \
R /
* '^2''>'
•R —•
.g ,.,....., .,
t
S
-a
!|
R \
t. -<^L
s ^
.g ,...„....— ,.,.....
X
s
3
g
" ^>
If
S ^
.« 1. ,
83
3aru.va3dH3i"
JJJAIiOnONOO
71
-------
* a K s "a
XJWSM
i !
VINOHNV
g S 3 S S *

X3QNI DM
X30NI OUOIS

i s *' '«
•I
t
a
S
s
•s
c
P s s~~s~ "i~~~g
lift \1KU3HO
AUS83MQ
S S ^
d3WS TV03J
Van
3323
VON H3SOH1IN
I I 3 I » S
Vow ss IKIOJ.
Ictd MINI1VS
q q o q a

I i • I I ;
3 S
Hd
VOI1 008
S S 3 .
VON oa
5 S
1 1 1
S 3 X
nOd U0103

^^
_
<

\
* /
?• ^
«g -=CL
*i <"
: 7
•s
•*
1 i i - i i •
s
t
8
85
*g
•s
K
c
s s
JJ 30V1S
•z
X
3
ac
S0
S
K
s
R a s =
SJO MO1J
5 s s ;
72
-------
orthophosphate and total phosphorus from the basin and the river substantially exceeded input
from Lake Okeechobee, while concentrations of ammonia from the river and basin were quite small
compared to input from the lake. In most tributaries, concentrations of nitrogen and phosphorus
compounds were lower than those in the river.

The phosphorus concentrations of the Caloosahatchee River were investigated as a comparison to
the Peace River, located further north, and the adjacent Gulf of Mexico (Graham et al, 1954). The
phosphorus concentrations of the Caloosahatchee were higher than the nearshore Gulf waters, but
averaged five times less than the concentrations of the Peace River (see Figure F10 in Section F-
13).

The Caloosahatchee River from the Franklin locks at the town of Olga broadens over 30 miles into
a tidally influenced estuarine system. Major urban centers are not present in the upper basin, but
the cities of Fort Myers, North Fort Myers and Cape Coral are located on the estuarine portion of
the Caloosahatchee River.

According to the 305(b) report of Hand et al. (1988b), the water quality in the upper basin of the
Caloosahatchee River is rated good; however, animal waste products and agriculture area runoff
have been identified as the likely source of nutrient laden waters affecting some low dissolved
oxygen problems. The estuarine segment of the river and some of its tributaries have had
problems with elevated nutrient concentrations, particularly phosphorus, and with low Secchi disk
transparencies (Hand et al., 1988b). The most recent Intensive Survey (1987) revealed high
chlorophyll values. The overall water quality rating for the estuarine portion of the system is fair,
with several of the tributaries rated poor (Figure F8) (Hand et al., 1988b). Representative water
quality data from the lower reaches of the Crystal River are shown in Figure F9. The domestic
waste discharges in the estuary have either been eliminated or significantly upgraded (Fort Myers
wastewater treatment plant), and new wasteload allocations are being developed. However, the
area is highly developed, and nonpoint source pollution will continue to impact water quality
(Hand et al., 1988b). San Carlos Bay receives inflow from both the Caloosahatchee River to the
east and Charlotte Harbor from the north. Water quality in San Carlos Bay was rated fair in the
most recent 305(b) report of Hand et al. (1988c). They state that nutrient loading in San Carlos
Bay may be resulting from urban runoff in the Ft. Myers area of the lower Caloosahatchee River.
The only serious pollution problem in the basin was in Sanibel River (see Figure Fl 1 in Section F-
13) located on Sanibel Island at the mouth of Charlotte Harbor (but included in the section for the
estuarine segment of the Caloosahatchee River) (Hand et al., 1988c). The Sanibel River has
previously received domestic wastewater and runoff from the island's more developed areas.
Leachate from local wastewater treatment plants has been controlled, but stormwater runoff
remains a problem. Samples in the mid 1970s showed significant nutrient and dissolved oxygen
problems in the river; however, there are no recent data to verify the continued existence of this
problem (Hand et al., 1988c).

Often, red tides of Gymnodiniwn breve move from offshore waters (see Section F-15.1) into San
Carlos Bay (Finucane, 1964). A red tide caused by the toxic dinoflagellate, Gonyaulax. monilata,
was widespread along the west coast of Florida in August 1966 as well as within San Carlos and
Estero Bays (Williams and Ingle, 1972).
REFERENCES: F-12

Degrove (1980)
Dragovich et al. (1961)
Finucane (1964)
Gunter and Hall (1965)
Graham (1954)
Handera/. (1988b)
LaRose and McPherson (1983)
McPherson and LaRose (1982)
Post etal., Inc. (1984)
Williams and Ingle (1966)
Williams etal. (1990)
73
-------
\ X
13.1
MOORE
HAVEN
13.2
LAKE
lOKEECHOBEE
\ 13.3'
CALOOSAHATCHEE RIVER
03090205
117
SAN CARLOS BAY
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA

RIVERS/STREAMS LAKES/ESTUARIES
r
FAIR

POOR
UNKNOWN [_
EPA WATER .... FLORIDA TROPHIC
QUALITY INDEX """ STATE INDEX
Fla.
Map Location
Figure F8. Caloosahatchee River basin [from 305(b) report of Hand et al. (1988b)].

74
-------
S 3 S 3 S
VOW N300M1IN

^~~~1

s 1 s s s
VOW SS TViOi
1 I § 8
idd AllNRVS
AllNriWTV
3 3 S S S
Hd
s a s 3
ooa
S S 3 S S S
Von oa
I
viNoniw
s a s
X30NI DM

~\^

•I
•1
2
85
ag
f
X
B
.g „ .,,..,....
•X
3
2
85
sg
•P!
S •
B
£
-»
-I
-3
•85
^sg
*
a
•s
.«
Noaava oiNwoyo j. QNvnaa ^Qa^XQ a
3831
TUHdOSOIHO
§111:
3 5 5 S
Van snaoHdsoHd
75
-------
F-13 Charlotte Harbor/Peace/Myakka Rivers

Charlotte Harbor is a major embayment which receives inflow from two main tributaries: the Peace
and Myakka Rivers, both of which have been altered to control stream flow. Both are polluted to
some degree from pastureland, citrus groves and cultivated ground [Taylor, 1974(1975)]; in
addition, the Peace River traverses a large area containing phosphate strip mines. Until the 1980s
the area was not heavily developed, but rapid growth has occurred since then. Little historic data is
available for this estuarine basin, but several studies were in progress in the mid-1980s as outlined
by Delfino et al. (1984). The studies focus on three areas: the impact of land development on
water quality, the distribution of hydrocarbons in the sediments, and water quality problems related
to the influx of nutrients and other constituents from tributaries.

The nearshore habitats of the Charlotte Harbor area have been lost to filling and stabilization for
housing and commercial development, including construction of extensive finger fill canal systems
(Estevez et aL, 1984), and other marshes have been impounded for mosquito or urban runoff
control and creation and maintenance of navigation channels. Dredging for fill material as oyster
shell was at one time a large industry in the Charlotte Harbor area. The number of shell dredging
leases declined sharply by the mid 1970s, and current regulations limit the leases and dredging
activities (Estevez etal, 1984).

Water quality studies in Charlotte Harbor have emphasized the influx of nutrients, particularly
phosphates, from the drainage basin. The major source of phosphate is the Peace River where
levels are influenced by mining activities upstream. The impact of the phosphate discharges was
studied by Harriss et al. (1972) [cited in Delfino et al. (1984)] who found that the phosphate waste
discharges, in combination with domestic wastes, were causing eutrophic conditions to occur in
certain areas of the Harbor. Fraser and Wilcox (1981) [cited in Delfino et al. (1984)] noted
seasonal pulses in nutrients transported by tributaries into the Harbor and found that the wet
summer season provided the highest loads of phosphate and nitrate compared to other seasons.
Plankton productivity responded directly to the nutrient pulses, with the highest productivity
occurring near the tributary mouths and then decreasing towards the mouth of the Harbor. Similar
results were found in an investigation by Graham et al. (1954) to determine whether the outflow of
the Peace River caused any enrichment of the local Gulf of Mexico waters. The system is believed
to be nitrogen-limited as opposed to phosphorus- because of the high phosphate content of the
freshwater inflow [Taylor, 1974(1975)]. The concentrations of phosphorus in the Peace River are
extremely high as compared with those in the Caloosahatchee River, Charlotte Harbor, or in the
open Gulf (Figure F10) (Graham et al., 1954). In this study, however, the high concentrations in
the Peace River were not reflected in the concentrations in Charlotte Harbor, with one exception.

Radium-226 and radon-222 activities are greater in the estuarine waters of northern Charlotte
Harbor and the lower tidal Peace and Myakka Rivers than in either the freshwater reaches of the
rivers or waters of the lower estuary and the Gulf of Mexico (Miller et aL, 1990). The geologic
strata for the rivers is phosphate rich, and phosphate mining and processing can expose these
deposits and may accelerate transport of suspended radium-226 in streams (Upchurch et al., 1985,
cited in Miller et al., 1990). The highest radium-226 activities in upper Charlotte Harbor occur in
brackish, nearshore waters. Radium-226 in oyster shells and radon-222 in water confirm that the
tidal Myakka and Peace Rivers and their embayments are a major source of radium-226. Inflow of
artesian ground water that is high in radium-226 appears to be the dominant source of radium-226
in upper Charlotte Harbor and the lower reaches of the Peace and Myakka Rivers.

In the most recent 305(b) report (Hand et al., 1988c), Charlotte Harbor and the associated estuaries
between it and the Caloosahatchee River (see Section F-12) compose an area of critical concern due
to its rapidly expanding population with the potential for severe damage. Water quality is generally
good (Figure Fll), although nutrient levels, particularly phosphorus, are elevated, and Secchi disk
readings are somewhat low in areas (Figure F12). Upper Charlotte Harbor is probably impacted to
76
-------
5
•I
•8
ID
•s
•s
I
I
s
on
77
-------
MYAKKA
QPEACE RIVER

>
GASPARILLA
ISLAND ~"~~V?
•:^.,:' SLOUGH
'•'•v CANALN
r^
[PINE I
\ISLAND.
ALLIGATOR CR.
Fla.
CAPTIVA
ISLAND"
Map Location
SAN CARLOS
BAY
CALOOSAHATCHEE RIVER
SANIBEL RIVER
SANIBEL
ISLAND
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA

RIVERS/STREAMS LAKES/ESTUARIES

-1 ' >—* GOOD PI I I I
&.'.-.:•.:'.:.'.'.•.:'.'.: FAIR
POOR
UNKNOWN*
EPA WATER FLORIDA TROPHIC
QUALITY INDEX fl"a STATE INDEX
Figure Fl 1. Charlotte Harbor basin [from 305(b) report of Hand et al. (1988c)].
78
-------
s s s s
X J.VSOO
SS88
-
8 SaSSS"2

" X3<3NI OM
1 ONVM30 N39.OCO 0
\
TUHdOMOIHO
wa°JnoDJ
d d d d d
SrtHOHdSOHd
\
« n * a o g o g o oooop o

Vow NMoW nVo^ssnvloi0 8 idd JUINHVS" S
1/SH 008
S 3 S 3
vew oa
S 2 «
uiaiaani
79
-------
some degree by urbanization at the mouth of the Peace River. Because of the rapid urbanization in
the basin, a comprehensive environmental assessment of the area is being conducted by the U.S.
Geological Survey.

The long-term (1976-1984) water quality characteristics in upper Charlotte Harbor were examined
for evidence of temporal trends (Eraser, 1986). The data suggested an increasing trend for
temperature and orthophosphate and a decreasing trend for near-surface dissolved oxygen (Figure
F13). The temperature trend was related to low winter temperatures early in the period. The
orthophosphate trend was related to a major source, the Peace River. The source of the dissolved
oxygen trend was not identified, but a relation with primary producers was likely. Evidence of a
trend was not found for total phosphate, reactive silica, and organic nitrogen (Figure F14). Nitrate
plus nitrite and ammonia data were not sufficient for analysis.

Often, red tides of Gymnodinium breve move from offshore waters (see Section F-15.1) into
Charlotte Harbor (Finucane, 1964). A compilation by Estevez et al. (1984) counted 24 red tides in
the Charlotte Harbor region since 1900 (along with other natural "catastrophes" such as hurricanes
and freezes).
REFERENCES: F-13

Dragovich et al. (1961)
Dragovich et al. (1966)
Estevez etal. (1984)
Finucane (1964)
Fraser (1985)
Graham (1954)

F-14 Sarasota Bay
Handera/.(1988c)
Huang and Goodell (1967)
Miller etal. (1990)
Taylor (1974/75)
Williams and Ingle (1966)
Williams etal. (1990)
Sarasota Bay connects with the Gulf of Mexico through three tidal passes and is also connected
with Tampa Bay through Anna Maria Sound to the north which receives the inflow of the Manatee
River. Little Sarasota Bay and Lemon Bay are connected to Sarasota Bay on the southern end
through tidal passes. Three freshwater streams contribute to the freshwater inflow to Sarasota
Bay. To various degrees, all tributaries to Sarasota Bay have been channelized or otherwise
modified to facilitate stormwater drainage (Flannery, 1989). Because Sarasota Bay does not
possess any significant water flow-through characteristics and net tidal transport through the
system is minimal, any pollutants entering the Bay will have relatively long residence times prior to
eventually being flushed out into the Gulf of Mexico (Delfino et al., 1984),

The Sarasota Bay area is experiencing many of the growth-related problems that are occurring
elsewhere in the region, although most of its development having adverse environmental impact
has occurred only in the last 50 years (Estevez and Merriam, 1989). The barrier islands are
completely developed, and nearly the entire upland watershed is also developed. Most
development is residential, light commercial and tourist with no heavy industry; percentage of
agricultural land is low and decreasing due to urbanization. Direct and indirect effects of dredging
and filling have not been evaluated with respect to water quality but are considered serious (Estevez
and Merriam, 1989). The bay supports an extensive recreational industry and is showing signs of
overuse (Estevez and Merriam, 1989). Sarasota Bay was identified in the National Estuarine
Program for priority consideration as a national estuary (Hand et al., 1988i) in 1987 and was
designated by the U.S. EPA as part of the National Estuary Program in July 1988.

A series of comprehensive studies were conducted to assess the environmental status of the Bay
[Tiffany (1980) cited in Delfino et al. (1984)]. Turbidity was suggested as being responsible for
the decline in the seagrass community, while biological diversity indices indicated that Sarasota
80
-------
10
cc
.111
> rr

00 7
CO _J
co =J
OS

*™ O
1976 1977 1978 1979 1980 1981
s

1 ' YEAR
1982 1983
Z t
6

(£ -,
in '

0.6
tc 0.5
uj
tu
CC,0.4
il .
^™* "j 0.2
,o I
So..

. 0.0
1976 1977 1978 1979 1980 1981 1962

YEAR
1983
1976 1977 1978 1979 1980 1981 1982 1983
Figure F13. Three-month moving average for near-surface dissolved oxygen (upper panel), near-
bottom dissolved oxygen (middle panel, and near-surface orthophosphate, as P
(lower panel) for upper Charlotte Harbor (from Fraser, 1986).
81
-------
IU 0.6

Lit
en

I!0'4

5*1
0.2
0.0
1976 1977 1978 1979 I98O I9SI 1982 1983
2.5
2.0
<
Og 1.0
0.5
0.0
1976 1977 1978 1979 1980 1981 1982 1983
2.0
-5j 1.5
s
z to
o!'-°

IS
C3 _|
CC -1
01
Z0.5
OX)
1980
1983
Figure F14. Average monthly near-surface and near-bottom total phosphate concentration, as P

(upper panel), average monthly near-surface and near-bottom reactive silica

concentration, as Si (middle panel), and three-month moving average for near-surface

organic nitrogen, as N (lower panel) for upper Charlotte Harbor (from Fraser, 1986).
82
-------
Bay is a moderately stressed ecosystem. High zinc concentrations were found in organisms from
the Bay and indicated an anthropogenic influence on the biota. A variety of water quality
parameters (including nutrients, turbidity and dissolved oxygen) were measured on a monthly
basis since 1960 (Larkin and Tiffany, 1984) [also cited in Delfino et al (1984)].

Water quality data are available for the tributaries to Sarasota Bay including the two largest
drainage systems, Whitaker Bayou and Phillippi Creek (Table F2 in Section F-15) (Flannery,
1989). Nutrient concentrations are very high near the mouth of Whitaker Bayou due to discharges
from the City of Sarasota's wastewater treatment plant. The plant discharges an average of 8.3
mgd of secondarily treated effluent during 1987, but all discharges to the bayou were scheduled to
cease in late 1988. The City's wastewater treatment plant is overloaded due to rapid development
(Hand el al., 19881) and has a long history of enforcement actions. Phillippi Creek, which is
highly channelized and drains into Little Sarasota Bay, similarly receives domestic wastewater
discharges in addition to stormwater runoff. Nutrient concentrations at one station in the creek,
particularly for nitrogen species, were high (Table F2 in Section F-15), with greater concentrations
found upstream closer to point source discharges. Agricultural and urban stormwater runoff is a
problem in the basin (Hand et al., 1988i), and many of the streams running through developed
areas are affected by septic tanks. Tributaries and direct runoff supply the bay systems with heavy
nutrient loading. Seagrass beds are declining in upper Sarasota Bay, especially the eastern side,
presumably because high algal concentrations are reducing transparency (Hand et al., 1988i).
Runoff from the Bradenton area and the Manatee County wastewater treatment plant sprayfields (a
flower farm) provide further nutrient loading.

According to the most recent 305(b) report (Hand et al., 1988i), the water quality of the bays is
rated good to fair; that of the tributaries, rated fair to poor (Whitaker Bayou) (Figure F15).
Representative water quality data for Sarasota Bay are shown in Figure F16. Nearly all the
streams which enter the Sarasota Bay estuarine system have dissolved oxygen problems, similar to
other southern Florida areas. Sarasota Bay, Little Sarasota Bay (Figure F17) and Lemon Bay have
been declared Outstanding Florida Waters, which should afford them greater protection from both
point source and nonpoint source pollution. However, all are threatened by increased boat traffic,
landscape alterations, and replacement of mangroves by lawns and drainage canals. Lemon Bay
and Little Sarasota Bay have the most pronounced degrading trends (Hand et al., 1988i).
Incomplete nutrient and other data suggest a general trend of improvement and a decline in salinity
which has been most evident along the mainland shore (Figure F15). The decline in salinity has
been attributed to urban stormwater runoff (Heyl and Dixon, 1988, cited in Estevez and Merriam,
1989). The water quality rating in the Hand et al. (1988i) report was downgraded from that of the
Hand and Jackman (1984) assessment given in Windsor (1985).

Between 1948 and 1979, there was a 54 % decrease in seagrass cover along the eastern bay; a 65
% loss around New Pass; and an 83 % loss around Whitaker Bayou (Sauers and Patten, 1981,
cited in Estevez and Merriam, 1989). Baywide losses are estimated at 20 to 30 % (Steidinger and
Phillips, 1988, cited in Estevez and Merriam, 1989). Causes of these losses are not definitely
known, but turbidity from dredging and organic enrichment are suspected (Estevez and Merriam,
1989). Loss of suitable habitat indirectly effects secondary production (e.g., scallop, oyster and
hard clam populations; blue crab, bait shrimp and mullet landings, red drum and snook stocks).

Often, red tides of Gymnodinium breve move from offshore waters (see Section F-15.1) into
Sarasota Bay (e.g., 1971) and can cause fish kills (Finucane, 1964; Steidinger, 1973). A red tide
caused by the toxic dinoflagellate, Gonyaulax monilata, was widespread along the west coast in
August 1966 as well as within Sarasota Bay and adjacent waters (Williams and Ingle, 1972).
83
-------
TAMPA BAY
BRADENTON
1 O
SARASOTA
BAY
LONGBOAT
KEY
SARASOTA WWTP

WHITAKER
SIESTA
KEY
LITTLE SARASOTA
BAY
GULF OF
MEXICO
Hap Location
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA

RIVERS/STREAMS LAKES/ESTUARIES

H 1 1 1- GOOD I I I I • I
;£££%££& FAIR

t POOR
UNKNOWN^
EPA WATER
QUALITY INDEX
AND
FLORIDA TROPHIC
STATE INDEX
LEMON BAY.
CHARLOTTE
HARBOR
Figure F15. Sarasota Bay basin [from 305(b) report of Hand et al. (1988i)].
84
-------
I/an
1 s s I °
Vsn ss 1VJ.01
p q q q o
s a a 5 s
Idd
I i. i i
AiiNrw>nv
3 s :
3 S 2 5 3
Vsn oos
3 3 S S
Von OQ
oo
oo
SB
s
aoioa
s 2 s 3
H IH003S
JJ 3JW1S
£

h«3

•K,

•a
S I
VINOMW5
•N08MV3
N3OAXO 0
X3QN1 OUOI8
S S S S
Van snaoHdsoHd
,85
-------
s
•!
8

S
B
R
B
VON N3SOailM
s s a s -
Vsn ss ivioi
• S — * *" £
' ldd"AlJNnVS~
! S
Van ooa
3 3
3 S S
VOM Od
00
oo
o\
S S R
03d HOTOO
: i : s s
VI IH003S
S S 3 J
* iVSM
8 g I S 8
R a x s
• X30NI DM

aavo o^wouo
s
•X
•3
'!§
B
: i
• 82-'
L aNvrtaa ^Ga^xo a
X3QNI 3UQ18
naojnoo
HHOjnoo i Van snaoHdsoHd
86
-------
REFERENCES: F-14

Buck and Pierce (1989)
Dragovich et al. (1961)
Estevez (1989)
Finucane (1964)
Flanneiy (1989)
Graham (1954)
Handera/. (19881)
Lewis (1989)
Williams and Ingle (1966)
F-15 Tampa/Old Tampa/Hillsborough Bays

Tampa Bay is the largest of Florida's estuaries. It is subdivided into a number of distinct water
bodies including Old Tampa Bay, Hillsborough Bay, Middle and Lower Tampa Bay, Terra Ceia
Bay, and Boca Ciega Bay (Figure F18). Major surface waters that flow into the bay include the
Alafia, Hillsborough, Manatee, Braden and Palm Rivers, and Booker, Bullfrog, and Sweetwater
Creeks (Figures F18 and F19); small tributaries and tidal creeks are additional important
components of the Tampa Bay estuarine drainage area. Tampa Bay and its contiguous water
bodies have been the site of numerous studies.
28*i6
82*46
• e • 10 it KitpuiT«na

SUBDIVISIONS OF TAMPA BAY

1 OLD TAMPA BAY 6 BOCA CIEQA BAY N
2 HILL8BOROUQH BAY 8 TERRA CEIA BAY

3 MIDDLE TAMPA BAY 7 MANATEE RIVER
14 LOWER TAMPA BAY
rT
28*00
/^
27*30'-
2*18'
28*18'
427*4B'
82*30'
82*19'
Figure F18. Subdivisions of Tampa Bay (from Clark and MacAuley, 1989).
87
-------
700
Tampa Bay Major Tributaries
Average Yearly Streamflow and Withdrawals
Strearnflow
After Withdrawals
Withdrawals
Figure F19. Average yearly streamflow and withdrawals from eight tributaries to Tampa Bay
' (fromFlannery, 1989).

Many activities impact the water quality, of this system. The estuary is urbanized, and development
activities have substantially altered natural processes (Lewis and Estevez, 1988). Water quality has
degraded in much of the bay because of the current discharge of treated sewage and industrial
wastes historical discharges of untreated or poorly treated wastes, and urban stprmwater
discharges. Population is expected to increase by 50 % per decade; continued expansion of the
Port of Tampa is expected (Lewis and Estevez, 1988).

Tampa Bay receives more domestic waste than other Florida Gulf coast areas (Figure F20, see also
Figure F2) For years, the Tampa Sewage Treatment Plant provided primary treatment and the
others secondary (Estevez el a/., 1984); the result has been a progressive eutrophication of
Hillsborough Bay. The reversal of these trends is documented below. Phosphate mineral
extraction and processing is a prevalent industrial activity in the Tampa Bay area. Studies of the
discharges indicated elevated levels of total phosphorus, fluorides and radionuchdes in the thermal
effluents- impacts to the fauna have been documented (several studies cited in Estevez et al, 1984).
Dredging for fill material, either as sand or as oyster shell, was at one time a large industry in the
Tampa Bay system. Oyster shell has been dredged from Hillsborough Bay for some time (Estevez
et al 1984) and impacts were seen as increased turbidity, and immediate species loss, density
88
-------
decline and biomass decrease (several studies cited in Estevez et al., 1984). Current regulations
limit the leases and dredging activities.

Water quality data for streams flowing to Tampa Bay is quite extensive and was summarized by
Flannery (1989). Overall, tributaries to Tampa Bay contain high levels of nutrients, both total
phosphorus and nitrogen species (Figure F21). Mean total phosphorus values listed in Table F2
ranged from 0.3 to 0.77 mg/1, with the exception of Alafia River and Delaney Creek with mean
values of 2.4 and 2.7 mg/l. For the remaining tributaries, phosphorus values were highest for
those impacted by urban runoff or point source discharges. The concentration of nitrogen species
in tributaries is important because primary production in Tampa Bay is primarily nitrogen limited.
20*16
82*46
28*00
27*46
27*30'-
- 27*46'
- J-27'30'
82*46
aa'ao'
82*16'
«> DOMESTIC DISCHARGE

H INDUSTRIAL DISCHARGE

Figure F20. Reported discharge sources, Tampa Bay area, 1980 (from Moon, 1985).
89
-------
pH
~N (MQ/U PTOTAL (UQ/L)
0.2 0.4 0.8 0,0 1.0 1.83 1.0 2.0 4.0 6.0
* _ ' • _ I _ i__i, _ i - 1 - •• •
HILL8BOROUQH RIVER
ALAFIA RIVER
MANATEE RIVER
LITTLE MANATEE RIVER
CHANNEL A
DOUBLE BRANCH CREEK
ROCKY CREEK
LAKE TARPON OUTFALL CANAL
TAMPA BYPASS CANAL
8WEETWATER CREEK
HILL8BOROUQH RIVER
ALAFIA RIVER
MANATEE RIVER
LITTLE MANATEE RIVER
CHANNEL A
DOUBLE BRANCH CREEK
ROCKY CREEK
LAKE TARPON OUTFALL CANAL
TAMPA BYPASS CANAL
SWEETWATER CREEK
6 0.2 0.4 0.8 O.e I.O 1.2 S.O 8.0 7.0 8.0
NH3-N NOROANIC •TOTAL DO (MO/U
(HQ/L)
(MO/L)
FLUORIDE MQ/L
HILLSBOROUQH RIVER
ALAFIA RIVER
MANATEE RIVER
LITTLE MANATEE RIVER
CHANNEL A
DOUBLE BRANCH CREEK
ROCKY CREEK
TAMPA BYPASS CANAL
SWEETWATER CREEK
1.0
2.0
9.0 10.0
TOTAL ORGANIC CARBON
MG/L
HILLSBOROUQH RIVER
ALAFIA RIVER
MANATEE RIVER
LITTLE MANATEE RIVER
CHANNEL A
DOUBLE BRANCH CREEK
ROCKY CREEK
TAMPA BYPASS CANAL
SWEETWATER CREEK 1
Figure F21 A. Conductance of selected streams entering Tampa Bay.
Figure F21B. Data for selected chemical parameters for streams entering Tampa Bay.
Figure F21C. Mean concentrations of fluoride and total organic carbon for streams entering
Tampa Bay (from Dooris and Dooris, 1985).
90
-------
Table F2. Mean concentrations of selected nutrients for nineteen tributaries to Tampa and Sarasota
Bays (from Flannery, 1989).
Tributary
Period
Total Total Organic NC>3+ NH3
P N N N02 N
Color BOD
Source
1.
2.
3.
4.
5.

7.
8.
9.

10.

11.
12.
13.
14.
15.
16.
17.
18.
19.
All
Booker Creek2
Allen Creek2
Alligator .Creek
Lake Tarpon
Double Branch
Creek3
Rocky Creek
(upper)
Sweetwater Creek3
Gandy Blvd. Ditch2
Hillsborough R.
(Fowler Ave.)
Hillsborough R.
(S.R. 585)
Tampa Bypass Canal
Delaney Creek3
Alafia River
Little Manatee R.
Manatee R. (upper)
Manatee R. (reser-
voir site 1)
Manatee R.3 (lower
zone 3)
Whitaker Bayou3
Phillippi Creek
'units expressed as
07/75-05/80
07/75-05/80
10/83-09/85
10/83-09/85

01/84-12/85

10/83-09/85
01/84-12/85
07/75-05/80
10/83^09/85

01/84-12/85
01/84-12/85
01/84-12/85
01/84-12/85
01/84-12/85
10/83-09/85

01/84-12/85
02/82-03/83
01/84-12/85
01/84-12/85
mg/1 except
ll 0.50
28-34 0.52
13 0.45
12

12
24
20
12

24
24
24
24
24
4

24
12
6-9
6-9
color
0.06

0.33

0.78
0.31
0.30
0.34

0.36
0.54
2.67
2.40
0.38
0.29

0.21
0.2D
1.53
0.97
2.40
2.40
1.36
0.65

1.19

1.27
1.33
0.76
1.06

1.17
1.50
24.10
1.87
1.32
0.44

0.91
1.43
6.14
2.98
2.10
1.80
0.93
0.47

0.98

0.67
0.89
0.66
0.66

0.93
1.19
4.00
0.49
0.60
0.34

0.71
1.28
2.37
1.20
0.16
0.45
0.29
0.09

0.06

0.47
0.19
0.24
0.37

0.11
0.11
9.70
1.30
0.63
0.04

0.10
0.11
0.24
1.03
0.14
0.22
0.14
0.09

0.14

0.13
0.25
0.40
0.04

0.13
0.20
11.30
0.08
0.09
0.05

0.10
0.04
3.53
0.75
—
55

. _
32

43
24
67
39
52
65

131
—
4.9
5.6
2.0
_

1.7

__.
1.7
5.0
m,^

1.8
3.4
5.1
0.08
1.3
1.1

2.5
1.8
Lopez & Giovannelli 1984
Lopez & Giovannelli 198'4
USGS 1986a, 1986b
USGS 1986a, 1986b

HEPC 1986

USGS 1986a, 1986b
HEPC 1986
Lopez & Giovannelli 1984
USGS 1986a, 1986b

HEPC 1986
HEPC 1986
HEPC 1986
HEPC 1986
HEPC 1986'
USGS 198 6a, 198 6b

Manatee Co. Urpubl. data
Manatee Co. & Camp, Dresser
& McKee, Inc. 1984
Sarasota Co. 1985, 1986
Sarasota Co. 1985, 1986
(Pt-Co units) . ~~~ ~~ ~
1Number of observations.
2Stormwater runoff samples, flow-weighted average.
3Brackish stations.

Table F3. Estimated average annual loading of selected nutrients for seven tributaries to Tampa

Bay. Asterisks denote results that should be viewed with caution, as they do not
account for substantial downstream nutrient additions (from Flannery, 1989).
AVERAGE ANNUAL LOADING (Kg/Year)
Tributary
Alafia River (14) and Lithia Springs
Hillsborough River (9)*
Manatee River (16)*
Little Manatee River (15)
Tanpa Bypass Canal (12)
Rocky Creek (.6)*
Lake Tarpon Outfall (4)
Total
P
9.2X105
1.7xl05
6.9xl04
7.9X104
2.7X104
2.6X104
2.2X103
Total
N
8.6X105
5.2X105
3.0X105
2.7X105
7.6X104
4.2X104
2.4X104
Organic
N
1.9X105
3.2X105
2.3X105
1.2X105
6.0X104
2.2X104
1.7X104
N02+
NO3
6.4X105
1.8X105
3.3X105
1.3X105
5.5X103
1.5X104
3.3X103
91
-------
With the exception of Delaney Creek, mean ammonia concentrations in Table F2 ranged from 0.05
to 0.40 mg/1, with the highest values reported from streams with point source discharges or large
urban runoff. Mean nitrate concentrations for the Mafia River (1.23 mg/1) and Delaney Creek (9.7
mg/1) were exceptionally high compared to other stations, which ranged 0.06-0.63 mg/1. Organic
nitrogen and total nitrogen values were also high in many of the same tributaries named above
(Table F2). The seven tributaries for which nutrient loading estimates were made (Flannery, 1989)
are listed in Table F3. In total, the seven tributaries listed are estimated to contribute an average of
1.95 X 105 kg/yr total nitrogen and 1.35 X 105 kg/yr total phosphorus to Tampa Bay (substantial
nutrient additions to the lower reaches of certain rivers not accounted for). These summed nutrient
loading values gives a N:P ratio of 1.6, indicating that tributary inflow to the bay is very
phosphorus enriched, much of which is due to the load of the Alafia River. The causes for these
high phosphorus loadings include leaching of phosphate beds, agricultural runoff and point source
discharges (Flannery, 1989).

Extensive data bases exist for Tampa Bay. A series of hydrographic surveys in Tampa Bay and
the adjacent Gulf of Mexico, over a several year period, were conducted by Saloman and Taylor
(1971a,b, 1972) and Saloman (1973,1974), primarily as a supplement to red tide investigations,
and provide an excellent historical baseline. Other data are collected by the Hillsborough County
Environmental Protection Commission (HCEPC), 1972-1987, (e.g., Boler, 1987), and many
reviews and reports are available. The material presented below is taken from the summary of
Lewis and Estevez (1988). Their review concentrated on water column chemical properties, rather
than sediment chemistry, largely because the latter largely corroborates trends and patterns depicted
by water quality data.

The general conclusions of Lewis and Estevez (1988) were that 1) Tampa Bay is not grossly
"polluted," certainly not beyond the point of rehabilitation; 2) parts of the bay are "cleaner" than
others for natural as well as cultural reasons; and 3) levels of some pollutants have been declining
over the past decade, while others have increased. A generalized scheme of water quality based on
ranked averaged values for total coliform bacteria, turbidity, chlorophyll a and organic or
biochemical oxygen demand is given in Figure F22. Water quality in the lower bay is generally
good to excellent, although the HCEPC documented a decline to poor in 1978 because of increased
turbidity caused by harbor deepening. In summary, general water quality is good to excellent for
much of Tampa Bay, declining in Old Tampa Bay, and undesirable in Hillsborough Bay. Terra
Ceia Bay has very good water quality and has recently been declared an Outstanding Florida Water
(Hand et al., 1988m). Development around this bay threatens it with increased runoff and
mangrove cutting; although there have been some enforcement cases which will deter the latter
(Hand et al., 1988m). The Pinellas County portion of Tampa Bay is also designated as an
Outstanding Florida Water to protect it from further degradation; however, under current law,
many of the existing discharges to the bay will be allowed to continue. Point sources throughout
the Tampa Bay system, especially sewage treatment plant effluents, greatly affect water quality but
improved effluents have resulted in improved water quality (Lewis and Estevez, 1988).

The water quality status of the components of Tampa Bay as reported in the 305(b) reports (Hand
et al., 1988m) summarizes water quality data from 1970-1987 (Figure F23), and general
categorizations follow those given above in Lewis and Estevez (1988). Degradation of the water
quality of Tampa Bay spurred intensive efforts over the last ten years (1975-1985) by local
scientists, environmental organizations, politicians and engineers to reverse the trends. Protective
management policies, legislation and regulation have been adopted. As a result, at least one
portion of the Bay, Hillsborough Bay, has shown some recovery (Hand et al., 1988m, and see
below). Data for the Boca Ciega Bay section were included in the Crystal River 305(b) report
(Hand et al., 1988e). Water quality for the bay was rated as fair and tributaries to it, as fair to poor
(see Figure F35 in Section F-16). Although only one station in Boca Ciega Bay has been
consistently sampled, it appears that the bay has extremely high phosphorus values and moderately
92
-------
high nitrogen and chlorophyll values (Figure F24). All of the tributaries in the area have pollution
problems usually with elevated coliform and nutrient concentrations and depressed dissolved
oxygen values. Two of these problems creeks, Long Bayou and the Gross Bayou Canal, have not
been sampled recently, but the point and nonpoint pollution sources have not changed significantly
since the last sampling. Bear Creek, which also receives urban drainage, appears to have organic
and metal toxicity problems (Hand et al., 1988e).
1978
1980
1982
1979
Figure F22. Trends in water quality for body contact in Tampa Bay since 1977 (HCEPC, 1978-
1983). E=excellent, G=good, F=fair, P=poor, U=undesirable (adapted from Lewis
and Estevez, 1988).
93
-------
DELANEY CR.
ECO GANNON. * '
-7 J-HILLSBOROUGH BAY
CLEARWATER
MCKAY,4r FEASTSIDE WWTP
CANAL
/, ST.
^PETERSBURG C
ALAFIA RIVER
- (GARDINIER)
\
\
5
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA
CEIA BAY

MANATEE RIVER
EPA WATER .... FLORIDA TROPHIC
QUALITY INDEX STATE INDEX
MULLET KEY
FT. DE SOTO
PARK JT;
GULF OF MEXICO
Figure F23. Tampa Bay basin [from 305(b) report of Hand et al. (1988m)].
94
-------
X3QNI SllOia
i 1 s
J.MV ADSM3/UO •
s a s s 3
AUSH3AIQ
TlAHdOSdlHO
I I 1 *
dials 1W3J
! | S •

wyojnoo j
i I r *
MKMITOO 1
Van

''
AUAUOnONOO
95
-------
MS? but Sso £ JhySplankton blooms that are more frequent and prolonged in Hillsborpugh

fiSdc'conditions in Ta5i£ Bay are natural or cultural in origin is not known, but aU cjramBttimaL
Snce Scales municipal wastes as the primary factor. Another measurement of the indirect
efS of SXngs £ the system are s'een in Secchi disk Art* which indicate a difference
by bay component as well as a general decline from 1974-1985 (Figure F25d)

Tamm Bav is considerably enriched in phosphate (Lewis and Estevez, 1988), but there has been a
SSSSta ^meanSS phosphate concentration in Hillsborough Bay and other bay segments
See 1972 (FSs K6 K8). The Alafia River is regarded as the primary source of phosphorus
SlsborouehBay (see above), but this does not explain elevated levels of the nutnent in Tampa
Bav Also Sil -Little Manatee River drains similar geological formations but concentrations and
foads of phS?hoSS are very much lower. Contributions by the phosphate industry have been
reduced by changes in technology and reduction of effluents.

SSta Swer bay? with little interannual or seasonal variability (Figure F29). Mean organic
Kteo&nco^nttaten in Hillsborough Bay was 'much greater, and so was temporal v^abiht^
Nitriie and nitrate concentrations were low and steady everywhere in the bay, except m
Korough Biy. Ammonia levels were variable in all zones. Seasonably was evident fix : total
inorgardc nitrogen, which decreased subsiantially after rainy seasons (Lewis and Estevez, 1988).

Fanning and Bell (1985, as cited in Lewis and Estevez, 1988) calculated a N:P ratio of 0.3 in 1971
aMl 3 M1981 and concluded lhal phyioplankton have been mttogen-luniied since 1972. They
Sulioned however^ againsl an interrelation thai nilrogen Inflation has deckned because lower
phSate levds indicate that plants may be consuming more of the available phosphate.

Both commercial and recreational fisheries are on a decline in Tampa Bay (Lewis and Estevez,
1988 T H^/esis of scallops and oysters have collapsed; shellfish landings peaked in 1956.
Finfish landings peaked in 1964 and have shown a steady decline (Figure F30).

Tt is estimated lhat 44 % of the original intertidal wetiands and 81 % of ihe original seagrass
meadow^oler tafcebay have. been destroyed either by dredging and filling or pollution (Lewis
Sfd L EsTevez 1988). Nutrienl enrichmeni from improperly ireaied sewage discharges would
cSntribute to toased phyloplanklon sianding slock in ihe water column and subsequent reduction
KwnweUinglighl ^growih of epiphytic algae on ihe leaves of macrophyles; both would
impact Ihe biomass of submerged macrophyles.
tides of
onium breve move from offshore waters (see Section F-15.1) mlo ihe
ay 0*agovich et al, 1963; Finucane, 1964; Steidinger, 1973) The red
o and caused locally limited fish kills. Larger red tides occurred in 1946-
1947, 1953-1954 and 1957 (Steidinger, 1973).
96
-------
OO
oo
oo
ON
OO
ON
2
en
w
***

I
•s s,
a IHOOBB HV1H
ff-if
fc« a o -Sk
V
V
K
/
\
V
s p
oo

< « U Q
-
1/OH 'Q3A1OGSIO MO1XO8 &nNln 33VdtinG
97
-------
«o- ss1 so' tt'2i'
Figure F29. Nutrient distributions (in mg/1) in Tampa Bay. A, orthophosphate, Sept. 1972; B,
ammonia, Dec. 1973; C, nitrate, Dec. 1972; D, organic-N, Dec. 1973 (from Lewis
and Estevez, 1988).
100
-------
q cq co I*-; <0 in
c> o o ci o'
(spuesnoijjj
AVQ/OM
l/Buj
-S
-S
• CM
CO
-8
— CM
r*
-00

-------
20-

19-

w 13
z
Finfiah
V
Figure F30. Tampa Bay commercial shellfish and finfish landings (from Lewis and Estevez,
1988).
As mentioned on page 48, improvements in sewage treatment and pollution abatement from
fertilizer processing plants has reduced the nutrient loadings and phosphorus concentrations in
Hillsborough Bay and its tributaries (Figure F31) (Johansson and Lewis, 1991). A time lag of
several years appears to exist between reduced nitrogen loading and the response of ambient
chlorophyll a concentrations in Hillsborough Bay (Figure F32). The substantial decrease of
chlorophyll a correlates with the loss of a planktonic filamentous blue-green alga, which prior to
1984 dominated the phytoplankton population from late summer to early winter (Figure F32).
Water column light transparency has also improved as measured by Secchi disk depth (Figure
F32). Modest seagrass recolonization was observed in 1984 in Middle Tampa Bay, just south of
Hillsborough Bay, and in 1985 in Hillsborough Bay proper. The new seagrass growth followed
the substantial decrease in chlorophyll a concentration and increase in water column light
penetration. Further, test plantings of the seagrass Halodule wrightii have been successful at
several locations in Hillsborough Bay (Figure F33). .
REFERENCES: F-15

Boler (1987)
Cardinale and Boler (1984)
Dauer(1984)
Dauer and Simon (1976)
Dennis etal. (1984)
Dooris andDooris (1985)
Doyle (1985)
Dragovich etal. (1961,1963,1966)
Drew et al. (in review)
Lewis and Estevez (1988)
Lindalletal. (1974)
Lopez and Giovannelli (1984)
McCoy and Bell (1985)
Moon (1985)
Robison (1985)
Saloman (1973,1974)
Saloman and Taylor (1968,1971a,b)
Saloman et al. (1964)
101
-------
^1974 1976 1978 1980 1982 1984 1986 1988 1990
1.5-
1.4-
1.3-
1.2-
1.1-
1-
0.9-
0.8-
0.7-
0.6-
0.5-
0.4-
0.3-
0.2-
0.1-
T 1 1 1 1 1 1 1 1 1 1 1 1 1 1 r
73 74 75 76 77 78 79 80 81 82 83 84 85 86 87 88 89 90
79 | 80 | 81 | 82 | 83 | 84 | 85 I 86 | 87 | 88 | 89
Figure F32. A, chlorophyll a concentrations in Hillsborough Bay; B, monthly concentrations of a
filamentous blue-green alga (Schizothrix calcicola sensu Drouet) in Hillsborough
Bay; C, Secchi disk depth in Hillsborough Bay (adapted from Johansson and Lewis,
1991).
103
-------
CO
E
400-
350-
300-
250-
200-
150-
100-
50-

™P
11

1987 1988 1989 1990
YEAR
Figure F33. Area coverage of Halodule wrightii test plantings in Hillsborough Bay (adapted
from Johansson and Lewis, 1991).
Estevez (1989)
Estevez and Merriam (1989)
Fanning and Bell (1985)
Fehring (1985)
Finucane (1964)
Finucane and Dragovich (1966)
Flannery (1989)
Graham (1954)
Handera/. (1988m)
Johansson and Lewis (1990)
Johansson etal. (1985)
Lewis (1989)
Santos and Simon (1980)
Simon (1974)
Steidinger (1973)
Steidinger and Gardiner (1985)
Taylor (1970)
Treat etal (1985)
Van Vleet (1985)
Weiss and Phillips (1985)
Williams and Ingle (1966)
Williams etal (1990)
Wolfe and Drew (1990)
Zieman and Zieman (1989)
F-15.1 Florida inner continental shelf (sw)

Examination of water quality along the Florida west coast has been conducted in conjunction with
monitoring of red tide blooms (Graham et a/., 1954; Dragovich et a/., 1961,1963). In the surface
water, there is a gradual decrease in phosphorus content with increase in distance from shore out to
a distance of 130 km (Graham et a/., 1954). At distances >24 km from the Florida west coast, the
concentration of total phosphorus in the surface water was usually below 0.25 tig-at/1; the
concentration of inorganic phosphorus usually below 0.1 u.g-at/1; and the amount of organic
phosphorus usually exceeded the inorganic (Figure F34) (Graham et al, 1954). Higher
concentrations of phosphate below 50 m water depth were attributed to upwelling features. There
was no indication that the contributions of the Peace River or the Caloosahatchee River contributed
significantly to the phosphorus content of nearshore coastal waters.
104
-------
0
O «
CN *^
II
Jao

ll
-§^
&=£
61
e ^
M
0000
vr CD cj
bfl »

ii
tio

O .0

C^ J3
-a W)

ll
en
Nl HidBQ
105
-------
A series of hydrographic surveys in Tampa Bay and the adjacent Gulf of Mexico, over a several
year period, were conducted by Saloman and Taylor (197la,b, 1972) and Saloman (1973,1974),
and supplement the data of Graham and Dragovich to provide an excellent historical baseline.
More recent studies (Danek and Lewbel, 1986) supplement these data with those from 1982-1984
for the southwest Florida shelf (Table F4), and represent typical oceanographic data.

The occurrence of Gymnodinium breve red tides have been scientifically documented along
Florida's west coast since 1946-1948, although records of similar outbreaks date back to 1844
(Steidinger and Joyce, 1973; Roberts, 1979). Substantial red tides caused by the unarmored
dinoflagellate occur periodically along the west coast of Florida. In addition to causing toxicity in
shellfish, G. breve directly kills large numbers offish and some marine invertebrates, produces a
highly irritating aerosol in coastal areas, and can rarely cause contact dermatitis (Quick and
Henderson, 1975). Red tides initiate in offshore waters where populations increase for
approximately two weeks, then the bloom in transported into inshore areas depending on
meteorologic and hydrologic conditions (Steidinger, 1975; Roberts, 1979). Offshore blooms can
either subside offshore, become established inshore and subside offshore, or continue offshore,
periodically seeding inshore areas (Steidinger, 1975). The progression of the September-
December 1976 red tide off southwest Florida supported the prediction of offshore initiation, and
support and maintenance with subsequent movement inshore. Red tides most commonly occur
between an area bounded by Tarpon Springs on the north and the Ten Thousand Islands area on
the south (Steidinger, 1973), but do occur along the Florida panhandle (see Section F-24.1). G.
breve is a coastal species rarely found in estuaries, but on occasion survives and prospers in bays
when recruitment from coastal waters coincides with higher than normal estuarine salinities and
favorable nutrient conditions. Dinoflagellates are known for their facility to thrive in nutrient-poor
water; dinoflagellate blooms often follow diatom blooms when inorganic macronutrients are less
readily available (Ryther, 1955). Correlation of heavy rainfall with initiation of red tides has
implicated chelated iron and naturally occurring chelators (e.g., humic substances) in land runoff
following rain (Steidinger, 1973). It has been suggested that red tide blooms occur every year in
coastal areas of the Gulf, and that with optimal conditions for development (calm seas, gentle
onshore winds, suitable salinity and temperature) the bloom will progress to a major outbreak.

Another toxic dinoflagellate, Gymnodinium monilata, was responsible for an extensive red tide
along the west coast of Florida in August 1966 (Williams arid Ingle, 1972). Bloom proportions,
discolored waters, and reports of dead marine life persisted through most of the month, but
dissipated in September. This red tide was prevalent in many of the adjacent bays.

Blooms of Trichodesmiwn are common along the Florida west coast and often cover the waters
surface with a thick scum that may wash onshore (Graham et al., 1954). Heavy blooms occur in
water containing very little inorganic phosphorus, but high concentrations of total phosphorus;
however, Trichodesmium is able to live in water of very low phosphate concentration and by its
drifting nature can accumulate a large volume of water and phosphorus content.
REFERENCES: F-15.1

Atwood (1981)
Churgin andHalminsta (1974)
Cons. Perm. Int. Exp. Mer (1936)
Danek and Lewbel (1986)
Dragovich and Kelly (1966)
Dragovich et al. (1961)
El-Sayed etal. (1972)
Fanning etal. (1982)
Finucane (1964)
Finucane and Dragovich (1966)
Freebergetal. (1979)'
Graham (1954)
Roberts (1979)
Saloman (1973,1974)
Saloman and Taylor (1968, 1971a,b)
Saloman et al. (1964)
Stuntz et al. (N.D.)
Thompson and Bane (1986a,b)
Thompson etal. (1988)
Williams and Ingle (1966)
106
-------
Table F4 Summary of near-bottom hydrographic and water chemistry characteristics from 5-yr
field study of southwestern Florida continental shelf (from Danek and Lewbel, 1986).
Station Salinity
Nuafcer Woo)
44
55
7
52
' 21
23
29 •
36
34.8
35.8
35.6
35.1
35.9
36.1
36.1
36.1
- 36.0
- 36.5
- 36.5
- 36.3
- 36.7
- 36.7
- 36.6
- 36.7
Toispemcure
CO
20.3 -
22.0 -
19.1 -
17.0 -
19.5 -
17.5 -
17.5 -
15.0 -
29.6
28.0
27.8
30.8
27.3
24.3
26.0
23.8
DO Transoiuivity T.ishr Fen.
(as/1) CJ) OX1)
5.6
5.9
7.7
6.3
6.1
6.1
6.4
4.4
- 10.1
- 9.3
-9.4
- 9.4
- 10.3
- 9.3
- 8.6
-6.6
77-100
.83-94
90-99
67-100
82-100
87-97
86-98
88-98
0.14-
0.11 -
0.08,-
0.11 -
0.06 -
0.06 -
0.07 -
0.06 -
0.38
0.19
0.17
1.13
0.68
0.11
0.19
0.08
Chi. a
to
ND
0.1 - 0.9
1C
0.5 - 1.0
0.3 - 0.6
0.1 - 0.6
4
• (uCDltt)
fD
1C
43.1 - 0.1
1C
j - tOr—sane as Chlorophyll a.
EO^—Mae as Chlorophyll *..
SiOj—sooe as Chlorophyll £.
F-16 Crystal Bay/River

The coastal basin from the north of Tampa Bay to Crystal Bay/River consists of many short
meandering streams, many of which have tidal characteristics (Hand et al., 1991). Three of the
rivers, Weekiwatchee, Homossasa and Crystal, have headwaters which are major Florida springs;
spring fed rivers are naturally low in dissolved oxygen and the bacteria levels are high: Crystal
River has been designated an Outstanding Florida Water (Hand et al., 1988e). There are two
streams in the central portion of the basin, the Pithlachascotee and Anclote Rivers, which are
affected by urban growth, especially in the lower segments (Hand et al., 1988e). The Crystial Bay
estuary drains an area of 1290 mi2 with an average freshwater inflow of 975 cfs (Windsor, 1985).
Population in the area is approximately 7000 inhabitants, with one sewage treatment plant, seven
hazardous waste treatment facilities, and two power plants in the basin (Windsor, 1985).

The springfed rivers in the northern basin generally have very good water quality, although some
have naturally low dissolved oxygen levels (Figure F35) (Hand et al., 1988e). Crystal River is
also subject to summertime algal blooms and mats in the King's Bay area possibly due to the
Crystal River wastewater treatment plant discharge and stormwater runoff. In addition, the
Homasassa River has some bacterial problems of unknown source. The lower Pithlachascotee has
some bacteria problems, presumably from septic tank drainage and/or New Port Richey runoff.

Few recent water quality data are available for Crystal Bay (Windsor, 1985). The main focus of
research activity in the Crystal River area has been the potential impacts of thermal and radiological
discharges from a power plant, and more recently the protection of manatees (Delfino et al., 1984).

REFERENCES: F-16 ' _

Handera/. (1988e)
107
-------
CRYSTAL RIVER TO ST. PETERSBURG BEACH BASIN J
AVERAGE OVERALL WATER QUALITY
1970-1987- STORET DATA

RIVERS/STREAMS LAKES/ESTUARIES
H—'—i—i- GOOD i rn i r
iv.'X-.' ••:•••;%•»••••••:• FAIR |^

POOR £

UNKNOWMF
EPA WATER
QUALITY INDEX
FLORIDA TROPHIC
STATE INDEX
CLEARWATER
CRYSTAL RIVER-
"HOMOSASSA RIVER
CHASSAHAWITZKA <.
RIVER \
WEEKIWATCHEE RIVER /
ITHLACHASCOT
RIVER
~4
LONG BAYOU

CROSS BAYOU CANAL
r; ST. PETERSBURG
1.6 V

BOCA CEIGA
• BAY
Figure F35. Crystal River to St. Petersburg Beach [from 305(b) report of Hand et al. (1988e)].
108
-------
F-17 Withlacoochee River

The Withlacoochee River estuary is located north of Crystal Bay/River The river is open to the
Gulf of Mexico. No additional information was available since the Windsor (1985) review, parts
of which are repeated here.

Population within the river basin is approximately 99,300, and land use is primarily agriculture in
Scupper reaches and forestry in the lower reaches There are two sewage raiment Plantvfive
hazardous waste treatment facilities and two textile plants. The report of Hand and Jackman
Q984) (cited in Windsor, 1985) stated that water quality in the basin is generally good with some
low dissolved oxygen, due primarily to natural conditions; the tributaries to the Withlacoochee
River drain swampy areas. Low dissolved oxygen has been measured near the Wysong Dam and
at the Cross Florida Barge Canal Control Structure, where waters are not well mixed A paper mill
effluent discharged to the northern Withlacoochee has had little impact on water quality below the
plant Water quality for the estuarine portion are limited, but coliform bacteria are not a problem
within the estuary where shellfish beds remain open for harvesting (Windsor, 1985).

F-18 Waccasassa Bay

The Waccasassa River drains forest land and wetland with an average flow of approximately 300
cfs The area is sparsely populated (11,400) (Windsor, 1985), and there are no major urban areas.
The Waccasassa Bay estuary has a surface area of 82 mi2. No major industries discharge their
effluents into the bay (Windsor, 1985). The only point source discharge m the basin is a
wastewater treatment plant on Cedar Key, located on the western end of Waccasassa Bay (Hand et
al., 1988n).

Historically this river basin has very good water quality and few sources of pollution (Figure F36)
(Hand et al, 1988n). Forestry clear-cutting in the basin could be a potential nonpomt source of
pollution. The river has a relatively high sediment load, possibly from forest runoff (Hand et al.,
1988n). '(

REFERENCES: F-18

Handera/. (1988n)

F-19 Suwannee River/Sound

The Suwannee River receives the flow of many tributaries, the Withlacoochee, Alapha and Santa
Fe Rivers, and it opens into the Gulf of Mexico in Suwannee Sound. No additional information
was available since the Windsor (1985) review, parts of which are repeated here.

Population in the area is approximately 42,700. Major land uses in the basin are forestry and
agriculture- developed and urban areas are minimal. Little or no domestic or industrial effluent is
discharged to the lower river. Dissolved oxygen concentration violations have been recorded fairly
frequently in the tributaries of the Suwannee River and in the lower river basin; and bacterial levels
were also high in some locations.

*The Hand and Jackman (1984) report (cited in Windsor, 1985) reported the water quality to be
good in all reaches of the lower Suwannee River. Phosphorus concentrations were as high as 21
mg/1 below mining operations. Elevated phosphate concentrations were evident to the mouth of the
river, however, eutrophication is apparently not a problem to the system, because flushing is so
rapid. Effects of elevated levels of phosphate have not yet been thoroughly examined for the
Suwannee Sound.
109
-------
CEDAR
KEY -
WWTP
-1
K /
1 v/~
/
\
/
\
\
\

1
/
/
V
>
1
/
/
WACCASASSA ^x
RIVER \
03110101
/ WACCASASSA
\ \ BAY
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA

RIVERS/STREAMS LAKES/ESTUARIES

•> 1 1 h GOOD ,
;:iSL;.i.UJ.U.i::;::a FAIR
^::^ POOR. F
UNKNOWN^
EPA- WATER
QUALITY INDEX

FLORIDA TROPHIC
STATE INDEX
Fla.
Hap Location
Figure F36. Waccasassa River basin [from 305(b) report of Hand et al. (1988n)].
110
-------
REFERENCES: F-19

Williams etal. (1990)

F-20 Deadmans Bay/Steinhatchee River

The Steinhatchee River has two tributaries, Eightmile Creek and Kettle Creek which drain mostly
Ihe at^^™^*? ~>,ow_ directly into the Gulf of Mexico into Deadmans Bay. Spring

of the uwer coSbasTn has been purchased recently by the State. There is a very sma
noBuTation of 4100inhabitants within the basin, and no sewage treatment plants discharge effluents
STbav The FenhoUoway River is not typical of streams in this area due to the discharge of a
1± vo'umeof effluent from a paper mill. This effluent makes up most of the flow of this system
during the dryer portions of the year (Hand et dl, 19881).

Most of the streams in this coastal area are meeting the use designations (Figure F37) (Hand et al.,
1988« L^wTSd dSolved oxygen concentrations are believed to be due to the sluggish flow
of SeadwaSrs ofthese streams Bacterial counts are sometimes greater than expected, but these
&^S^to«&lly explained. Much of the basin is pensively logged and the rivers
receive periodic impact (mostly turbidity) from both planting and logging operations.

The Econfina River appears to have degraded somewhat since the late 19?9s but still meets the use
Ssimati^S er a/! 19881); no caSse for this decline has been determined The lower portion
of sSg Greet has historical bacteria problems, likely due to the City of Perry wastewater
treatment plant and a package plant discharge upstream.

The FenhoUoway River does not meet the low Class V (industrial use) dissolved oxygen standard

violations have been noted (Hand et al., 19881).

No data were available for the Deadmans Bay portion of the study area.

The shallow nearshore areas of the Gulf of Mexico adjacent to the polluted FenhoUoway River
were chaSSerized by elevated levels of color and turbidity compared to the receiving waters of an
unpoUuS rivS• §coynfma) (Zimmerman and Livingston, 1976). Areas associated with high levels
SteSSuBats were characterized by severely reduced benthic macrophyte biomass, reduced
numbers of species/unit area, and altered species composition when compared to control stations.
ArSis of ctonTc impact also had reduced levels of biomass, although the total number of species
Sken^ wereTot significantly different from the controls. There were uniform increases in the total
number of specie! on either side of the affected drainage system. Such areas were considered to be
Sition zonls between the polluted and unpolluted parts of Apalachee Bay (Zimmerman and
Livingston, 1976).

Work bv Heck (1976, cited in Windsor, 1985) has shown that benthic community structures were
exhibiting effects from the discharge of pulp mill effluents in spite of the fact that traditional
physico chemical water quality monitoring parameters showed little difference from background
levels; Although sections of the bay tributaries were anoxic, by the time the nver waters reached
111
-------
A
,'

%./ .'
,' V
r- '^\ r
K STEINHATCHEE /

RIVER
AVERAGE OVERALL W
1970-1987 STO
RIVERS/STREAMS
GOOD
aoxo.:1' :.;:.::::• FAIR
L*;!iUV.'.'.:...,...,,!.^i POOR

&TER QUALITY
RET DATA
-AKES/ESTUARIES
1 1 II
i
1

EPA WATER FLORIDA TROPHIC
QUALITY INDEX WNU STATE INDEX
Figure F37. Steinhatchee River Bay basin [from 305(b) report of Hand et al. (19881)].
112
-------
the well-mixed waters of the Gulf of Mexico, they were apparently no longer a problem
(Livingston, 1975; cited in Windsor, 1985).

A 7-vr study of epibenthic macroinvertebrates compared the Gulf of Mexico receiving area for the
SteSufwv« with the Gulf adjacent to the polluted area in the Fenholloway River
andLMngston 1982). The relative abundance of dominant species and species richness
esSfwere stoilar, although the number of individuals collected in the Econfina area
al™?^St^lSSton in the Fenholloway. This difference was attributed to the
greatt seag^ass biomass in the Econfma estuary. Comparisons of the constancy of species
comtSsitiof over the study period, as weU as changes in species rankings following a pollution
abSS proSn in me Fenholloway River, showed that there was enhanced species persistence
in the unpolluted area.

The same stations in the Gulf of Mexico adjacent to the unpolluted Econfma River and polluted
r were used in a 9-yr study of the response of fish assemblages to habitat
ton 1984). During the study period, extreme natural habitat changes due to
and low winter temperatures were superimposed over water quality changes
cSo?, turbidity, nutrients; reduced dissolved oxygen) associated with release of pulp
eueMs Various gVassbed fishes followed regular seasonal, age-specific feeding patterns
Zich did not chSSe substantially in terms of qualitative food composition in die unpolluted
Stuary over a 7-Tperiod. Anthropogenic habitat alterations were associated with reductions in
^oph^e distribution, enhanced phytoplankton productivity, and changes in the relative
numerical abundance of associated fish assemblages. Grassbed species were
nktiv^ous fishes, and disruption of feeding habits of various species was apparent
eaeta relative to the unpolluted estuary. Those fishes dependent on specific ben hie
food o7ganisms altered their feeding habits during the years of pollution in the affected estuary.
Subseauen waterDuality improvement was associated with shifts in the age-specific dietary
patterns ofvSus Species toward those observed in the unaffected estuary. In spite of a highly
?esiUent system slight water quality changes due to pollution can cause senous disruptions of the
task^habUafsttuctSe, energy* flow, and community composition of the grassbed assemblages at
various levels of biological organization (Livingston, 1984).

The results of experiments to determine nutrient limitation in the nearshore northeastern Gulf of
Mexico were reported by Myers and Iverson (1979); one station was located in the Gulf of Mexico
adkcenuo me outflow of Econfma River. The seasonal variability of nutrient and phytoplankton
biomass in the Econfina estuary are presented in Figure F38 and details given in Table F5
Sent fluSuations of this area were trimodal, with distinct seasonal cycles. Nitrate and
Phosphate seasonal variability were not closely coupled except during the summer and fall.
PhvtoplaScton chlorophyll a concentrations were bimodal with peaks in April-May and September-
oSfM^ophytL^seagrasses and associated macroalgae) dominate the^productiv*y of this
system with peaks in biomass and productivity occurring during the summer (Bittaker, 1975, cited
kSS and Iverson, 1981). The N:P ratios for this area were greater than 10 and suggested a
surplus of available nitrogen and possible phosphorus limitation (Myers and Iverson 1981)
Results of both carbon uptake and phosphate nutnent enrichment bioassays indicated that
phosphorus was more important than nitrogen in limiting phytoplankton productivity during the
summer months in this coastal estuary (Table F6). The authors cautioned that any alterations in
laMuse that increase phosphorus mobility should be discouraged since these activities could lead
to eutrophication in the system.
REFERENCES: F-20

Handera/. (19881)
Myers and Iverson (1981)
113
-------
Table F5. Summary of environmental, nutrient, and phytoplankton data from northeastern Gulf of
Mexico (from Myers and Iverson, 1981).
Station

E-12

M.L.

Ock-1
Ock-2

Apal-lA

Apal-7
Temp
°C

28.40
1.01
27.80
1.78
28.20
0.90
28.20
0.80
27.50
1.19
27.50
1.34
Salin
PPT

26.20
2.48
29.70
3.53
4.20
1.60
10.30
0.70
3.74
2.58
11.70
8.26
Turb
FTU

3.15
0.35
3.15
0.49
4.97
0.78
4.93
0.61
16.50
8.96
11.70
6.88
Light
lyhr-1

26.50
5.60
37.80
3.73
37.90
7.22
37.90
7.22
33.90
9.17
36.90
3.50
N03
yE
atomN
1-1
.0.32
0.14
0.55
0.10
1.83 '
0.37
2.24
0.83
3.08
2.63
3.55
3.69
N02
yg
atomN
1-1
0.01
0.03
0.02
0.02
0.05
0.01
0.12
0.05
0.15
0.16
0.21
0.16
NH4
yg
atomN
1-1
0.31
0.20
0.61
0.49
0.79
0.44
0.91
1.04
0.60
0.83
0.81
0.89
PO4
atoniP
I"1
0.04
0.01
0.19
0.04
0.37
0.07
0.36
0.09
0.34
0.08
0.40
0.09
Pri Prod
JJgC 1-1 hr-1

6.00
1.25
9.20
0.58
30.80
2.57
26.40
4.74
40.30
10.70
36.70
5.81
Chl-a
ygH

0.61
0.17
0.52
0.21
2.14
0.41
3.00
0.51
5.13
1.12
4.11
0.84
iData are from surface samples collected between May and September, 1974-1976. The first value under each
factor is the mean value of that factor for a given station and the second value is the standard deviation of the
* salinity> Turb is turbidity'
Table F6.
Summary of analysis of variance of carbon uptake and phosphate uptake nutrient
enrichment bioassay from northeastern Gulf of Mexico (from Myers and Iverson,
1981).
Station
Date
E-12
E-12
E-12
E-12
M.L.
M.L.
M.L.
M.L.
Ock-1
Ock-1
Ock-1
Ock-2
Ock-2
Ock-2
6/03/75
7/18/75
7/12/76
9/10/76
6/13/76
7/03/76
8/30/76
9/22/76
6/17/76
7/28/76
8/30/76
6/17/76
7/28/76
8/30/76
Carbon
Phosphate
Uptake Uptake
P04 P04
Phosphate
Carbon Uptake Uptake
Station Date NOs P04 PO4
N
N
N
N
N
4c
-

*
*
-
-

*
•

•
»
-

,
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-lA
Apal-7
Apal-7
Apal-7 .
Apal-7
Apal-7
Apal-7
Apal-7
Apal-7
Apal-7
Apal-7
9/02/74
5/29/75
7/11/75
9/11/75
9/15/75
6/10/76
6/24/76
7/05/76
8/15/76
8/26/76
9/02/74
5/29/75
7/11/75
7/11/75
9/15/77
6/10/76
6/24/76
7/05/76
8/15/76
8/26/76
the effect of the
N
N
N
-.-
was always stimulatory to the physiological process measuTed.
114
-------
.9-
UJ
£ .6

z
.3
u,
-09
-06
.03
o
i
I
O
cr
3
o
_l L.
i i i i i i . i
DJFMAMJJ A S 0 N D

SEASONAL CYCLE
Figure F38 Seasonal cycles in the Econfina estuary of surface dissolved nitrate (pg-at/1), soluble
reactive phosphate 0/g-at/l), and phytoplankton chlorophyll a (j/g/l) from 1973
through 1976 (from Myers and Iverson, 1981).

F-21 Aucilla River

The Aucilla River receives the flow of the Little Aucilla and Waccasassa Rivers, and it opens
directly into the Gulf of Mexico in Apalachee Bay. No additional information was available since
the Windsor (1.985) review, parts of which are repeated here.

The land area in the basin is sparsely populated (21,800 inhabitants), and land use is primarily
forestry and agriculture. There are no major urban areas within the basin, no sewage treatment
plants and no industries discharging into the river. In general, the water quality is good in this
basin.' Naturally low pH and dissolved oxygen values result from waters originating in swampy
areas (Windsor, 1985).
115
-------
F-22 Apalachee Bay/St. Marks River

The St. Marks, Aucilla (see Section F-21), Fenholloway (see Section F-20) and Ochlockonee (see
Section F-23) Rivers drain into the waters of Apalachee Bay, which is a broad embayment on the
easternmost end of the Florida panhandle. The St. Marks River basin drains approximately 1800
mi2, extends from south Georgia to the Gulf of Mexico, and has an average flow of 700 cfs at a
point 11 mi upstream of the confluence of the St. Marks and Wakulla Rivers. The Wakulla River
is spring fed and has an average flow of 400 cfs. Land use within the basin is predominantly
forestry with about 10 % urban; population within the basin is 180,900 (Windsor, 1985; Hand et
al., 1988k). Apalachee Bay has a surface area of 96 mi2, with an average depth of 1.5 m. There
are no sewage treatment plants discharging into the bay. Studies conducted on Apalachee Bay
have emphasized the impact of pulp mill effluents on the biota of the bay (Delfino et al 1984) (see
also Section F-20). ''

Water quality within the basin is excellent, with a few exceptions (Figure F39) (Hand et al,
1988k). Water quality problems in Lake Munson and Munson Slough are related to the city of
Tallahassee. The St. Marks River has been declared an Outstanding Florida Water except for the
portion downstream of Rattlesnake Branch (the lower 3-4 river miles, which receives the effluent
from Seminole Asphalt and Purdom Power Plant. Water quality problems related to toxic effluents
are attributed to the Seminole Asphalt plant, which is no longer in operation (Hand et al., 1988k).
The Wakulla River is fed by one of Florida's highest discharge springs and has excellent water
quality. The upper portion of the river was recently purchased by the State and made into a state
park; however, the lower portion of the river is threatened by continued waterfront development
with insufficient buffer areas along the water's edge. No routine water quality monitoring for the
open Gulf of Mexico were available (2 observations for 1979-1980).

See comparative studies described in Section F-20 on the areas of the Gulf of Mexico adjacent to
the Econfina and Fenholloway Rivers. See discussion in Section F-20 concerning nearshore
nutrient distributions and nutrient limitations to phytoplankton growth in the Gulf of Mexico waters
adjacent to Econfina River, and a similar discussion for Ochlockonee Bay (Section F-23) and
Apalachicola Bay (Section F-24).

In July 1964, a Gymnodiniwn breve bloom developed 35 to 140 km offshore in Apalachee Bay
and moved into northern Apalachee Bay in September. The area affected was estimated to be
approximately 36,000 km2. Numerous and substantial fish kills were associated with the bloom
(See Section F-24.1.)
Myers (1977)
Stephens and Oppenheimer (1972)
Williams etal (1990)
Zimmerman and Livingston (1976,1979)
REFERENCES: F-22

Dugan and Livingston (1982)
Florida Board of Conservation (1966)
Handera/. (1988k)
Livingston (1984)

F-23 Ochlockonee Bay

Ochlockonee Bay is located on the panhandle of Florida near the town of Panacea and adjacent to
Apalachee Bay. The major tributary of the estuary is the Ochlockonee River, which is 102 mi
fe1^'/^8™!?0-^2 ?f northern Florida and southern Georgia, with a mean flow of 1583 cfs
(Windsor, 1985). The bay is about 5 mi long and averages a little more than 1 mi wide The bav
averages 1 m deep, has a tidal range of a little over 0.5 m, and thus is fairly well mixed (Windsor
116
-------
GEORGIA
^ BRADFORD

_->x-'" T.P. SMITH
^--V^ . WWTP
I
I 15 ,
* r~^\^
I nf ^^ APALACHEE
) Vu - BAY
\J^^
Fie,
Location
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA

RIVERS/STREAMS LAKES/ESTUARIES

H , , •- GOOD |~ I I I [
- FAIR |~

POOR. [_

UNKNOWN^
EPA WATER ..... FLORIDA TROPHIC
QUALITY INDEX RND STATE INDEX
Figure F39. St. Marks River basin [from 305(b) report of Hand et al. (1988k)].
117
-------
1985). The basin is relatively unpopulated (38,900 inhabitants), and land use type is primarily
forestry, agriculture and wetlands.

Effects of human activities appear to be minimal within the bay system. No sewage treatment
plants are discharging into the estuary. The Ochlockonee Bay system has recently been described
as pristine (Kaul and Froehlich, 1984; cited in Windsor, 1985). In the Hand and Jackman 305(b)
report cited in Windsor (1985), the water quality for the entire basin was listed as good There
were no data reported for Ochlockonee Bay proper.

The results of experiments to determine nutrient limitation in the nearshore northeastern Gulf of
Mexico were reported by Myers and Iverson (1979); two stations were located in Ochlockonee
£ay' ,-rr; es or nutrients and phytoplankton biomass are given in Table F5 (Section F-20)
The Ochlockonee and Apalachicola Bay stations exhibited higher nutrient concentrations'
phytoplankton productivity, and chlorophyll a levels, than the Econfina estuary (see Section F-20)'
Relatively low mean salinity values and high turbidity were characteristics of the Ochlockonee
stations, due probably to watershed runoff and higher river discharge. The higher phytoplankton
and nutrient values were considered by the authors to be indicative of productive, but not eutrophic
estuarme systems. The N:P ratios for this area were between 5 and 10 and were thus not
informative with regards to potential nutrient limitations (Myers and Iverson, 1981) Results of
both carbon uptake and phosphate nutrient enrichment bioassays indicated that phosphorus was
more important than nitrogen in limiting phytoplankton productivity during the summer months in
this coastal estuary (Table F6). The authors cautioned that any alterations in land use that increase
phosphorus mobility should be discouraged since these activities could lead to eutrophication in the
s jr seem •

Work of Wells and Froelich (1982) indicates that the bay is nitrogen limited, that phosphate input
occurs in the lower estuary, that intense nitrate and phosphate removal coincides with
phytoplankton blooms (high chlorophyll a biomass), and that N:P:Si ratios vary seasonally
according to nver flow, but occur approximately in the Redfield ratios.

REFERENCES: F-23
Pascale and Wagner (1982)
Wells and Froelich (1982)
Wolfe and Reidenauer et al. (1988)
Florida Board of Conservation (1966)
Myers (1977)
Myers and Iverson (1981)

F-23.5 St. George Sound

The coastal areabetween the Ochlockonee and Apalachicola Rivers is poorly drained and consists
of two main regions (Wolfe et al., 1988). The eastern portion of the basin is the area drained by
toe New River and its tributaries, which discharge into St. George Sound at the town of Carabelle
The western portion drains into East Bay of the Apalachicola Bay system (see Section F-24) The
major causes of water quality problems in this basin are the discharges to the coast from the
sewage treatment plants in Carabelle and Eastpoint, and surface runoff from forest clearcutting
The system at Eastpoint is bong upgraded and expanded. The system for the City of Carabelle is
?Ct!?n yu? • m .narthwest Ftonda providing only primary treatment (Wolfe et al 1988) The
highly chlorinated sewage discharge degrades the water in the vicinity of the outfall to St George
fv^cc- ,1t0/^ Sludge deP°sits- Overly-enriched waters produce plankton blooms and
excessive growth of filamentous algae, bacteria, virus, and fungi that are pathogenic to the
seagrasses of St. George Sound (Wolfe et al., 1988). pimugenic to tne

REFERENCES: F-23.5

Wolfe etal (1988)
118
-------
F-24 Apalachicola Bay/River/East Bay

Apalachicola Bay, located in northwest Florida, is the estuarine terminus of the Apalachicola
cHtahSee Cupola, and Flint River systems. The Apalachicola River has the largest annual
dischargTof Florida's rivers (24,000 cfs) with seasonal high flows occasionally exceeding
140000 cfs (Livingston and Joyce, 1977). The Apalachicola Bay system is composed of six
maior^ubdiv sions: the Apalachicola River delta, East Bay, Apalachicola Bay, St. Vincent Sound,
sl George Sound (see Section 23.5) and Alligator Harbor. Apalachicola Bay is a shal ow lagoon-
tieesm^y, bounded by a series of barrier islands, and dominated by the Apalachicola River In
tte bay, salinity, nutrient and detritus distribution, primary and secondary productivity, and other
factors are dependent on seasonal changes in the drainage characteristics. The bay system s
characterized by high levels of primary productivity (phytoplankton) and relatively little
development of benthic macrophyte assemblages except in fringing areas. This combination makes
teesSS a center of a significant oyster fishery and important habimt for many cornmerciaily
important crabs, shrimp, and fmfish. This section of the Honda panhandle, includini: Apalachee
Bay is considered by Swanson et al. (1972) (cited in Myers and Iverson, 1981), to be one of the
least-polluted, least man-influenced subtropical regions in North Amenca. The region, however
is coming under development pressure from residential development on the barrier islands and
modifications to the Apalachicola river for navigation and industrialization.

This system is the most comprehensively studied water body in Florida, due primarily to the
research efforts of scientists from Florida State University, particularly R. J. Livingston and his
colleagues (Livingston, 1991). Continuous water quality monitoring has been performed since
1972 A resource atlas of the estuary (Livingston, 1983) provides a comprehensive data base
alone with a master bibliography of the technical research that has been performed in the estuary
(updated somewhat by this report). The Apalachicola River estuarine system was designated a
National Estuarine Sanctuary in 1972, which is now part of the National Estuarine Research
Reserve system to be preserved and managed for research and educational purposes. The entire
bav as weU as the Apalachicola River has been declared an Outstanding Honda Water. In addition
it is an Area of Critical State Concern which requires more intensive regulation of planning and
development in the area.

Analysis of long-term scientific data indicate that dominant commercially important estuarine
populations are associated with river flow, local salinity characteristics and biological (predation,
competition) interactions with the salinity regime, and food web structure (Livingston, 1991).
Such complex interactions involve freshwater influxes and biological response in the estuary
Species-specific responses to the principal driving factors further complicate the biological
relationships of the Apalachicola system (Livingston, 1991).

According to the most recent 305(b) report (Hand et al., 1988a), the bay has very good water
quality (Figure F40). Representative water quality monitoring data are shown in Figure *41. ine
most serious threats to the water quality in the bay are associated with nonpomt sources from the
more urbanized areas in the basin. In the northern part of the bay, untreated stormwater runott
from the City of Apalachicola and nearby fish houses has had a localized impact on the bay.
Problems associated with fish houses include BOD from fishing wastes, and pollutants due to boat
traffic, docking and fueling.

In the southern bay area, there has been rapid development of St. George Island, and there is
concern over septic tank drainage into the bay (Hand et al, 1988a). A recent inspection revealed
that 23 % of the 724 septic tanks were failing and that many did not meet State regulations.
Finally on the island, there is a boat basin connected with the bay that receives runoff from a
shopping area and wastes associated with the mooring, fueling and offloading activities of oyster
boats.
119
-------
APALACHICOLA
RIVER
APALACHICOLA
ST.GEORGE ;.
SOUND
ST. VINCENT
SOUND
ST. VINCENT
ISLAND
3MT
APALACHICOLA
BAY
ST. GEORGE
ISLAND
J-.- 03130014
Fla.
Hap Location
AVERAGE OVERALL WATER QUALITY
1970-19S7 STORET DATA
RIVERS/STREAMS LAKES/ESTUARIES
I
— — I

oxo;. ':':'.':':'.:'::'.'.': FAIR f
.,.x..,.,,™,.™,....v..,,..... r

! II
1

i
EPA WATER FLORIDA TROPHIC
QUALITY INDEX H"U STATE INDEX
Figure F40. Apalachicola Bay basin [from 305(b) report of Hand et al. (1988a)].

The most extensive damage to the bay recently has been through the action of Hurricane Elena and
Hurricane Kate in 1985. Theentire bay was closed to oystering to allow recovery from damage
nd ^**8 ft Water quality from ±esQ hurricanes can be seen in
The results of experiments to determine nutrient limitation in the nearshore northeastern Gulf of
Mexico were reported by Myers and Iverson (979); two stations were located in Apalachicola Bay
and one between it and Apalachee Bay. The seasonal trends in nutrient and chlorophyll a values
120
-------
g s i g

AUNnwnv
I/OH ooa
5 § 5

Vow oa
oo
oo
1
ffi
1
'?
*2
nod aoioD
W IH003S
:i
S £
jujaiaanj.
BS
•BW
a
JJ 3OV1S
*£

R
I
3
O

-------
are shown in Figure F42 and details are given in Table F5 (Section F-20). The nutrient and
phytoplankton levels were an order of magnitude higher in the Apalachicola Bay estuary than in the
Econfina estuary (see Section F-20). Maximum nitrate and phosphate concentrations occurred
during March-May during the period of maximum river discharge. Phytoplankton chlorophyll a
levels were maximum during July-October. Relatively low mean salinity values and the highest
turbidity values for the entire study area were characteristic of the Apalachicola Bay stations due
probably to watershed runoff and higher river discharge. The higher phytoplankton and nutrient
values were considered by the authors to be indicative of productive, but not eutrophic estuarine
systems. The N:P ratios for this area were greater than 10 and suggested a surplus of available
nitrogen and possible phosphorus limitation (Myers and Iverson, 1981). Results of both carbon
uptake and phosphate nutrient enrichment bioassays indicated that phosphorus was more important
than nitrogen in limiting phytoplankton productivity during the summer months in this coastal
estuary (Table F6). In Apalachicola Bay, where the water column contains high turbidity for
several days following periods of high winds, phytoplankton are not phosphate limited but become
so after sediments settle to the bottom. The authors cautioned that any alterations in land use that
increase phosphorus mobility should be discouraged since these activities could lead to
eutrophication in the system. uiu icau iu
SEASONAL CYCLE

Figure F42. Seasonal cycles in the Apalachicola Bay estuary of surface dissolved nitrate (ug-at/1)

1 S?t hrnn^^^^^
1973 through 1976 (from Myers and Iverson, 1981)
122
-------
Changes in nutrient concentrations in the bay and river were documented by Livingston et al.
[1974(1975)1 for a 12-mo period in 1972-1973 (Figure F43). Nitrate showed the greatest seasonal
variation. River nitrate concentration remained relatively stable, however, thus indicating that
decreased bay nitrate concentration was not due to decreased river concentrations but to decreased
river flow rates and increased summer levels of biological activity. There were no seasonal trends
in ammonia values in the bay. The bay sometimes had ammonia concentrations greater than the
river, which suggested some other source of ammonia. Orthophosphate had no obvious
seasonality. The phosphate concentration in the river was always greater than that of the bay, but
when the river flow decreased in summer, the average phosphate concentration did not decline
dramatically in the bay. Nutrient enrichment experiments in August 1973 indicated that low
concentrations of both nitrate and phosphate were limiting phytoplankton productivity in the bay at
the time. These nutrients were usually, present in sufficient quantities during most of the year.
Silicate concentrations showed a seasonal trend similar to river discharge. Minimal levels of
chlorophyll a productivity occurred during February and were associated with high river discharge
and flushing of the bay. Except for a surface maximum during a calm day in January, productivity
was uniform during the remainder of the year [Livingston et al., 1974(1975)].
A
B
I 15(-
o
E 10
• ^surface
.. .bottom
K7H
2500

2000

5 1500
T3
W

^ 1000
u

?
E 500

0
JASONDJ FMAMJ JAS
1972 1973
ON DJ FMAMJ JAS
1972 1973
24Q

ZOO
. surface
> .bottom
•bottom

*river
JASONDJ FMAMJ J'AS
1972 1973
C /
. .turf ace
_. ^bottom
* *river
JASONOJ FMAMJ J AS
1973 1973
JASON' DJ FMAMJ J AS
1972 1973
Figure F43. Average seasonal variation in chlorophyll a for Apalachicola Bay, average seasonal
variation in productivity for Apalachicola Bay, and average seasonal variation for the
Apalachicola River-Bay system in nitrate, ammonia, silicate and orthophosphate
[from Livingston et al., 1974(1975)].
123
-------
A survey of 24-h variations in dissolved oxygen at two stations in Apalachicola Bay over a 9-mo
period indicated that there was no significant cultural eutrophication in the Apalachicola Bay system
(Livingston, 1974; cited in Livingston et al., 1977). Eleven years of monitoring water quality
stations monthly in the bay indicated no nutrient enrichment which leads to low dissolved oxygen
levels (Livingston, 1983). Overall, the general distribution of water quality parameters (dissolved
oxygen, turbidity, water color) during the 11-yr monitoring program indicates that the Apalachicola
Bay estuary has not been adversely affected by man's activities in the region except in areas
adjacent to population centers (Figure F44) (Livingston, 1983).

A recent evaluation (Livingston, 1991) noted growing evidence of changes in upland
characteristics and within-system habitat alterations that are associated with changes in nutrient
distributions and salinity relationships and that such changes can have serious impacts on estuarine
Bottom Water Dissolved Oxygen
MJSDMJSDMJSDMJSDMJSDMJSDMJSD MJSDMJSDM J S D M J S D
| 1972 | 1973 | 1974 | 1975 | 1976 [ 1977 | 1978 | 1979 | 1980 | 1981 | 1962 |

Flv«°«rtonlh moving avaraga,
Surface Water Color
|- | station 1

Stations
•nJSOMJSDMJSDMJSDMJSDMJSOMJSDMJSDMJSDMJSDMJSO
| 1972 | 1973 | 1974 | 1975 | 1976 | 1977 | ' 1978 | 1979 | 1980 | 1981 | 1982 |

Ftvt-monlh moving avaraga.
Surface Water Turbidity
Station 1

Station S
MJSDMJSOMJSDMJSDMJSDMJSDMJ.SDMJSDMJSDMJSDM
1972 | 1973 | 1974 | 1975 | 1976 | 1977 • | 1978 | 1979 f 1980 | 1981

Flvamonth moving averaga.
JSD
1982 |
Figure F44. Trends in water quality parameters for Apalachicola Bay (from Livingston, 1983).
124
-------
systems. In a river-dominated estuary, like the Apalachicola system, management should be based
on the control of freshwater sources, nutrients and organic matter with a minimization of physical
alterations that lead to increased salinity stratification (Livingston, 1991). Increased land
development, waste loads, dredging and channelization of the Apalachicola River, and demands
for freshwater sources will likely lead to the alteration of the water quality and productivity of the
system (Livingston, 1991).
REFERENCES: F-24

Elder and Mattraw (1982)
Elder etal. (1986)
Estabrook (1973)
Florida Board of Conservation (1966)
Haddad and Carder (1979)
Hand etal. (1988a)
Isphording er fl/L (1987)
Livingston (1983,1987))
Livingston and Joyce (1977)
Livingston etal (1974,1976, 1977,1991)
Menzel and Cake (1969)
Myers (1977)
Myers and Iverson (1977,1981)
National Estuary Study (1970a)
Williams etal. (1990)
Wolfe etal. (1988)
F-24.1 Florida Inner Continental Shelf (Panhandle)

The nearshore environment of the northeastern Gulf of Mexico off the Florida panhandle is
characterized by a broad, shallow continental shelf. The region is a low wave energy coast, with
maximum tidal amplitudes of 1 m. The area receives discharge from several rivers, the largest of
which is the Apalachicola. In a hydrological survey of the northeastern Gulf of Mexico, Curl
(1959) noted the influence of the Apalachicola River as far as 160 mi to the south (cited in
Livingston and Joyce, 1977).

Large scale water circulation in the northeastern Gulf of Mexico is influenced'by the Loop Current
and associated eddies. Water from the Loop Current flows north into the Gulf and then veers to
the right to form a clockwise gyre which is bounded by two or more smaller counterclockwise
gyres off West Florida. Impacts from the Loop Current are more frequent on the eastern end of the
Florida panhandle than on the western end; the boundary for many oceanographic processes,
geological structures and biological communities is Cape San Bias.

The occurrences of the red tides caused by blooms of the toxic dinoflagellate, Gymnodinium
breve, were discussed in detail in section F-15.1. While the area between Tarpon Springs and Ten
Thousand Island on the Florida west coast experiences the most and most frequently recurring red
tides, there have been numerous instances of red tides in the offshore coastal waters of the Florida
panhandle (Steidinger, 1973)". In July 1964, a G. breve developed 35 to 140 km offshore in
Apalachee Bay and moved into northern Apalachee Bay in September. The area affected was
estimated to be approximately 36,000 km2. Numerous and substantial fish kills were associated
with the bloom. A detailed description of the bloom is available in Florida Board of Conservation
(1966). A red tide occurred along the panhandle coast in early September 1974, necessitating the
closure of these waters for shellfish harvesting (Keys, 1975). A red tide of an unconfirmed
organism was extensive off Pensacola in July 1960 (Florida Board of Conservation, 1966).

A bloom of the toxic dinoflagellate, Gonyaulax monilata, occurred in waters adjacent to Pensacola
Bay during an extensive bloom within the estuary in August 1979 (Perry et al., 1979). Fish kills
were associated with the bloom.

See Sections F-20 and F-23 on nearshore portions of Econfina estuary.
125
-------
REFERENCES: F-24.1

Atwood (1981)
Churgin and Halminsta (1974)
Cons. Perm. Int. Exp. Mer (1936)
El-Sayed etal. (1972)
Florida Board of Conservation (1966)
Freebergetal. (1979)
Haddad and Carder (1979)
Myers and Iverson (1979)
Schroederetal. (1988)
Stuntz et al. (N.D.)
Thompson and Bane (1986a,b)
Thompson et al. (1988)
F-25 St. Andrews/West/North/East Bays

The St. Andrews Bay system is composed of North, East and West Bays, St. Andrews Bay,
Grand Lagoon, St. Andrew sand, and, to the east, St. Joseph Bay. There are no large rivers
within the watershed; the largest inflow to the St. Andrews Bay system comes from Econfina
Creek, which most of the year is composed predominantly of ground water from springs fed by
the Floridan Aquifer. Drainage from the Choctawhatchee and East Rivers flows into the West Bay
area. The watershed is primarily forested with an urbanized area concentrated adjacent to St.
Andrews Bay at Panama City, Lynn Haven and a narrow strip of development along the Gulf of
Mexico. Point sources of pollution in the area include two large paper-pulp processing plants (one
in St. Andrews Bay and another in St. Joseph Bay) and several wastewater treatment plants
(Figure F45). Little research has been performed in this estuarine system.

The St. Andrews Bay system was studied in 1974 in order to calculate a waste load allocation
amount and quality of waste that could be discharges to the system based upon its calculated ability
to assimilate that waste without damage to its ecosystem (Johnson et al. 1974; cited in Wolfe et al.,
1988). During this study, St. Andrew Bay had the poorest water quality of the four bays in this
drainage. Some locations, particular Watson Bayou and the International Paper Company outfall,
did not meet dissolved oxygen, turbidity, or bacterial standards for Class III standards (i.e.,
recreation, propagation and maintenance of a healthy, well-balanced population of fish and
wildlife). The other bays met Class II standards (i.e., shellfish propagation or harvesting).

Ten years later, Hand and Jackman (1984; cited in Wolfe et al., 1988) reported that of 400 km2 of
estuary in this basin, all but 14 km2 has good water quality. The major urban development in the
area centers around Panama City. Major point sources of pollution include two large paper-pulp
processing plants, one discharge via a regional sewage treatment and one directly to St. Joseph
Bay. Historically, problem areas included Watson Bayou, Martin Bayou, and Deeper Point Lake
at the head of North Bay.

In the most recent 305(b) report (Hand et al., 1988J) lists the St. Andrews Bay system as generally
good water quality. The major river, Econfina Creek, is nearly pristine, and the bay waters are
generally well flushed by the Gulf of Mexico. The bay is threatened, however, not only by the
growth of nonpoint source pollution, but also by several important domestic and industrial point
sources. There are several areas of concern in the Basin: Deer Point Lake and its tributaries,
exclusive of Econfina Creek; Beatty Bayou, wastewater treatment plant effluent; Watson Bayou,
historical wastewater treatment discharges; West Bay, Panama City waste water treatment plant; St.
Andrews Bay, regional wastewater treatment plant discharges. Two of the wastewater treatment
plants receive more industrial wastes (paper-pulp mill and chemical company discharges) than
domestic sewage. Both of the receiving bays show biological degradation and shifts in sediment
composition; however, because of the bays' circulation patterns, the effluent is relatively quickly
dispersed (Hand et al., 1988J). Other pollution sources in this basin include many small package
plants and septic tanks which discharge poorly treated waste into ditches that empty directly into
the bay system, along with significant runoff from highway construction and logging operations.
Powell Lake, although relatively pristine, is undergoing rapid development. Localized problems in
126
-------
~^.s~
WEST BAY

PANAMA CITY BEACH WWTP

ST. ANDREWS BAY

WATSON BAYOU
MILITARY POINT

BAY COUNTY REGIONAL WWTP
AVERAGE OVERALL WATER QUALITY
1970-1987 STORET DATA
| RIVERS/STREAMS

G00°
FAIR
LAKES/ESTUARIES
Figure F45. St. Andrews Bay basin [from 305(b) report of Hand et al. (1988J)].
within the St. Andrews estuarine area result in high ammonia levels, elevated nutrients, fish kills,
increases in aquatic vegetation, reductions in biological richness, decreased dissolved oxygen
values, and increased BOD loadings.
REFERENCES: F-25

Handera/. (1988J)
Williams etal. (1990)
Wolfe etal (1988)
127
-------
F-26 Choctawhatchee Bay

Choctawhatchee Bay is a hypopycnal lagoon that is connected to the Gulf of Mexico via East Pass
(Delfino et al., 1984). East Pass Lagoon (Destin Harbor) opens into Choctawhatchee Bay just
north of East Pass. The highly alluvial Choctawhatchee River drains into the eastern portion of the
bay which is separated from the Gulf of Mexico by Santa Rosa Island. Other tributaries to the bay
include Lafayette, Magnolia, Alaqua, Rocky, Turkey and Juniper Creeks. The Bay is 40 km long
by 5 km wide, averages 3 m in depth at the eastern end, and is 9 m deep in the remainder (Wolfe et
al., 1988). The bay is characterized by its minimal connection with the Gulf of Mexico. East
Pass, a narrow channel west of Destin and east of Santa Rose Island, is the only connection and is
often shoaled to a depth of 2 m (Collard, 1976; cited in Wolfe etal, 1988) requiring maintenance
dredging to keep a 4 m channel open. East Pass Lagoon is subject to minimal flushing, resulting
in stagnant waters in the eastern area where almost anoxic conditions prevail (Delfino et al., 1984;
Windsor, 1985).

The major land uses in the basin are forestry and agriculture, but urban development is occurring
rapidly along the coast and in the northwestern bay area. Fort Walton Beach, Destin and
Valparaiso are the largest cities in the basin, and the area around these cities along the Gulf coast is
undergoing rapid urban development (Wolfe et al. 1988). One sewage treatment plant is located in
the basin; there is little industrial activity (Windsor, 1985).

Historically, water quality in this basin has been good; however, there have been several problem
areas associated with rapid development occurring along the coast (Hand et al., 1988d). In the
Hand and Jackman 305(b) report (1984; cited in Windsor, 1985), water quality for most of the bay
was listed as good, but fair for localized points in St Andrews Bay, the eastern end of the bay and
several tributaries. The water quality assessment for the area in the most recent 305(b) report
(Figure F46) (Hand et al., 1988d) is rated as good. The report, however, notes several
fluctuations in the water quality conditions of the St. Andrews Bay system. In the 1970s, treated
wastewater effluents caused eutrophication, fish kills, and seagrass bed die-offs in portions of the
bay. The wastewater treatment plants have been converted to spray irrigation discharge, and a
basin assessment in 1984 indicated that the water quality had improved since this upgrading.

Recently water quality in the bay is again being degraded due to the continued development of the
watershed (Hand et al., 1988d). The nonpoint pollution sources are associated with highway
runoff, ditching and draining of water-cleansing swampland, and surficial water table seepage
from package plant perc-ponds and wastewater treatment plant sprayfields. The poorly circulating
Old Pass Lagoon at Destin is experiencing eutrophication and fish kills. Dons Bayou near Ft.
Walton has experienced a low grade, chronic fish kill from unknown sources. Recent studies
indicate localized metals contamination in sediments near urban areas. Other sources of pollution
in the bay include discharge from meat and poultry processing plants and runoff from agricultural
areas in the upper basin. Another area of concern is the construction of a proposed bridge across
the bay with its associated ecological damage and the eventual further development of Gulf islands.

A State-funded, in-depth ecological baseline study of Choctawhatchee Bay during 1985-1986 was
recently completed (Livingston, 1986) and summarized in Wolfe et al. (1988). Portions of this
summary are presented below. This study was prompted by plans to construct a cross-bay bridge,
but much data relevant to the ecological health of the system was presented.

Portions of the bay are much deeper, and vertical stratification of salinity is prevalent with
associated stratification of dissolved oxygen and hypoxia at depth during various times of the year
(Livingston, 1986; cited in Wolfe et al:, 1988). Freshwater input on the eastern end, salt water
inflow on the western end, low tidal range (0.2 m within the bay and 0.4 m in the adjacent Gulf of
Mexico) results in minimal tidal flushing and poorly mixed bay waters. The resulting stratification
(sharp in the western two-thirds of the bay, and weak in the .eastern one-third) produces a
128
-------
FT. WALTON
BEACH OLD'PASS LAGOON
CHOCTAWHATCHEE '
RIVER
AVERAGE OVERALL HATER QUALITY
1970-19S7 STORET DATA
RIVERS/STREAMS LAKES/ESTUARIES

;••••••::•:•.•;:•:•::•:•:;•;• FAIR [
:rr'z:~n. p°°R I

I_II
!
i
I
EPA WATER ..... FLORIDA TROPHIC
QUALITY INDEX ' STATE INDEX
Fla.
Hap Location
Figure F46. Choctawhatchee Bay basin [from 305(b) report of Hand et al. (1988d)].

stagnation of high salinity bottom waters. Collard (1976; cited in Wolfe et al., 1988) found that in
summer the bottom of the bay was "biologically barren." Livingston (1986; cited in Wolfe et al.,
1988) found that low dissolved oxygen levels associated with the salinity gradients in the deeper
portions of the bay were life-limiting to various estuarine forms during certain months of the year.
Low dissolved oxygen was most evident during summer months, and by August the entire bay
was hypoxic to anoxic at depth.
129
-------
The baseline study of Livingston (1986) (cited in Wolfe et al., 1988) also found that nitrogen and
phosphorus levels were highest in the western sections of the bay. This was attributed to
stormwater runoff from the Destin peninsula and adjacent developed areas. A wasteload allocation
study was performed on the bay using a water quality model (Johnson et al., 1974; cited in Wolfe
et al., 1988). The model determined that water quality was generally good with the exceptions of
the Cinco, LaGrange, Boggy and Alaqua Bayous, and that nutrient levels in most of the bay
indicated no eutrophication processes. Macroinvertebrate sampling in the basin (Ross and Jones,
1979;- cited in Wolfe et al., 1988) indicated areas of healthy benthic populations and others that
were impacted.
REFERENCES: F-26

Blaylock (1983)
Handera/. (1988d)
Kaufmann etal. (1988)
Livingston (1986)

F-27 Pensacola/East/Escambia Bays
Sale etal (1988)
Williams etal. (1990)
Wolfe etal. (1988)
The Escambia Bay estuarine system is located in the extreme northwestern section of Florida's
panhandle and has a surface area of 159 mi2. The port city of Pensacola is located on Pensacola
Bay. The Yellow, Blackwater and Escambia Rivers drain into the estuarine system which is
generally divided into Pensacola, Escambia, East and Blackwater Bays and Santa Rosa Sound.
Major flows come from the Escambia River (6500 cfs), the Blackwater River (400 cfs), and the
Yellow River (1500 cfs) (Hand etal., 1988g). The bay system is relatively shallow, ranging from
less than 1 m to 6 m deep and averages 2.5 m at mean low water. Water depth increases from the
north to the south. The system has been described by Ellis (1969; cited in Wolfe et al., 1988) as a
low energy estuary. The opening of the bay to the Gulf of Mexico is restricted and shallow, and
the bay is generally considered to be vertically homogeneous but does become partially stratified
seasonally (Windsor, 1985).

The City of Pensacola, with more than 60,000 inhabitants is located on the estuary (Windsor,
1985). Land use is primarily for forestry, but large acreage is used for agriculture and developed
and urban areas. In the estuarine drainage basin there are nine sewage treatment plants, many
hazardous waste facilities, two major dredging operations, three pulp and paper plants, one
petrochemical plant, one power plant and two steel mills. Historically, this system received
national attention as a result of numerous fish kills and the effects of industrial pollution (Windsor,
1985). Years of abuse had severely degraded and damaged the estuarine waters and resulted in
poor water quality and the occurrence of extensive fish kills. As a consequence many such areas
were closed to commercial fishing and recreational activities. In addition to the growing sewage
burden, inadequately treated chemical effluents contributed to high BOD, high nutrients, lowered
dissolved oxygen and a what has frequently been described as an advanced state of
"eutrophication" (Windsor, 1985). Commercial fisheries harvests dropped or ceased; fish kills
were prevalent in die late 1960s and early 1970s. Fish kills were reported in miles of dead fish.
Comparative studies suggested that nearly all the seagrass beds in the bay were destroyed
(Windsor, 1985).

Significant improvements in water quality, particularly dissolved oxygen, have been noted for the
bays as a result of decreasing the discharges from the industrial and municipal effluents by more
than 90 %. Fish Mils are smaller in size and less frequent (but see below). Water quality for most
of the bays was described as good to fair (Hand and Jackman, 1984; cited in Windsor, 1985) with
a few notable exceptions of low dissolved oxygen and high bacteria, which were related primarily
to point source discharges of sewage treatment plants and some industrial wastes. The figure from
130
-------
oo

ON
ffi
8
CO
en

.8
pa
I

S?
fc
-------
u
o

V)
Ul
*_4
J- OC
1- <
n 3
_J 1—
O >- UJ
d < ~-
CC UJ
UJ h- ^
1

H- UJ < 1
-^~

_—

—

t~t
X X
O- UJ
o a
a: z
o t—
o; h-
O V)
IA_
30 2
_J t/> '• O Q
II Q o: o: z z
S r«- o •-< o K: <
o: eo o < o z
«ii 0* (/) O *^- u- — J
> t- E X
O 1 <
O UJ
ui r- a
o o- H
< r- M
OL "^
uj tn
> • «£
< UJ
^
Of

*
^

V
(

UJ
, a o
UJ Z

3 >-
^

5 D. _l
! UJ <
| n
1 a
oo
oo
O

to
132
-------
the 1984 305(b) report (Figure F47) is shown here for comparison with the most recent report
(Hand et al., 1988g) (Figure F48). The fair water quality assessment for portions of the East Bay
area have been upgraded to good. Tributaries to Blackwater Bay which were listed as fair have
been upgraded to good. Problems in Blackwater Bay were attributed to nutrients at the mouth of
the Blackwater River (Hand and Jackman, 1984). Pensacola Bay is generally listed as good, but
previously had localized fair assessments. Escambia Bay is still listed with fair water quality as it
was previously, but poor ratings for several of the tributaries have been changed to fair or good,
with the exception of Bayou Chico which is still listed as poor. Representative water quality data
from several of these areas are shown in Figures F49-F52.

The Hand et al. (1988g) reports cites the main water quality problems in upper Escambia Bay and
the two bayous (Bayou Chico and Bayou Texar) which drain the Pensacola urban area. In addition
to stormwater runoff, Bayou Ghico (rated poor) receives shipyard runoff, historic discharge and
runoff from Reichold Chemicals, and a wastewater treatment plant discharge. Historically, it was
also impacted by chemical, lumberyard and creosote industries. Sediments are polluted with
metals and support almost no macroinvertebrate life. The bayou has bacteria, fish kill and nutrient
problems. Two creeks which fed this bayou also exhibit water quality problems. Upgrades to the
wastewater treatment plant are scheduled.

Bayou Texar has had increasing fish kill problems in recent years. It receives discharge from 68
storm sewers and heavy suspended solids loads from Carpenters Creek. Modifications to the
treatment of stormwater runoff are proposed for this area.

Further up the estuary, water quality problems are evident in the northern portion of Escambia Bay
with reduced dissolved oxygen concentrations, fish kills and bacteria problems. A wastewater
plant, an industrial discharge and a thermal discharge enter the Escambia River upstream of the
mouth at Escambia Bay. Two chemical manufacturing companies discharge into Escambia Bay.
Problems in upper Escambia Bay are complicated by poor flushing due to natural circulation
patterns and a somewhat restrictive railroad trestle which is scheduled to be replaced. On the
eastern side of Escambia Bay is Mulatto Bayou which exhibits dissolved oxygen, nutrient and
transparency problems. Indian Bayou, in the southeastern portion of Escambia Bay, still supports
a seagrass bed community.

In Pensacola Bay proper, water quality improved and is currently assessed as good (Hand et al.,
1988g). A recently completed sampling effort to study the impacts of Pensacola's Main Street
wastewater treatment plant showed that the bay was assimilating the current discharge but that
loadings should not be increased. Florida Dept. of Environmental Regulation (DER) sampling
indicated low diversity and heavy organic sedimentation. Studies are ongoing in Escambia River,
Escambia Bay and Pensacola Bay by Florida DER staff.

Santa Rosa Sound is assessed with good water quality, but is threatened by development of the
barrier island, dredge and fill operations and stormwater runoff (Hand et al., 198 8g). A previous
assessment by Moshiri et al. (1980) concluded that the Sound exhibited serious degradation of
water quality relative to other local estuarine systems and that during warm months red tide
outbreaks were possible. Little Sabine Bay at the terminus of the causeway on Santa Rose Island
exhibited signs of eutrophication evidenced by high nutrient concentrations, low water
transparency, increased algal populations, and low dissolved oxygen concentrations. The study
recommended that no further discharges be allowed to Little Sabine Bay.

A variety of studies in this area have focused on water quality, including nutrient levels, chemical
pollution and pesticide monitoring. The location of a U.S. EPA laboratory on Sabine Island in
Gulf Breeze has facilitated numerous studies of water quality and environmental assessment.
Additional research has been conducted by the faculty of the University of West Florida in
Pensacola.
133
-------
saiaorru
X3QN1 OUOia
q a '
1 s
lift A1ISH3AJO

-------
S 8 8

5 ivsoo
B S S S
X3QNI DM
Noaavo oiNvoao i I • 1

ONVH30

z
a
Eg
rtt
B
£
aoaorru
X3QNI SUCIS
6JD
oo
1H¥ MISM3AIQ
Van snaoHdsoHd

-z
rf
•«E
-ss
-S

/UJAliOnQNOD
135
-------
s s s
« ivsoa
s s 8
X30NI DM
S 2 g B i
Nosavo oiNvoao J. £ S £ c ?
QNVM3Q N3O«0 3
X3QN1 OUOI8
naojnoo i
SnaOHdSOHd
5 a : s
VSM N300U1IN
136
-------
X30NI OUOIS
VOn SnHOHdSOHd
s< s i
Auaiaaru
U 3SV1S
S S S S '
3aniVH3dM3I
137
-------
Moshiri et al. (1974, 1978a,b) examined the extent of nitrogen and phosphorus inputs and their
effects on algal production in Bayou Texar. Nitrogen and phosphorus concentrations decreased
toward the south in the bayou, apparently being related to carbon fixation rates. Ecologically, the
Bayou was approaching eutrophication in 1971 as evidenced by highly fluctuating oxygen and
primary productivity patterns well correlated with algal cell numbers and distribution. As
mentioned earlier in this report, Moshiri et al. (1981) reported a reversal of eutrophication
following the construction of a retention reservoir and weirs in the upstream channel of Bayou
Texar and repair of sewage treatment plants. The authors reported an almost total reduction in fish
Mils, a 90 % reduction in phytoplankton primary production, a virtual elimination of algal blooms
and re-establishment of public use. Fish kills in recent years (1988-1990), however, indicate that
the problem has not disappeared (D. A. Flemer, personal communication).

Dissolved oxygen concentrations obtained by continuous monitoring were used to evaluate
sampling strategies for water quality conditions based on oxygen levels for several northern Gulf
of Mexico estuaries (Summers and Engle, 1992). Dissolved oxygen conditions for estuaries
chosen for expected high frequencies of low dissolved oxygen concentrations in near-bottom
waters (Bayou Chico, Escambia Bay, lower Perdido Bay, and middle Perdido Bay) based on the
assessments of Bault (1972), Rabalais et al (1985) and Windsor (1985) were consistent with the
pre-determinations of water quality. Data from Bayou Chico and Perdido Bay are shown in Figure
53. Sites which were expected to be low-frequency hypoxia stations (Upper Perdido Bay and
Wolf Bay) rarely encountered low dissolved oxygen, and two sites (Pensacola Bay and Santa Rose
Sound) never experienced dissolved concentrations <2 ppm (Figure F53).

Escambia and East Bays have experienced severe vegetation losses since 1949 (Delfino et al.,
1984). A comparison of aerial photographs from 1949 and 1974 indicated that all of the seagrass
beds were gone except for one bed in East Bay. The loss of seagrasses was ascribed to the
synergistic effects of sewage and industrial effluents, dredging and filling activities, beachfront
alterations, and changing watershed characteristics (Rogers and Bisterfeld, 1975, cited in Delfino
etal., 1984).

Fish kills in warm summer months have plagued portions of the system in 1990 and previous
years (Press Gazette, August 16, 1990). The kills of 1990 were of menhaden, a species more
common in offshore waters than estuarine environments. Algal blooms associated with runoff
from nutrient overloading from septic tanks and lawn fertilizers would tend to concentrate these
planktivorous fish. High concentrations of the motile, active fish would rapidly deplete the
available oxygen content of the waters, especially in the heat of the season.

A bloom of the toxic dinoflagellate, Gonyaulax monilata, occurred in the Pensacola Bay estuary
during the same time as an extensive bloom in Mississippi Sound in August 1979 (Perry et al.,
1979). Large areas of discolored water were reported in the Pensacola Bay estuary and in offshore
waters. Fish kills were associated with the bloom.
REFERENCES: F-27

Handera/. (1988g)
Kaufmannetal. (1988)
Moshiri etal (1974,1978,1979,1980)
Olingeretal. (1975)
Sale etal (1988)
Summers and Engle (1992)
Williams etal (1990)
Wolfe etal (1988)
138
-------
j o eo to •* c

(ujdd) N3QAXO 03ATOSSIQ
8

5
in
CM
•^ t- M
• £ S a
o
. m

• 8

- §

-------
ALABAMA

The estuarine systems of Alabama are dominated by the Mobile River delta and Mobile Bay. Other
significant water bodies include Mississippi Sound and Perdido Bay. The Mobile Bay system,
which supports significant natural resources, is experiencing intensive growth and development of
coastal areas, and water quality stress (Horn, 1990). Population growth is evidenced by an
upsurge of condominiums in Baldwin County. Waterborne transportation may increase with the
completion of the Tennessee-Tombigbee Waterway with Mobile Bay as its southern terminus.
Exploitation of mineral resources, particularly natural gas, will increase. There are 106 industrial,
15 sewage and 29 semi-private/small service sources of wastewater discharging into the bay. The
major facilities in the National Coastal Pollutant Discharge Study are shown in Figure Al (Pacheco
et al. 1989a). Nonpoint source contributions (agriculture, forestry, construction, urban runoff) are
not illustrated nor managed to the same degree.

Fish kills and closure of oyster shellfishing grounds, as an obvious indicator of poor water quality,
have been prevalent in coastal Alabama for many years (Crance, 1971). The largest fish kill to
occur in Alabama was attributed to domestic waste which depleted oxygen in the receiving water
body. A summary of the NOAA Fish Kill Inventory Data is given in Table Al.

Much emphasis has been, and is being given, to measuring water quality conditions and trends in
the Mobile-Baldwin County area by the Alabama Department of Environmental Management
(Trend Stations) with support from EPA and NOAA (Horn, 1990). Although increasing
discharges and growth are occurring, water quality measurements over the last two years indicate
that water quality standards in Mobile and Baldwin County have been met 86.7 percent of the time
(Horn, 1990). Several management plans exist or are in preliminary stages for Mobile Bay and
surrounding areas: 1) the South Baldwin County EIS project with EPA to develop and assess
various wastewater management alternatives for coastal Baldwin County, 2) water quality
modeling for Oyster and Wolf Bays, 3) the establishment of the Weeks Bay National Estuarine
Research Reserve, which is managed by the State in a cooperative effort with NOAA, 4) extensive
water quality studies of Perdido Bay involving the States of Alabama and Florida, U.S. EPA,
NOAA and Champion International, and 5) the plans for submission of a nomination of Mobile
Bay as an EPA National Estuary.

The Cooperative Gulf of Mexico Estuarine Inventory (Bault, 1972) covered five areas: East
Mississippi Sound, Mobile Bay, Mobile Delta, Little Lagoon, and Perdido Bay. From April 1968
through March 1969, samples were taken monthly at 21 stations located in the five estuarine areas
for selected chemical and physical properties. The average concentrations of nitrate-nitrogen,
nitrite-nitrogen, and total phosphorus are given in Table A2. During this study, nitrate
concentrations indicated low to moderate pollution (1.0 to 7.0 j/g-at/1) with the Mobile River delta
highest (5.9 /vg-at/1) among the five estuarine areas and Perdido Bay the lowest (2.5 j/g-at/1).
Nitrite values indicated very little pollution, and total phosphorus values indicated moderate to high
pollution (0.5 to 1.0 A/g-at/1). Progressive dilution of the high nutrients in the Mobile River delta is
evident with movement down the axis of Mobile Bay to the Gulf of Mexico.
GENERAL REFERENCES: ALABAMA

ASIWPCA (1984)
Basta and Bower (1985)
Burrage (1989)
Culliton and Blackwell (1989)
Ehler and Basta (1985)
EPA (1974,1978)
Jones et al. (973)
Keys(1975)
Main etal (1987)
NOAA/EPA Team (1990)
Pechmann et al. (1986)
140
-------
Facility Reference
Number (see
Table 5)
Note: Facilities 5,6, and 11
discharge Into the
Intracoastal Waterway
connecting Perdldo Bay and
Mobile Bay. Discharges from
(adlllles 5 and 6 were
assigned to Perdldo Bay, while
discharges from facility 11
were assigned to Mobile Bay.
Mississippi
Sound
Gulf of Mexico
Figure A1. Detailed location of major facilities in the NCPDI study area in Alabama (from
Pacheco, 1978a).
141
-------
Table Al. Summary of NOAA Fish Kill Inventory Data for Alabama (draft data base, 1991; J. A.
Lowe, personal communication; see section on Data Sources).
AREA
County

PERDIDO
Escambia, FL
Baldwin
MOBILE
Mobile
Records
per County

50
23

77
Cause
Low DO

8
18

23
Cause
Eutrophication

• '2
0

1
Cause
Red Tide

0
0

0
Cause
Nutrient

6
0

0
Cause
Unknown or
Unspecified

4
0

7
Table A2. Average concentration of micronutrients in Alabama estuarine study areas from April
1968 through March 1969 (from Bault, 1972).
Nitrate- Nitrite-
nitrogen nitrogen

i
ii
nr
IV
V

Area
Mississippi Sound
Mobile Bay
Mobile Delta
Perdido Bay
Little Lagoon2

Surface
Bottom
Surface
Bottom
Surface
Bottom
Surface
Bottom

Averages of all samples
46.3
67.3
83.1 '
39.0
35.0
Averages of surface and bottom
46.6
45.9
79.8
52.5
103.3
61.3
38.7
39.3
Micrograms
0.8
0.7
0.3
0.3 .
0.9
samples
0.7
0.9
0.5
0.8
3.3
1.1
0.2
0.4
Totml
phoaphorus
per liter
63.2
77.5
98.8
57.9
57.3

60.1
66.6
63.2
91.4
89.9
107.5
61.6
53.9
Fertility
index'

110.3
145.5
184.1
97.3
93.2

107.4
113.4
143.5
144.7
196.5
169.9
100.5
93.6
•Fertility index is the total of nitrate-nitrogen, nitrite-nitrogen and total phosphorous
concentrations. •
'Only surface water was sampled in this area.
F-28 and G-l Perdido Bay/River

The Perdido Bay estuary and River 'are located along the border of Florida and Alabama and is
under the control of environmental departments from both states. This estuary was coded F-28 in
the synthesis of Windsor (1985) and G-l in the synthesis of Rabalais et al. (1985). The main
tributary to the bay is the Perdido River with an average flow of 700-900 cfs (Hand et al., 1988h),
with a total freshwater inflow of 1254 cfs (Windsor, 1985). An unknown quantity of exchange
occurs through the Intracoastal Waterway connections with Pensacola Bay and Mobile Bay. The
estuary is approximately 17 mi long with an average width of 2 mi covering 40 mi2 (Windsor,
1985). The bay averages 3 m deep with a 0.2 m average tidal range at the outlet and a calculated
residence time of 5 d. Water depths slightly in excess of 4.9 m occur in areas near Perdido Beach
142
-------
in the western part of the bay (O'Neill and Mettee, 1982). Deeper areas of the lower reaches of
Perdido River and Elevenmile Creek range 6-8 m in depth (Flemer, 1989). The only outlet to the
Gulf of Mexico is shallow and restrictive. According to Windsor (1985), the bay was considered
to be vertically homogeneous for much of the year but occasionally becomes partially stratified.
More recent syntheses have determined that the bay is moderately to highly stratified (Flemer,
1989).

Wolf Bay is located entirely within the State of Alabama. The Bay, excluding Bay La Launch, is
about 7 km long and the widest point near the southern end is 3.8 km. Water depths in the bay are
shallow, and the deepest parts are slightly in excess of 2.7 m (O'Neill and Mettee, 1982). Wolf,
Sandy, Miflin and Hammock Creeks flow into Wolf Bay at the northern end. Wolf Bay connects
to middle Perdido Bay through Bay La Launch; both then empty to the Gulf of Mexico through
Bayou St. John. Tidal flats and marshes border the northern part of the bay and along the western
side.

The highly urbanized western edge of the City of Pensacola is located along the system and may
contribute significantly to the nonpoint sources of pollutant discharges within the basin. Land use
in the basin is primarily forest and urban. The Perdido Bay system has been the subject of several
water quality studies with the major focus on water quality problems associated with treated pulp
mill effluents which are discharged to Elevenmile Creek and eventually to Perdido Bay. The U.S.
EPA Region IV conducted a survey of .Elevenmile Creek and Upper Perdido Bay in 1986 (Lord,
unpubl.); studies are in progress by the U.S. EPA Gulf Breeze Laboratory (D. Flemer) and Florida
State University (R. Livingston).

Historically there has been little research conducted in the Perdido estuary. One of the more
notable is that by the U.S. Dept. of Interior (1970) on the effects of water pollution on water
quality in Perdido River and Bay. The report concluded that the inadequately treated waste effluent
from the paper company on Elevenmile Creek is the major cause of the low dissolved oxygen,
unsightly foam, excessive sludge deposits and increased lignin in Perdido Bay and River, as well
as degraded water quality in Eleven Mile Creek. Water quality problems in Bayou Marcus were
attributed to the collective discharges to the bayou from six small sewage treatment facilities.

More recently, however, there is a flurry of research activity and resource management plans
(Flemer, 1989). These include: a 1-yr study of nutrients and hydrography, funded by Coastal
Zone Management, NOAA, conducted by Florida Dept. of Environmental Regulation and the
Alabama Dept. of Environmental Regulation (Schropp et at., 1990); U.S. EPA provided funds to
the U.S. Fish & Wildlife Service and a citizens group for an environmental assessment of the bay
and a management plan; Champion International has funded a 2-yr water quality and ecological
assessment of the system, conducted by R. Livingston, Florida State University (Livingston,
1989). The bay system is poorly characterized ecologically except for preliminary studies on the
benthic macroinvertebrate fauna and a partial, recent inventory of trawl and seine collections of
fishes and invertebrates (Flemer, 1989).

An overall degradation of the water quality of the Perdido Bay estuary can be deduced from a
comparison of the figures from the Hand and Jackman (1984) 305(b) report (Figure A2) and that
of the Hand et al. (1988h) report (Figure A3). Elevenmile Creek is still assessed with poor water
quality. Bayou Marcus Creek, which was a combination of poor to fair, is now rated fair. Upper
Perdido Bay, which was rated generally good previously, is now rated poor, middle Perdido Bay,
which was rated generally good, is now rated fair. Representative water quality from middle
Perdido Bay and upper Perdido Bay are shown in Figures A4 and A5, respectively.

According to the most recent 305(b) report (Hand et al., 1988h), the most concentrated and
voluminous pollution source in the basin is a paper company which discharges 28 mgd of partially
treated pulp mill waste into Elevenmile Creek. The historical record shows that the creek has had
143
-------
ELEVEN MILE CREEK
Historic and recent DO,
bacteria, nutrient and
aesthetics problems below
St. Reqis Paper Co. outfall.
BAYOU MARCUS CREEK
Historic and recent DO,
bacteria and nutrient
problems due to several
STP's and urban runoff.
PERDIDO BAY BASIN
Hap Location
EPA Region X Water Quality Index

Good Water Quality

Fair Water Quality
Poor Water Quality
Each symbol location is a STORE!
water quality sampling station.
The larger the symbol size, the
poorer the quality.
Figure A2. Perdido Bay basin [from 305(b) report of Hand and Jackman (1984)].
144
-------
^ CHAMPION
~ ^PAPER
CO.
V "X
^-EIGHTWILE CR,
I J^y
1 y*^AYOU
I ^f M
^S^ AVONDALE ^
UMTP .'
AVERAGE OVERALL HATER QUALITY
1970-1987 SIORET DATA
Map Location
Figure A3. Perdido Bay basin [from 305(b) report of Hand et al. (1988h)].
145
-------
aaraonu
acini ouoia
OO
oo
ON
i i s
datus ivoaj
waojnoo i
Van snaoHdsoHd
• * a

Von NasoaiiN*
Vsw ss
idd AJJNITTS
Vsn oca
S S
VON oa
146
-------
X 8 R B S S
* JWSCW

•z
3
a
s
s
.0 ,
•E
•X
2
*
•S
.£
Noaavo oisivoao i ONVHSQ ^Qao(0
1MV AJJSM3AIO
S S
.ujaiaaru
147.
-------
major water quality problems since the early 1970s. After the installation of a treatment facility at
the paper company, water quality parameters showed some improvement in the mid 1970s;
however, in the early 1980s, production and concomitant pollution increased. Proposed changes
in processing technology are requiring new permitting standards which is being contested by an
environmental group and the State of Alabama. The paper company discharge negatively affects
many water quality parameters, particularly color, dissolved oxygen, BOD, nutrients, turbidity and
solids. The effects of the creek on color, nutrients and biological parameters are seen to about 12
mi into Perdido Bay (the upper two thirds of the bay).

Upper Perdido Bay is also negatively affected by Eightmile Creek and Bayou Marcus Creek which
receive runoff from urbanized areas and have elevated water quality index values. In addition, a
wastewater treatment plant with historical spill problems discharges to Bayou Marcus Creek.
Increased development pressures have kept the plant in operation; but dissolved oxygen problems
below the plant will require higher levels of treatment under a new permit.

Bayou Garcon, which empties into middle Perdido Bay, exhibits transparency and dissolved
oxygen problems. In addition, there have been local reports of increased siltation at the mouth of
the Bayou which has been attributed to new development in the watershed. Within the last few
years, there has been an increase in development in the swampy areas west of Pensacola. During
rainy seasons, runoff from these developments can affect much of the eastern portions of the Bay
and thus exacerbate the degradation of the Bay caused by Elevenmile Creek.

The results of the interstate study of the physical and chemical processes affecting the management
of Perdido Bay are given in Schropp et al. (1990). The report concludes that 1) Perdido Bay
receives nutrients from anthropogenic sources, dominated during the study by materials delivered
by Elevenmile Creek; the Styx and Blackwater Rivers and Bayou Marcus Creek also show
evidence of anthropogenic contributions of nutrients; 2) a substantial portion of carbon delivered to
the estuary is trapped in the upper Bay; 3) physical conditions resulting from natural forces are
such that stratification and hypoxia occur during a major portion of the year, but that oxidation of
carbon trapped in the bay can aggravate seasonal hypoxia; 4) there is evidence of some toxic
contamination of sediments from urban runoff, although contaminants have not reached levels
encountered in other, more developed parts of Alabama and Honda.

The monthly micrpnutrient data from the Cooperative Gulf of Mexico Estuarine Inventory (Bault,
1972) are shown in Figure A6. Perdido Bay had the lowest concentration of nitrite and next to
lowest concentration of nitrate of the five areas. The combined total for the nutrients measured was
the next to lowest. Data from a more recent study (Lord, unpubl.) are shown in Figures A7-A10.
These results indicate that Perdido Bay proper is characterized by low nutrient concentrations.
Dissolved inorganic nitrogen is <1 mg/1 orthophosphate is usually <0.02 mg/1, and phosphate
levels are low.

Data from the Alabama portion of the Perdido Bay/River area were collected by the Alabama
Marine Resources Division at four stations, including two in Wolf Bay (one in the Gulf
Intracoastal Waterway), one in Bayou St John which connects Wolf Bay to Perdido Bay, and one
in Perdido Pass which empties into the Gulf of Mexico. The study by Bault (1972) included
stations in Wolf Bay and Perdido Pass, as well as a station in Perdido Bay proper.

Bault (1972) reported few records of low dissolved oxygen. On the other hand, the data collected
by the Alabama Marine Resources Division show several incidences of oxygen-depleted water in
most months at all stations (values mostly between 1 and 2 mg/1). The lowest values are in the
Wolf Bay area; at one station over 90 % of the incidences have been since March 1983. Personnel
from the agency indicated that Wolf Bay/Perdido Bay are very susceptible to low dissolved oxygen
and have been since initiation of hydrographic sampling there in October 1980 (M. Van Hoose,
personal communication). Loadings from pulp mill effluents and increased sewage from
148
-------
Total phoiphonia
Xltnt4 - nltropn
Xltrlu - Bitropn
Figure A6. Monthly average concentrations of micronutrients in Perdido Bay from January 1968
through March 1969 (from Bault, 1972).

residential and recreational housing development are credited as probable causes for the increased
incidence of low oxygen concentrations. Several instances of dissolved oxygen violations were
noted by Windsor (1985) for Perdido Bay, particularly the tributaries, Elevenmile Creek and
Bayou Marcus Creek. More recent dissolved oxygen values were collected by Van Hoose (1988)
for April 1987 to March 1988 at trawl sampling stations (thus presumably bottom dissolved
oxygen levels). In the lower bay oxygen concentrations ranged from 3.2 (June) to 10.4 (April)
ppm; in the middle bay, 0.4 ppm in August to 1L4 in April; in the upper bay, 11.0 ppm in April
and 0.4 ppm in August. Long-term changes of dissolved oxygen concentrations in Perdido Bay
were analyzed by Livingston (1989) who demonstrated no change in the upper river, but a
decrease in summer dissolved oxygen levels in the lower river which became progressively lower
with time (Figure All).

See comments in Section F-27 regarding continuous dissolved oxygen measurements in Perdido
Bay (upper, mid and lower) and Wolf Bay as well as Figure F53.

The USFWS report (in prep.) on fish and shellfish populations for the period 1975 through 1988,
indicates a reduction in certain finfish diversity measures and numbers of trawl-catchable finfish in
upper Perdido Bay, and a pronounced masculinization of mosquitofish in Elevenmile Creek. For
the lower Bay, a general pattern that seems to emerge is that summertime finfish resources have
declined during the period 1983-1988; while wintertime finfish resources have varied considerably
during the same period, with a peak in abundance as recently as the winter of 1986-1987.
Analysis of trawlable-fish data by Livingston (1989) indicates that during the 1980s there was a
serious deterioration of the fish fauna of Perdido Bay. The community indices showed that this
trend was based on reduced numbers of species as well as increased dominance. Because of
inadequate habitat data, however, no real estimate can be made concerning the reason(s) behind the
marked decline of the Perdido Bay fish fauna during the 1980s. ,
149
-------
B

C
03
-

•a
o
•a
I
o
o
C/5

3
c/2

"8
T3

I
3
C/5 /^

•3s
T3 C

C 3
ctt ^

v> O

11
r-~
oSo

&•§
o 2
cC

tU)r
-
S o
o *

150
-------
151
-------
2
o
O
OH

4-*
00

• O
•a

I
85
•7
o a
« 3
SB
.2 3
I-8.
a _r
§^
it
il

s-
11
oo
ON
S
152
-------
C/3 •

It
0
&&
If
•SB
•§•8
!§
£3
o\ -a
it

13
^

II
It
•a-s-
II

153
-------
•z.
tu
(3

X
o

Q
US

O
O)
CO

Q
12

11 -

10-

1 -
N -*r
MONTHS: 5/70-8/86
ui
(3

X
O

Q
UI
O
CO
CO

Q
MONTHS: 10/66-9/88
Figure Al 1. Dissolved oxygen concentrations in the Perdido River at the surface (upper panel)
and near the bottom (lower panel) for periods indicated (Livingston, 1989).
154
-------
REFERENCES: F-28andG-l

Bault (1972)
Butts (1983)
Crance (1981)
Dardeau (1987)
Flemer (1989)
Flor. Dept. Envir. Reg. (1989)
FWPCA(1970)
Gunning and Suttkus (1986)
Handera/. (1988h)
Heck (1987)
Livingston (1989)
Lord (unpubl.)

G-2 Mobile Bay/River/Tensaw River
O'Neil and Mettee (1982)
Pachecoero/. (1989a)
Rabalais etal (1985)
Schroeder (1976)
Schropp et al (1991)
Summers and Engle (submitted)
Swingle (1971)
Swingle and Bland (1974)
U.S. Fish Wild. Serv. (in prep.)
Van Hoose (1988)
Williams etal. (1990)
The surface area of Mobile Bay is 984 km . The average depth is 3 m and the maximum depth is
20 m off Fort Morgan at the Gulf entrance. Although the bay is a relatively shallow basin, it has a
complex bathymetry with topographic lows throughout the northeastern part and a dredged ship
channel, 120 m wide and 12 m deep, traversing die length of Mobile Bay and into the Mobile
River. There are two natural openings into the Gulf of Mexico at Main Pass and at Pass aux
Herons into Mississippi Sound. A dredged channel, the Gulf Intracoastal Waterway crosses the
southern end of the Bay, linking Perdido Bay with Mississippi Sound. The entire system of
channels in the delta is collectively called the Mobile River, but this name actually refers to the
largest and most westerly channel. The delta receives the inflow of the Mobile-Tensaw, Alabama
and Tombigbee Rivers. The Mobile River system delivers 95 % of the total freshwater input to the
bay (Schroeder, 1978, cited in Turner et al., 1987), with a discharge rate of 60,000 cfs
(Isophording and Lamb, 1979). The Mobile and Tensaw River systems receive drainage from
over 64 % of the land area of the state of Alabama (Horn, 1990).

The Bon Secour River enters the southeastern corner of Mobile Bay, and flows from Dog River
and E. Fowl River enter the western side of the Bay. Weeks Bay is a subestuary on the eastern
shore. Little Lagoon (1047 ha) is considered in many treatments of Mobile Bay. Freshwater
enters the Lagoon from rainfall, groundwater seepage and a connection with Shelby Lake. A
small, shallow pass sometimes connects the Lagoon with the Gulf of Mexico, although most of the
time this pass is completely closed (Swingle, 1971).

The monthly micronutrient data from the Cooperative Gulf of Mexico Estuarine Inventory (Bault,
1972) are shown in Figure A12. Mobile Bay had the second highest total concentration of all the
areas (highest in the Mobile River delta). The area also ranked second in nitrate-nitrogen and total
phosphorus. Mobile Bay receives fresh water from the Mobile River delta. Domestic and
industrial effluents from the city of Mobile and other nearby areas .contribute to the nutrient
loading. Surface values of nitrate were higher than bottom waters, most probably due to
stratification of the two water sources—Mobile River delta and Gulf of Mexico. Total phosphorus
was low in surface waters and similar to the other areas, with the exception of Perdido Bay which
was higher.
•- \
Data from the Cooperative Gulf of Mexico Estuarine Inventory (Bault, 1972) for the Mobile River
delta are shown in Figure A12. Each of the nutrients measured was highest in this study area.
Nutrients from the Alabama-Tombigbee river system and effluents from municipalities and
industries above Battleship Parkway contribute significantly to the nutrient loads. Nitrate
155
-------
- Total phosphorus
-Hltr»U-
• IHiiU -
Figure A12. Monthly average concentrations of micronutrients in Mobile Delta (upper panel),
Mobile Bay (middle panel), and Little Lagoon (lower panel) from January 1968'
through March 1969 (from Bault, 1972).
156
-------
concentration was much greater than that of any other area. Nitrite nitrogen concentrations were
also high. Total phosphorus averaged a significant amount more than in Mobile Bay. Similar
values from the Cooperative Gulf of Mexico Estuarine Inventory (Bault, 1972) for Little Lagoon
are given in Figure A12.

J. Pennock (personal communication) has been conducting studies of nutrients, nutrient limitation,
and features of the physical environment that may be affecting biological processes in Mobile Bay
beginning in 1989. The work is in progress, but he has made a preliminary assessment of the
nutrient enrichment status of Mobile Bay (abstract in Hinga et al., 1991). Pennock states that
Mobile Bay receives moderate loadings of bqth nitrogen and phosphorus, primarily from upstream
nonpoint sources. Despite significant loadings, however, ambient nutrient concentrations at the
upper end of the Bay attain concentrations of <20 j/M inorganic N and <2 /;M inorganic P (10 and
five times less than those for the Delaware Bay estuary) as a result of the relatively high flushing
rate of the system. Although these nutrient concentrations suggest that Mobile Bay should have a
relatively low susceptibility to nutrient enrichment, several responses often associated with
eutrophication are evident. For example, chlorophyll a concentrations have been observed as high
as 100 j/g/1 during the winter, and recurring hypoxic conditions are seen during summer. While
organic loading to Mobile Bay is undoubtedly important to the observed response in chlorophyll a
and dissolved oxygen (these data are not yet available), it is evident that stratification in Mobile Bay
resulting from salinity intrusions through the shipping channel is important in the low oxygen
concentrations as well.

Schroeder and Wiseman (1986, cited in Turner et al., 1987) report that strong vertical stratification
occurs in Mobile Bay during periods of both 1) high river discharge and weak winds and 2)
persistent southward-directed wind stress and low river discharge. Large areas of the bay are
affected by hypoxic conditions (Figure A13) (Schroeder and Wiseman, 1988). Strong winds,
however, can rapidly dissipate these conditions. Hypoxia quickly redevelops following re-
establishment of the stratification after a wind event. Oxygen depletion in the shallow bottom
waters of Mobile Bay, and in adjacent nearshore and continental shelf waters, was shown by
Turner et al. (1987) to be directly related to the intensity of water column stratification (Figure
A14). Low wind speeds were coincident with the onset of water column stratification and the
occurrence of hypoxic events. Hourly, daily and seasonal changes in the relationship between
percent oxygen saturation or oxygen concentration in bottom wasters and surface-to-bottom
density differences indicated that the oxidized materials were recently formed and were not relic or
overwintering carbon sources.

The deeper areas of Mobile bay experience hypoxic or anoxic bottom waters throughout the year.
These include Mobile Ship Channel, Theodore Industrial Canal and Theodore Barge Channel
extension (Alabama Marine Resources Division; Marine Environmental Sciences Consortium;
Swingle and Bland, 1974). Two deep holes off Brookley Field are subject to low dissolved
oxygen values in the colder months; these low values are often associated with speckled trout kills
(M. Van Hoose, personal communication).

"Jubilee" is the local name for the shoreward movement of dense concentrations of fish and
invertebrates (Loesch, 1960; May, 1973). This phenomenon has been presumed to be associated
with the movement of the leading edge of a low oxygen zone. When hypoxic bottom water
conditions coincide with a period of light (< 5 m/s) to calm winds followed by a day or two of
persistent easterly winds, often associated with a rising tide, the surface waters move away from
the eastern shore and the lower hypoxic layers move toward the eastern shore and cause a mass
migration of estuarine organisms into shallow waters. This celebratory collection of moribund but
often edible seafood has been observed to occur in Mobile Bay since at least 1867 (May, 1973),
before significant man-made changes in the estuary that might affect the occurrence of jubilees
(Figure A15) (May, 73). Man-made modifications have interacted with the bays geomorphology
157
-------
Figure A13. Bottom dissolved oxygen field on July 18,1978 (concentrations are in ml/1) (from
Schroeder and Wiseman, 1988).

and natural hydrology to result in zones of oxygen-depleted bottom waters. Dredged channels
complicate the otherwise shallow Mobile Bay. Dredge disposal material island and shoals are
located along the ship channel. Deep holes are found in the central area of the northeastern part of
the bay. Natural, not man-made factors, are principally involved in jubilee events, although recent
anthropogenic activities may have increased their frequency or intensity, according to Turner el al.
(1987).
158
-------
0 2.5 5 7.S 10 12.5 15 17.5 20 22.5
ASigmat
Figure A14. The relationship between surf ace-to-bottom differences in sigma t and dissolved
oxygen for northern Mobile Bay (upper panel) and southern Mobile Bay (middle
panel) and the adjacent continental shelf (lower panel) (from Turner et al., 1987).
A bloom of the toxic dinoflagellate, Gonyaulax monilata, occurred in lower Mobile Bay during the
same time as an extensive bloom in Mississippi Sound in August 1979 (Perry et al., 1979). Fish
kills were associated with the bloom. Dinophysis caudata has been recognized recently as a toxic
dinoflagellate which may contribute to the accumulation of toxins responsible for diarrhetic
shellfish poisoning (DSP) in Mobile Bay (R. Hickey, personal communication).
REFERENCES: G-2

Abbott (1975)
Abston etal. (1987)
Bault (1972)
Crozier and Heath (1974)
Dauphin Isl. Sea Lab (1983)
Dennis etal. (1984)
Donohoe and Calhoun (1982)
McPhearson (1970)
NOAA (1990b)
O'Neil and Mettee (1982)
Pachecoera/. (1989a)
Renaud (1985)
Ruckeretal. (1990)
Schroeder (1976,1979)
159
-------
a
W)

1
•s
o
cd
PH
"8
o
t:
- *
,O CO
CQ •

l
TO Cv

It
bO
E
160
-------
GURC (1979)
Horn (1990)
Ingle etal. (1955)
Isphording (1982)
Isphording and Lamb (1979)
Loesch (1960)
Lowery (1987)
Lysinger (1982)
Mar. Envir. Sci. Cons. (1979)
May (1973)
Schroeder and Lysinger (1979)
Schroeder and Wiseman (1988)
Schroeder etal (1990)
Shaw etal. (1982)
Skupien (1989)
Swingle (1971)
Swingle and Bland (1974)
Turner etal. (1987)
Williams etal. (1990)
Wiseman etal. (1988)
G-2.1 Alabama inner continental shelf

In a series of five cruises between March 1987 to March 1988 along three north-south transects
across the Alabama and Mississippi continental shelf (Darnell, 1991), nitrate concentrations were
uniformly low during the summer months but fairly high during the winter especially along the
transect closest to the Chandeleur Islands and the outflow of the Mississippi River (Table A3).
Phosphate values were uniformly low during both seasons (Table A4).

Low dissolved oxygen values were not found on the Alabama inner continental shelf offshore of
Mississippi Sound and Mobile Bay in a benthic survey conducted by Shaw et al. (1982); sampling
was conducted, however, in spring and fall when hypoxia would be less likely to occur. Oxygen
deficient bottom waters have been documented by W. Schroeder and colleagues (personal
communication) in bathymetric depressions on the inner continental shelf just offshore of and
adjacent to Mobile Bay. In the same series of cruises listed above (Darnell, 1991), bottom water
dissolved oxygen concentrations were not reported as hypoxic at three stations along the 20-m
isobath (Table A5). In two instances, however, where no data were recorded in the tables of the
text of the report, data were recorded in the Appendices (Brooks and Wolff, 1991). These values
were 2.48 mg/1 (March 1988, station M-l) and 0.00 mg/1 (October 1987). The water column was
highly stratified near the seabed in both instances, and nutrient concentrations in bottom waters
were elevated; these conditions indicate that low oxygen concentrations would not be unusual.
Although the Mississippi and Alabama inner shelf has the potential for bottom water hypoxia, such
events are not considered frequent nor widespread.

A bloom of the toxic dinoflagellate, Gonyaulax monilata, occurred in waters adjacent to Mobile
Bay during a bloom within the lower bay in August 1979 (Perry et al., 1979). Fish kills were
associated with the bloom.
REFERENCES: G-2.1

Abstonetal. (1987)
Atwood(1981)
Brooks and Wolff (1991)
Churgin and Halminsta (1974)
Cons. Perm. Int. Exp. Mer (1936)
Darnell (1991)
El-Sayedetal. (1972)
Eleuterius and Beaugez (1981)
Eleuterius etal. (1981)
Fanning etal (1982)
Kjerfve and Sneed (1984)
O'Neil and Mettee (1982)
Riley (1937)
Russell (1977)
Schroeder (1976)
Schroeder and Crozier (1974)
Schroeder etal (1988)
Shaw etal.( 1982)
Stuntz et al. (N.D.)
Thompson and Bane (1986a,b)
Thompson and Leming (1978)
Thompson et al. (1988)
Turner et al. (1987)
Wiseman etal. (1988)
161
-------
Table A3. Dissolved oxygen values (mg/1) for bottom waters of Mississippi and Alabama
continental shelf. Stations C-l, M-l and D-l are on 20-m isobath on north-south
transects offshore of Mississippi Sound, Mobile Bay and Perdido Bay,
respectively (from Darnell, 1991).
Winter
Cruise No.
B-O
B-2
B-4
X
c
1
5.18
5.08
7.74
6.00
2
3.98
5.59
7.47
5.68
3
3.11
—
4.85
3.98
' 4
2.99
—
4.83
3.89
M
1
5.30
—
8.28
6.79
2
3.87
5.28
7.94
5.70
3
3.02
6.43
5.30
4.92
4
2.93
4.62
4.98
4.18
D
1
5.50
8.99
8.24
7.56
2
3.68
7.78
7.02
6.16
3
3.17
4.89
7.93
5.33
4
3.1O
4.63
4.22
3.98
Summer
B-l
B-3
X
—
7.00
7.00
4.70
6.40
5.55
4.62
4.78
4.70
4.82
4.84
4.83
—
5.88
5.88
5.80
6.13
5.97
4.63
6.00
5.32
4.70
5.69
5.20
7.77
6.05
6.91
--.
6.44
6.44
5.48
5.23
5.36
4.60
4.26
4.43
Table A4. Surface water nitrate values (uM/kg) [sic] of Mississippi and Alabama continental shelf.
Stations C-l, M-l and D-l are on 20-m isobath on north-south transects offshore of
Mississippi Sound, Mobile Bay and Perdido Bay, respectively (from Darnell, 1991).

Winter
Cruise No.
B-O
B-4
X
C
1
1.32
0.08
0.70
2
1.47
1.85
1.66
3
O.47
0.28
0.95
4
1.59
0.31
0.95
M
1
O.29
0.27
0.28
2
O.12
0.10
0.11
3
0.26
1.26
O.76
4
0.08
0.18
0.13
D
1
0.08
0.16
0.12
2
0.19
0.25
0.22
3
O.20
—
0.20
4
O.O4
0.18
0.11
Summer
B-l
B-3
X
0.2O
0.09
0.15
O.2O
0.06
O.13
0.20
0.07
0.14
0.20
0.02
0.11
0.10
0.07
O.O9
0.10
0.04
O.07
0.20
0.11
0.16
0.1O
0.10
0.10
0.20
0.15
0.18
0.20
O.O6
0.13
O.10
O.O6
0.08
0.10
0.14
0.12
Table A5. Surface water phosphate values (uM/kg) [sic] of Mississippi and Alabama continental
shelf. Stations C-l, M-l and D-l are on 20-m isobath on north-south transects
offshore of Mississippi Sound, Mobile Bay and Perdido Bay, respectively (from
Darnell, 1991).

Winter
Cruise No.
B-O
B-2
B-4
X
C
1
0.13
0.15
O.O2
0.10
2
0.19
O.32
O.14
0.22
3
O.10
—
0.08
0.09
4
0.20
—
0.12
0.16
M
1
0.18
O.13
O.30
0.20
2
0.17
O.17
O.ll
0.15
3
0.23
0.20
0.14
0.19
4
0.16
0.20
0.05
0.14
D
1
0.17
O.O9
0.24
0.17
2
0.12
—
0.16
0.14
3
0.12
0.15
0.16
0.14
4
0.09
0.18
0.00
0.09
Summer
B-l
B-3
X
0.18
0.15
0.17
0.27
0.26
0.27
0.20
0.12
O.16
0.28
0.37
0.33
0.15
0.23
0.19
0.09
0.14
0.12
0.06
0.13
0.10
0.03
0.14
0.09
0.15
0.25
0.20
0.15
0.14
0.15
0.05
0.08
0.07
0.09
0.26
0.18
162
-------
G-2.2 East Mississippi Sound

A general description of Mississippi Sound is given in the introduction to the State of Mississippi.
Several studies have been conducted within the Alabama portion of the Sound and are detailed
below. The artificial western boundary for East Mississippi Sound is the State border which runs
north from Petit Bois Island, on the south, to the Grande Batture Islands on the northern side. The
north part of the Sound is typically shallow and bordered by marshes and portions of modified
shoreline. The mid Sound is characteristically an area of quiescent waters and slow sedimentation.
The barrier islands of Dauphin Island and Petit Bois Island separate the Sound from the open Gulf.

The monthly micronutrient data from the Cooperative Gulf of Mexico Estuarine Inventory (Bault,
1972) are shown in Figure A16. Mississippi. Sound ranked third in nitrate-nitrogen, nitrite-
nitrogen, total phosphorus and the total of these three (= fertility index). Minimal differences
between surface and bottom water samples indicated that the water column was generally well-
mixed. The level of nutrients is influenced by waters from the Gulf of Mexico which are relatively
low in the nutrients measured. Some nutrient loadings, however, enter from Mobile Bay, Bayou
LaBatre, Bayou Coden and Dauphin Island. Pascagoula Bay in Mississippi may also be a.
significant source of nutrients. The average nitrate concentration for Mississippi Sound was not
significantly different from that in Perdido Bay. This similarity may be due to the shallow depths
and well-mixed water column. Total phosphorus was low in surface waters and similar to the
other areas, with the exception of Perdido Bay which was higher.

Oxygen-depleted bottom waters have been recorded at the stations of Bault (1972) in mid-Sound
and those of Swingle and Bland (1974) in tributaries to the Sound. Oxygen-depleted bottom
waters have been recorded at these stations, but infrequently (2 out of 20 records at Bayou
LaBatre, 3 out of 200 records mid-Sound). Salinity stratification of Gulf waters intruding into the
less saline waters of the Sound through the deeper channel of Petit Bois Pass is implicated in
oxygen depletion in the latter location (M. Van Hoose, personal communication).

The extensive bloom of Oscillatoria (Trichodesmiwn) erythraea, which occurred in Mississippi
Sound in 1974 was also recorded in the eastern end of the Sound within Alabama State waters, but
the extent of the distribution was not determined (Housely, 1976 cited in Eleuterius et al., 1981).
REFERENCES: G-2.2

Bault (1972)
Donohoe and Calhoun (1982)
Eleuterius and Beaugez (1981)
Eleuterius etal. (1981)
Isphording and Lamb (1980)
Kelly (1981)
Lytle and Lytle (1990)
McPhearson (1970)
O'Neil and Mettee (1982)
Pachecoera/. (1989a)
Schroeder(1976)
Shaw etal. (1982)
Swingle (1971)
Swingle and Bland (1974)
163
-------
16.0

9.0,

ll.O.

2.0.

J 1.0.
I 0.6
•

b °-s

2 0.1,.

0.3.

0.2.

0.1.
0.0.
•*
Figure A16. Monthly average concentrations of micronutrients in Mississippi Sound from January
1968 through March 1969 (from Bault, 1972).
MISSISSIPPI

Mississippi Sound dominates the estuarine system of the State. According to many authors, the
complex includes the small bays, marshes, bayous, and rivers along the northern shore. Others
treat the secondary bays as separate hydro-logic units. For this review, we will incorporate data,
where available, for the entire complex into a single synthesis. Where data are specific to the
Sound, or a bay, they will be identified as such in the appropriate units designated below. The
hydrology and physical and biological characteristics of Mississippi Sound cross state borders.
The Mississippi-Louisiana state line traverses Mississippi Sound between Cat Island to the Pearl
River which forms the landward border. The Alabama-Mississippi state line runs directly north of
the most easterly end of Petit Bpis Island. Water circulation does not recognize political
boundaries. Water quality monitoring programs, however, do. Data for the Sound should include
the westerly portions where Lake Borgne and the Pearl River enter and the easterly portion which
falls within the state of Alabama. Where systemwide studies have been conducted, the results are
more appropriate for comparisons and observations of trends. Political subdivisions, however,
dictate much of the data collected, and it is sometimes less informative to compare data of varying
temporal and spatial coverage and differing foci or analytical methods.
GENERAL REFERENCES: MISSISSIPPI

ASIWPCA (1984)
Basta and Bower (1985)
Burrage (1989)
Culliton and Blackwell (1989)
Ehler and Basta (1985)
EPA (1974,1978)
Jones era/. (973)
Main etal (1987)
NOAA/EPA Team (1990)
Pechmann et al (1986)
Turner and Rao (1990)
164
-------
AL
Mississippi
Sound (3.12)
Mississippi
' River (3.13)
Gulf of Mexico
LEGEND

Dots indicate locations of major point source dischargers

Stippling patterns show the Mississippi portion of the NCPDI study area
Figure Ml. Location of major point source discharges in Mississippi (from Pacheco, 1989b).

Table Ml. Pollutant variables in Mississippi Sound surface sediments (from Lyde and Lytle,
1990). ,
Location
Pascagoula River
(26 samples)
Biloxi Bay
(19 samples)
St. Louis Bay
(4 samples)
Mississippi Sound
(15 samples)
Gulf of Mexico
(1 sample)
TOC
. <*>.
4.05 - 3.98
0.145-14.0
1.76 -*- 0.832
0.315-3.67
1.45 ± 0.777
0.328-2.08
0.869 •+• 0.420
0.096-1.36
1.09
TKN
(mg g-1)
1.43 + 1.21
n.d.-4.24
0.88-<- 0.616
0.07-2.59
1.19 ± 0.200
0.97-1.39
0.568 -«- 0.505
0.0045-1.55
0.73
Phenols
(egg-).
1.04 ± 0.727
n.d.-2.75
0.604 ± 0.510
0.254-2.39
0.543 ± 0.167
0.378-0.773
0.647 ± 0.493
0.224-1.77
0.285
Total HC
(Mg g-1)
1,800 ± 3,520
0.20-13,300
686 ± 1,970
1.15-8,600
36.6 ± 21.0
12.8-63.9
16.8 ± 12.2
0.986-69.9
18.9
Aromatic HC
(egg-1)
211 ± 432
n.d.-l,930
186 ± 595
0.410-2,610
7.37 = 2.82
a K9 Q 77
3.07 + 2.96
0.070-11.0
3.77
'Total Kjeldahl nitrogen, total organic carbon, total hydrocarbons, aromatic hydrocarbons, and phenols. Reported values are
mean ± one standard deviation/minimum-maximum values, n.d. is not detected and entered as 0.0 in mean calculations.
165
-------
Table M2. Summary of NOAA Fish Kill Inventory Data for Mississippi (draft data base, 1991;
J.A. Lowe, personal communication; see section on Data Sources).
AREA
County

MISSISSIPPI
Hancock
Harrison
Jackson
Records
per County

SOUND
5
3
2
Cause
Low DO

0
0
0
Cause
Eutrophication

0
0
0
Cause
Red Tide

0
0
0
Cause
Nutrient

0
0
0
Cause
Unknown or
Unspecified

0
. 0
1
G-2.3 Mississippi Sound, Gulf Islands area and mid-Sound

A general description of the Mississippi Sound Complex is given by Eleuterius (1976a).
Mississippi Sound is an elongate water body which is separated from the open Gulf of Mexico by
a series of barrier islands. Narrow peninsulas and shallow shell reefs connecting Dauphin Island
to the Alabama mainland separate the Sound from Mobile Bay on the east. Fresh water enters the
Sound on this eastern end from Mobile Bay. It is estimated (Austin, .1954; cited in Eleuterius,
1976a) that one-fifth of the discharge from Mobile Bay is diverted into Mississippi Sound mainly
via Grants Pass. On the western end, the Sound receives input from Lake Borgne and the Pearl
River, and indirectly from Lake Pontchartrain and the Mississippi River, even more infrequently,
when the Bonnet Carr6 spillway is opened. Several other major sources of fresh water enter the
Sound directly: The Pearl River on the western end with a flow of 11,580 cfs, and the Pascagoula
River with an average flow of 13,369 cfs. The Biloxi and Tchoutacabouffa Rivers (flows of 494
and 437 cfs, respectively) reach the Sound via Biloxi Bay. The Jourdan and Wolf Rivers empty
into St. Louis Bay with average flows of 1,535 and 706 cfs, respectively. Tidal bayous contribute
lesser amounts of fresh water. Connection through passes and over shoal areas along the barrier
island chain permit the intrusion of higher salinity Gulf of Mexico waters.

The Sound is relatively shallow with an average depth of 3 m (Eleuterius, 1976a). The greater
depths, caused by tidal scouring action, are located at the immediate western tips of the barrier
islands. Three channels traverse Mississippi Sound. The ports at Pascagoula and Gulfport have
deep water access with authorized depths of 13 and llm, respectively. The third, Biloxi Channel,
used primarily by barge, commercial fishing vessels and pleasure craft, has an authorized depth of
4 m. A fourth channel, The Gulf Intracoastal Waterway, spans the east-west axis of the Sound at
an authorized depth of 4 m which is exceeded in most parts of the Sound by the natural
bathymetry.

Circulation and salinity in the eastern end of Mississippi Sound is controlled by influx of Mobile
Bay discharge through Petit Bois Pass and topographic features which direct the outflow of the
Pascagoula River (Eleuterius, 1976a). Circulation and salinity in the central portion of Mississippi
Sound is largely attributable to tidal flux through Dog Keys and Ship Island passes. Tides entering
through the two passes converge approximately along a north-south line bisecting Camille Cut.
Since there are no fresh or low salinity water sources between Biloxi Bay and St. Louis Bay, this
convergence zone brings higher salinity water closer to the mainland than anywhere else in the
Sound. West Mississippi Sound displays an overall consistently lower salinity. The water column
is usually well-mixed, but occasionally during periods of moderate freshwater inflow, it displays a
pronounced halocline.
166
-------
The greatest abundance of industrial development has occurred in the Pascagoula River, Escatawpa
River and Bayou Casotte (Lytle and Lytle, 1990). Biloxi Bay has a moderate degree of
industrialization and St. Louis Bay and Heron Bay have little industrial development. Figure Ml
shows the location of the major point source discharges within the estuarine drainage area of
Mississippi Sound. Extensive work by Lytle and Lytle (1985, 1990, and references therein) has
documented the distribution of organic pollutants. Sediment sampling was conducted over a 3-yr
period. TOC values were greatest in the Pascagoula River with Biloxi Bay having considerably
lower TOC values, and TOC in St. Louis Bay occurred at levels only slightly higher than the
Sound and Gulf samples (Table Ml) (Lytie and Lytle, 1990). Using TOC as a gross indicator of
pollution, the strongest evidence of pollution exists for discrete sample sites along the Pascagoula
River, with some sites in Biloxi Bay also showing unusually high TOC. Ranges of TKN were
less dramatic, although there were generally higher values in the bays and rivers compared to the
Sound and Gulf with isolated highs near municipal sewage discharges, as expected (Table Ml).
Phenols were observed at highest levels in the eastern Sound near industrial sources, but at most
sampling sites were <1 ppm (Lytie and Lytie, 1985). Hydrocarbons were the most significant of
the pollutants found in the sediments of Mississippi Sound. Concentrations were found in Bayou
Casotte and other regions in the eastern Sound and were related to petroleum associated with an oil
refinery, fuel oil, and sewage. Land runoff apparently also contributed some of the pollutants. Of
particular concern was the presence of significant levels of polynuclear aromatic hydrocarbons.

Several freshwater tributaries of the estuarine system in Mississippi have been closed to
commercial fishing because of the presence of dioxin in flathead catfish (Houma Daily Courier,
October 7, 1990). Two of the tributaries enter the Pascagoula River which eventually enters
Mississippi Sound. The dioxins are attributed to the operations of the Georgia-Pacific pulp and
paper mill.

The general results from the studies of Lytie and Lytle indicate highly localized areas of
contamination existing within the rivers and bays of the Mississippi Sound region while there are
much larger areas that have relatively little pollution from hydrocarbons. Even in rivers emptying
directly into the sound, e.g., the Pascagoula rivers, there is little evidence that riverine pollutants
have much impact on Sound sediments (Lytle and Lytie, 1990). The movement of pollutants
related to a paper mill revealed that the only sediments which were significantly enriched were in
the immediate vicinity of the paper mill (in the Escatawpa River). Tracing hydrocarbon pollutants
from Bayou Casotte east of the Pascagoula River also revealed minimal migration of these
pollutants from this heavily industrialized bayou into the Sound.

An increase in recurring fish kills of mostly juvenile menhaden was noted in the text supporting the
need for the Cooperative Gulf of Mexico Estuarine Inventory and Study within Mississippi
(Christmas, 1973). The data for Mississippi in the NOAA Fish Kill Inventory data base were
limited, and none indicated aspects of nutrient enrichment and eutrophication as causes (Table M2).
However, anecdotal evidence and the Mississippi Dept. of Natural Resources Water Report (1988)
points to fish kills as a cause for concern within the Mississippi Sound estuarine complex.

The Cooperative Gulf of Mexico Estuarine Inventory and Study for Mississippi (Christmas, 1973;
Christmas and Eleuterius, 1973) documented water quality, including dissolved oxygen and
nutrients during 1968-1969 for Mississippi Sound and its sub-basins. Additionally, nutrient
samples were taken as part of a hydrography study of Mississippi Sound in 1973-1975
(Eleuterius, 1976b).

The average values for nitrate, nitrite, orthophosphate and total phosphorus for Mississippi Sound
are shown in Figures M2 and M3 (Eleuterius, 1976b). Eleuterius documented lower nutrient
levels above the Escatawpa River-Pascagoula River confluence than in the lower Pascagoula River.
The high levels and variability of phosphorus and nitrogen in the lower Pascagoula River reflect
the local introduction of effluents. The apparent inverse relationship between levels of nitrate and
167
-------
02
•a
a
03
OJ
tin
a
O
jf'l
.^w
.5 a
si
168
-------
S S

3 S
s a
8 8

S S
I

o
-a
•a

I?
"^ OH
0> OS
11
as
169
-------
phosphorus was limited to the lower Pascagoula River and attributed to changes in activities within
the drainage basin. In general, levels of all nutrients declined seaward to the barrier island passes.
Seaward of the passes, nitrate levels exceeded those of the Sound. General trends for a decrease in
nutrients with less variability were seen with distance westward in the Sound. The primary
sources of nutrients in the Sound are Pascagoula River, Bayou Casotte, Biloxi Bay and Pearl River
(Eleuterius, 1976), but the Pearl River's contribution appears to be low.

The waters within and in the vicinity of Bayou Casotte showed consistently high levels of
phosphorus and nitrate (Eleuterius, 1976). The major portion of the phosphorus is inorganic;
several chemical plants that manufacture fertilizer are located in an industrial plant next to the
bayou.

There are no new data that would indicate a different assessment of Mississippi Sound with
regards to dissolved oxygen level; but the general summary is presented again in the context of a 2
mg/1 criteria. Low dissolved oxygen levels are infrequently found in Mississippi Sound during the
warmer months of April through September. The lowest values are found just inside the passes
which cut through the barrier islands (as well as just off the passes). Stations 81 and 84 of the
GCRL, FAM data set, are those with the most frequently recorded hypoxia (F. Sutter, personal
communication). Suspected mechanisms for the low dissolved oxygen content found in bottom
waters just inside and outside of the passes, involve density stratification from higher salinity,
lower temperature bottom water intruding onto the inner shelf and into the Sound. The degree of
density stratification in the water column would differ depending on the east-west salinity
differences present in the Sound. The effects of these oxygen-depleted bottom waters are seen in
the death of crabs in traps, occasional jubilees of adult white shrimp (Penaeus setiferus) along the
Mississippi shore, and a suspected decline in the white shrimp fishery following a summer when
low dissolved oxygen levels were present in the Sound (K. Stuck, personal communication).
Fisheries yields, however, are dependent on many factors, e.g., climatic factors and suitable
nursery habitat. The heavy rains, flooding, and extremely low salinities in Mississippi Sound in
the late spring and summer of 1991 have been blamed for a poor shrimp catch (Baton Rouge
Morning Advocate, June 30, 1991). On the other hand, Russell (1977) attributed an enhanced
catch of annual landings of industrial bottom fish following the flooding of the Mississippi River in
1973, the opening of the Bonnet Carre spillway, and concomitant nutrient increases.

Blooms of the toxic dinoflagellate, Gonyaulax monilata, occurred in coastal waters of the northern
Gulf in August 1979, September 1980 and July 1981 (Perry etal, 1979; Perry and McLelland,
1981a). The blooms were concentrated within Mississippi Sound, but also extended into the
nearshore waters of the Gulf of Mexico. No fish kills were associated with these blooms.
Concurrent blooms in Florida and Alabama occurred with the extensive bloom in Mississippi
Sound in 19790. A red tide attributed to blooms of the dinoflagellate, Prorocentrwn minimum,
occurred in Mississippi Sound and coastal bayous in February 1977 and in January and February
1981. Fish kills were associated with blooms of this dinoflagellate where the outbreaks occurred
in enclosed waters (Perry and McLelland, 1981a,b). P. minimum appears to be an occasional
component of the phytoplankton community in local waters.
A large bloom of Oscillatoria (Trichodesmium) erythraea developed in situ in Mississippi Sound in
August 1974 and extended the length of the sound on the northern edge of the barrier islands to a
distance of 10 km and up to 1 km into the adjacent Gulf of Mexico (Eleuterius et al., 1981). No
dead fish or other animals were seen during the bloom, either in the Gulf, estuary, or on adjacent
beaches. The authors attributed the bloom to high temperature, very high salinity, very transparent
water, a slightly alkaline pH, low nutrient concentrations, moderate oxygen concentrations, calm
seas (no wind) and brilliant sunlight. Trichodesmium blooms have occurred in Mississippi Sound
of relatively short duration (2-3 weeks) in 1976,1978 and 1980 (Eleuterius etal., 1981; Perry and
McLelland, 1981).
170
-------
REFERENCES: G-2.3

Anon. (1981, 1984)
Christmas (1973)
Christmas and Eleuterius (1973)
Donohoe and Calhoun (1982)
Eleuterius (1976a,b, 1978a,b, 1979)
Eleuterius and Beaugez (1981)
Eleuterius et al. (1981)
Higgins and Eleuterius (1978)
Kelly (1981)
Lytle and Lyde (1985,1990)
Miss. Dept. Nat. Res. (1988)
Pachecoera/.(1989b)
Perry and McLelland (1981a,b)
Perry etal. (1979)
Shaw etal (1982)
G-3 Pascagoula Bay/River/Escatawpa River

The Pascagoula River and its tributaries combine to form one of the largest drainage systems in
Mississippi. The Escatawpa River joins the lower Pascagoula River approximately 7 mi upstream
of its mouth. The West Pascagoula River diverges from the Pascagoula River 17.7 mi upstream of
its mouth; both flow parallel southward. The waters of the lower reaches of the two rivers are
interconnected by drainage through swamps, marshes and bayous.

A study of the water quality of the Pascagoula and Escatawpa Rivers was conducted by Bednar
(1978c). Concentrations of nitrite, nitrate and ammonia nitrogen at high and low tide are shown in
Figure M4. The total phosphorus concentrations in the rivers at sites in this study were
comparatively low. Ranges were between 0.01 and 0.16 mg/1.

A similar study was conducted in Bayous Casotte and Chico by Bednar (1979). Concentrations of
most nitrogen species were higher in Bayou Casotte at low tide than at high tide and were higher at
the most interior station than those closer to Mississippi Sound (Figure M5). The composition and
concentration of nitrogen specie's at high and low tide were more uniform in Bayou Chico than
Bayou Casotte. The nitrite plus nitrate concentrations in both estuaries were comparatively low.
Variable and high concentrations of organic and inorganic phosphorus were likely the result of
industrial wastewaters being released near the upstream sites. The comparatively small difference
between the phosphorus concentrations at high and low tide at the mouth of both Bayou Casotte
and Bayou Chico is an indication that phosphorus was being transported out of both estuaries in
low concentrations during the study.

Stations in Pascagoula Bay rarely had dissolved oxygen concentrations less than 2 mg/1 (GCRL,
FAM data set; Christmas and Eleuterius, 1973). Portions of the Pascagoula Bay subestuary are
subject to oxygen-depleted bottom waters. This was particularly evident at depth in the Pascagoula
and Escatawpa Rivers where there was little circulation and mixing of the more dense salt water
(Bednar, 1978b). These values, however, ranged mostly between 2 and 3, with few below 2
mg/1. Stations in the tidal reaches of the West Pascagoula and Pascagoula Rivers and at the mouth
of the Pascagoula River are frequently hypoxic or anoxic in the warmer months, March through
October (Bednar, 1978b; Bednar, 1979; Christmas and Eleuterius, 1973). Eleuterius and Beaugez
(1979) also noted a zone of low dissolved oxygen waters in Mississippi Sound near the mouth of
the Pascagoula River. Probable causes of oxygen depleted waters in these areas, besides density
171
-------

n>
•aain aaa SHVHOITIIH HI '
3
CO P4
>iaill
SWVHOiniW KI '
172
-------
SITE NUMBERS
2 3
PERCENT OF TOTAL
NITROGEN THAT IS
ORGANIC
55
H

C/3

§
2.0
w -
o
§
0 1.6
1.2

0.8

0.4

0
- TOTAL P
BAYOU CASOTTE
NITROGEN (N) SPECIES

SITE NUMBERS
2 3
BAYOU CHICO
BAYOU CASOTTE BAYOU CHICO

ORTHO AND TOTAL PHOSPHORUS (P)
Figure M5. Concentration and composition of nitrogen and the ortho- and total phosphorus
species in Bayou Casotte and Bayou Chico at high and low tide on July 25, 1978
(from Bednar, 1979).

stratification (Bednar, 1978b; Eleuterius and Beaugez, 1979) are pollutant loadings from paper mill
effluents (F. Sutler, personal communication), menhaden rendering plant effluents (F. Sutler,
personal communication), and domestic and industrial effleunts from the city of Pascagoula (see
Figure Ml). In a 3-day study of Bayous Casotte and Chico in July 1978 (Bednar, 1979), oxygen
depleted waters were found in the lower reaches of Bayou Casotte. A ship channel and harbor
with industrial activities, including petroleum fuels, petrochemicals, metal processing and
fabricating, and nitrogen, potassium and phosphorus fertilizers, characterize the area.
173
-------
REFERENCES: G-3

Bednar (1978c, 1979)
Christmas (1973)
Christmas and Eleuterius (1973)
Eleuterius (1976a)
Lytle and Lytle (1985,1990)
G-4 Biloxi/Bay Bays

In its 1988 Water Quality Report (Mississippi Dept. of Natural Resources, 1988), the state
identified current water quality and trends in its waters along with causes for nonsupport of
designated uses. Two estuarine areas were identified for special study: Bayou Cumbest/Heron
Bayou area (see Section G-3) and Ocean Springs. For a number of years the state has monitored
severe water quality problems in Ocean Springs Harbor (Tidewater Bayou). This waterbody flows
directly into Biloxi Bay which is classified for shellfish harvesting. A pollution abatement plan for
the area included the termination of the discharge from the wastewater treatment plant and the
construction of a new land treatment system north of the city. Prior to the abatement period, fecal
coliform counts were extremely high, oxygen concentrations were depressed at all stations,
concentrations of ammonia, nitrogen and orthophosphorus in harbor waters were greatly elevated,
total hydrocarbon concentrations in sediments were high, TOC in sediments were two to five times
higher than typically found in Gulf coast estuaries, heavy metals were elevated, and benthic fauna
were depressed in abundance and species richness. Following abatement, significant positive
changes were seen in the water quality of the harbor in decreased inorganic nutrient concentrations
and BOD values, reduced fecal coliform bacteria counts, and increased dissolved oxygen
concentrations. The effect of abatement was not as easily seen on other parameters: 1) heavy
metals, TOC and total hydrocarbon levels were lower but reductions were attributed to tidal surge
and sediment movements as a result of Hurricane Elena in September 1985; 2) phytoplankton
populations did not indicate a definite effect; 3) benthic fauna showed only slight change in
numbers of individuals and numbers of species. Limitations of abatement were identified as the
time required for recovery of the system from chemical pollutants, the physiography of the harbor,
and uses of the harbor. The report identified a more far-reaching concern as the failures in the
sewage collection system of Ocean Springs which allows raw sewage to enter the harbor.

In a study of the Back Bay of Biloxi, water quality and water flow characteristics were used to
determine the residence time of water (Bednar, 1978a) (Figure M6). Nitrite plus nitrate nitrogen
concentrations were less than 0.1 mg/1 and the concentrations of ammonia, organic and total
nitrogen were generally higher at high tide than low tide. The concentrations of ammonia nitrogen
ranged from 0.09 to 0.22 mg/1 at high tide and 0.06 to 0.16 mg/1 at low tide. Organic nitrogen
comprised about 85 % of the total nitrogen (Figure M7). The highest concentration of organic
nitrogen was 0.97 mg/l and ranged from 0.65 to 1.1 mg/1 at high tide and from 0.54 to 1.1 mg/1 at
low tide. The concentration of total phosphorus leaving the bay at low tide was very low and in
about the same concentration as that entering the bay at high tide. Total phosphorus concentrations
ranged from 0.1 to 0.24 mg/1 at high tide and 0.08 to 0.14 mg/1 at low tide (Figure M6).

Within Biloxi Bay, there were few instances of hypoxic bottom waters; these values (1-2 mg/1)
occurred in May-September (GCRL, FAM data). Lower oxygen levels were found in waters in
the Back Bay during the summer months, but never fell below 2.5 mg/1 (Christmas and Eleuterius,
1973: Bednar, 1978a). In flie GCRL, FAM data set, two stations in Back Bay were consistently
hypoxic in summer. In the stations in Big Lake, Cladophora blooms occur in the summer and
oxygen is depleted to 1-2.5 mg/1, but this does not occur every year (F. Sutler,, personal
communication). At another station, midway between Big Lake and Biloxi Bay, hypoxia has been
rare since 1979.
174
-------
CO ~
X
co g
aain aaa SHVHOITIIW NI 'snaoiidsoHd iviox
naxn aaa siwaomin NI '
175
-------

f*
Ul
£
3
ofi
W
P-
w 2.0
§
M
*"
g 1.0
g
S
0

1
1

• NOTE: BAR GRAPH ON LEFT OF GRID LINE
_

*
-
•

W,
CONCENTRATIONS

ftfi

m
, HIGH

till

82
till

REPRESENTS
OF TOTAL NITROGEN
DURING
TIDE, BARS ON RIGHT REPRESENT LOW TIDE '

-INORGANIC N /
(NH3,N02,N03) /

ft/,

///I

•tit,
/
83

///,
/

-PERCENT OF TOTAL
NITROGEN THAT I
ORGANIC

///

It/I

'ttl
5
-TOTAL N

\7Tt<
86

777

7777

///

79 1
7771
87

ttt

ORGANIC

777

t/t

N —

////

85
777
'/It,

-
-
-
, :

85~]

in,
567

SITE NUMBERS
10
11
12
Figure M7. Concentrations and composition of nitrogen species in the Back Bay of Biloxi, June
14, 1977 (from Bednar, 1978b).

The bloom of the dinoflagellate, Prorocentrum minimum, which occurred in Mississippi Sound in
January and February 1981, extended into the adjacent coastal waters of St. Martin Bayou, an inlet
off the Back Bay of Biloxi and at the mouth of Fort Bayou in February 1977 (Perry and
McLelland, 198 Ib). Fish Mils were reported coincident with the bloom in St. Martin Bayou in
1981.
REFERENCES: G-4

Bednar (1978b)
Christmas (1973)
Christmas and Eleuterius (1973)
Eleuterius (1976a)
Lytle and Lytle (1985,1990)
Pacheoma/. (1989b)
Perry and McLelland (198 Ib)
G-5 St. Louis Bay/Wolf/Jourdan Rivers

In a study of the Back Bay of Biloxi, water quality and water flow characteristics were used to
determine the residence time of water (Bednar, 1978c). The average total organic nitrogen,
ammonia, and total concentrations for sites on Jourdan River and St. Louis Bay during July 1977
are shown in Figure M8. Concentrations of total nitrogen were somewhat higher in the river than
the bay. These values are lower than those of Back Bay at Biloxi where a similar study was
conducted (Bednar^ 1978a). Bednar (1978) suggested that the total nitrogen content of Jourdan
River and St. Louis Bay was not abnormally high during the study. Bay waters containing higher
concentrations of organic nitrogen were moved upstream by the incoming tides.

In the most comprehensive set of temporal data (GCRL, FAM) there were no dissolved oxygen
levels below 4 mg/1 in five stations located in St. Louis Bay or just outside the Bay in Mississippi
Sound. A few samples between 3 and 4 mg/1 were reported in the Jourdan River in July (Bednar,
1978c), but only one value fell below 3 mg/1 and none below 2 mg/1. Krutak (1978) who sampled
numerous stations but over a limited time found low dissolved oxygen levels at nine of 43 stations;
these were mostly in the tributaries, in the bayous or at the mouth of a bayou, but not in the open
Bay. The Cooperative Gulf of Mexico Estuarine Inventory (Christmas, 1973) revealed only three
values in 27 collected from April 1968-April 1969 below 2 mg/1. Paulson et al. (1977), not
unexpectedly, found a decrease in dissolved oxygen content (as low as 1 mg/1), along with an
increase in coliform bacteria, with distance away from St. Louis Bay and into a dead-end canal
system.
176
-------
Prorocentrwn minimum, which caused extensive blooms in Mississippi Sound and the Back Bay
of Biloxi Bay in the winters of 1977 and 1981, appears to be an occasional component of the
phytoplankton community in local waters of St. Louis Bay, but has not been reported in bloom
proportions (Perry and McLelland, 1981).
REFERENCES: G-5

Bednar (1978a)
Christmas (1973)
Christmas and Eleuterius (1973)
Eleuterius (1976a)
Housley (1976)
Krutak (1978)
Lytle and Lytle (1985,1990)
Pachecoera/. (1989b)
Paulson etal. (1977)
Perry and McLelland (198 Ib)
Turner and Rao (1990)
§
o
8
H
H
@
O
M
S3
H
I
o
S3
o
1.00
0.50
0.00
l.OQ
0.50-
0.00
4 5
SITE NUMBERS

9 10
11
12
-1-
~r
13
—r
LOW TIDE
-TOTAL NITROGEN AS N
TOTAL ORGANIC AS N

^v-TOTAL AMMONIA AS N
J_
_L
_U
1 23 4 5 6 7 8
DISTANCE FROM 1-10 BRIDGE, IN MILES
10
4 5
~l T-
SITE NUMBERS

9 10
11
12
13
HIGH TIDE
TOTAL NITROGEN AS N
TOTAL ORGANIC AS N

^^- TOTAL AMMONIA AS N
JL
1 2 3 45 67 8

DISTANCE FROM 1-10 BRIDGE, IN MILES
Figure M8. Profiles of total nitrogen, organic nitrogen, and ammonia nitrogen in Jourdan River
and St. Louis Bay, July 12-13, 1977 (from Bednar, 1978a).
.177
-------
G-5.1 Mississippi inner continental shelf (outside Gulf Islands)

In a series of five cruises between March 1987 to March 1988 along three north-south transects
across the Mississippi and Alabama continental shelf (Darnell, 1991), nitrate concentrations were
uniformly low during the summer months but fairly high during the winter especially along the
transect closest to the Chandeleur Islands and the outflow of the Mississippi River. Phosphate
values were uniformly low during both seasons (see Section G-2.1).

Bottom water oxygen levels are not normally hypoxic along the inner and mid continental shelf off
Mississippi, even in mid summer (Schroeder and Crozier, 1974 data for July 1973; SEAMAP data
for June 1983 and 1985, Thompson and Bane, 1986a, Thompson et al., 1988). SEAMAP data
for the Mississippi inner shelf in the summer of 1984, however, indicated low oxygen bottom
waters offshore of Mississippi Sound at Ship Island Pass and Cat Island Pass (Marine Briefs,
August 1984, GCRL; Thompson and Bane, 1986b;R. Waller, GCRL, personal communication),
where low oxygen has been noted in previous years. Trawl catches in the area of bottom water
hypoxia were small or contained only catfish. For the station M-l on the 20-m isobath in the
Darnell (1991) study described above, bottom water dissolved oxygen concentration did not fall
below 5 mg/1 in any season. Based on the limited data set, there appears to be no widespread
hypoxia on the Mississippi inner shelf nor any seasonally definable or recurring event.

Blooms of the toxic dinoflagellate, Gonyaulax monilata, occurred in coastal waters of the northern
Gulf in August 1979, September 1980 and July 1981 (Perry etal., 1979; Perry and McLelland,
1981a). The blooms were concentrated within Mississippi Sound, but also extended into the
nearshore waters of the Gulf of Mexico. (See Section G-2.3.) High concentrations of
Trichodesmium erythrem were found on the eastern side of the Mississippi River delta in the 5-yr
study by Housley (1976).
REFERENCES: G-5.1

Anon. (1984)
Atwood(1981)
Brooks and Wolff (1991)
Churgin andHalminsta (1974)
Cons. Perm. Int. Exp. Mer (1936)
Darnell (1991)
El-Sayedetal. (1972)
EPA (1990)
Fanning etal (1982)
Perry and McLelland (1981a)
Riley (1937)
Russell (1977)
Schroeder and Crozier (1974)
Schroeder etal. (1988)
Shaw etal. (1982)
Stuntz et al. (N.D.)
Thompson and Bane (1986a,b)
Thompson and Leming (1978)
Thompson et al. (1988)
Turner and Rabalais (1991a,b)
LOUISIANA
Louisiana estuaries are experiencing some of the impacts of nutrient enrichment and eutrophication.
Some examples are: 1) the Louisiana Depts. of Wildlife and Fisheries and Environmental Quality
frequently receive reports of estuarine fish kills that they ascribe to low oxygen conditions that are
likely the result of high algal production (see Table LI below), 2) chlorophyll a concentrations in
several coastal water bodies frequently exceed 50 ng/1, which is high (R.E. Turner, personal
communication), 3) fertilizer use in Louisiana has risen dramatically since the 1940s (Figure LI)
and has almost certainly not stayed where applied, and 4) the dissolved silica:nitrate-N atomic ratio
fluctuates between 2 and 0.5 in many estuaries, indicating potential chemical control of diatom
abundance (R.E. Turner, personal communication).
178
-------
Although an in-depth analysis of the long-term trends in water quality of the Mississippi River has
been completed (Turnerand Rabalais, 1991a), data for Louisiana estuaries remain unanalyzed.
Data are on file with the U.S. Corps of Engineers (early 1960s), the Louisiana Dept. of Wildlife
and Fisheries (part of their estuarine inventories) (Louisiana Wild Life and Fisheries Commission,
1971; Barrett et aL, 1978), the U.S. Geological Survey water quality network, and the Louisiana
Dept. of Environmental Quality. Larger towns, such as Houma, monitor water quality from their
drinking water intake systems. Data for fertilizer consumption is available by parish from records
collected by the U.S. Dept. of Agriculture. The water quality in southern Barataria Bay and
Terrebonne Bay may be affected by changes in Mississippi River water quality because of its
relatively large freshwater inflow and evidence that salinity in Barataria Bay is inversely related to
river discharge (Wiseman and Swenson, 1987; Wiseman et al., 1990). However, the upper end of
most of Louisiana's estuaries receives a significant source of nutrients from agricultural and urban
runoff. There is also sewage discharge from numerous small camps and towns.
GENERAL REFERENCES: LOUISIANA

ASIWPCA (1984)
Basta and Bower (1985)
Burrage (1989)
Culliton and Blackwell (1989)
Day and Culley (1979)
Ehler and Basta (1985)
EPA (1974, 1978)
Jones etal (973)
Louis. Wild Life & Fish. Comm. (1971)
Main etal. (1987)
NOAA/EPA Team (1990)
Pechmann et al. (1986)
Turner and Rao (1990)
Wiseman and Swenson (1990)
200
o 300
1930 1950 1970 1990
Figure LI. Fertilizer consumption in Louisiana for selected years (R.E. Turner, unpublished
data).

G-6 Pearl River

In the Cooperative Gulf of Mexico Estuarine Inventory, limited samples were collected in the Pearl
River. Lowest nitrate levels recorded were 0.16 to a high of 2.16 p.g-at/1. Lowest nitrate levels
occurred in late spring and early summer. Inorganic phosphate levels were lowest in winter and
spring (0.5 ug-at/1) with a high of 6.8 u.g-at/1 recorded at a nearshore station in July (Christmas and
Eleuterius, 1973). Mean dissolved oxygen levels were 9.8 and 9.4 mg/1, respectively. The
surface and bottom concentrations were usually similar and differences rarely exceeded 1 mg/1.
From April 1968 to April 1969 (Christmas, 1973), no dissolved oxygen values below 6 mg/1
(three stations sampled monthly for a year) were recorded.
179
-------
Table LI. Summary of NOAA Fish Kill Inventory Data for Louisiana (draft data base, 1991; J.A.
Lowe, personal communication; see section on Data Sources).
AREA Records
County per County

PONTCHARTRAIN
Livingston 5
Orleans 9
St. Tammany 64
Tansipohoa 16
BRETON/CHANDELEUR
St. Bernard 24
MISSISSIPPI RIVER
Plaquemines 23
BARATARIA
Jefferson 29
Lafourche 36
St. Charles 20
TERREBONNE
Terrebonne 53
ATCHAFALAYA
Iberia 40
St. Mary 18
Vermilion 0
CALCASIEU
Calcasieu 8
Cameron 3
Cause
Low DO

5
5
31
1

4
10
5

6
9
0

3
1
Cause
Eutrophication

0
1
0
0 ,

0
5
0

0
0
0

0
0
Cause
Red Tide

0
0
0
0

0
0
0

0
0
Cause
Nutrient

0
0
0
0

0 .
0
0

0
0
0

0
0 .
Cause
Unknown or
Unspecified

0
2
12
4

3
0
1

0
0
0

1
0
REFERENCES: G-6

Christmas (1973)
Christmas and Eleuterius (1973)
Eleuterius (1976a)
Gunning and Suttkus (1986)

G-7 Lakes Pontchartrain/Maurepas
Lytle and Lytle (1985)
Pachecoera/. (1989b)
Turner and Rao (1990)
rj
Lake Pontchartrain is a large (1630 km ), shallow, oligohaline (salinity generally less than 5 ppt)
water body located immediately north of New Orleans. Highest salinities (usually 7-11 ppt) occur
during dry, late-summer and autumn months in southern and eastern parts of the lake. It is part of
an estuarine lake and bay system in which water enters from the Gulf of Mexico via the Rigolets,
Chef Menteur Pass, and the Mississippi River Gulf Outlet (MRGO, completed in 1962). The
MRGO connects to the open Gulf of Mexico and has facilitated mixing of Gulf water with that of
Lake Pontchartrain (Orvos, 1978). Poirrier (1978) documented an increase in the salinity in the
eastern section of the estuary. The expected increase in salinity from the construction of the
MRGO was 5 ppt, but the actual increase was 2 ppt (Sikora and Kjerfve, 1985); freshwater
discharge is the most important factor controlling salinity variations in Lake Pontchartrain. Lake
180
-------
circulation is wind-driven, the water column is usually well-mixed and the 11 cm tides are
primarily diurnal (Chuang and Swenson, 1981). The flushing time is about 60 days (Swenson,
1980). Freshwater enters through several tributaries on the northern shore and through Lake
Maurepas on the west where combined annual flow amounts to about 5 % of the volume of the
tidal prism entering through tidal passes (Swenson, 1981). The Amite, Blind, Tickfaw and
Natalbany Rivers flow into Lake Maurepas. The Bonnet Carr6 Spillway, located on the western
end of the lake debouches Mississippi River water into the lake when opened occasionally to
relieve flooding pressure in New Orleans, e.g., in 1937, 1945, 1950, 1973, 1975, 1979 and
1983. (See comments in Section G-10 regarding freshwater diversions from the Mississippi
River.) Pass Manchac, rain and northshore rivers account for the bulk of freshwater to Lake
Pontchartrain (Table L2).

Table L2. Major freshwater sources of Lake Pontchartrain (taken from Craig and Day, 1977).
Source
% Water Supply
Pass Manchac
Tangipahoa River
Rain-Evaporation on Lake
Tchefuncte River
Bayous Lacombe and Liberty
New Orleans Metropolitan Runoff
TOTAL
5.10
1.53
1.42
0.72
0.34
0.4
9.51
54%
16%
15%
7.6%
3.6%
4.2% :

The Lake Pontchartrain Basin Foundation was established by the State Legislature in July 1989 to
"restore and preserve the environmental and ecological balance" of the lake basin. Besides its
primary focus, the Foundation has also initiated an Information Resources Project to inventory and
catalog the source, location, description, and accessibility of information application to the
protection, restoration, and maintenance of the environmental quality of the basin (S. Goriri,
personal communication).

Over the past 60 years, human population in this drainage area has risen dramatically. While all
sections have shown growth, a large percentage of the residential development incurred by the
increase has been located in reclaimed wetlands adjacent to the lake. As a consequence of the rapid
development, many of the natural streams and drainage canals which bring fresh water into Lake
Pontchartrain now also serve as conduits for domestic wastes and fertilizer residues rich in
nitrogen and phosphorus. These inputs have caused a decline in water quality throughout the lake
and are responsible for increased incidence of eutrophic conditions (Craig and Day, 1977). A
comprehensive study (Stone, 1980) concluded that 1) average turbidity has increased by about 50
% since the early 1950s, 2) nutrients (phosphorus and nitrogen) are significantly higher in areas
fringing and surrounding the lake such as in Lake Maurepas, in the marshes and along the,
southeastern shoreline just off New Orleans, 3) total phosphorus loading to Lake Pontchartrain has
increased by about 70 % since the 1950s (Figure L2).
181
-------
VI
rt
»
O
ex,
c«

i
UID iii Bureau MJdaQ asjQ mooas ueav\| SB passajdxg AouajedsueJi

C)
oju|
182
-------
Lake Pontchartrain is not uniformly eutrophic (Craig and Day, 1977; Stone, 1980; and data, in
Tarver and Dugas, 1973). The most affected area is the south shore adjacent to the metropolitan
area. This area is characterized by high nutrient and coliform levels and pollution indicative
species. The southwestern part of the lake from Jefferson Parish to Pass Manchac also seems to
be eutrophic. The northshore and eastern end of the Lake seem to be fairly clean because of low
nutrient input and more rigorous tidal flushing. Thus, there is a gradient in eutrophic conditions
from south and west to north and east. This gradient is due to differential inputs of nutrients and
rates of flushing. Data for Lake Maurepas (Tarver and Dugas, 1973) show somewhat elevated
means for nitrite and nitrate above that of Lake Pontchartrain. Stern and Stern (1968) found that
the discharge of storm water into Lake Pontchartrain affects the water quality and increases the
coliform count. Phosphates, nitrates, and nitrites brought to the lake from storm runoff increase
the phytoplankton and bacterial abundances.

A study of the nutrient and carbon geochemistry in the lake (1977-1979) was conducted by
Stoessell (in Stone, 1980). He found that seasonal trends were fairly consistent throughout the
lake except for the area bordering the southern shoreline, which was being contaminated by New
Orleans' waste waters. Maximum concentrations of inorganic nutrients, organic carbon fractions,
and dissolved phosphorus usually occurred during the spring; minimum concentrations occurred in
the summer. Levels of inorganic nitrogen fractions and undissolved organic carbon commonly
remained low during the fall. Concentrations of phosphate, silicate, dissolved organic carbon and
dissolved P tended to increase in the fall. Higher than average concentrations of phosphate and
dissolved phosphorus occurred on the south side of the lake. Inorganic carbon content increased
spatially from west to east and southeast across the lake. High concentrations in the spring for
inorganic nutrients, dissolved phosphorus, and the organic carbon fractions was likely related to
maximum river input and to stream flooding through adjacent swamps and marshes into the lake.
Assimilation of inorganic nutrients by organisms followed in the summer when concentrations
were lower; increased levels of silicate in the fall followed the death and dissolution of diatoms.
Higher phosphate and dissolved phosphorus contents in the fall were probably due to nutrient
release from suspended sediments. Continued low values of inorganic nitrogen fractions in the fall
implies that nitrogen is growth limiting for some lake organisms.

While there is documentation for an increase in phosphorus loading to Lake Pontchartrain, the
picture for nitrate is not as clear. Analysis of a long-term data set (R.E. Turner, personal
communication) revealed that the nitrate concentrations in Pass Manchac and Lake Pontchartrain
were very similar and that the concentrations were on a general decline from 1975 to present
(Figure L3).

A study conducted by the Louisiana Dept. of Environmental Quality (Schurtz and St. Pe, 1984)
examined the environmental conditions in Lake Pontchartrain with regards to water quality. The
study was concerned primarily with the reports of "dead zones" in the lake and the implications of
anthropogenic or toxic substances being the cause (see also below). Findings from the study
indicated the lake, particularly the southern portion, chronically receives the input of a" broad
spectrum of anthropogenic contaminants associated with urban, domestic and commercial
development. Most significantly impacted are the nearshore areas (within one mile of shore)
adjacent to the mouths of major drainage and navigation canals. Inputs of contaminants are
primarily through stormwater runoff and sewerage effluents that enter the drainage canals and are
subsequently pumped to the lake. Contamination levels are very much higher adjacent to the
urbanized southshore in Orleans and Jefferson Parishes, with regard to levels of nutrients and
oxygen-demanding wastes from sewage effluents and chemical contaminants from urban runoff
and industrial development.

Another environmental factor in Lake Pontchartrain is hydraulic dredging for the clams Rangia
cuneata. Dredging began around 1933 and increased to 1.5 million cubic yards in 1955 and to 3.8
million cubic yards by 1968. Dredging operations ceased in spring 1990 following extensive legal
183
-------
0.3
Annual Averages
o. t 0.2
N03+2 N mg/1
Lake Pontchartrain
0.4
0.2.
4-
m
o
0
1974
oPass Manchac
• Causeway (12 mi)
1978
1982
1986
1990
Figure L3. Comparison of nitrate concentrations in Pass Manchac and Lake Pontehartrairi (upper
panel) and change in nitrate concentration through time at Pass Manchac and at a
Causeway station in mid Lake Pontchartrain (R.E. Turner, unpublished data).
184
-------
proceedings. Before 1990, dredges were restricted to about 44 % of the lake, where they may
overturn that area in 1.4 to 2.4 years (Stone, 1980). The apparent effects of this dredging on the
benthic fauna, which may be considerable, include the loss of larger size classes of R. cuneata,
benthic infaunal species and biomass changes, low sediment bulk density, and lower soil carbon
content Of particular importance here is the observation that the average sediment bulk density in
surface samples in 1978 approached that of fluid mud (Sikora et aL, 1981).

Short-term and long-term changes in estuarine turbidity influence phytoplankton production,
pelagic food chain dynamics, and benthic community development, yet continuous long-term data
of estuarine light quality are rare. Two common management issues related to estuarine light
conditions in Lake Pontchartrain are eutrophication and dredging. The former may reduce light
penetration through increased phytoplankton biomass and species shifts; the latter may have the
same effect through resuspension of bottom sediments. Either dredging or eutrophication may
result in the decline of benthic macrophytes, for example, by reducing light penetration (e.g.,
Davis and Carey, 1981). There was a net decline in the abundance of two submerged macrophytes
(Ruppia maritima and Vallisneria americand) in Lake Pontchartrain from 1954 to 1973 (Turner et
al, 1980).

A long-term data set of Secchi disk depth (SDD) measurements taken between 1953 and 1978 have
been analyzed (Turner and Dow, unpubl. data). SDD was significantly lower in 1978 than in the
1953-1955 period. Possible explanations for this change are eutrophication, opening of the
Bonnet Carre spillway, dredging and variations in climatic wind patterns. Phytoplankton pigment
concentrations were too.low to reduce the light penetration and wind speeds were no higher in
1978 than in 1953-1955. The 1979 diversion of Mississippi River water introduced a water
volume that was "short-lived and affected about two-thirds of the entire lake area" (Swenson,
1981), and SDD measurements by Tarver and Savoie (1976a,b) during the 1973 diversion did not
appear to be signific'antly higher for the same wind speed immediately after the spillway closed
than in the previous or following years. The consequences of dredging remain a probable cause.
The benthic biota of the lake clearly changed between the 1950s and 1978 (Sikora et al., 1981)
with a reduction in sediment organic content, reduction of larger benthic invertebrates, and changes
in sediment bulk density. The types of meiofaunal organisms also reflects the fluid nature of the
sediments (Fleeger et al., 1983). These effects are likely agents for allowing the suspended
sediments to be scoured into the water column with greater efficiency during normal wind
conditions (Turner and Dow, unpubl. data). A prudent test of the hypotheses presented here
would be to re-examine the benthic and water column community over the next several years to
document if the conditions reverse, and, if so, how quickly.

During some years, when rainfall and Mississippi River flow are low, a more saline bottom water
layer occurs offshore from New Orleans, which is related to movement of higher salinity waters
from the MRGO. The recurring hypoxic or anoxic .bottom waters in Lake Pontchartrain are more
likely to be present east of the causeway. The problem is most severe and persistent in the
southeastern portion of the lake. On the other hand, those areas closest to canal outlets along the
southern shore, both east and west of the causeway also experience problems related to freshwater
runoff and pollutant loadings from urban runoff. Outfall canals discharge storm water low in
dissolved oxygen and high in organic matter, nutrients, sewage and other pollutants (Poirrier,
1978; Schurtz and St. Pe", 1984). While Stern et al. (1968) examined only surface water samples
in their study, dissolved oxygen concentrations were very low (near 0.5 mg/1) at stations along the
southern shore following heavy rains. Fish kills were associated with these low oxygen values.
Heavy rainfall, followed by the admixing of storm and sewer runoff into the lake, contributed to
the lowering of the dissolved oxygen content. In years of heavy river flow or rainfall, there is
likely more flushing of the system than when outflow is low and the limited tidal mixing does not
facilitate breakdown of haloclines developed along the southeastern shore.
185
-------
In 1982 rainfall and Mississippi River flow were low. Hypoxic and anoxic conditions developed
in part of the lake (Figures L4 and L5). In 1983 and 1984, both rainfall and Mississippi River
flow were high, and the severely oxygen-depleted waters did not develop in summer. Low
oxygen conditions have also been documented in Lake Pontchartrain in the summers of 1976,
1980 (Poirrier, 1978; Windham et al, 1980).

The Schurtz and St. Pe" (1984) study concluded that large areas in the southeastern and east central
Lake Pontchartrain are subject to severe dissolved oxygen depletions in the lower water column in
the warm water months. These depletions dramatically affect the numbers, survival and
distribution of organisms confined to the lower water column and bottom sediments. The most
noticeable effects are crab kills (e.g., Windham et al., 1980). The anoxic conditions result from
non-mixing characteristics brought by pronounced salinity stratification during summer months,
particularly in years exhibiting normal or below normal rainfall. The cause of seasonal salinity
stratification is the intrusion of highly saline waters from the Gulf of Mexico via the MRGO.
Examination of biological samples did not indicate the occurrence of "dead zones" in the Lake, but
some areas have been demonstrated to exhibit lower than expected species diversity. The causes
for depressed diversity were not attributed to toxic contamination but rather to environmental
stresses related to salinity stratification and oxygen depletion.

Many of the studies described above also included the environs of Lake Maurepas, a small (236
km2), shallow (average 2 m deep) lake that is minimally affected by astronomic tides. There are
occasional vertical water quality variations in the lake due primarily to the influx of brackish water
from Lake Pontchartrain in contrast to the freshwater inflow from tributary streams on the west and
north. Dissolved oxygen values for the entire water column in March and July 1970, however, did
not fall below 5 mg/1 (Shampine, 1971). On the other hand, G. Childers (personal
communication) indicated that there were isolated instances of low oxygen in Lake Maurepas. A
study of the microbiological and chemical quality of Lake Maurepas was conducted from July 1986
to June 1987 (Bancroft et al., 1988). They concluded that all concentrations of bacterial indicators
of pollution were found to be greater than those observed in 1983-1984 (Childers, 1985; cited in
Bancroft et al., 1988), indicating a significant decrease in the water quality of Lake Maurepas.

Two freshwater sources to the Maurepas-Pontchartrain system are listed by the Louis. Dept. of
Environmental Quality (1990) as "Waterbodies Under Advisories": 1) Bayou Trepagnier in the
southwest corner of Lake Pontchartrain near the Bonnet Carre spillway, which is heavily
contaminated with organic compounds, and 2) the Tangipahoa River, which flows into the
northwest corner of Lake Pontchartrain, and has high levels of bacterial pollution.
REFERENCES: G-7

Bancroft etal. (1988)
Cent, for Wetland Res. (1970)
Chuang and Swenson (1981)
Craig etal. (1977)
Dugas etal. (1974)
Fleegeretal. (1983)
Junotetal. (1983)
La. Dept. Envir. Qual. (1987-90)
Miller (1980)
Otvos (1978)
Poirrier (1978,1979)
Poirrier etal (1975)
Schurtz and St. Pe" (1984)
Shampine (1971)
Sikora and Kjerfve (1985)
Sikoraetal. (1981)
Stern etal. (1968)
Stern and Stern (1969)
Stone (1980)
Swenson (1980)
Tarver(1972)
Tarver and Dugas (1973)
Tarver and Savoie (1976a,b)
Turner etal. (1980)
Windham etal. (1980)
Wiseman and Swenson (1987)
Wiseman etal. (1990)
186
-------
Figure L4. Dissolved oxygen isopleths (mgA) in lower water column (0.5 m above bottom) for
Lake Pontchartrain, August 28-29,1980 (upper panel) and August 26-27, 1982
(lower panel) (from Schurtz and St. Pe", 1984).
187
-------
g
- T

- 3 i

Is
7 5
3fi
a

g
. Julian Day
Figure L5. Dissolved oxygen concentration in near-bottom water of Lake Pontchartrain in 1982 at
three stations (ordered by decreasing intensity of hypoxia/anoxia) (from Rabalais et
al., 1985).
188
-------
G-7.1 Louisiana inner continental shelf

The largest, most severe, and most persistent zone of hypoxia (operationally defined as oxygen
levels of <2 mg/1, based on effects on local biota) in the U.S. coastal waters is found in the
northern Gulf of Mexico on the continental shelf off Louisiana (Rabalais et a/., 1991a). The zones
of hypoxic bottom water in the northern Gulf of Mexico may cover 8000 to 9500 km2 during mid-
summer on the inner continental shelf, from the Mississippi River delta onto the upper Texas coast
(see Figure 12). Critically depressed dissolved oxygen conditions may occur in near-bottom
waters nearly continuously from April through October on the inner shelf off southeastern (Figure
L6) and southwestern Louisiana (Turner and Allen, 1982a; Pokryfki and Randall, 1987). The
zones of hypoxia are continuous, widespread, and persistent, and may include up to 40 % of the
water column in 10-30 m water depth. In mid-summer 1985, the low oxygen zone was most
intense and extensive on the southeastern Louisiana continental shelf and westward to Marsh
Island (Figure L7). The band narrowed to the west and was confined to 9 to 12 m water depth.
The configuration of the area of hypoxia in mid-summer 1986 differed from that in 1985 in that it
was disjunct and larger off southwestern Louisiana and smaller off southeastern Louisiana. The
configuration in 1987, 1989, 1990, and 1991 was similar to that of 1986, with disjunct areas on
the southeastern and southwestern parts of the coast. Bottom water hypoxia is considered to be
more patchy in distribution and ephemeral in duration on the southwestern Louisiana shelf. This is
supported by data from the West Hackberry Strategic Petroleum Reserve Program monitoring
study (DeRouen etal, 1982,1983; Hann etal., 1984a,b).
The Mississippi River system discharge creates strongly stratified nearshore waters, which flow
westward and southward along the Louisiana and Texas coasts. Mean flow reverses in late spring
and the flow actually reverses and flows against the mean wind at some locations along the
Louisiana coast (Cochran and Kelly, 1986, cited in Rabalais etal., 1991a). The reversal retains
freshwater on the mid to inner shelf. Stratification, as a rule, is strongest in spring, during high
runoff, and summer, when wind mixing is weak and solar heating is strong. The salinity of
surface waters on the nearshore continental shelf closely tracks the flow of the Mississippi River
(Geyer, 1950, 1955). The Mississippi and Atchafalaya River effluents and their influence on the
surface salinity distributions can be identified in shelfwide cruises during mid summer and at other
times during the year. Oxygen-deficient bottom waters often form beneath a strong salinity-
controlled pycnocline at 10 to 15 m water depth. Low oxygen conditions in bottom waters on the
Louisiana shelf are coincident with strong density stratification (Figure L8). The implication is that
oxygen-depletion is supported and maintained by strong density differences.

The principal source of organic matter in the bottom waters of the northern Gulf of Mexico is
probably from phytoplankton production in surface waters. The organic material discharged by the
Mississippi River as a source of oxidizable organic material has been largely discounted (Turner
and Allen, 1982a). The disjunct zones of hypoxia in 1986, 1987, 1990 and 1991 mirrored the
surface salinity field and surface phytoplankton biomass concentrations that resulted from the
Mississippi and Atchafalaya River freshwater inputs (Figure L9). Irrespective of the source, the
amount of phytoplankton biomass in the bottom waters across the Louisiana inner and mid
continental shelf is high, often exceeding 10 \ig/l total pigments, and a high percentage is
composed of phaeopigments (i.e., degradation products of chlorophyll). There are some
indications of the coupling of surface production with the accumulation of organic material in the
bottom waters (Figure L10). The amount of material that reaches the bottom should be high for
several reasons: 1) primary production in these waters is high (>300 gC/m2/yr, Sklar and Turner,
1981), 2) Suess' (1980) empirically-derived formula relating phytoplankton production in surface
waters to the amount of material falling into sediments traps at depths predicts that 50 % or more of
the surface production reaches the bottom in depths equal to that in hypoxia occurs.
189
-------
9/24
10/16
5/13
4/18
10 20 30
DISTANCE (km)
Figure L6. Isopleths for 2 mg/1 and 1 mg/1 dissolved oxygen along Transect C offshore of
Tenebonne Bay for the dates indicated in 1986 (Rabalais et al, unpublished data).
190
-------

Figure L7. Distribution of hypoxic (<2 mg/l) bottom waters on the Louisiana continental shelf in
July of 1985 and 1986 (from Rabalais et al, 1991a).
I 16^
g 1^
— 12.
O>
E loJ
8
(a
E

'w
<
Seasonal changes in surface-to-bottom
differences in sigma t and oxygen
Station C5 1986
°A sigma t
•A mg/l oxygen.
678
Month
10 11 12
Figure L8. Differences in surface to bottom water values for sigma t and dissolved oxygen
concentration by month for Station C5 during 1986 (from Rabalais et al., 1991a).
191
-------
TOTAL PIGMENTS - SURFACE (jjg/l)
7/15-20/85
SURFACE CHLOROPHYLL a (pg/l)
7/7-17/86
Figure L9. Shelfwide contours of surface water total pigment concentrations (//gA) across the
Louisiana continental shelf in July 1985 (upper panel); similar distributions of
surface water chlorophyll a concentration fag/l) in July 1986 (Rabalais et al,
1991a).

The implications of long-term changes in the water quality of the Mississippi River were outlined
in Section G-9. J-X>ng-term increases in nutrient concentrations in coastal waters have also been
documented elsewhere in the world (Rabalais et al., 1991a). Eutrophication in most of these
coastal waters has been linked to increased incidences and severity of hypoxia. Thus, changes in
nutrient concentrations and nutrient ratios in the Mississippi and Atchafalaya Rivers may have had
an impact on the coastal phytoplankton community composition and phytoplankton production.
The source of the organic material fueling respiration that depletes oxygen may therefore have
changed. It is not known, however, if all these changes have led to an increase or decrease in the
size, duration, or severity of hypoxia.
192
-------
O)

W
"p »—
QJ 2
E «

E
_ 0)
W H
•»-> (0

c
1985 Shelfwide Survey
Depths 5-20 m
Surface salinity > 20 ppt
0.68
y = 0.31 x + 0.62
0 2 4 6 8 10 12 14 16 18 20
Total Pigments in Bottom Water (p.g/1)

Figure L10. Relationship of total phytoplankton pigments 0/g/l) in surface waters to total
phytoplankton pigments in the bottom waters for those stations sampled in the
1985 shelfwide cruise that were most likely to have hypoxic bottom waters
(depths of 5 to 20 m and surface salinity of >20 ppt) (from Rabalais et aL,
199 la).

Low oxygen conditions have been documented every summer since 1972 on the Louisiana
continental shelf. Anecdotal data for trawl samples indicate the occurrence of bottom water
hypoxia prior to this date (W. W. Forman, personal communication). Inadequate data prevent an
analysis of long-term trends in severity, duration or extent Most of the records prior to 1985 were
collected peripherally to other studies. Consistent monitoring of oxygen-deficient bottom waters
was not initiated until 1985 (Rabalais et aL, 199 la). Current efforts in the examination of
eutrophication and/or hypoxia/anoxia indicators in the sedimentary record may shed some light on
this mystery (R. E. Turner et aL, personal communication). Work on areas of low oxygen on the
Louisiana shelf continue [Rabalais et aL, under NOAA Nutrient Enhanced Coastal Ocean
Productivity (NECOP) funding; Louisiana Dept. of Wildlife and Fisheries in monitoring studies of
the West Hackberry Strategic Petroleum Reserve brine disposal site; Southeast Area Monitoring
Assessment Program (SEAMAP)].

There is no doubt that oxygen-deficient bottom waters affect demersal finfish and crustacean
populations. Trawl catches in areas of hypoxia are minimal or non-existent (see Figure 14) (Pavela
et aL, 1983; Leming and Stuntz, 1984; Renaud, 1986a). Benthic animal densities are severely
depressed in these hypoxic areas or reduced to a few competitively superior species (Harper et aL,
1981, 1991; Gaston, 1985; Gaston etaL, 1985; Murrell andFleeger, 1989; Boesch and Rabalais,
1991; Rabalais et aL, unpublished data) (Figures 13, Lll, and L12). The behavior, if not
reproduction, of demersal finfish and crustacean species is affected by the low oxygen. Motile
organisms move out of the area, but are often more exposed to predation pressure or the size of
suitable habitat is reduced. Fish kills are sometimes the result. A major fish kill off Grande Isle in
the Mississippi River Delta bight in 1990 was attributed to the hypoxia/anoxia offshore. Crabs
have been killed when caught in traps while a hypoxic water mass excursion moved onto Point au
Per Island. The reproductive cycle of penaeid shrimp may be variously affected during different
parts of their life (see Figure 16). Hypoxic bottom waters may also affect the blue crab fishery in
that ovigerous females are migrating offshore to spawn during periods when oxygen depleted
bottom waters may be present. Dead and decaying adult blue crabs (and other crustaceans) have
been observed on the bottom during the severe 1990 hypoxia/anoxia, and crabs and shrimp have
been observed to be swimming in the mid-water column or at the surface to avoid hypoxic water
masses on several occasions (N. N. Rabalais, personal observations).
193
-------
o
ci
CO
O
8
LLI
CO
JUN JUL AUG SEP OCT DEC JAN MAR APR MAY JUN JUL AUG
1985 1986
800-1
O
d
CO
o
o
8
LLI
m
D
z
Other Macrofauna
JUN JUL AUG SEP OCT DEC JAN MAR APR MAY JUN JUL AUG
1985
1986
Hypoxic
Conditions
Figure LI 1. Abundances of meiofauna by taxon (Kinorhyncha and Copepoda) (upper panel)
and macroinfauna (grouped by Magelona polychaetes and others) from Station C5
off Terrebonne Bay; hypoxic period stippled (from Boesch and Rabalais, 1991).

Q. Dortch et al. (personal communication) and research teams at LUMCON are keeping an eye out
for high numbers of potentially toxic phytoplankton in samples from the Louisiana coast.
Ceratium tripos and C.furca, which are implicated in low oxygen events elsewhere in U.S.
waters, have been documented on the Louisiana shelf (Q. Dortch et al., personal communication).
Gonyaulax monilata was first recorded in the open waters of the Gulf of Mexico off the
southeastern coast near Bayou Lafourche (identification not verified) and west of the Mississippi
River in September 1980 (Perry, 1980). Patches of discolored water were also found south of the
Grand Terre Islands to Lanaux Island. A similar bloom was found off the eastern part of the
Mississippi River delta in 1979 (Perry, 1980). (See also Sections G-8.1 and G-10.) A bloom of
Gonyaulax cf. monilata was documented off Southwest Pass of the Mississippi River delta in
September 1990 (Q. Dortch et al., personal communication). The verified occurrence of a red tide
followed several reports of "red water" from local fishermen. Red tides of the heterotrophic alga,
Noctiluca sp., were verified off Terrebonne Bay in March 1992 (Q. Dortch et al., personal
communication). Nitschia pungens, a pennate diatom, some forms of which produce a powerful
neurotoxin, have been identified from Louisiana coastal waters; the morphological form has yet to
be be confirmed (Q. Dortch et al., personal communication) (see Section G-17).
194
-------
Dinophysis sp., most probably D. caudata, has been found in high concentrations in shelfwide
coastal waters during April and August of 1989 and during a two-week period in July 1990 and
along a cross-shelf transect off Terrebonne Bay in March-November 1990 (Q. Dortch et al.,
personal communication). The organism was present during the late spring and summer months in
surface layers at intermediate salinities of 20-30 ppL D. caudata has been recognized recently as a
toxic dinoflagellate which may contribute to the accumulation of toxins responsible for diarrhetic
shellfish poisoning (DPS) in shellfish in Mobile and Galyeston Bays (R. Hickey, personal
communication). The Dinophysis populations in Louisiana coastal waters have not been implicated
in shellfish poisoning (see also sections G-12 and G-15).

Four red tide producing species, Noctiluca miliaris, Oscillatoria (Trichodesmium) erythraea (bloom
proportions), Gonyaulax monilata (bloom proportions), and Prorocentrum minimum, were
recorded in offshore coastal waters of southwestern Louisiana in 1981 (Maples et al., 1983).
Occurrences were predominantly in the spring and summer, with the exception of P. minimum
which was found in all months. No fish kills, jubilees or discolored waters were associated with
the presence of G. monilata. Some of these organisms were also recorded in the estuarine waters
of Calcasieu Pass and Lake Calcasieu (see Section G-15).

See also comments in section G-27 concerning a dinoflagellate bloom (Gymnodiniwn splendens)
off Galveston, Texas, that was suggested to originate from the plume of the Atchafalaya River and
then transported into nearshore coastal waters of Texas (Harper and Guillen, 1989).

The presence of toxic algae and/or the potential for blooms have clear, negative effects on fishery
or shellfish resources. Concern about toxic algal blooms has risen in recent years because of their
impact on public health and economics of fisheries. There is evidence that the incidence of blooms
as been increasing in recent years (Smayda, 1990). Some attribute the apparent increased
incidence to awareness and increased observations, but there seems little doubt that the increase in
outbreaks is very real (Shumway, 1990).
REFERENCES: G-7.1

Atwood (1981)
Barrett and Ralph (1976)
Bedinger etal. (1981)
Bien etal. (1958)
Boenig(1990)
Boesch (1982, 1983)
Boesch and Rabalais (1991)
Brent (N.D.)
Brooks (1980)
Brooks and Wolff (1991)
Childers(1981)
Churgin and Halminsta (1974)
Comiskey and Farmer (1981)
Con. Perm. Int. Exp. Mer (1936)
Dagg (N.D., 1988)
Darnell (1991)
Dennis etal. (1984)
DeRouen et al. (1982, 1983)
Dinnel (1984)
Dinnel and Wiseman (1986)
Drake(1982)
El-Sayedetal. (1972)
Fanning et al. (1982)
La. Dept. Envir. Qual. (1984)
Landry and Armstrong (1980)
Leming and Stuntz (1984)
Lohrenzetal. (1990)
Maples etal. (1983)
Melancon and Kilgen (1991)
Murrell (1987)
Murrell and Fleeger (1989)
Oetking etal. (1974)
Parker etal. (1980)
Perry (1980)
Pokryfki (1985)
Pokryfki and Randall (1987)
Rabalais (1987,1988, 1990)
Rabalais and Boesch (1986/87)
Rabalais etal. (1986a,b, 1991a)
Raganetal. (1978)
Ray (1981)
Reitsema (1980)
Renaud (1986a,b)
Richards and Redfield (1954)
Riley (1937)
Russell (1977)
195
-------
Farrell (1974)
Fitzhugh (1983)
Foote (1982)
Fotheringham and Weissberg (1979)
Fox etal. (1987)
Frey etal. (1981)
Fuller etal (1990)
Gallaway (1981,1982)
Gaston (1985)
Gaston etal. (1985)
Gazey etal. (1982)
Geyer (1950,1955)
Gosselink etal (1975)
Griffin and Ripy (1974a,b)
Hannera/.(1984a,b)
Hams etal (1976)
Hausknecht (1980)
Ingham (1982)
La. Ct. Sh. Sys. Wrk. Gr. (1982)

G-8 Lake Borgne
Schroederetal. (1988)
Shaw etal (1988)
Sklar and Turner (1981)
Steidinger (1973)
Stetson (1953)
Stuntz (1982)
Stuntz et al. (N.D., 1982)
Temple etal (1977)
Thomas and Simmons (1960)
Thompson and Bane (1986a,b)
Thompson and Leming (1978)
Thompson et al (1988)
Trask (1953)
Turner and Allen (1982a,b,c)
Turner etal. (1987)
Turner and Rabalais (1991a,b)
Wiseman (1982)
Wiseman etal. (1986)
No additional information is available for Lake Borgne. Mortalities of blue crabs in traps, resulting
from hypoxia, have been assumed in the past (Rabalais et al., 1985). Limited data from Barrett et
al. (1978) indicate no occurrences of dissolved oxygen less than 2 mg/1 (none less than 3 mg/1).
REFERENCES: G-8

Barrett ef al. (1978)
Cent. Wetland Res. (1970)

G-8.1 Breton/Chandeleur Sounds
Wiseman and Swenson (1987)
Wiseman etal. (1990)
No additional data were obtained for Chandeleur or Breton Sounds. Based on very limited data
(Barrett et al., 1978) low dissolved oxygen in bottom waters of Breton Sound is not a problem. In
monthly samples from October 1974 to September 1976 there were no oxygen values below 2
mg/1. The station on the Breton Sound transect at which the lower dissolved oxygen values were
recorded (2.7 and 3.7 mg/L) were located at the most offshore end of the transect. Chandeleur and
Breton Sounds are much shallower than Mississippi Sound, are open and exposed to wind mixing,
and experience no large freshwater discharges which may induce stratification. There may be a
localized influence of the MRGO, because its water column is normally stratified (Fagerburg,
1990).
See comments in Section G-10 regarding freshwater diversions from the Mississippi River.

A study of the phytoplankton production in the Mississippi River delta (Thomas and Simmons,
1959) included a station in Breton Sound. Compared to the remainder of the stations in the river,
plume, and open Gulf of Mexico, the station in Breton Sound generally had higher surface
phytoplankton production, similar levels of phosphate, and similar levels of soluble Kjeldahl
nitrogen. The higher phytoplankton production could be attributed to increased water clarity.

The red tide caused by the dinoflagellate, Gonyaulax monilata, documented in Louisiana coastal
waters in September 1980 (Perry, 1980) also occurred in the waters of Breton and Chandeleur
Sounds.
196
-------
A major freshwater diversion project has been completed to reroute waters of the Mississippi River
into Breton Sound. The intent of the project (Caernarvon Freshwater Diversion) is to lower
salinities in the sound by opening the structure when salinities reach a certain level. The structure
has been finished and tested, but not yet used. Officials of the Louisiana Dept. of Natural
Resources are questioning the usefulness of this project as well as all diversions planned for the
Mississippi River (Baton Rouge Morning Advocate, May 28, 1991).
REFERENCES: G-8.1

Barrett etal (1978)
Fagerburg (1990)
Lurry (1983)

G-9 Mississippi River
Perry (1980)
Shirzadetal. (1989)
Thomas and Simmons (1960)
The Mississippi and Atchafalaya Rivers are the primary source of fresh water to the Louisiana
continental shelf (Dinnel and Wiseman, 1986) and to the Gulf of Mexico (90 % of freshwater
inflow to Gulf). The Mississippi River watershed is the largest in the U.S. (41 % of the area of
the conterminous 48 states). The river ranks third, eighth, and sixth, with respect to length,
discharge, and sediment yield (Milliman and Meade, 1983). Approximately 33 % of the flow of
the Mississippi River system enters the Gulf of Mexico via the Atchafalaya River (see Figure LI 6)
(Turner and Rabalais, 1991a). Approximately 53 % of the discharge from the Mississippi River
delta proper flows westward onto the Louisiana shelf (U. S. Army Corps of Engineers, 1974)
Several studies have documented long-term changes in Mississippi River quality. According to
Meade and Parker (1985), suspended sediment loadings declined abruptly in the mid 1950s
following dam and reservoir construction on major tributaries of the Mississippi River, (Figure
L12, Turner et al., 1987). Along with the reduction in suspended sediments, there has been a
reduction by half the 1950s values, of silicate concentrations, but the decline is less precipitous
than that observed for suspended sediments (see Figure 8, Turner and Rabalais, 1991a). A
seasonal summer-fall maximum in silicate concentration is no longer evident. The coincidental
decline in silicate as phosphorus fertilizer application increased (see Figure 8) is support for the
hypothesis of Schelske et al. (1983, 1986; cited in Turner and Rabalais, 1991a) that freshwater
diatoms growth in the streams and lakes feeding the main river channel is stimulated by
phosphorus additions, and that the increased diatom growth leads to a net loss of silicon from the
water column, and subsequently in the main Mississippi River channel. This hypothesis is also
supported by the small, but significant, increase in silicon from 1986-1988, when phosphorus
fertilizer use declined a small amount, but nitrogen fertilizer use stabilized.

Several authors have noted the increase in nitrogen concentrations and loadings and phosphorus
concentrations and loadings in the upper Mississippi River, at the terminus of the river, and
throughout the Gulf coast (Walsh et al., 1981; Smith and Alexander, 1984; Smith et al., 1987;
Turner and Rabalais, 199la). The mean annual concentration of nitrate in the lower Mississippi
River was approximately the same in 1905-1906 and 1933-1934 as in the 1950s, but it has
doubled in the last 35 years (see Figure 4) (Turner and Rabalais, 199la). The mean annual
concentration of silicate in the lower Mississippi River was approximately the same in 1905-1906
as in the 1950s, then it declined by 50 %. Although the concentration of total phosphorus appears
to have increased since 1972, variations between years are large, and trends, if they exist, are not
clear. The seasonal concentrations of nitrogen have also changed; there was no pronounced peak
in nitrate concentrations earlier this century whereas there was a spring peak from 1975 to 1985,
due most likely to fertilizer application (see Figure 11). Computations of river flow and
concentrations of nitrogen and phosphorus have provided long-term data for total loadings of
nitrogen and phosphorus into the Gulf of Mexico by the Mississippi and Atchafalaya Rivers
combined (see Figure 5). Nitrogen loading doubled from 1954-1959 to 1980-1985; total
197
-------
phosphorus loading increased in the last 15 years, but there is too much variation to be precise
about the percent increase:
6°o
SUSPENDED LOAD
SUSPENDED
LOAD
(SHORT
TONS)
400
200
•
1950
1960
1970
YEAR
1980
Figure L12. Annual discharge of suspended load in the Mississippi River at Baton Rouge,
Louisiana, from 1950 to 1982 (adapted from Meade and Parker, 1984; in
Turner et al., 1987). Values in short tons (1 short ton = 2000 pounds, or 907
kilograms).

The silicaternitrate atomic ratios in the lower Mississippi River for this century have changed as the
concentrations varied (see Figure 12a,b). The silicaternitrate atomic ratio was approximately 4:1 at
the beginning of this century, dropped to 3:1 in 1950, and then rose to approximately 4.5:1 during
the next ten years, before plummeting to 1:1 in the 1980s. There has been a modest rise in the
recent three to five years, as a result of the coincidental concentration increase of silicate and
decrease of nitrate.

Water-quality changes in the Mississippi River are coincident with increased nitrogen and
phosphorus fertilizer use (see Figure 8). Fertilizer use recently reached a plateau; at the same time,
both the rise in river nitrate concentration and the fall in silicate concentration stopped. The rise in
nitrate in recent decades is evidence that the ability of watershed land to store the mostly ammonia-
based nitrogen fertilizers was exceeded.

The water quality changes documented also suggest that significant reduction of eutrophication is
not likely to occur without a reduction in fertilizer use. Limiting the amount of fertilizer used is a
more fundamentally sound management approach than is controlling its distribution. Significant
amounts of the currently applied nitrogen and phosphorus fertilizer eventually leak into the aquatic
environment, as well as possibly into the atmosphere (Turner, 1991). The riverine ecosystem
response to higher nutrient loading is consistent with the nitrogen-saturation hypothesis described
for northern forests by Aber et al. (1989).

The increase in nitrogen (and possibly phosphorus) and the reduction of silicon have profound
implications for coastal phytoplankton communities and, therefore, coastal food webs. Increased
phytoplankton production is the likely result in an otherwise nitrogen-Umited oceanic food web (the
current paradigm for many coastal systems; Harris, 1986; Valiela, 1984). Coastal diatom
198
-------
communities are certainly influenced by silicon supplies, and the Si:N atomic ratio of 1:1 is just
below the average for diatoms. Diatoms abundance would have declined, with a decrease in
silicate abundance, if all other factors remained constant Other nutrient concentrations did change,
however, and the increased nitrogen and phosphorus should favor flagellates (Office and Ryther,
1980), and this change may have a secondary impact on water column processes on the Louisiana
continental shelf. Hypoxic water masses form at the seabed and in overlying waters each spring
and summer at the terminus of the both the Mississippi and Atchafalaya Rivers (Rabalais et al.,
1991a). The disjunct zones of hypoxia in 1986 and 1987 both mirrored somewhat the surface
salinity field and surface phytoplankton biomass concentrations that resulted from the Mississippi
and Atchafalaya River freshwater inputs. [The surface water salinity in coastal waters adjacent to
the Mississippi River parallels the flow of the river (Geyer, 1950, 1955).] The presence of a
normoxic area between the hypoxic zones could be explained by 1) shallower depths, 2)
topographic bottom features, and/or 3) less stratified water columns. These explanations are not
entirely satisfactory, because the depth and density gradients in the normoxic area were similar to
those observed on the western end of the study area where hypoxia was present.

A doubling in riverine nitrogen loading would certainly be expected to increase phytoplankton
production, the most probable source of organic matter to fuel the respiration rates that deplete the
oxygen from bottom-water masses. However, because diatoms sink more rapidly than most other
phytoplankton, reduced diatom populations and/or biomass (through silicon limitation) have
compensated for the effects of phytoplankton community production that might have increased
through higher nitrogen loading. If flagellated autotroph density increased because of higher
nitrogen and phosphorus loading, community oxygen consumption rates may have shifted higher
in the water column, simply because diatoms sink much faster. The cumulative result may have
actually been no change, or even a decrease in the area! extent or intensity of hypoxia. Those
instances of lowered oxygen concentration in the upper water column, however, are consistent
through the entire water column (Rabalais et al., unpublished data). As mentioned earlier, the
diatom composition of waters adjacent to the Mississippi River may have changed over the period
for which there are water quality data (see page 34; Thomas and Simmons, 1959; Q. Dortch,
personal communication). Within the Mississippi River delta and its waters, phytoplankton
production and biomass is limited by the turbidity of the water, in spite of high nutrient
concentrations (R. E. Turner, personal communication).

Water quality data for the Mississippi River is collected by the U. S. Geological Survey in
cooperation with state and Federal agencies (e.g., USGS, 1980). Data for selected stations for the
Lower Mississippi River Basin and the Mississippi River Delta showed no values of dissolved
oxygen below 5 mg/1. The location of the sample in the water column was not indicated clearly but
assumed to be mid river, surface, or subsurface.
REFERENCES: G-9

Browder etal. (1987)
Cent. Wetland Res. (1970)
Fox etal. (1985)
Geyer (1955)
Gunning and Suttkus (1986)
La. Dept. Envir. Qual. (1987-90)
Lurry (1983)
Rabalais et al. (1991b)

G-10 Barataria Bay
Shiller (in press)
Shirzadetal. (1989)
Trefry etal. (1985)
Turner etal. (1987)
Turner and Rabalais (1991a,b)
Turner and Rao (1990)
Wiseman and Swenson (1987)
Wright (1970)
Significant sources of information concerning Barataria Basin are Conner and Day (1987), Madden
et al. (1988), and Boesch et al. (1989) and references therein. The Barrataria/Terrebonne Estuarine
199
-------
Complex has been named as a National Estuary under the U.S. Environmental Protection Agency
National Estuary Program. A conference was held in October 1991 for which there will be a
published synthesis of existing information on the systems.

The Barataria Basin is bordered by the leveed Mississippi River on the north and east, Bayou
Lafourche on the west, and the Gulf of Mexico on the south. The 628,000-ha Barataria Basin is
composed of three sub-basins: 1) fresh swamp and forest and a freshwater lake (Lac des
Allemands) comprise the upper basin, 2) brackish marsh and several large brackish lakes
characterize the middle basin, and 3) the lower basin is composed of two tidal saline bays
(Barataria Bay and Caminada Bay), several smaller saline lakes, and Spartina alterniflora salt
marshes (Madden et al 1988). The Barataria Basin is experiencing a high rate of land loss. With
the lack of direct sediment input from the Mississippi River since leveeing in the 1930s, the
important long-term mechanisms for sediment deposition in the Barataria Basin wetlands is storm-
driven resuspension with redistribution of sediments (Baumann et al., 1984).

Barataria Basin receives nutrient loadings on the same order of magnitude as Fourleague Bay in the
influence of the Atchafalaya River (see Section G-12), but the source is different (Madden et al,
1988). Barataria Basin is bordered by agricultural and urban areas, and its chemistry is impacted
' by high anthropogenic nutrient loadings in runoff. Hopkinson and Day (1979) estimated mean
total nitrogen and phosphorus concentrations in runoff water entering the upper Barataria Basin at
279 and 18 j/M, respectively. The altered hydrography of the upper Barataria Basin with its
extensive channelization has been implicated in the reduction of the ability of the natural wetlands
to assimilate high influxes of nutrients (Gael and Hopkinson, 1979). As a result, nutrient
concentrations are higher in the water column in channelized areas (Kemp and Day, 1984), and
receiving waters that drained the areas of highest canal density were the most eutrophic waters of
the basin with chlorophyll a levels of 43-59 j/g/1 (Seaton and Day, 1979). Basinwide averages for
chlorophyll a were 11 vgfl. Lac des Allemands retains about 55-60 % of the total phosphorus load
it receives, thus buffering the impact of phosphorus input downstream in the middle basin (Day et
al., 1976; Craig and Day, 1977).

In the lower end of the Barataria estuary, the Gulf of Mexico and the plume of the adjacent
Mississippi River become dominant physical and chemical factors (Madden et al., 1988). Ho and
Barrett (1975, 1977) measured pulses of freshwater carrying nitrate, phosphate and silicate
through the mouth of Barataria Bay during spring flood. The water quality in southern Barataria
Bay may be affected by changes in Mississippi River water quality because of its relatively large
freshwater inflow and evidence that salinity in Barataria Bay is inversely related to river discharge
(Wiseman and Swenson, 1987; Wiseman et al, 1990). There is a slight trend to support this idea
in a comparison of lower Barataria nitrate with that of the Mississippi River at St. Francisville, but
there is much variability in the limited data available for a preliminary analysis (Figure L13, R.E.
Turner, unpublished data).

There is a gradient along the axis of the Barataria estuary of nutrient concentrations, phytoplankton
production, chlorophyll biomass and turbidity (Witzig and Day, 1983; Madden et al 1988). The
upper end of Barataria Basin is eutrophic. Lac des Allemands has poor water quality and
biological oxygen demand is high, from nutrient loading due primarily to agricultural and urban
runoff from adjacent uplands. Dense blue-green algal blooms occur in Lac des Allemands and
Lake Cataouatche for nine or 10 months of the year (Day et al, 1976; Hopkinson and Day, 1979).
The upper Barataria Basin is characterized by frequent blue-green algal blooms, high turbidity,
dominance of fish such as gar and shad, and fish kills resulting from low levels of dissolved
oxygen. Lake Salvador, further south in the basin, is less productive and less heterotrophic than
Lake Cataouatche. From Lake Salvador southward, the waters of Barataria Basin are lower in
nutrient concentrations and productivity. While the central basin is far less affected by agricultural
runoff than the upper basin, nutrient enrichment is still a problem, stemming from urban runoff
200
-------
a I 0.5
OQ 0>
(0 ra

•g£
^^J ^^
ra ^.
fe ^ ° 25
CD £
0
0 1 2
St. Francisville
mg/1 nitrate-n

Figure LI3. Comparison of nitrate concenttations at the lower end of Barataria Bay to those of the
Mississippi River at St. Francisville, Louisiana, for similar time periods (R.E.
Turner, unpublished data).
from the New Orleans area. Dissolved organic and inorganic nutrients are largely removed by
flocculation in Salvador's brackish waters; waters south of this point in the basin do not receive
high anthropogenic nutrient loading. In Little Lake, mid basin, light penetration is greater where
depths are also shallower and benthic primary production becomes a dominant feature in the overall
productivity of the system. The water quality of Little Lake is good, but the Barataria Waterway
allows urban runoff to flow unhindered to the upper part of Barataria Bay. Sewage entering from
this route, as well as from fishing and hunting camps located throughout the basin, has resulted in
periodic closures of numerous oyster beds due to fecal coliform contamination (Louisiana DepL of
Environmental Quality, 1988). The saline end members have lower nutrient Concentrations, water
clarity is much greater and benthic photosynthetic production is significant. Witzig and Day (1983)
developed a trophic state index (TSI) to classify the water bodies in the Barataria Basin using
existing water quality data. Positive TSI scores indicate high nutrient enrichment. Most water
bodies in the upper and middle basin were classified with positive values (Table L4).

Barataria Bay is one of the estuarine areas in southeastern Louisiana currently experiencing closure
of some of its oyster beds (Louisiana Dept. Environmental Quality, 1990). The oyster growing
grounds are impacted by numerous sources* of pollution including untreated and partially treated
sewage, urban runoff, agricultural runoff, runoff from pasturelands, discharges associated with oil
field activities and vessel waste discharges (Louisiana Dept. of Environmental Quality, 1985).
Sewage treatment plant by-passes and drainage from non-sewered communities are the main
sources of bacterial contamination in the bay.
201
-------
Table L4. Trophic state index (TSI) of Barataria Basin. O=oligotrophic, M=mesotrophic,
E=eutrophic, and H=hypereutrophic (from Boesch et al., 1989, after Witzig and
Day, 1983).
Location
Caminada Pass
Bayou Rigolettes
Barataria Bay
Lake Salvador
Bayou Perot
Little Lake
Bayou Barataria
Barataria Waterway
Natural swamp stream
John-the-Fool Bayou
Little Lake oil and gas field
Bayou Chevreuil
Lake Cataouatche
Bayou des Allemands
Burtchell Canal
Bayou Citamon
Lac des Allemands
Bayou Chevreuil
St. James Canal
Position
in Basin
lower
lower
lower
middle
lower
lower
lower
lower
upper
lower
lower
upper
upper
middle
middle
upper
upper
upper
upper
TSI Trophic
score classification
-4.8
-4.3
-3.8
-3.3
-2.8
-2.7
-1.8
-1.6
-1.4
-0.6
-0.4
6.0
0.7
2.6
2.7
3.7
3.8
4.0
6.4
M-O
M .
M
M
M
M
M
M
M
M
M
E
E
E
E
E-H
E-H
E-H
H
Data on the dissolved oxygen content of the waters of the Barataria estuary are limited. Hewatt
(1950) collected data from a total of 60 stations at various times, mostly during April-July from
1945-1947. Out of 95 measurements, only one fell below 2 mg/1. Barrett et al. (1978) recorded
no instances of dissolved oxygen less than 2 mg/1. Near-bottom water oxygen concentrations
substantially below 2 mg/1 were found in a canal adjacent to a produced water (oilfield brine)
effluent in the Lafitte Oil and Gas Field. The low oxygen was associated with a highly stratified
water column and the dense, hydrocarbon-laden effluent which was flowing along the bottom
(Boesch and Rabalais, 1989b); dissolved oxygen levels returned to ambient levels at 250 m from
the point of lowest oxygen concentrations.

Two of the predominant causes of habitat degradation in the Barataria estuary are believed to be
saltwater intrusion and reduced sediment input and retention (EPA, Region VI, 1988). [Yet data
from Wiseman et al. (1990) indicate no trends in the Barataria Bay stations analyzed with the
exception of a decrease in salinity at the station nearest the Gulf of Mexico.] A major strategy to
divert a portion of the Mississippi River flow into Barataria Basin has been developed by the New
Orleans District of the U.S. Army Corps of Engineers. At least 17 alternative freshwater diversion
sites are in the Barataria Basin. The Davis Pond project, near Luling in the uppermost reaches of
the basin, is the most imminent. The Caernarvon Diversion Structure, which will drain into Breton
Sound, has been completed and had its first test. Proponents and opponents of these diversions
have differing views as to the effectiveness in providing sediments to be incorporated in marsh
habitats and the ultimate effect of the river's nutrients and chemical constituents upon the receiving
systems (see comments in Section G-8.1).
202
-------
The red tide caused by the dinoflagellate, Gonyaulax monilata, documented in Louisiana coastal
waters in September 1980 (Perry, 198Q) also occurred in the waters of Bayou Lafourche where a
fish kill, attributed to this water mass, occurred later in the afternoon.
REFERENCES: G-10

Barrett etal (1978)
Boesch and Rabalais (1989b)
Boesch etal (1989)
Browderetal (1987)
Cent. Wetland Res. (1970)
Childers and Day (1990a,b)
Conner and Day (1987)
Craig etal. (1977)
EPA (1988)
Gael and Hopkinson (1979)
Garrison (1982)
Hewatt (1950)
Ho and Barrett (1975,1977)
Hopkinson and Day (1979,1980)
Hopkinson et al. (1985)
Khalidetal. (1978)

G-ll Terrebonne/Timbalier Bays
La. Dept. Envir. Qual. (1987-90)
Lurry (1983)
Madden etal. (1988)
Perry (1980)
Rabalais et al. (1991b)
Seaton (1979)
Seaton and Day (1979)
Shirzad etal (1989)
Sklar and Turner (1981)
Smith and DeLaune (1985)
Van Sickle etal. (1976)
Waldrop (1983)
Williams (1956)
Wiseman and Swenson (1987)
Witzig and Day (1983)
Significant sources of information concerning Barataria Basin are provided in Boesch et al. (1989).
The Barrataria/Terrebonne Estuarine Complex has been named as a National Estuary under the
U.S. Environmental Protection Agency National Estuary Program. A conference was held in
October 1991 for which there will be a published synthesis of existing information on the systems.

The northern portion of the Terrebonne/Timbalier drainage system is composed mostly of high
land broken by bayous, canals, and swamps which is utilized for agriculture, pastureland, and an
ever increasing amount of urban development. Extensive marshes border the southern land
extremities and intermingle gradually with an extensive estuarine system, namely Terrebonne and
Timbalier Bays and Lake Pelto. These are connected to the Gulf of Mexico through a series of
broad passes. The area lies approximately halfway between the Mississippi and Atchafalaya
Rivers, but receives no appreciable influence from either, the major factors influencing fluctuations
in salinity are rainfall and local drainage (Adkins and Bowman, 1976).

The sources of eutrophication in Terrebonne are similar to other basins. In the upper basin,
agricultural runoff is primarily from sugarcane fields. From the available data, industrial waste
seems to be the source of extremely high phosphorus inputs, particularly in the Lake Verrett region
(Craig and Day, 1977). Municipal sewage from the Houma area is also a source of high nutrient
input and is the cause for shellfish bed closures throughout much of the estuary.

Several studies were conducted in the eastern portion of Timbalier Bay from August 1972 to
January 1974 in conjunction with an analysis of the effects of oil drilling and production (Offshore
Ecology Investigation/Gulf Universities Research Consortium, OEI/GURC) (Ward et al., 1979).
These included hydrographic profiles, water column nutrients and sediment nutrients along a
transect from the upper bay to the intersection with the Gulf of Mexico (Price, 1979; Burchfield et
al., 1979). Mean dissolved oxygen concentrations ranged from slightly less than 6 mg/1 to almost
11 mg/1, except for the July 1973 cruise when the mean value was near 3.6 mg/1; these low oxygen
levels coincided with the flood of the Mississippi River in 1973 (Figure L15) (Price, 1979). The
highest readings, >13 mg/1, occurred in the winter months; the lowest was 1.3 mg/1 in July 1973.
203
-------
61 ="

||=u
-3

C/5

<
to

'
rs
a:
o
UJ
o
CM
h-
q
CVJ
q
c>
q
03
ID
r—
co f"- to

Nl A1IAISSWSNVH±
CM
m
q
6
02.="
6S=u

001="
-3

•z.

<
u.

-3

o
UJ
CO
cr
o
LU
o
CM
r-
cn
q
to
in
OD
in
ro
*"S ra *
Wdd Nl N33AXO Q3ATOSSia
204
-------
V////////////////M
\- ffl
o z
D
Y/////////////////.
a.
uj
<
OQ
V////////////////////M
888888888888888888888888=
V////////////////////////M
188888888888888888888888888883
aiVHdSOHdOHlUO
vonis
(I/6UJ) VINOWWV
205
-------
Transmissivity showed a different seasonal pattern from that exhibited by the other parameters
(Figure L14). The maximum (99 %) and the highest mean (88 %) were observed during the July
1973 cruise which occurred during the 1973 flood.

The seasonal variations in nutrient concentrations in the OEI/GURC study (Figure LI5)
(Burchfield et al, 1979) were generally comparable to data collected by Barrett et al. (1978).
Nitrogen levels peaked during the winter months, increased in July in response to the heavy
summer rainfall, decreased slightly in October and then increased during the following winter. The
highest phosphate levels were observed during the fall, then decreased and remained relatively
constant throughout the remainder of the study. Silica concentrations were highest during October
of both 1972 and 1973 and minimal during the winter months. Price (1979) suggested that there is
less seasonal and spatial variability than is typical of many other bays along the central Gulf coast;
however, despite the paucity of streams entering the bay and its relative isolation from the
Mississippi River, it was responsive to the flooding of the Mississippi River in July 1973.

During the same period of the OEI/GURC investigations in Timbalier Bay, faunal studies of
dredged canals were underway in the Terrebonne .Bay portion of the estuary (Adkins and
Bowman, 1976). No values of dissolved oxygen (1 ft below the surface) less than 2.5 mg/1 were
recorded; the 2.5 mg/1 value was near Terrebonne Bayou in a closed canal. Barrett et al. (1978)
recorded no dissolved oxygen levels below 3.8 mg/1 for three stations in Terrebonne Bay sampled
monthly from October 1974 to September 1976. Dissolved oxygen data collected from Lake
Boudreaux (upper Terrebonne system) did not fall below 5 mg/1 in monthly samples taken in 1968
(Shampine, 1971). A study conducted by Williams (1956) in the Grand Bayou Blue section of the
upper Timbalier Bay estuary looked at water quality for the period December 1954 to August 1955.
Dissolved Oxygen concentrations were taken at approximately 1 m below the water surface;
however, several very low readings were obtained in August. All of the stations in the Williams
(1956) study were in dredged canals or narrow bayous where flow is expected to be reduced and
stagnation may occur during hot weather. Water quality measurements made in similar areas of the
Grand Bayou Blue in September 1988 did not reveal any low dissolved oxygen concentrations
(Boesch and Rabalais, 1989b). From the limited data available, low dissolved oxygen in bottom
waters of the Terrebonne/Timbalier Bay complex cannot be considered a problem. In some areas,
such as canals or channels, problems may be encountered in the warmer months.

Adkins and Bowman (1976) also provided nutrient data for their study (see Table L5). Generally,
nitrates decreased during cooler months, reaching an average low during December 1972 and
during April 1973. During previous studies in coastal Louisiana, Pollard (1973) (cited in Adkins
and Bowman, 1976) found much higher average nitrate values, typical of stations further removed
from Gulf of Mexico influence. The stations of Adkins and Bowman (1976), however, more
closely resembled seaward stations and thus had depressed nitrate levels. Nitrate values in
Terrebonne Bay are influenced by freshwater run-off, of which Coastal Study Area IV has very
little, which would explain the lower nitrate concentrations. Nitrate, nitrite, and ammonia values
did, however, reflect freshwater flooding experienced during the study.

A year-long study (October 1982 - October 1983) of the water column characteristics was
conducted along a Terrebonne Bay transect and into adjacent Gulf of Mexico waters (Dagg, N.D.).
Chlorophyll a levels seldom exceeded 20 fjg/l and were more commonly in the range of 10 A/g/1.
Nutrient concentrations were also generally low as seen by Adkins and Bowman (1976). Secchi
disk measurements indicated a normally turbid system.
206
-------

«
*••<
ft
TO
JH
*
® |
S; £«,
r~l O c*
v~' -Q O5
S -H ™
** Lrf
£ * -I
o S £
CQ j3 §
12 "£ "cu
| gw
•§ s£ "S

< •£ g
s S ^
£ ££
1 f-s
Ow JH
O Q)
wi | 3
« «0
3 "«
cd ^
t;
.—
in
*S
i»
V
13
>

0)
2
•5
1

i
s

i«
•^
03 1
buo 1

C^ £H

X
CS
So '
S .S
« S

CO
^ g
E" '-i3
o

?
03
gi
•*
di
t-

c2
i

?
03
[-•_

1
£2

CO
t-
1
t-

TI« o in oo o

co '-*'-* CM* rr
cQOOCDeocomi-itocoo
^i«^tH^-*^oicd'«jJw
CO

co-^rO'-''Ht~<'~'CMi^r»nt^
CO
CO Ol "fl1 CO O> CO CO O to O O
tDOdeOCOOCMCMOJCOCD'o
^

O O rf rp in O CO CO CO O O
C*dcDO'- D.** c
0*0 oooooooo c
f-tpQE-". OQt-'CQcHCQtHCQE-
o
CO
in
£
CO
O
g*
CO

in
fe
CO
o
§
^

0
c>

o
i-H

o
o

-
£

CM
c-

T
\ \
rl

o
s

0
3
O
CM
CO

o
o
CO

o
CO

o
g

CO
en

,]
: c
C.
N
o
CO
s
Q
~
O CO
cd t-:
CM

0 t-
CD t^
O CO
CM* CO

O rH
CO* t^
CO

o in
CD CO*
in
CO

0 CO
CM t-

r3< in
en en

CM CC

1»
: e
i *"*
! ™
a £ tl
> o c
rU
to

to eo
i-H

t- CO
C^ CM
CO O
06 *-<

CO OO
t> o

in oo
co to
CO

co to
t- «-l

in to
en en

.•

C
b
a
t
s
i
|i
>. i c.
"1 j
CO
CM* ,
1—1
O
CM
co in
^ CO
rH O
^^

C- O
«-H* d
TH
00 O
r-J CD

OO O
° 8

CM O
CO S
CM

in o
^ to'
in

s s

CM tD
C— C3

o
' -S
?'§
* >> C
L .-*? ^
• -^ b
om Condi
AIL-QlintH
1, ±J C
3 0 C
•^ CQ E-
oo
1
in
s
o
g
t— 1

o
o
o
CD*
CO

o
CM
CO

o
a

o
to*
CD

CM
C-

Z
- 1
f |

? =!
s i
i «
! s
rl

in
to
to
o
1

o
d
CM

o
1

o
s

CO
en

?
? S
s t
!i
i f
i c
? c
3 t-
00
S
oo
t-
m
to
to

o
to'
c-
o
in*
en
CO

o
CM*
CM

O
i-H
CM

O
S

L
, t
>
, «
1
! I
!• i
• c

0
CO

o
s
t-
o
g
§

o
d
OS

o
d

o
CO
LC

CD
cn

1
- J

i
"5
fc^
: c
c
CO
CO
tr-
O
S
t-
m
c-

o
i
o
1
s

0
I

20130.0

O
s

CM
t-

^ ,1
?*~
, 1
—
s
ii
rl

O
s
s

o
^
o
i
CM

O
e
TT

26800.0

o
c

", "5
• 1
1
"
I
i
> i
E-
0
t-
m
CO
o
t-

o
t-"
o
1
s

0
t-
Tj*

o
s

«=:
b
* E
:i
•c
V
•5
i
1
I
"• t
o:

o
o
•^

o
"
o
s

d
o

O
CD
C

O
o

) f~
, b
*-
1
•5
]
c
£
O
g
O
CD
O
S

o
10
o
1

0
d

o
a
CO

;CM
t-

, ^
3 *"*"
, 2
S

1
! S"
ii
i. t!
5 S
207
-------
REFERENCES: G-ll
Adkins and Bowman (1976)
Barrett era/. (1978)
Boesch and Rabalais (1989b)
Boesch etal. (1989)
Browder etal (1987)
Burchfieldera/. (1974,1979)
Gaboon and Groat (1991)
Cent. Wetland Res. (1970)
Craig etal (1977)

G-11.1 Caillou Bay
Dagg (N.D.)
Farrell (1974)
La. Dept. Envir. Qual. (1987-90)
Murrell and Fleeger (1989)
Price (1974,1979)
Rabalais etal. (199Ib)
Shampine (1971)
Ward etal (1979)
Wiseman and Swenson (1987)
No additional information updates the Rabalais et al. (1985) review. No dissolved oxygen values
less than 2 mg/1 Were recorded in a transect from Lake Mechant to Caillou Bay (Barrett et al.,
1978) and in limited collections in Lakes DeCade and Mechant (Shampine, 1971).
REFERENCES: G-11.1

Barrett etal. (1978)

G-12 Atchafalaya Bay/River
Shampine (1971)
Approximately 33 % of the flow of the Mississippi River system enters the Gulf of Mexico via the
Atchafalaya River (Figure L16) (Turner and Rabalais, 1991a). The long-term changes in the
Mississippi River were described above in Section G-9. The concentrations of nitrate, silicate, and
total phosphorus at Morgan City (0.5 km from the delta of the Atchafalaya River) were 69 %, 94
%, and 130 %, respectively, of that in the Mississippi River at St. Francisville for the combined
data for the years 1973-1987 (Table L6; Turner and Rabalais, 1991a). Differences between
nutrient concentrations in the Atchafalaya and Mississippi rivers are presumably a consequence of
differences in the water quality of the Red River (which mixes with the Mississippi to form the
Atchafalaya) compared with that in the Mississippi. These percentages are consistent across the
1973-1987 period, which indicates similar increases in nitrate (but at lower overall concentrations)
and similar reductions in silicate (but at lower overall concentrations).
Table L6. The average annual concentration of nitrate, silicate and total P at Morgan City,
Louisiana as a percentage of that at St. Francisville, Louisiana (paired samples)
(developed from data in Turner and Rabalais, 199la).
Nutrient
% at St. Francisville
Years
Silicate

Nitrate-N

Total P
69

130
12

15
208
-------
£^
.2J2
u-o
800
y = 0.328x -12161,257, R-squared: 0.966
250
500 750 1000 1250
Mississippi River Monthly Flow
atVicksburg(XIOOOcfs)
1500
175
Figure LI 6. Comparison of annual discharge of the Atchafalaya and Mississippi Rivers (R.E.
Turner, unpublished data).
Water quality during a phytoplankton study of the lower Atchafalaya River basin (Sager, 1976)
was determined in riverine, lacustrine and swamp habitats. The river stations had high sediment
loads, high discharges, stable pH levels, high nutrient levels and high dissolved oxygen percent
saturation levels. Swamp stations were characterized by clear waters (low suspended solids)
during the low water periods, relatively large variations in pH, low dissolved oxygen saturation
percentages, comparatively low nutrient levels, and often humate-rich waters. Lake stations were
commonly influenced by swamp waters draining into them but they generally had higher dissolved
oxygen concentrations, higher and more stable pH levels and more turbid waters than the swamps
during low water periods.

Wells and Demas (1977) and the USGS (1980) both noted that dissolved oxygen concentrations in
the main channel and major distributaries of the Atchafalaya River generally exceed 5-6 mg/1. The
USGS (1980) water quality data were for stations located in the lower Atchafalaya (Bayou
Penchant at Bayou Chene, near Amelia, Louisiana) and in Atchafalaya Bay (at Eugene Island).
Neither showed values below 5 mg/1 (location of sample in water column not indicated but
assumed to be mid river and surface or subsurface).

Several studies have been conducted in Fourleague Bay, a subestuary of Atchafalaya Bay (Caffrey
and Day, 1986; Madden, 1986; Randall and Day, 1987; Madden etal, 1988; Teague etal, 1988;
Childers and Day, 1990a,b; works in progress of J. Day, R. Shaw, and L. Rouse, LSU; works in
progress of R. Twilley, Univ. of Southwestern Louisiana, Lafayette; works in progress of M.
Dagg and B. McKee, LUMCON). Flow of the Atchafalaya River strongly influences spatial and
seasonal patterns of nutrients, suspended sediments and primary production. The estuary receives
most of its sediment input and high loadings of nutrients during spring. During low flow in
summer and fall, Gulf of Mexico waters dominate Fourleague Bay and increased water clarity
provides an opportunity when riverborne and regenerated nutrients can be exploited maximally by
phytoplankton. Even during periods when one would expect the river discharge to dominate,
climatic conditions can have a significant effect (Caffrey and Day, 1988).
209
-------
N:P ratios in Fourleague Bay waters average about 30:1, but upper bay ratios are often >100:1
(Madden et al., 1988), thus indicating a potentially large deficiency of phosphorus relative to
nitrogen (Figure L17). The seasonal decline in nitrate input with reduced river discharge is
followed by a reduction in the N:P ratio, although it rarely falls to 16:1 in the upper bay. During
summer and fall there is a major shift in the ratio of inorganic nitrogen to phosphorus in the lower
bay. During the spring flood nitrate concentration in upper Fourleague Bay averages 120 j/M; in
lower Fourleague Bay, 15 A/M (Figure LI8, Madden et al., 1988). During low flow nitrate
concentration in the upper bay averages 30 //M and in the lower bay is often <1
UPPEH BAY ENTRANCE
JF MAMJJASONO
JF MAMJJASONO

Figure L17. Atomic ratios of inorganic nitrogen to inorganic phosphorus in the Fourleague Bay
water column during 1981. Discontinuity at 16:1 Redfield ratio (from Madden et
al., 1988).

APRIL. 1981 OCTOBER, 1981
100 ,
NITRATE
20
DISTANCE DOWN-BAY
km
DISTANCE DOWN-BAY
km'
Figure LI 8. Typical inorganic nutrient concentration gradients in Fourleague Bay along the
midbay axis during high and low river flow (from Madden et al., 1988).
210
-------
Dinophysis sp., probably Dinophysis caudata, has been documented recently in an estuary of the
Atchafalaya River, Fourleague Bay (Q- Dortch et al., personal communication). D. caudata has
been recognized recently as a toxic dinoflagellate which may contribute to the accumulation of
toxins responsible for diarrhetic shellfish poisoning (DSP) in shellfish in Mobile and Galveston
Bays (R. Dickey, personal communication). The population of Dinophysis sp. documented in
Fourleague Bay was not in bloom proportions and not implicated in shellfish poisoning.
REFERENCES: G-12

Boesch and Rabalais (1989b)
Caffrey and Day (1986)
Cent. Wetland Res. (1970)
Childers and Day (1990a,b)
Craig etal. (1977)
Cunningham (1980)
Hern etal. (1978)
Juneau (1975)
La. Dept. Envir. Qual. (1987-90)
Lurry (1983)
Madden (1986)
Madden etal. (1988)
Rabalais et al. (1991b)
Randall and Day (1987)
Sager (1976)
Teague etal. (1988)
Turner and Rabalais (1991a)
Wells and Demas (1977)
Wiseman and Swenson (1987)
G-13 Vermilion/West Cote Blanche/East Cote Blanche Bays

Water quality of the Vermilion-Atchafalaya Bay complex is strongly influenced by the discharge
from the Atchafalaya River delta and Wax Lake Outlet There are obvious east-west differences in
water temperature and salinity (Juneau, 1975). Water quality data were collected for 17 stations in
1972-1974 in surface and near-bottom waters (Juneau, 1975). Surface and bottom water
temperature, salinity and dissolved oxygen levels were similar during the study period, indicating a
well-mixed water column. Dissolved oxygen concentrations averaged near 8 mg/1. The highest
average nitrate value was at East Bay during April 1972 with a value of 26.73 ng-at/1; the highest
single value was 39.90 A/g-at/1 at Dry Reef-Vermilion Bay. The lowest monthly average nitrate
value occurred at Oyster Lake during July 1972 with a value of 0.3 j/g-at/1. These differences in
nutrients reflect the high and low flow periods of the river, respectively. Similar lows and highs
for nitrate, inorganic phosphate and total phosphorus were found seasonally.

Environmental data were collected along with day and night trawls in 1968-1969 (Dugas, 1975).
The dissolved oxygen readings, as expected, decreased during the night and gradually increased
during the day (not indicated, but assumed to be surface readings); values through all seasons did
not fall below approximately 6 mg/1. Turbidity was controlled by wind mixing events in the
shallow bay.

Dissolved oxygen values for this system were determined for three stations sampled monthly
between October 1974 ad September 1976 (Barrett et al., 1978). In August at each station,
dissolved oxygen levels decreased but did not fall below 2.6 mg/1.
REFERENCES: G-13

Barrett etal. (1978)
Cahoon and Groat (1991)
Cent. Wetland Res. (1970)
Cunningham (1980)
Dugas (1975)
Juneau (1975)
Wiseman and Swenson (1987)
211
-------
G-14 Mermentau River/Grand/White Lakes

No update since the Rabalais et al. (1985) review. These systems are mostly freshwater marshes
and lakes, although they once contained brackish water as a result of saltwater intrusion from the
Gulf of Mexico. Control systems to prevent this and create reservoirs suitable for rice irrigation
make the lakes freshwater most of the time (Shampine, 1971). No data were available for this
area. Data concerning several marsh management areas are given in Gaboon and Groat (1991).
REFERENCES: G-14

Cahoon and Groat (1991)
Cent. Wetland Res. (1970)
La. Dept. Envir. Qual. (1987-90)

G-15 Calcasieu River/Lake/Pass
Shampine (1971)
Wiseman and Swenson (1987)
Calcasieu Lake, with the exception of the 12-m ship channel, is quite shallow, averaging 2 m in
depth (Lee et al., 1990). The lake is surrounded by brackish marsh and receives discharge from
the Calcasieu River, which enters from the norm. The long north-south axis of the lake is
approximately 28 km. Calcasieu Pass joins the lake with the Gulf of Mexico. Calcasieu Lake is
vertically homogeneous, a reflection of its shallow depth, the tidal and wind energy available for
mixing, and the low mean discharge of the Calcasieu River.

The Calcasieu River is heavily industrialized within the city of Lake Charles north of Lake
Calcasieu. Land use around Lake Calcasieu is rice farming to the north, particularly north of the
Gulf Intracoastal Waterway, and marshland (mostly managed) and wildlife refuges.

The Calcasieu Basin was the focus of a major water quality program by the Water Pollution
Control Division of the Louisiana Dept. of Environmental Quality beginning in 1978. These
studies were designed to address the sources, fate and effects of point and nonpoint sources of
oxygen-consuming materials and toxic substances in order to define water pollution control and
best management practices necessary to meet the State's water quality standards for water quality
limited segments of the Calcasieu Basin. The Calcasieu Estuary is currently listed (Louisiana Dept.
of Environmental Quality, 1990) as a "water body under advisory: toxics related concerns." The
Calcasieu Estuary has a history of unpermitted discharges (spills) and discharges exceeding
effluent permit limitations. Wastewater discharge permits for the major industrial facilities are
being reviewed and revised. The state will continue efforts to monitor and improve water quality
in the Calcasieu Estuary.

Several water quality monitoring programs have been conducted in the Calcasieu estuary. Barrett
et al. (1978) conducted monthly sampling between October 1974 and September 1976 in the Lake
and Pass. Additional data were collected during the DepL of Energy, Strategic Petroleum Reserve
Program, monitoring of the West Hackberry brine disposal site. These data (for February 1981
through February 1983) were obtained originally from G. Gaston (Univ. of Mississippi, Oxford,
formerly McNeese Stat Univ., Lake Charles) and subsequently published in reports (DeRouen et
al., 1982, 1983). Data were obtained from the Louisiana Dept. of Environmental Quality in the
form of field reports and some synthesized synoptic surveys of the basin on selected dates in mid
summer 1984.

The surveys of Barrett et al. (1978) recorded no dissolved oxygen values below 3 mg/1. In
general, low dissolved oxygen values are not a problem in Lake Calcasieu where there is little
stratification in the shallow, wind-mixed water column. Strong salinity stratification is restricted to
the Calcasieu Ship Channel and Calcasieu Pass. Within the ship channel, low oxygen levels (1.4
to 3.0 mg/1) are more prevalent in the area between the Gulf Intracoastal Waterway and the city of
212
-------
Lake Charles. In Calcasieu Pass, the DEQ data indicated less of a problem than the upper reaches
of the channel, because there is better tidal flushing. The data provided by G. Gaston, however,
indicated anoxic and hypoxic water in the Pass in June, July, September and October. The
Calcasieu River experiences very low oxygen concentrations which are lowest in July-October and
frequently reach anoxic levels, 0.0-0.3 mg/1.

A limited set of nutrient data was available from a June 1984 survey of the Calcasieu basin, but
provided no insight.

Two red tide producing organisms were documented in water samples taken monthly along a
transect through Lake Calcasieu and Calcasieu Pass (Maples et al., 1983)~these were
Prorocentrwn minimum and Gonyaulaxmonilata. No fish kills, jubilees or discolored waters were
associated with the presence of these organisms. Another dinoflagellate, Dinophysis caudata, was
recorded at the opening of Calcasieu Pass to the open Gulf of Mexico. D. caudata has been
recognized recently as a toxic dinoflagellate which may contribute to the accumulation of toxins
responsible for diarrhetic shellfish poisoning (DSP) in shellfish in Mobile and Galveston Bays (R.
Dickey, personal communication). The population of Dinophysis sp. documented in Calcasieu
Pass was not in bloom proportions and not implicated in shellfish poisoning.
REFERENCES: G-15

Barrett etal. (1978)
Cent. Wetland Res. (1970)
Craig et al. (1977)
Day etal. (1979)
Dennis etal. (1984)
DeRouen et al. (1982,1983)
Haddad and Carder (1979)
La. Dept. Envir. Qual. (1987-90)
Lee etal. (1990)
Lurry (1983)
Maples etal (1983)
Wiseman and Swenson (1987)
Wiseman etal. (1990)
TEXAS
Several state agencies collect data on water quality. The primary agencies are the Texas Water
Development Board (formerly Texas Department of Water Resources), Texas Water Commission,
and Texas Parks and Wildlife Department. Much of the data collected is used in modeling the
freshwater inflows to the estuaries for management needs. With the exception of the Sabine and
Galveston estuaries, the remaining Texas estuaries fall into a semi-arid habitat classification with
rainfall averages of less than 24 in/yr. Freshwater inflow into Texas estuaries is, therefore,
disproportionate with dramatic decreases southward (Figures Tl and T2). Much of the rainfall
along the Texas coast is aperiodic and extremely variable between years. Prolonged trends of
moist periods and droughts last 10 to 25 years. Many streams and rivers in Texas are controlled
by dams and reservoirs; the need to manage fresh water is important within the State. In order to
provide necessary water planning and management information on the effects of and needs for
freshwater inflows to the bays and estuaries of Texas, a Texas Bays and Estuaries Program was
established to conduct estuarine-wide studies. The research has been performed in cooperation
with the Texas Parks and Wildlife Department, the Texas Water Commission and other interested
state agencies and universities, including the Texas Department of Health, The University of
Texas, Texas A&M University, and Corpus Christi State University. Many of these research
programs will be identified in the following area descriptions.

Parts of the Texas coast are heavily urbanized and industrialized. These centers of point-source
discharges are located in the Sabine estuary, the Galveston estuary, and the Corpus Christi estuary
(Figure T3).
213
-------
c

50-

10
Annual Inflow/Estuary Volume
s
Z
I

*s
T3
C!
3

o
o
•s
.4
s
2
JS
e
a
w
Figure Tl. Average annual inflow, estuary volume, and inflow/volume ratio, 1941-1987 (Texas

Water Development Board, G. Powell, personal communication).
214
-------
A synthesis of nutrient loadings into each of the major Texas estuaries was developed by
Armstrong (1982) (cited in Armstrong, 1987) (Table Tl). The relative proportions of nutrients are
influenced by several factors, including the amount of freshwater inflow and the receiving volume.
The Sabine estuary receives the highest areal loading, because of its large freshwater inflows.
There is a general decrease in areal loading rates with direction southward to the Laguna Madre.
Nutrients derived from freshwater inflows dominate the nutrient budgets of all estuaries; marsh
contributions and precipitation are minimal. Armstrong (1987) also provides a synthesis of the
information concerning phytoplankton assemblages, primary production and zooplankton and
nekton population estimates across the major Texas estuaries (Table T2).

The Texas Parks and Wildlife Department collects surface water samples with its monthly gill net
and bag seine samples throughout Texas estuaries during spring and fall collection periods. For all
the Texas Bay systems sampled (G-16, G-17, G-19, G-21, G-22, G-23, G-24, G-26.1, land G-
26.2) between 1975 and 1986, the surface oxygen levels were within the range expected, and there
were no obvious trends for an increase in these values (Hegen, 1983; Rice et al, 1988). Surface
dissolved oxygen readings are available in previous reports by Martinez (1969-1975). Turbidity
readings taken at the same time indicate that concentrations of suspended materials are controlled
by meteorological events. Recent trends in increased turbidity within the Laguna Madre system,
however, may be related to changes in land use on its periphery, i.e., increased pastureland being
converted to cropland.

Fish kill data from the NOAA Fish Kill Inventory are shown in Table T3.

Algal bloom information is routinely collected and synthesized by the Texas Water Commission in
Corpus Christi (formerly by D. Jensen, now with Corpus Christi State University, Oil Spill
Prevention and Cleanup School, and currently by J. Bowman).

MEAN SALINITY IN TEXAS ESTUARIES
30
a 20
y^x
£
;a
'ct
02 10
§
o>
B
B

•"—I 1 —
>> >»
Cfl CQ
CQ «
to C3
S 6
CU
g tS
B

CQ
1
-a
&
B
B

i i
a >f
.!_! CQ
I/I CQ
1- O
3 |
B
B

B
1 1 1
>>
CQ £ CQ
* J i
1 s
-5
•a
B

1
a
CQ
•a
1
B

Mesquite Bay-
B

Diritu Santo Bay"
B

§>
CQ
CQ
O
CO
'1
B

&
CQ
CO
4J
a
c
t*
B
B

pper Mata. Bay •
Trinity
B

01
3
^
CQ
O>
O

Mid Galveston-
B

^
a
CQ
^j
CO
o>
B

B
I
cc? C
m -i :
^j CO
w CQ C
" 1 \

B
3
v o
: c
S '£
CQ
-------
Figure 7
Study Areas outside EDAs
EDA Boundary
Point Source
Figure T3. General location of major facilities in the NCPDI study area in Texas (from Pacheco
et al, 1989c).
216
-------
Table Tl.
Carbon, nitrogen, and phosphorus loading budgets for Texas estuaries (from
Armstrong, 1987).
Freshwater
Nutrient
Carbon

Nitrogen

Phosphorus

inflows
Estuary (106kg/yr)
Sabine Lake
Galveston Bay
Matagorda Bay
San Antonio Bay
Copano-Aransas Bays
Corpus .Christi Bay
Laguna Madre
Sabine Lake
Galveston Bay
Matagorda Bay
San Antonio Bay
Copano-Aransas Bays
Corpus Christi Bay
Laguna Madre
Sabine Lake
Galveston Bay
Matagorda Bay
San Antonio Bay
Copano-Aransas Bays
Corpus Christi Bay
Laguna Madre
115.70
103.44'
75.75
17.95
5.98
8.21
6.00
9.32
11.58
3.58
5.80
0.44
0.55
0.61
0.74
3.63
1.31
1.00
0.07
0.22
0.72
Marshes
Tidal
(106kg/yr)
2.50
4.02
5.35
0.88

9.11

0.02
0.12
0.05
0.01

0.02

0.50
0.09
0.11
0..02

0.18

Flood
(106kg/yr)
1.44
0.14
0.14
0.30

0.42

0.36
0.04
0.04
0.08

0.01

0.41
0.04
0.04
0.09

0.12

Precipi-
tation
(106kg/yr)

0.04
0.34
0.51
0.14
0.11
0.11

0.01
0.04
0.04
0.02
0.01-
0.01

Total
(108kg/yr)
119.64
107.60
. 81.62
19.13
5.98
•17.74
6.00
9.75
12.08
4.33
6.02
0.55
0.68
0.61
1.21
3.81
1.54
1.12
0.08
0.53
0.72
Area!
loading
(g/m2/yr)
672.20
75.20
80.50
34.10
12.90
39.90
2.90
54.80
8.40
, 4.30
10.70
2.00
1.52
.28
6.82
2.66
1.52
2.00
0.18
•1.20
0.34
GENERAL REFERENCES: TEXAS

ASIWPCA (1984)
Basta and Bower (1985)
Burrage (1989)
Culliton and Blackwell (1989)
Diener (1975)
Ehler and Basta (1985)
EPA (1974, 1978)
Hackney (1978)
Longley (1992)
Main etal. (1987)
Martinez (1969-1975)
Orlando etal (1991)
Pechmann et al. (1986)
NOAA/EPA Team (1990)
Shew etal. (1981)
Texas Water DvlL Bd. (1973)
Trebatowski (1988)
217
-------
Table T2. Summary of the major characteristics of phytoplankton assemblages in the open-bay
bottom biotopes of Texas estuaries (from Armstrong, 1987).
Seasonal phytoplankton
abundance
(cells/ml)3
Dominant groups
Primary production
estimate
Estuary
Sabine Lake
Galveston Bay
Minimum
70 (W)
50 (F)
Maximum
200 (S)
400 (W-Sp)
(by % of)
Diatoms (45%)
Green algae (36%)
Diatoms (41%)
(g C/rnVdayr
ND
5,87
(Trinity Bay)

Lavaca Bay 150 (S) 4,500 (W)

San Antonio Bay 549 (F) 19,000 (W)

Aransas Bay 6 (S) ' 381 (W)

Corpus Christi Bay 50 (S-F) 900 (W-Sp)
Nueces Bay
7 (S-F) 300 (W-Sp)
Oso Bay and ND (S)
Upper Laguna Madre 1,600 (W)
Lower Laguna Madre ND
ND
Green algae (25%)
Blue-green algae (23%)

Diatoms

Dinoflagellates

Diatoms

Diatoms
Blue-green algae

Diatoms

Diatoms
1.0

'2.52 (0.91)c

0.52

2V75

1.79
.Seasons are: S = summer, F = fall, W = winter, Sp = spring.
Carbon fixation based on oxygen method of measurement.
°Carbon fixation based upon 14C method of measurement and converted to gross
production.
G-16
Pass)
Sabine Lake/Pass (Sabine-Neches Estuary, includes Sabine Lake, Sabine
The Sabin estuary lies along the Texas-Louisiana border, has a surface area of 17,798 ha, and
receives inflow from the Sabine and Neches Rivers (Armstrong, 1987). Water depths at mean low
water vary from about 3 m or less in Sabine Lake to greater than 12 m in dredged areas; the
average depth is about 1.8 m. Much of the area around Sabin Lake is in urban and industrial land
use in the "Golden Triangle" area of Beaumont, Port Arthur and Orange (see Figure T3 for the
relative proportion of point source discharges in the estuarine drainage basin.). Marsh land
comprises a sizable percentage of lands near the estuary with urban populations centered on the
south and west of Sabine Lake, while the balance parallels the Sabin and Neches Rivers at the head
of the estuary.
218
-------
Table T3. Summary of NOAA Fish Kill Inventory Data for Texas (draft data base, 1991; J.A.
Lowe, personal communication; see section on Data Sources).
AREA
County
SABINE
Jefferson
Orange
GALVESTON
Chambers
Galveston
Harris
BRAZOS
Brazoria
MATAGORDA
Matagorda
SAN ANTONIO
Calhoun
ARANSAS
Aransas
Refugio
San Patricio
CORPUS CHRIST!
Nueces
Records
per County
60
50
45
176
100
78
68
23
25
3
11
24
UPPER LAGUNA MADRE
Kenedy 1
Klegerg 4
LOWER LAGUNA
Cameron
Willacy
MADRE
14
0
Cause Cause
Low DO Eutrophication
6
8
16
100
34
19
16
16
1
0
4
6
0
2
4
0
0
0
0
0
1
0
2
2
0
0
0
.1
... o
0
0
0
Cause
Red Tide
0
0
0
0
0
0
6
0
1
0
0
1
0
0
0
0
Cause
Nutrient
1
0
0
0
0
0
1
0
0
0
0
0
. 0
0
0
0
Cause
Unknown or
Unspecified
9
5
12
8
16
9
8
4.
3
1
0
3
1
0
1
0
Little new environmental data were available for this estuary. A reassessment of bottom water
dissolved oxygen values from the Texas Department of Water Resources, Coastal Data System,
indicated that most of the low dissolved oxygen values occur in the deeper channels and tidal
rivers. Many values in the Sabine and Neches Rivers fell below 1 mg/1 or were anoxic. There
were fewer low oxygen values (<2 mg/1) in Sabine Pass than in the Sabine-Neches Canal and the
Port Arthur Canal because of increased tidal flux at the former. A few values at the opening of
Sabine Pass approached anoxia. In Sabine Lake, of many values for the open water environments,
only one fell below 2 mg/1.
REFERENCES: G-16

Armstrong (1987)
Dennis etal. (1984)
DeRouenetaL (1982)
Hahl and Ratzlaff (1970,1972,1975)
Lind(1983)
Monaco etal (1989)
Pachecoetal. (1989)
Rice etal (1988)
TDWR(1981b)
Turner and Rao (1990)
219
-------
G-17 Galveston/East/West Bays (Trinity-San Jacinto Estuary, includes
Galveston, East, West, and Trinity Bays, Bolivar Pass, GIWW)

The Galveston Bay estuary is the second largest on the Texas coast with a surface area of 143,153
ha (Armstrong, 1987). It has an average depth of 2.1 m, although it is traversed by a major
navigation channel, the Houston Ship Channel, which extends from the mouth of the estuary
through Galveston Bay and into the San Jacinto River Channel, turns west into Buffalo Bayou and
ends on the east side of Houston. Most of the industrial complex in the Houston area borders this
navigation channel. The major freshwater inflows to Galveston Bay come from the Trinity and
San Jacinto Rivers.

The Galveston Bay complex is heavily industrialized (see relative proportion of point-source
discharges in Figure T3). Major chemical and petrochemical plants line the estuary and extend far
inland along the Houston Ship Channel and other dredged canals. Unpermitted discharges (spills),
inadequate waste treatment and stormwater runoff are mechanisms by which chemical pollutants
enter the Galveston Bay system. Evidence for the potential impacts that toxics carried into the
system may have is a recent report of the occurrence of the solvent, 2-butoxy ethanol, in Gulf of
Mexico waters adjacent to Galveston Bay (Baton Rouge Morning Advocate, July 6, 1991). The
compound was isolated from Gulf waters which were used in laboratory toxicity tests and found to
be toxic to larval shrimp. The report indicated that heavy rains in the Galveston Bay complex
during the spring and early summer flushed the toxic chemical into the nearshore waters of the
Gulf. Other contaminants affect fisheries resources. During the last 30 years, large portions of the
bay, usually around the shoreline, have remained closed to shellfishing, primarily as a result of
high levels of coliform bacteria introduced by runoff from surrounding lands.

Galveston Bay was designated an estuary in the EPA National Estuary Program because of its
significant natural resources and the threats impinging upon those resources from pollution,
development or overuse. The EPA Galveston Bay National Estuary Program has established a
Galveston Bay Information Center which will 1) conduct a Galveston Bay literature survey and 2)
develop a reference collection of the identified literature. This work is in progress (F. Shipley,
personal communication). A workshop to characterize problems in Galveston Bay as part of the
EPA National Estuary Program was held in February 1991 (Shipley and Kiesling, 1991). The
purpose of the meeting was to synthesize information prior to the development of a Comprehensive
Conservation and Management Plan.

A NOAA-funded study was conducted in the Galveston Bay estuarine complex to determine long-
term trends in water quality and their relationships to the living resources (Stanley, 1989); similar
studies were conducted in Narragansett Bay, Delaware Bay, and the Pamlico River estuary. Data
for the Houston Ship Channel, open Galveston Bay and the Trinity River were targeted for
analysis. The Houston Ship Channel is heavily populated and industrialized. The analysis of the
long-term data set indicated that low dissolved oxygen levels in bottom waters have been alleviated
during the last 20 years (Figure T4) and that BOD loading to the system has gone down (Figure
T5). Data from 1968-1988 in the ship channel indicated that surface water dissolved oxygen
content has gone up, bottom water oxygen levels no longer fall below 1.5 mgA, ammonia has
decreased, nitrate has increased, and overall DIN has decreased but not as dramatically (Figure T6)
(Stanley, 1989). Phosphorus concentrations in the ship channel have shown about the same
temporal spatial trends as those for nitrogen.

Analyses of nekton populations in the upper portions of the Houston Ship Channel indicate an
increase in abundance and diversity with concomitant improvement in water quality since the mid
1970s (Seiler et at., 1991). Dissolved oxygen data compiled for 1988-1989 by Seiler et al. (1991)
in their nekton studies indicated extended periods in mid summer of both years where bottom
waters in Segment 1007 (uppermost Houston Ship Channel near turning basin) were hypoxic or
near-anoxic (Figure T7). Bottom water dissolved oxygen concentrations in Segment 1006 (lower
220
-------
AVERAGE
<1.5MG/L
6 5 4 3 2 1 0 20 40 60 80 100
D.O;(MG/LITER) PERCENT OF SAMPLES

• AVERAGE • <2.oMG/L
6 5 4 3 2 1 0 20 40 60 80 100
D.O.(MG/LITER) PERCENT OF SAMPLES

Figure T4. Trends in annual mean surface dissolved oxygen in Houston Ship Channel Segment
1007 (Turning Basin) (upper panel) and Channel Segment 1006 (Greens Bayou to
San Jacinto River) (lower panel) (from Stanley, 1992).
221
-------
500
Ibs/day (Thousands)
400-
300-
200-
100-
Municipal
Industrial
1968 1970 1972 1974 1976 1978 1980 1982 1984 1986
YEAR
Figure T5. Trends in BOD loading to the Houston Ship Channel between 1968 and 1986 (from
• Stanley, 1992).

Houston Ship Channel near Tabbs Bay confluence) were consistently higher for the same timer
period, in spite of an apparent lack of stratification (Figure T7).

In open Galveston Bay, analysis of trends was more difficult given the paucity of bottom water
oxygen data; however, surface water data did not show any obvious trends (Figure T8) (Stanley,
1992). High BOD or low dissolved oxygen have never been found to be problems in the open
waters of Galveston Bay (Rabalais, et a/., 1985; Stanley, 1992). The average concentration of
surface water dissolved oxygen concentrations would be expected to increase as a result of nutrient
enrichment and eutrophication (see section on Altered Habitats).

The long-term data for nitrogen and phosphorus were also examined by Stanley (1992). He found
that nitrate concentrations appear to have declined after 1972, but that this may be an artifact of the
data sets (Figure T9). There was a trend of decreasing nitrate along the increasing salinity gradient
from Trinity Bay toward the Gulf of Mexico. Nitrate levels in this system do not seem abnormally
high in comparison to other Gulf coast or Atlantic coast estuaries. There have been no obvious
trends in the ammonia concentration data (Figure T10). Other than an apparent decrease in total
phosphorus in Trinity Bay, there have been no obvious trends in phosphorus concentrations in the
222
-------
M
G
T
E
R
M
G
7
L
I
T
E
R
1963 1968 1973 1978 1983. 1988
1963
1968
1973
1978
1983
1988
1963 1968
1973 1978

YEAR
1983 1988
Figure T6. Trends in ammonia and nitrate concentrations in Houston Ship Channel Segment 1007
(Turning Basin) (upper panel), Segment 1005 (San Jacinto River to Morgan's Point)
(middle panel), and Segment 1006 (Greens Bayou to San Jacinto River (lower panel)
(from Stanley, 1992).
223
-------
CO
: 2 s
UJ
LU
UJ
CO
LU
UJ
X
UJ
CO
CO

1
UJ
$2 8
m
UJ
UJ
UJ
ui
LU

p
Q

UJ
CO

CO
o
m
UJ
00

i
u
00
3
c«

1
ca

8.
S"

g£
CO T—I

58^
g a
x ***
S "w

i.i
-rt 4>
eco
e* a

8§

cgfe
g •—i
S.g

CQ OT
flj r"*

224
-------
DO (MG/LITER)
12-

1O -

8 -

e -

4 -

2 -
TRINITY BAY
O
1 963
1388
1973 1978 1983 1988
YEAR
DO (MC3/L.ITER)
12-

10 -

6 -

•4. -

2 -
' GAUVESTOIM BAY
1983 1988 1973 1978
YEAR
DO (MC3/LITER)
12 -

1O -

8 -

6 -

•4 -

2 -
WEST BAY
1963 1968 1973 1978
YEAR
DO
-------
2.s
NO3-N (MG/LITER)
2 -

1.S -

1 -

o.s -
TRINITY BAY
a
1968 197O 1972.1974 1976 1978 1 9SO 1 98Z 1984 1988 1988
YEAR
NO3-N (MG/LITER)
1968 197O 1972 1974 1976 1978 1 98O 1982 1984 1986 1988
IMO3-1M j£MG/l_ITER)
O.6 -
0.4 -
WEST BAY
an
-O-t nnC3 I I "ilifiBij
1968 197O 1972 1974 1976 1978 198O 1982 1984 1986 1988
YEAR
0.8
NO3-N (MC3/LITER)
O.6 -
O.4 -
O.2 -
EAST BAY
•*a a a
% i_m ji i LI LI g r
1968 1970 1972 1974 1976 1978 198O 1982 1984 1986 1988
YEAR
Figure 19. Nitrate nitrogen concentration trends in four areas of the Galveston Bay system, 1968-
1986 (from Stanley, 1992).
226
-------
NH4-N (MG/LITER)
0.6 -
o.s -
O.4 -
O.3 -
O.2 -
0.1 -

a TRINITY BAY a

iZ3C3
oan-
-, ^- °
ra a rain o a an
a
o -1 ' • '
1 968 1 970 1 972 1 974

NtH4-N (MG/LITER)
1 .2 -]
1 -
O.S -
O.6 -

O.4 -
O.2 -

"^JkaJlitf* AolS^

1976 1978 1980 1982 1984 1986 1988
YEAR

ta GALVESTOW BAV a

a a

Cfl3 MM iiu i
O -1 1 1 1 — —
1 968 1 97O 1 972 1 974
NH4-N (MG/LITER)

O.3 -
0.2 -

O.I -

° WEST BAV

CD a

a ca
ODD

O -1 1 1 1
1 968 1 97O 1 972 1 974

NH4-N (MG/LITER)
0.8 -
0.6 -

O.4 -

0.2 -

S» EAST BAV

CD
a
a o (-] a
CD a i iP » r-O c
O] i^1

a
a
a a
r? cfeffifih™ ^iffi? ts«S^a^&_

1 976 1 978 1 9BO 1 982 1 984 1 986 1 988

a CD

a
o ™^
o
DCOd cP D a a P
Q a , 0 ^^^^ED ^a

1976 1978 1980 1982 1984 1986 1988
YEAR
'

en
a

1 " ' ' i—i _J— ' f-j

1968 1970 1972 1974 1976 1 978 198O 1982 1984 1986 1988
YEAR
Figure T10. Ammonia nitrogen concentration trends in four areas of the Galveston Bay system,
1968-1986 (from Stanley, 1992).
227
-------
bay system over the past 20 years (Figure Til). Preliminary results from a similar analysis of
Galveston Bay nutrient data (1980-1989) (Santschi and Samuell, 1991) indicated strong seasonal-
and salinity-related patterns to the distribution of phosphate, nitrate and total inorganic nitrogen
concentrations.

Very few low dissolved oxygen values are found in the bottom waters of the shallow open bays.
There were area-wide low dissolved oxygen values (but only a few <2 mg/1) hi July 1976 in
Galveston Bay and those stations in East Bay closest to Galveston Bay, but this did not occur in
other years (Rabalais et al, 1985). Limited low oxygen values have been recorded in Trinity Bay
and East Bay in the hottest months when wind mixing of the water column does not occur. In the
East Bay area, dissolved oxygen concentrations fluctuated between 0 and 4 mg/1 in July and
August 1982 (Figure T12) (Ambler, 1982).

In the upper parts of Trinity Bay, there are more problems year-round with low dissolved oxygen
concentrations in bottom waters because of reduced mixing and the heavy industrialization of the
area. Historically, the lowest oxygen levels are in the channels, particularly the Houston Ship
Channel, but the trend in the Houston Ship Channel has reversed over the last 20 years. Low
values, below 2 mg/1 and often below 1 mg/1, have been recorded in Barbour's Cut, Texas City
Ship Channel, Bayport Channel, Galveston Channel and Dickinson Bayou. Among the channels,
those closer to the Gulf of Mexico with increased tidal exchange have less frequent occurrences of
low dissolved oxygen.

The Texas Water Development Board has conducted many long-term deployments of water quality
instrumentation in selected Texas estuaries to follow continuous variations in near-bottom water
salinity, temperature and dissolved oxygen (Longley, 1992). Results from these deployments
have been provided by the Texas Water Development Board (Longley, 1992). The results for
dissolved oxygen concentrations must be reviewed in the context of the instrumentation and the
environments in which deployed. The instruments become fouled with algae and bryozoans and
the oxygen probe fails at the end of the record (G. Powell, personal communication). Weekly
changes in the instrumentation across a series of sites is prohibitively expensive and logistically
difficult; still, pilot studies have been conducted in a few estuaries.

Deployments were made in Galveston Bay, off Dollar Point for most of 1988. While the data from
the deployment in October 1988 (Figure T13) show no dissolved oxygen levels below 2 mg/1, the
data are displayed to show the decay in the oxygen probe with time and the recovery of the signal
when exchanged with a new instrument with a freshly installed and calibrated oxygen probe.
During 1988 no values from February-June or August-December fell below 2 mg/1. [This analysis
is based on the first seven days of the instrument deployment] During January, many values were
below this level and registered zero; however, changing of the instrumentation in February
alleviated this problem. The data from January are assumed to be inaccurate, especially since the
water temperatures should have been conducive to high dissolved oxygen content

Stanley (1989) presented data summarized by Johnson (1975) on Galveston Bay fish kills for the
period 1962-1974. Most kills occurred during the summer, many were located in the semi-
enclosed harbor at Texas City; few were in open water, most of the kills in the ship channel were
attributed to oxygen depletion or sewerage operations; open bay kills were attributed to oxygen
depletion, pesticides, petrochemicals, bacterial infections and unknown causes. Although there is
an increase in the number of fish killed in the system since 1975, this has been attributed to
increased monitoring and reporting (Stanley, 1989). Fish kills in Dickinson Bayou in 1972 were
directly related to sewage outfall, increased and dense algal blooms, and subsequent oxygen
depletion (Knudson and Belaire, 1975). According to the NOAA Fish Kill Data Inventory (Lowe
et al., 1991), the Galveston Bay estuary drainage area had the highest number of fish killed of all
counties in the entire Gulf of Mexico study area. Half of these kills were attributed to low-
dissolved oxygen levels that were not associated with a land-use cause. This drainage area also
228
-------
TP (MG/LITER)
O.8 -
O.6 -
O.4 -
O.2 -
0 -
19
1 -
O.S -
O.6 -
O.4 -
O.2 -
o -
19
1 -
0.8 -

0.4 -
0.2 -
0 -
19
1 -
O.S -
O.6 -
'0.4 -
0.2 -
o -
o a a "
o o o
o TglNIT^V BAY g ' ''
o a
f~^i t C3 i • _
[=1 ff3 a a a

64 • 1968 '1972 -1976 . ,198O 1984 1988
YEAR
TP (MG/LITER)
' • • 'a
a GAUVESTOIM BAY o
• •• '
o . Q o
a o
jj^ ° QQO ^ D^^^OcPa^
agl . ^° o°a oaD^-^|-gff

64 1 9S8 i 972 1 976 1 9SO 1 9S4 1 9S8
YEAR
TP (MG/LITER)
a . . -
° NA/EST BAV
a
a •• •
^1 O
a- a
""^J^ 3^4.3^

64 1968 1972 1976 1 98O 1984 1988
YEAR
TP (MG/UITER)
o .
1=1 EAST BAY
00 0
° B • •*
^ "=^^^>r%,^

1 968 1 972 1 976
YEAR
1 98O 1 984
Figure Tl 1. Trends in total phosphorus concentrations in four areas of the Galveston Bay system
1963-1986 (from Stanley, 1992).
229
-------
O)
4
17 21 25 29
TEMPERATURE (°C)
4
12 2O *28
SAUNITY (0/00)
36
15 JULY
0 2 4 6 8 10
DISSOLVED OXYGEN (PPM)
17 21 25 29
TEMPERATURE (°C)
12 20 28
SALINITY (0/00)
36 0 2 4 6 8 10
DISSOLVED OXYGEN (PPM)
Figure T12. Vertical profiles at 0.5 m intervals of temperature, salinity, and dissolved oxygen at
the East Lagoon sampling station on several consecutive days during two sample
periods (from Ambler, 1982).

contains the highest concentration of point sources in the U.S. coastal area (Lowe et al., 1991; see
also Figure T3).

Studies of benthic and nektonic communities in Galveston Bay have generally concluded that the
community structure is controlled primarily by salinity, but that some areas of the bay have a
preponderance of organisms that indicate some level of environmental pollution (Chambers and
Sparks, 1959; Bechtel and Copeland, 1970; Holland et al, 1973).
230
-------
Galveston Bay, off Dollar Pt.
October. 1SBS
Salinity
Temp C
Dis. Oxy.
4-0. —i

36. —

32. —

28. —

'24-. —

2O. —

IS. —

12. —

8. —

4-. —

O. —
o.o
4-.0
S.O 1 2.O
1
1 6.O

Day
20.0 24-.O 28.0 32.O
Figure T13. Oxygen meter deployment data (Longley, 1992).

Pulich. and White (1991) have documented the decline of submerged vegetation in the Galveston
Bay system and attributed these losses to critical physical alterations, including shoreline erosion
and dredging and development activities, and to water quality degradation related to Galveston
Island development projects (secondary treatment plants), noxious chemical effluents and chemical
spills (Pulich et al. (1991). Loss of SAV in West Bay is likely related to differences in chlorophyll
a levels in West Bay compared to Christmas Bay between 1972 and 1980 (Pulich et al., 1991).
Resultant reduction in light availability and anoxic conditions may have ultimately decimated many
of the West Bay seagrass beds.

Historically, excessive growth of phytoplankton has not occurred with any regularity in the open
waters of the Galveston Bay system (Stanley, 1989); however, the few reports are worth noting.
Red tides associated with the dmoflagellate, Gonyaulax, have been reported from locations within
Galveston Bay. The notable example is the 1949 summer episode in Offatts Bayou (Connell and
Cross, 1950). The organism was tentatively identified as G. catenella by Connell and Cross
(1950X but subsequently confirmed by Howell (1953) as G. monilata. Few fish were killed and
no oysters were contaminated during the peak of the "red water," but fish died quickly when the
bloom settled out of the surface waters and the water became "white" or "milky." Similar red tide
incidences had been reported by residents and fishermen for the previous 15-20 years (circa 1930).
Gunter (1942) attributed the mass mortality of fish in Offatts Bayou, during years previous to the
massive red tide, to the stagnation of the inner portions of the bayou plus the accumulation and
anaerobic decomposition of organic matter during the summer months. Several other authors
(cited in Wardle et al., 1975) have noted common inshore summer blooms of G. monilata in the
Galveston area.
231
-------
High cell concentrations of the dinoflagellate, Exuviella baltica, were recorded in three areas of the
Galveston Bay system, including portions of Trinity Bay (Zotter, 1979). The bloom persisted
during the winter of 1976-1977 and was similar to the bloom of winter 1972-1973 that persisted
two to three months in the western half of Galveston Bay. In addition to the high cell
concentrations of the dinoflagellate, there were high numbers of the blue-green alga, Schizothrix
calcicola, and the green alga, Chlorella sp.

Nitzchia pungens f. multiseries has been identified from Galveston Bay samples (1989) and
archived East Lagoon samples (1974) (Fryxell et al., 1991). This morphological form of the
pennate diatom N. pungens, produces a powerful neurotoxin domoic acid that is responsible for
amnesiac shellfish poisoning (ASP). While not encountered in bloom conditions in Galveston
Bay, N. pungens f. multiseries is presumed to become toxic during senescent blooms. Systematic
surveys and laboratory experiments with the diatom are underway (Fryxell et al., 1991).

Dinophysis caudata has been recognized recently as a toxic dinoflagellate which may contribute to
the accumulation of toxins responsible for diarrhetic shellfish poisoning (DSP) in shellfish in
Galveston Bay (R. Hickey, personal communication).
Lind (1983)
Monaco etal. (1989)
NOAA (1989)
Pacheco etal (1989)
Pulich and White (1991)
Pulich etal. (1991)
Pullen etal (1971)
Renaud (1985)
Rice etal. (1988)
Santschi and Samuell (1991)
Seileretal. (1991)
Shepard and Rusnak (1957)
Shipley and Kiesling (1991)
Stanley (1989)
TDWR (198 Ic)
Zotter (1979)
REFERENCES: G-17

Ambler (1982)
Armstrong (1987)
Baldauf etal (1970)
Bechtel and Copeland (1970)
Benefield etal. (1983)
Chambers and Sparks (1959)
Connell and Cross (1950)
Dennis etal. (1984)
Fryxell (1990)
Fryxell etal. (1991)
Gillard (1974)
Gunter(1942)
Harper and Guillen (1989)
Hegen (1983)
Holland etal. (1973)
Johnson (1974)
Knudson and Belaire (1975)

G-18 Brazos River (Brazos River Estuary, includes Brazos River, San Bernard
River, Freeport Ship Channel)

The Brazos River is the longest and largest in basin area of eight Texas river basins (Johnson,
1977). It empties directly into the Gulf of Mexico near Freeport. The lower 9.6 km were dredged
to form the "new river" or Brazos River Diversion Channel when the original river mouth was
made into the Freeport Harbor. The Freeport Ship Channel empties directly, into the Gulf of
Mexico. The San Bernard River enters the Gulf 6.4 km southwest from the Brazos River mouth.

No new data concerning oxygen depletion or nutrient concentrations are available for this area.
Most low dissolved oxygen values (well below 2 mg/1 and near anoxic) were found in the upper
reaches of the San Bernard and Brazos Rivers where there is infrequent flushing of the rivers.
Johnson (1977) discussed additional factors of chemical plant discharge, waste treatment outfall
and salinity stratification compounded by a drought in 1974. The Freeport Ship Channel does not
experience the low dissolved oxygen values, observed in man-made channels in other areas (G-16,
G-17, G-26.2). It is not as deep (18-20 ft) and the distance between Freeport Harbor and the Gulf
232
-------
of Mexico is much less, than for example, the Houston Ship Channel or the Corpus Christi Chip
Channel.

The red tide of 1986 which occurred along the length of the Texas coast from near Galveston to
Port Isabel did not enter the waters of the Brazos River or the Freeport Ship Channel
(Trebatowski, 1988).
REFERENCES: G-18

Armstrong and Goldstein (1975)
Hahl and Ratzlaff (1972,1975)
Johnson (1977)
Lind (1983)

G-19 East Matagorda Bay
Monaco etal. (1989)
Pacheco etal. (1989)
Seadock (1974)
Steidinger (1973)
Portions of the flow of the Colorado River reach East Matagorda Bay, but the majority of its flow
goes directly into the Gulf of Mexico through a dredged channel (Armstrong, 1987).

No new data concerning oxygen depletion or nutrient concentrations are available for this area. No
low dissolved oxygen levels below 2 mg/1 were found for this bay in the Texas Department of
Water Resources, Coastal Data System.

The red tide of 1986 which occurred along the length of the Texas coast from near Galveston to
Port Isabel did not enter the waters of East Matagorda Bay (Trebatowski, 1988).
REFERENCES: G-19

Hahl and Ratzlaff (1972,1975)
Hegen (1983)
Lind (1983)
Pacheco etal (1989)
Rice etal (1988)
G-20 Colorado River (Colorado Estuary)

Portions of the Colorado River flow into the northeast arm of Matagorda Bay and adjacent parts of
East Matagorda Bay to its north. Because of the configuration of the Colorado River delta, the
proportion of the river flow that actually reaches the adjacent estuaries is largely unknown
(Armstrong, 1987). A dredged channel through the river delta permits most of the discharge to
flow directly to the Gulf of Mexico, but there are points of access between the river channel and the
estuaries.

No new data concerning oxygen depletion or nutrient concentrations are available for this area.
The lowest dissolved oxygen values (1.8 and 0.3 mg/1 out of 76 records) were found in the upper
reaches of the estuary in deep channels (11-15 m). No stations located below the Gulf Intracoastal
Waterway had dissolved oxygen levels less than 3 mg/1. These stations were shallower (3-4.5 m),
closer to the Gulf of Mexico and more subject to tidal exchange and flushing.

The red tide of 1986 which occurred along the length of the Texas coast from near Galveston to
Port Isabel did not enter the waters of the Colorado River (Trebatowski, 1988).
REFERENCES: G-20

Groover and Sharik (1974)
Hahl and Ratzlaff (1970,1972,1975)
Lind (1983)
233
-------
G-21 Matagorda/Lavaca Bays (Lavaca-Tres Palacios Estuary, includes Lavaca,
Matagorda and Tres Palacios Bays)

The Matagorda Bay system is the third largest estuary on the Texas coast with a surface area of
101,368 ha (Armstrong, 1987). Its average depth is 2.3 m. Like Galveston Bay, Matagorda Bay
is traversed by a navigation channel that extends from a cut through the barrier island up to Lavaca
Bay in the northwest corner of the estuary. Major freshwater sources include the Lavaca River,
flowing into Lavaca Bay, and the Colorado River, which flows into the northeast arm of
Matagorda Bay. Because of the configuration of the Colorado River delta, the proportion of the
river flow that actually reaches the estuary is largely unknown (Armstrong, 1987). A dredged
channel through the river delta permits most of the discharge to flow directly to the Gulf of
Mexico, but there are points of access between the river channel and the bay. Matagorda Bay has
relatively little urban development around its periphery. Small cities are scattered along its western
and northern boundaries, and some major industry is located on the shores of Lavaca Bay. The
Matagorda estuarine drainage areas is one of three drainage areas in the Gulf of Mexico (others are
Galveston Bay and Lower Laguna Madre) which received the highest applications of fertilizer to
adjacent agricultural lands (NOAA, 1990a).

Two studies update the previous review by Rabalais et al. (1985). These are 1) a synthesis on
Matagorda Bay by Ward and Armstrong (1980), and 2) the comprehensive studies funded by the
Texas Water Development Board and conducted by The University of Texas at Austin, Marine
Science Institute, on the freshwater inflow effects on the Lavaca River delta and Lavaca Bay (Jones
et al, 1986).

The average concentrations of several nutrients and forms of carbon were synthesized by Ward and
Armstrong (1980) and are shown in Table T4. In general, the average concentrations at these
stations, which give representative spatial coverage of the entire system, indicate relatively uniform
nutrient levels throughout the system. Nearly two-thirds of the inorganic nitrogen is in the form of
nitrate with the remainder as ammonia and nitrite. Since Matagorda Bay is lightly impacted by the
activities of man in comparison to other Texas Bays (e.g., Galveston Bay, Sabine Lake, and
Corpus Christi Bay), numerous nutrient point-source loadings from municipal and industrial
discharges do not currently exist, as reflected in the measured nutrient levels (Ward and
Armstrong, 1980).

On the other hand, strong patterns in the distribution of nutrients were demonstrated in the Jones et
al. (1986) study and were often related to the influence of fresh water. High concentrations of
nitrate were associated with low salinities in the first study year (1984-1985) which was relatively
wet, and concentrations were very low in the following dry year (1985-1986). Pigment
concentrations were significantly higher in the first year, consistent with, but not demonstrating
higher primary production. Total phosphorus was also higher in fresh water. Total Kjeldahl
nitrogen (TKN) concentrations were higher in the dry second year. Total nitrogen, defined as
TKN + nitrate + nitrite, was not significantly different between years. The ratio of phosphorus to
nitrogen in the water column declined as a function of salinity, and it appeared that phosphorus
declined more sharply than would be predicted from mixing of different water types (i.e., P was
removed from the water column, either physically, chemically or biologically). Even though
inorganic nitrogen levels were often very low and the potential for phytoplankton growth may have
been limited by the supply of nitrogen, it was possible that the supply of phosphorus could
ultimately exert an important control on productivity of the system.

Data from the Texas Department of Water Resources, Coastal Data System, were re-examined for
values less than 2 mg/L There was only one occurrence of oxygen deficiency in the open, shallow
bay system (in Tres Palacios Bay). The Jones et al. (1980) study, reported that fresh water
introduced to a rather salty bay system formed a lens over the river in June 1986, vertical mixing
was restricted, and anoxia (0.3 mg/1) formed below the surface at two river stations. Another
234
-------
o
00
0\
T-H
bB
I

1
1
£
|
«§•
03
c3
T3
«
CX

^^
C™^
s
o
*
Wi
^
o
•a
g
c
8
c
8
I
•fi
s
'C

CM ro
0. t-

1^ vO
"«^" rH
0 0
0 0

*3" sO
r~ co
0 0
0 0

o ro
CM r— 4
0 O

00 f-
=N ro
0 0
O Q

VD ro
m in
o o

n)
East Matagorda E
Matagorda Bay
(Mid-bay)

r~t t—4
0 0
-H rH

%
&
^

235
-------
instance of hypoxia (1.4 mg/1) was recorded at a river station in October 1985. Similar low values
(0.3 and 0.4 mg/1) were documented in Rabalais et al (1985) for the Lavaca River and Navidad
Rivers in 3 m water depth. In the relatively shallow bays, strong wind-induced mixing results in
generally uniform dissolved oxygen concentrations vertically (Ward and Armstrong, 1980). Low
dissolved oxygen values occurred in deep channels (approximately 9 m) where slight stratification
occurs (Ward and Armstrong, 1980). Some of the most frequent occurrences of low dissolved
oxygen (<2 mg/1) were in the Palacios Channel (two of 58 records) and the Alcoa Ship Channel at
its terminus (10 of 37 records).

The extensive 1986 red tide (Gymnodinium breve) which affected most of the Texas coast spread
throughout the Matagorda-Lavaca Bay system, entering via the Matagorda Bay Ship Channel and
Cavallo Pass, and extending up into Lavaca, Cox and Keller Bays. The organism existed in the
Matagorda-Lavaca Bay system throughout September (Trebatowski, 1988).
REFERENCES: G-21

Armstrong (1987)
Benefield etal (1983)
Blanton etal (1971)
Cullen and Jones (1986)
Cullen and Lane (1986)
Gilmore etal (1976)
Groover and Sharik (1974)
Hahl and Ratzlaff (1970,1972,1975)
Hegen 1983)
Jones etal. (1986)
Kalke (1986)
Kalke and Montagna (1989,1991)
Lind(1983)
Maurer and Parker (1972)
Monaco etal. (1989)
Montagna and Kalke (1989b)
Rice etal. (1988)
Seadock (1974)
Shepard and Rusnak (1957)
TDWR (1980b)
Ward etal. (1980)
G-22 San Antonio/Espiritu Santo Bays (Guadalupe Estuary, includes San
Antonio, Espiritu Santo and Mesquite Bays)

The San Antonio Bay complex has a total surface area of 56,162 ha (Armstrong, 1987).
Freshwater inflow is from the Guadalupe River, which has built a large delta at the upper end of
the estuary. This estuary is connected with Matagorda Bay to the northeast and the Aransas Bay
complex to the southwest. The average depth of the estuary is 1.4 m. Land use in surrounding
areas is primarily agriculture (irrigated rice crops) and ranching.

Two studies supplement the review of Rabalais et al. (1985): 1) a study of the effects of freshwater
inflow on hydrological and biological parameters (Childress et al., 1975) and 2) the comprehensive
studies funded by the Texas Water Development Board and conducted by The University of Texas
at Austin, Marine Science Institute, on the freshwater inflow effects on the San Antonio Bay
system (Kalke and Montagna, 1989; Montagna and Kalke, 1989; and Whitledge, 1989).
236
-------
Freshwater inflow into San Antonio Bay introduced nitrate concentrations of 68-120 //g-at/1 into
'the upper bay with the highest concentration in November and the lowest in July .1987 (Figure
T14) (Whitledge, 1989). The range of observed nitrate concentrations in surface waters was 0.1 to
120 /;g-at/l. In all samples the surface nitrate was reduced to less than 1.0 j/M in lower San
Antonio Bay. Surface chlorophyll a distributions throughout the sampling period had maximum
concentrations in the middle or lower bay regions due to the combination of rather large nutrient
concentrations and increased light penetration with distance from the river source. The
concentration of chlorophyll a in the river source ranged from 0.6 to 13.5 //g/1 and in the open bay
water reached as high as 50 fjg/l (Figure T15) (Whitledge, 1987). Ammonia concentrations were
highest on the west side of San Antonio Bay suggesting an apparent link in space of the inflow of
nutrients, production of organic matter and decomposition into recycled nutrients (Whitledge,
1989).

Out of 58 stations throughout the system, with hydrographic data from 1972-1984 (Texas
Department of Water Resources, Coastal Data System), no bottom water dissolved oxygen values
fell below 2 mg/1, and only two values were <3 mg/1. Of the Texas estuaries, this area had the
lowest frequency with the least intensity of oxygen-depleted waters. Although Whitledge (1989)
indicated an area of depressed oxygen concentrations in the west and central regions of San
Antonio Bay in April 1987, only one of these values fell below 4 mg/1 and all others were greater.
Although low dissolved oxygen values were indicated for the lower bay station in the Montagna
and Kalke (1989) portion of the 1986-1988 San Antonio Bay program (R. Kalke, personal
communication), these data were not included in the report

The Texas Water Development Board has conducted many long-term deployments of water quality
instrumentation in selected Texas estuaries to follow continuous variations in near-bottom water
salinity, temperature and dissolved oxygen (Longley, 1992). Results from these deployments
have been provided by the Texas Water Development Board (Longley, 1992) (see Section G-17
for details). Deployments were made in San Antonio Bay near Seadrift in December 1986,
January 1987, January-July 1989 and September 1990. The data indicated no dissolved oxygen
levels below 2 mg/1 based on the first seven days of the instrument deployments; data for March-
April 1989 are displayed in Figure T16). [N. B., the decay in the oxygen readings with time.]
The record for October 1990 picked up the extreme daily fluctuations in dissolved oxygen
concentrations associated with the bloom of a blue-green alga (G. Powell, personal
communication).

The extensive 1986 red tide (Gymnodiniwn breve) which affected most of the Texas coast was
spread throughout the Espiritu Santo Bay through Saluria Bayou and by the end of September all
of Espiritu Santo Bay contained red tide and resultant fish kills (Trebatowski, 1988).
REFERENCES: G-22

Armstrong (1987)
Benefield etal. (1983)
Childress (1966)
Childless era/. (1975)
Hahl and Ratzlaff (1970, 1972, 1975)
Hegen(1983)
Kalke and Montagna (1989)
Lind (1983)
Maurer and Parker (1972)
Mclntyre and Cullen (1988)
Monaco etal. (1989)
Montagna and Kalke (1989a,b)
Montagna and Yoon (1989)
Montagna el al (1989)
Pachecoetal. (1989)
Rice et al. (1988)
Shepard and Rusnak (1957)
TDWR (1980a)
Whitledge (1989)
237
-------
OO
ON
1
I
o
•a
2
CO
c
I/I
§
'i

1
§
o
g
• 1—t

I
1
CO
H

I
238
-------
o\
oo
a
•8
I
Jw,

>>
cS
«

1
00
'•T"«

I
»—

.1
00
239
-------
x° *

c ~

MhO

1
I I I I I I I I I I
•0
0
.00
XO)
0,-
m

O'C

'E£
o<
4->
c
<
c
0
in
tni-Q
0
D
1/10)
03
OQ .
r
o o
c
0
i i i r

3 10 M N
q

q
•od
CN

q
•6
q x

•« Q
q
•DO
•R
n

q
•ai
q
• t
(N

q
6

o x
ID 0
- Q

q
CM

q
03
CN
Ctf
4-^
cd
,
"
(D
e
c
X
O
I
240
-------
G-23 Aransas/Copano Bays [Mission-Aransas Estuary, includes Mission,
Aransas, Copano and Redfish (part) Bays and Aransas Pass]

The Aransas Bay complex is made up primarily of Copano and Aransas Bays, with a very small
area immediately northwest of Copano Bay in Mission Bay and part of Redfish Bay, for a total
surface area of 46,279 ha (Armstrong, 1987). Major freshwater inflows are from the Mission and
Aransas Rivers, although these inputs are relatively small. Land use in the estuary is dominated by
agricultural and ranching activities with only minor areas of irrigated crops. Population density is
low.

The studies of Holland et al. (1973, 1974, 1975) documented the nutrient and hydrographic
characteristics of Copano, Redfish and Aransas Bays. Means of data from transects across these
three areas are given hi Tables T5-T7). Additional values are given by Henley and Rauschuber
(1981) for Redfish Bay (Table T8).

There are few occurrences of low dissolved oxygen values in the shallow, open bay waters. Of
these, only two fell below 2 mg/1 (out of 500+ samples). Most of the low dissolved oxygen
values, often anoxic, were associated with tidal rivers and creeks (e.g., Heffernan, 1969-1970,
1972); some of the anoxic waters may be related to oilfield brine discharges (Heffernan, 1972).
The Mission-Aransas estuary occurs in an area of the Texas coast in a transition to semi-arid
climatic conditions. Rainfall averages 35 in/yr but is coupled with a subtropical temperature regime
and persistent southeasterly winds. The annual precipitation deficit is 12 to 16 inches (Brown et
al., 1976). Thus, reduced freshwater inflows in the peripheral tidal creeks and rivers of this
estuary coupled with climatic factors, contribute to the occurrence of low oxygen values.

The extensive 1986 red tide (fcymnodiniwn breve) which affected most of the Texas coast entered
Aransas Bay through Aransas Pass and quickly spread into Aransas, Corpus Christi, and Redfish
Bays (Trebatowski, 1988).

Table T8. Statistical summary of water quality data for the Redfish Bay portion of the Nueces-
Corpus Christi Bay System for 1972-1976 (from Henley and Rauschuber, 1981).
Parameter
Mean
Median
Variance
Standard deviation

Water temperature (°C)
Dissolved oxygen (mg/1)
Salinity (ppt)
Organic nitrogen (mg/1)
Nitrite (mg/1)
Nitrate (mg/1)
Ammonia nitrogen (mg/1)
Orthophosphate (mg/1)
Total phosphate (mg/1)
Inorganic carbon (mg/1)
Organic carbon (mg/1)
Turbidity (JTU)
PH

21.35
7.90
24.74
0.387
0.013
0.028
0.100
0.014
0.0315
19.28
16.95
23.58
8.52
Redfish Bay
22.05
7.40
25.25
0.350
0.005
0.030
0.100
0.010
0.030
16.75
17.50
16.25
8.40

46.54
2.35
18.04
0.020
0.0002
0.00002
0.00
0.00003
0.00015
59.16
123.47
396.70
0.062

6.82
1.53
4.24
0.142
0.016
0.005
0.00
0.0057
0.0121
7.69
11.11
19.92
0.249
241
-------
in
s
en
r~
ON
I
8
I
o
•«-^
o
2
'O

ctf

S'
ca

.§
I

R
i
8

*
t*
I*
°i

al
0

si
TOTAL .P04 H3/L
.Kin. Kax. Ave.
g
SJ
fl
J
ax
f1
J
I;
J y
a'*
M
.*!

Ii
t^ .
s*
§j!
o
ii
.
\\
I1
si

1 IKtlcoOHrHin
CM rH rH H i-4 CM
0 00000
CM CM rH rt «H Kl
O O O O O O
1 'S '3 ""-a 2?
o L coin CM tn in
I I co t O 01 m in f
H CM rH H CM rH
o o o o o o
i i CD t f CM r- m r»
H CM CM CM CM H
O O O O O O
• -3 'ssass
!!ld!2l^
0 0 ' 0 ' ' 0
tp f KI in
o o 4o * o
in co co O
1 1 r-( CM 1 CM 1 1 rH
1 * oo o ' o
o o o o
I 1 CMf 1 CO 1 1 >-t
1 ' oo ' o ' ' o
o o o o
1 t rHM t H 1 1 rH
1 'dd 'd ' 'd
m Kt KI co
1 t O O 1 O 1 1 O
1 'dd 'd ' 'd
t 1 CMO 1 O 1 t 3
1 'dd 'd ' 'd
K..O „ *, S
1 1 O O 1 O I t O H
' 'dd 'd ' 'd ?
tn in rH o *
t 1 O O 1 i-4 1 1 H M
t i o o i o t i o in
o o " o
tn in in u
t 1 0 0 1 K| t 1 rH 2
1 1 O O 1 O t 1 O M
00 0 0 *^
i ill is : :§ 1
00 0 O X
tn CM co H
i t f in t K» | t r» u.
1 ' o o ' o ' ' o* |
o o o
! !23 !5 ! '3
o o o o
I 1 CM <-H 1 CM 1 If
1 'dd !d ' 'd

sssssssss.
«"" 333333°

rH H rH
I!!!1IZ
mr-^qoior-toKt
m co u> KI « in CM CM 10
CM CM rH CM .-H CM CM
CM CM H CM H CM CM
CM CM rH CM rH CM CM

t i u> t as r-» i— o o
CM r-t (H CM
O O O O O O
o . o o o o o
i i 10 I r- <» r* o in
CM r-\ i-1 H
. , °. otncMOO
1 1 tn I M GO CM Kl CM
rH CM r-l CM H
O O O CM O O
O O O CM O O
1 1 10 I rH in CMKI CO
«H CM r-l CM
«t lp H Kl
I IOO | O | | O
i i • • i • i i •
o o o. o
in o H KI
t 1 0 H 1 O 1 10
1 'dd 'd ' 'd
**• CM H Kl
1 1 0 0 1 0 | |0
1 'dd 'd ' 'd
o o o o
o o o o
O 0 0 0
o o o o
o o o o
1 1 rH rH 1 H 1 1 rH
' 'do 'd ' 'd
SK| Kl Kl
O 1 O 1 1 O
' 'dd 'd ' 'd
f Kl Kl Kl
Kl Kl Kl Kl
t I 0 0 | 0 | |0
1 'dd 'd ' 'd
en in * in
1 t O 0 1 0 | 10
i ( o S i o i to
O 0 0 0
1 1 H O 1 O t 1 O
1 t O O 1 O 1 1 O
o o o o
m in KI in
t 1 O O 1 O 1 1 O
1 1 OO 1 0 t 10
o o o o
o o in tn
1 I into | rH | 1 Kl
O O O O
O O O O
t 1 lOr-i | CM t 1 f
1 'dd 'd ' 'd
000 0
1 1 V Kl | H 1 | K|
' ' dd ' a ' ' d
CMCMCMCMCMCMCMCMC«I
CMCMtMCMKICMCMCMCM
incMHmcoKitncnin
CMCMCMCMCMCMCMrHCM

™II^I
01 HrlrH """*
rH
^ r* CM 10 m ^ co co o
CM rH rH CM rH CM CM
CnfKlOHCMOCMOl
CM H CM rH CM CM
CM CM K»
6
ys
a .
rfjj
J .
al
•j
i&
z •
Ii
J J

5 <
Js
,*
t
"B
t
$
,«
\i
C
S
s

3x'
f
' c
x
,
S •
J
jjj
>
1 1 • 1
' 'S '
o
! ! g !
r-
1 'a !
o
! Id!
O
! ls'l
, ,S8

o o
, ,ss

t too
1 'oo
O3
i J • *^
o o
1 1 CM Kl
1 'dd
, ,ss
' 'dd
f Kl
1 IOO
' ' 00
SKI
0

Kt K»
i too
oo
\a in
! !§g
O 0
Sin
0
1 1. O O
o o
Kt rj H ul CO
O O O O O
o r- Kt eo tn
f* o co Kt in
CM CM CM CM rH
O O O O O
CM CM CM CM CM
0 O 0 0 O
m en o in *t
fH rH CM CM H
m u>
t o t i o
i • t i •
0 0
1 K| | | rH

in co
1 O 1 t O
I 0 1 t 0
0 0
in f
1 O 1 | rH
1 0 1 | 0
o o
1 t •» CM 1 CM 1 | in
CM • O O
Z X i i en tn

a* *' '°o'
MHino
MCMiHCM
>< - - KI r-
iu>- £ r--
^!
u c
S3
L.E
£„

1!
242
-------
•n
s;
CO
f-
I
52
O
8
CD

I?
fe
e
'i
a
sT
.1
tn o o o o w in
t^ d co t^ cd 06 co
o i" oo w o oo e* in m

•inCO
(po aScC)Tiii?5rti75ioTr^
^o ooddocJddd
o o o o o o o o o o
i ddd
p go rHi-

3° S S ° PJ S ° S TT §

ddd !
iJ
tj .OOOOOOOOOO
a !• OOOOOOOOOO
-S
3
o o i

OOOOOOOOOO

dddddddddo
w dddr-Jodddd

*-s S S 01 S 8 8 co R 8 °
>< dddddddddd
.g - : -
fOO O I
. 5d d i
U >:Qt3»^S!3S3GP<3

Iddddddddo'd

. CO CO CO to CO (
2 O O O O O '
3 o' d d d d i
88258888888
dddddddddd

CO CO I
O O I
dddddddddd
OOOOOOOOOO
J

§«
ooocs888888
dddddddddd
8cp in t
O o t
) O O O (
OOOOOOOOOO
ff
Z -in 11
dddddddddd
oo tQ in i
8
181
OOOOOOOOOO
^ in i/p in in in i
:888§88
^jddddddddd
sssassssss
dddddddddd

oooooooooo
rHrHrHrHSSRr^SS
dddddddddd
OOOOOOOOOO

SCO CO CO CO CO CO CO CO CO
ooooooooo
OOOOOOOOOO
OOOOOOOOOO
o ooo o.o o o o o
f» CO CO TT
01 co r» c* ^s» t^
-------

in*
^^
<*"
T-H
rt
1-M
•s
13
1
O
ffi
E
2
fc<
B
OJ
g
1
PI
.a
"§
&
&
•a
Si
(D
13
•s
1
1

•a
B
03
E
S
1
"S
5§

P
0
g

•r
a
a
o
a

f^ M
°3
3
S p

fl
U K
.a1
u fl
oS
1?;
8*5
1
b c
P X

2*3
0*
i-3

—
s"

-»H -HT
OIKV3B
OX
,
>
I'-
g
2

-I

fl
,
~l
§ .
"J
c •

Ho^vMtnr4Hiu>r4nno

rM rs| r>4 «-( rH >H
OrHOOHOOOOOOOO

OOOOOOOOOOOOO

OOOOrHOOOOOOOO

°.^°.°r<.°°o°°^°<::
0 00 0000
0 0 0 0 0 O 0 0 0 0 0 0 0 •»
o
-1
wwininintn-vcnri^-vnM g

fi)
OOOOOOOOOOOOO M
OOOOOOOOOOOOO Z
OOOOOOOOOOOOO *

OOOOOOOOOOOOO
OOOOOOOOOOOOO
*••!•••*>.••••,
OOOOOOOOOOOOO
•
OOOOOOOOOOOOO
OOOOOOOO-OOOMO
OOOOOOOOOOOOO
inmooooooooooo
ooooooooooooo
inmooooooooooo
OOOOOOOOOOOOO
ooinmuiwiMrt^ir-i^Hj-its
OOOOOOOOOOOOO
r- *r •* wi

«— H

•H IN iHi-t
OOOOOOOOOOrHOO

OOOOOOOOOOOOO

OOOOOOOOOOOOO
OOOOOOOOOOOOO

ri » * en «i ri * r, m fnin « n

OrHOOOOOOOOOOO
OOOOOOOOOOOOO

OOOOOOOOOOOOO
OOOOOOOOOOOOO
OOOOOOOOOOOOO

OOOOOOOOOOOOO
OOOOOOOOOOOOO
OOOOOOOOOOOOO
otnoooooooor* ^ r* r- in p-

rH rH C* rH rH
OOOOOOOOOOOOO
OOOOOOOOOOOOO
V
OOOOOOOOOOOOO

OOOOOOOOOOOOO

m ooooooooooooo
rH
rH

a
r£ OOOOOOOOOOOOO
•C OOOOOOOOOOOOO
Q
S

OOOOOOOOOOOOO

•OOOOOOOOOOOOO

OOOOOOOOOOOOO
OOOOOOOOOOOOO
OOOOOOOOOOOOO
J.
OOOOOOOOOOOOO

OOOOOOOOOOOOO
OOOOOQOOOOOOO
r* *r ^ in
( r^ a> m r^- m
en IH r-i ci 1-4 in in
M •-( t*r»-
i
t c r-4 m u. -
3 a 3 ti
244
-------
REFERENCES: G-23

Armstrong (1987)
Brown etal (1976)
Hahl and Ratzlaff (1970, 1972,1975)
Heffernan (1970. 19071, 1972)
Hegen(1983)
Henley and Rauschuber (1981)
Holland et al. (1973,1974,1975)
Lind(1983)
Maurer and Parker (1972)
Monaco etal. (1989)
National Estuary Study (1970b)
Pachecoetal. (1989)
Rice etal (1988)
Rileyetal. (1989)
Shepard and Rusnak (1957)
TDWR (198 la)
G-24 Corpus Christi/Nueces Bays (Nueces Estuary, includes Nueces, Corpus
Christi and Redfish (part) Bays and Aransas Pass)

The Corpus Christi Bay estuarine system is made up of Nueces Bay, Oso Bay, Corpus Christi Bay
and the southern end of Redfish Bay for a total surface area of 44,451 ha (Armstrong, 1987). The
average depth is 2.4 m and, like many other Texas bays, is traversed by a major navigation channel
that begins in the Aransas Pass Inlet and ends in the port of Corpus Christi. Land use around the
estuary is dominated by agriculture and ranching. The City of Corpus Christi, with its associated
port and industrial complex is located on the west side of the estuary and dominates land use in that
area. An increasing number of additional industrial complexes are located on the north shore of
Corpus Christi Bay in Ingleside. Suburban sprawl affects much of the land adjacent to the bay.

Table T9. Statistical summary of water quality data for the Nueces-Corpus Christi Bay System for
1972-1976 (from Henley and Rauschuber, 1981).
Parameter
Mean
Median
Variance
Standard deviation

Water temperature ( G)
Dissolved oxygen (mg/I)
Salinity (ppt)
Organic nitrogen (mg/1)
Nitrite (mg/I)
Nitrate (mg/1)
Ammonia nitrogen (mg/1)
Orthophosphate (mg/1)
Total phosphate (mg/I)
Inorganic carbon (mg/1)
Organic carbon (mg/I)
Turbidity (]TU)
PH

Water temperature ( C)
Dissolved oxygen (mg/1)
Salinity (ppt)
Organic nitrogen (mg/1)
Nitrite (mg/1)
Nitrate (mg/1)
Ammonia nitrogen (mg/1)
Orthophosphate (mg/1)
Total phosphate (mg/1)
Inorganic carbon (mg/1)
Organic carbon (mg/I)
Turbidity (JTU)
pH

21.05
8.10
20.34
0.641
0.091
0.038
0.125.
0.057
0.117
21.84
23.32
67.34
8.35

21.15
7.59
26.16
0.444
0.017
0.053
0.124
0.032
0.059
20.19
17.64
19.03
8.42
Nueces Bay
22.50
8.20
22.10
0.620
0.010
0.030
0.100
0.040
0.110
21.60
23.00
62.50
8.30
Corpus Christi Bay
22.70
7.10
26.70
0.430
0.006
0.030
0.100
0.030
0.050
17.55
17.65
17.45
8.40

51.90
2.45
53.70
0.025
0.029
0.0002
0.003
0.001
0.002
52.47
412.54
2,001.80
0.047

45.47
2.17
19.66
0.009
0.0003
0.006
0.002
0.0002
0.0006
43.86
109,31
110.05
0.051

7.20
1.56
7.32
0.158
0.171
0.0145
0.054
0.036
n n
-------
The studies of Holland et al (1973, 1974,1975) and Henley and Rauschuber (1981) documented
the nutrient and hydrographic characteristics of Corpus Christi and Nueces Bays. Means of data
from transects across these three areas are given in Tables T9-T12. The work of Flint (1983) and
Flint et al. (1986) documents the importance of freshwater inflow into this system with its
accompaniment of nutrients. Primary production is positively related to the amount of ammonia in
the water column which' is inversely related to the salinity (Figure T17).

There were no occurrences of low dissolved oxygen values (<2 mg/1) in the open, shallow bay
waters. Most low values were found in the deeper channels, e.g., Corpus Christi Chip Channel
and associated turning basins, 12-15 m; LaQuinta Channel, 12 m. Fewer and less intense low
dissolved oxygen values were found in other channels, less deep, e.g., Aransas Shrimp Channel,
4.6 m; Redfish Bay, Conn Brown Harbor, 4.6 m. A few other low values (2-4 mg/1) were
reported in the tidal reaches of the Nueces River. These values were probably present when there
was reduced flow in the river. This estuary is situated in an area of semi-arid climatic conditions.
Yearly rainfall averages 28.5 inches and is coupled with a subtropical temperature regime and
persistent southeasterly winds. The annual precipitation deficit is 16 inches (Brown et al., 1976).
Reduced freshwater inflows, coupled with climatic factors, is aggravated by a series of dams and
reservoirs along the course of the Nueces River.

The Texas Water Development Board has conducted long-term deployments of water quality
instrumentation in selected Texas estuaries to follow continuous variations in near-bottom water
salinity, temperature and dissolved oxygen. Preliminary results from these deployments have been
provided by G. Powell (Texas Water Development Board, personal communication) (see Section
G-17 for details). Deployments were made in mid Nueces Bay in May-June 1987. The data
indicated no dissolved oxygen levels below 2 mg/1 based on the first seven days of the instrument
deployments.

The extensive 1986 red tide (Gymnodiniwn breve) which affected most of the Texas coast entered
Aransas Bay through Aransas Pass and quickly spread into Corpus Christi Bay (Trebatowski,
1988). The bloom of Gymnodiniwn breve which extended along most of the Texas coast in 1986-
1987 was monitored at two sites near Port Aransas (Riley et al.* 1989). High cell densities of 10
to 50 X 106 cells/1 were commonly found during October 1986. Densities of red drum larvae were
substantially lower following the onset of the red tide bloom than prior to the bloom. Hatch rates
of laboratory-spawned red drum eggs were unaffected by various concentrations of the red tide
organisms; however, once hatched, larvae were negatively affected by all concentrations >40
cells/ml (Riley et al., 1989). See additional comments in Section G-26.
REFERENCES: G-24

Armstrong (1987)
Benefieldera/. (1983)
Brown etal (1976)
Flint (1983,1984)
Flint and Kalke (1985,1986)
Flint and Younk (1983)
Flint etal. (1986)
Hahl and Ratzlaff (1970,1972,1975)
Hegen(1983)
Holland etal (1973,1974,1975)
Kalke and Montagna (1989)
Kalke and Montagna (1989)
Lind (1983)
Maurer and Parker (1972)
Monaco etal. (1989)
Montagna and Kalke (1989a)
Montagna etal. (1989)
Pachecoetal (1989)
Rice etal. (1988)
Steidinger (1973)
TDWR(1981a)
Whitledge and Pulich (1991)
246
-------
r* w ID mo
» « CD m o
a*
o «

°i !
j ,
al •
CJ
"i i
si! '
j
CM CM v
H , CM CM 0* CM CM
O O O O O O
1 !;q !a'jjssm
VOW V
1 1 O H 1 O 1 1 -*
1 'dd 'd ' 'd
f- cn H CM
1 | O *H 1 rl 1 1 CM
1 'dd 'd ' 'd
CM V H O
1 | O O | O 1 1 «H
II * • 1 • 1 1 •
O O O O
j
?3
* .

J
Q .

jox
* .
i
s
j*
Sx
§3
$
*•
J F
s«
CM •

H
§ J
oS
.
si'
o
O ID
1 | CM CM.
1 ' oo
0 0
1 1 CM -f
1 'dd
0 0
I t CM CM

11 do
in in
1 1 0 0
1 'dd
, ,ss

''do
SKt
o
1 'dd
CO CO
1 1 H Q
i i o 5
* "
i !§§

i iii
o o
i i £"
o o
o
! 1 * °.
' ' d H
0 0
1 1 fO CM
1 'dd
O CM m«H
CM r- * in
_,U>CM^
o
) •-(
o
o
1 *-l
'd
o

0
to
1 0
'd
,s
1 •
0
.s
1 •
o
,s
1 0
d
1 O
1 O
d
to
:s
d
t "
o
o
i •*•
1 d
,s
' 0
r* CM
Sw
VOl
in
1 1 H
O
O
1 1 CM
1 'd
, ,3

1 ' d
r-
1 1 0
1 'd
, ,8,'
||*

O ,
tn CM
1 1 O 1
1 1 • CM
0 g
I i to y
1 ' ° p
d 3
(it >•
1 1 0 <
d ffl
1 1 O W
S
d S
1 t S V>
o C
o u
1 1 CO
d
o
1 1 m
O
»O <-i to
co o tn
toinin
cn co
1 1 i-i CM
1 'dd
0 O
i i o «r
1 'nd
O O
1 I «H tN
1 1 • •
00
in tn
i i to o
1 d d
So
rH
1 1 * •
O O
1 1 O O

, ,s§
1 100
d d
r-
1 1 H O
1 1 0 H
o o
1 1 O O
1 I O O
o o
! |3°.
11 do
o o
1 IOO
' tOrH
0 0
1 1 i-i CM
1 'dd
CM V CM H
'2<
,a ,
'd '
,S ,
l • l
o
to
i O I
'o '
to
1 0 t
1 • 1
0
to
1 0 1
'd '
.0 ,
1 O 1
o
1 O 1
1 O 1
d
to
•18 !
d
03
1 M 1
' d '
o •
! *. !
1 d '
,8 ,'
'd '
f~ O4 M
tn cn co in ID r- oo
CM CM CM CM CM CM CM
votncM^
wmw
!d
O
1 CM
'd
O
1 H
1 •
0
r-
1 0
•d
,s
i •
o
in
1 O
'o
!S
d
is
d
1 CM
1 0
o
1 VO
1 d
' 0
1 CD
' 0*
0
t in
d
H to
S3
voin
•HOcnHtDr-fftHm
KirOCMtOCMOtCMtOd
MCMCMCMCMCMWCM
tor-Hcov "CM*1

US CO rj O CT> t* V
t r- u> to in
ooooaomuio
glDO\DCMCMin*0(n
r~\ r-4 r-\ CM .-! CM CM

oooinootnvoo
h-mr*«H«-iC4in«n(
Cl rH rH CM (H CM C
^*rcDinHCMtnt
MH H CM H C
CN C* tO
CM r» r^ to r-
r- - - i-» -
247
-------
C C
too o c* o oo o o o

00 v I inmuSuJModco
*H i—t i-t i—{ i-H C>3 C4 r-<

oo ooooooo

oo ooopooo

/as 'd^aggis*
tl

sTs
ON o co o* w V r-i o

(Dri Ico'eoininTjicQM

cap ooooooo

com" loioooodi-^oori
oo lootnooooNf
N
o t- M oo o m
co i^ m m en n ID
oo ooooooo

as
oo ooooooo

CQ l^
oo ooooooo

2ri IqcocoNwoiio
•^C3 Mi-HOIWM rM
OOOOOOOOOO

OOOOOOOOOO
8S8S8S8888
88888888S8

dddddddddd
88S8888S88
.OOOOOOOOOO

8838588883

oo <
oggppooooo
^-fr^r^l-^l-^l-^r^r^^-lr^

dd d d
rHggpporrobo
OrHrHr-HrHiHOf-Hi-lr-l

O I
8SS888-S8
883^338888

dddddddddd

cococococococococofo
oooooooodo
SSSS888888

O O O O O O O O O O
H
dddddddddd

j p 55 IQ in (D in to <
248
-------
X
S5 -* — "«""«'""-"•
in
RGMJIC

Hin. Ha

< H
•er-womoommcoomiN \or^owooeoo*»Hf~r~ina>
rimMMiHr-ifH «H »H r> « r-i 1*1 ri ** M»-i
r

"a
CO

E
OOOOOOOOOOOOO
4 eo o
OOOOOOOOOOOOO
<-40OOf-4OOOOOOOO
OOOOOOOOOOOOO

OOOOOOOOOOOOO
e
OOOOOOOOOOOOO OOOOOOOOOOOOO
PH
_o
I
-C
T3
OOOtHr-IOOOOOOOO OOO»H'*f'tMr>l**lPO»**OO

OOOOOOOOOOOOO O OOOOOOOOOOOOO
OOOOOOOOOOOOO *H OOOOOOOOOOOOO
OOOOOOOOOOOOO H OOOOOOOOOOOOO
» OOOOOOOOOOOOO & OOOHHHMr4V1V0OOO

> • • •, • • • o t'.........^.*
V3

-------
Figure T17. Phytoplankton primary productivity, salinity, and ammonia concentrations in Corpus
Christi Bay-during July and October, 1981-1983 (from Flint, 1983).

J-
E^23
PRIMARY PRODUCTIVITY
(G C/MZ/DAY)
i i i i i

I
o
l:
1 1

ll
1 \
o

•

1
-32

™

o
-24
•£
-16 5
Hj
fcO
-8
-3

11
-2 g
C3
1 — 1j
-1 p J
-0
JUL81 OCT81 JUL82 OCT82 JUL83
G-25 Baffin Bay

Baffin Bay is an extension of the Upper Laguna Madre. Depth in the central part of the Bay ranges
from 1.8 to 3.6 m but much of the Bay and its arms (Laguna Salada, Cayo del Grullo and Alazan
Bay) range in depth from 0.9 to 1.8 m (Brown et al., 1977) The Bay is subject to hypersalinity as
a result of low rainfall, high evaporation rates and isolation from tidal passes to the Gulf of
Mexico.

Only one bit of additional data was available for an update on this area; however, extensive studies
are in progress by researchers from The .University of Texas, Marine Science Institute, funded by
the Texas Water Development Board.

Data for Baffin Bay are limited but there were a few values of low dissolved oxygen in bottom
waters. One record in 33 fell below 2 mg/1 (1.8 mg/1 in 2 m of water). Russell and Baskin (1989)
reported that runoff from heavy rains associated with the passage of Hurricane Allen in 1980
subsequently entered the bay over the more dense saline water of the bay (50 ppt) and formed a
stagnant layer extending 1 m above the bottom of the main stem of Baffin Bay. The dissolved
oxygen content of this layer declined to zero, until mixing destroyed the identity of the stagnant
water mass approximately two months after passage of the hurricane.

See comments in section G-26 concerning a brown tide in 1990-1991.

REFERENCES: G-25
Breuer (1957)
Maurer and Parker (1972)
Monaco et al. (1989)
Russell and Baskin (1989)
TDWR (1983)
250
-------
G-26 Laguna Madre

The Laguna Madre estuary consists of Upper and Lower Laguna Madre, Baffin Bay and part of
Arroyo Colorado for a total surface area of 214,545 ha (Armstrong, 1987). The estuary is shallow
(1.2 m), has extensive seagrass meadows and is traversed along its length by the Gulf Coast
Intracoastal Waterway. A landmass separates the Upper and Lower Lagunas and is dissected by
the waterway. The South Bay system south of the causeway connecting Port Isabel to the
southern tip of Padre Island exchanges waters with the Lower Laguna Madre. Rio Grande tidal
water does not interchange directly with the Lower Laguna Madre.

The nutrient concentrations of Laguna Madre are generally low, with low nutrient loading, high
water clarity, and hypersaline conditions preventing species succession of primary producers.
Simmons (1957) pointed out that dissolved nutrient concentrations in the Laguna Madre are usually
low, which he attributed to the lack of an adequate watershed for the area. Pulich (1980) compiled
nutrient data from the Laguna Madre, which are presented in Table T13. These data show that
concentrations of nitrate, ammonia and phosphate are usually higher at the mouth of Arroyo
Colorado in the Lower Laguna and at the north end at the Kennedy Causeway near Corpus Christi
Bay and points of inflow to the system than they are in the central parts of the Laguna. Pulich
(1980) further outlined the implications of nutrient enrichment to the enhancement of periphytic
algae on seagrass stems which would cause an overall decline in macrophyte populations.

Table T13. Nutrient concentrations at Texas Department of Water Resources Monitoring stations
in Laguna Madre during 1978 (from Pulich, 1980).
Site
NO,
PO,,
Kennedy Causeway
Marker 59
Mouth of Baffin Bay
Marker 225A
Port Mansfield
Arroyo Colorado Mouth
Port Isabel
0.09
0.05
0.03
0.02
0.02
0.30
0.02
NDa
NO
ND
ND
ND
0.10
ND
0.320
0.160
0.122
0.140
0.150
0.550
0.120
Not detectable; less than 0.5 mg/£
The comprehensive survey by Merkord (1978) as reported in Pulich (1980) provides evidence of
the changes in seagrass populations, particularly in the Lower Laguna Madre since the work of
Simmons (1957) and McMahan (1968). Seagrass abundance has increased in the Upper Laguna,
with Halodule and Halophila expanding their ranges since 1966. A dramatic shift in species
distribution has occurred in the Lower Laguna Madre as evidence by the spread of manateegrass
(Syringodium) northward from the Arroyo Colorado and a decline in Halodule to the south of Port
Mansfield along the eastern half of the Lower Laguna Madre. This range expansion may be the
result of a general increase in turbidity noted in the Lower Laguna Madre (G. Merkord, personal
communication; cited by Pulich, 1980), although it has not been quantified. It is also possible that
runoff from the Arroyo Colorado which included nutrients, pesticides, herbicides and silt
(Warshaw, 1974; cited in Pulich, 1980) has allowed Syringodium to grow relatively unchecked.
}f Halodule is inefficient at using blue light, which would predominate in turbid water, then growth
of Syringodium could be favored.
251
-------
A recent algal bloom attributed to an undescribed chrysophyte has persisted in the Upper Laguna
Madre, Baffin Bay, Corpus Christi Bay and Redfish Bay (part) since since June 1990 (D.
Stockwell et al., personal communication). The so-called "brown tide" was still present as recently
as April 1992 (T.E. Whitledge, personal communication), but the extent and population levels have
declined. A conference, sponsored by the Texas Parks and Wildlife Department and the U.S. EPA
Gulf of Mexico Program, was held in July 1991 at The University of Texas Marine Science
Institute in Port Aransas to synthesize knowledge about the bloom (Whitledge and Pulich, 1991).

A brown tide bloom began in the hypersaline waters of Baffin Bay and the Upper Laguna Madre in
June 1990 and has persisted into 1992. The extensive bloom is composed of a 5 um-diameter,
non-motile, autotrophic chrysophyte in average concentrations of 1.9 X 109 cells/1, with maximum
values of 4.9 X 109 cells/1. Chlorophyll a concentrations increased to 30-80 ug/l from typical
values of 1-3 ug/L The bloom has caused increased turbidity in the usually fairly clear waters of
the Laguna Madre, Baffin Bay and Corpus Christi Bay. Indirect impacts of the bloom may be
shading of the extensive submerged aquatic vegetation beds of the Laguna Madre and a decrease in
seagrass coverage. Another indirect impact of the bloom has been the decline in populations of the
bivalve, Mulinia lateralis, which is a major food organism for black drum and some overwintering
waterfowl.

Researchers note that the brown tide is coincident with an extremely hard freeze during the winter
of 1989-1990 and elevated salinities within the Laguna Madre system in 1990. These conditions,
however, are not unusual for the Laguna Madre. It was also noted, however, by Hildebrand and
King (1978) (cited in Armstrong, 1987) that salinity was the controlling factor of phytoplankton
dynamics in the Upper Laguna Madre, that blooms generally occurred following salinity changes
and that blooms were never found in salinities >40 ppt. Simmons (1957) also noted that
phytoplankton were nonexistent in the Upper Laguna Madre in the higher saline areas (>60 ppt)
but that "red water," or "bad water," was often present in the Upper Laguna Madre, commonly
associated with high salinity, but not necessarily so. Other potential factors which may have lead
to the formation of the bloom include major changes in land use in the watershed of the Laguna
Madre as more land is converted from pastureland into cropland and fertilizer use increases. The
Lower Laguna Madre is one of three drainage areas in the Gulf of Mexico (others are Galveston
Bay and Matagorda Bay) which received the highest applications of fertilizer to adjacent
agricultural lands (NOAA, 1990a).

Brown tides, documented in Long Island Sound from 1985-1987 (several authors cited in Cosper
et al., 1989), were responsible for the reduction in extent and biomass of eelgrass beds and caused
starvation and recruitment failure of commercially important bay scallop populations. Brown tides
were also responsible for the near-elimination of mussel populations in areas of Narragansett Bay
[Olsen, 1986; Seiburth et al., 1986; as cited in Shumway, 1990]. Shellfish resources in most of
Laguna Madre are limited to scallops, which are not commercially harvested. Apparently, in the
Laguna Madre, the extensive seagrass beds have not been impacted by the reduced light penetration
from the highly concentrated populations of the chrysophyte (R. Kalke, personal communication).
REFERENCES: G-26

Armstrong (1987)
Brown era/. (1977,1980)
Hahl and Ratzlaff (1972,1975)
Lind (1983)
Maurer and Parker (1972)
Monaco etal. (1989)
Pacheco etal. (1989)
Pulich (1980)
Shepard and Rusnak (1957)
Smith (1988)
TDWR (1983,1984)
Whitledge and Pulich (1991)
252
-------
G-26.1 Upper Laguna Madre

No additional data were available for an assessment of low dissolved oxygen concentrations. Most
of the low dissolved oxygen values recorded in the area were in deeper channels, particularly the
Gulf Intracoastal Waterway. No occurrences were recorded in the shallower margins of the
lagoon. A series of low values in August 1980 can be attributed to stratification following heavy
rains and freshwater runoff following Hurricane Allen (see Section G-25). Some of the low
values in the deeper channels may be related to a high BOD from decomposing seagrasses which
may be moved with water currents into these areas. Seagrasses form extensive meadows in the
Upper Laguna Madre and undergo a general senescence and die off in late summer/fall.

The extensive 1986 red tide (Gymnodinium breve) which affected most of the Texas coast had a
limited impact on the Laguna Madre. In spite of the extensive and heavy densities of G. breve in
Corpus Christi Bay, impact in Laguna Madre was limited to the northern end at passes connecting
to Corpus Christi Bay (Trebatowski, 1988).

See comments in section G-26 concerning a brown tide in 1990-1991.
REFERENCES: G-26.1

Benefield etal (1983)
Hegen(1983)
Rice etal. (1988)
Simmons (1957)
TDWR (1983)
G-26.2 Lower Laguna Madre (includes Arroyo Colorado, South Bay,
Brownsville Ship Channel and Brazos Santiago Pass)

No additional data are available for an assessment of the dissolved oxygen concentrations of this
area. In the Lower Laguna Madre, proper, no low dissolved oxygen values occurred in the open
shallow waters. Low values were in deeper channels, particularly in the Gulf Coast Intracoastal
Waterway, where many of the samples were taken. Low values in a series of stations in August
1980 may be related to stratification following heavy rains and freshwater runoff following
Hurricane Allen (see Section G-25). Some of the lower values in the deeper channels may be
related to the decay of senescent seagrass populations. There were no oxygen-depleted waters
recorded in the few samples from South Bay. Arroyo Colorado is often hypoxic or anoxic. Flow
is low in the Arroyo and oxygen depletion is most severe in the summer when there are strong
vertical gradients associated with a high salinity salt wedge (Bryan, 1971). Hypoxia and anoxia
occur year-round in this natural drainage channel which has been dredged to 3 to 3.6 m. Oxygen-
depleted waters (often anoxic) occur in the Brownsville Ship Channel (12 m) in April-October.
There is little tidal mixing in the upper reaches of the channel. Those parts of the channel closest to
the Gulf of Mexico and Brazos Santiago Pass have fewer or no low dissolved oxygen values.
None of the few samples taken in Brazos Santiago Pass were below 4 mg/1

A research program was conducted in the Rio Grande River, Arroyo Colorado and lower Laguna
Madre to provide information to regulatory agencies concerning the potential impacts of
constructing another dam across the Rio Grande. This work, funded by the Public Utilities Board
of Brownsville, included surveys of nekton and benthos (D. Harper, personal communication).

The extensive 1986 red tide (Gymnodinium breve) which affected most of the Texas coast,
including waters in and near Mansfield Channel, did not impact the Lower Laguna Madre
(Trebatowski, 1988).

See comments in section G-26 concerning a brown tide in 1990-1991 which extended into the
Lower Laguna Madre. At the same time that a brown tide was affecting the Upper Laguna Madre
253
-------
in 1990, a red tide was occurring in the Lower Laguna Madre (J. Bowman, personal
communication). ~
REFERENCES: G-26.2

Benefield etal (1983)
Breuer (1962,1972)
Brown etal (1980)
Bryan (1971)

G-26.3 Rio Grande Tidal
Hegen (1983)
Rice etal. (1988)
TDWR (1983)
No additional data are available for the assessment of dissolved oxygen concentrations. Limited
data (Breuer, 1969-1970) indicated oxygen-depleted waters in the warmer months. Stations at
mile 0,4,8 and 12 are tidally influenced. There was no discussion of causes other than noting that
flow in the lower Rio Grande has been reduced considerably from upstream damming and removal
of river water for agriculture, industry and municipalities.

REFERENCES: G-26.3

Breuer (1969-70) Hackney (1978)

G-27 Texas inner continental shelf

The water quality of the Texas inner shelf can be typified by several data bases along an Aransas
Pass Inlet transect off Port Aransas (Flint and Rabalais, 1981a; Dagg and Checkley, unpublished
data). The dominant source of fresh water is discharge from Texas rivers. The effect of the
Mississippi River is evident along the upper coast but is minimized in the vicinity of Port Aransas,
although salinities at mid shelf in the spring are lower and thus reflect the influence of the
Mississippi River. In general, nutrients and chlorophyll biomass are much lower in mid shelf
waters of Texas than compared to the continental shelf of Louisiana (Figure T18). There are
distinct water masses along the lower Texas shelf which are typified by fresh water from rivers
(Texas), a mixing zone of Texas freshwater sources as well as the Mississippi River influence, and
an offshore zone where Mississippi River discharge dominates the shelf (however, variations in
salinity are minimal) (Figure T19).

Conditions of strong salinity stratification and high nutrient input are therefore limited to the upper
Texas coast. This is also the area to which conditions of oxygen-deficient bottom waters are
confined. Through three years of continental shelf baseline studies on the south Texas coast
between Port O'Connor and the Rio Grande (57 samples), the lowest dissolved oxygen
concentration found was 3.2 mg/1 in 18 m water depth in.June (Sackett and Brooks, 1976; Sackett
et aL (1977, 1979). On the inner shelf between Galveston Bay and Matagorda Bay, seasonal
sampling (four times per year) revealed scattered low oxygen concentrations in July 1973
(Seadock, Inc., 1974), with one value of 0.2 mg/1 in 15.5 m water depth and another of 2.0 mg/1
in 21 m water depth. Shallower stations and deeper stations did not experience low oxygen.

Oxygen conditions off Galveston and Freeport, Texas, however, are considerably different. While
the Louisiana continental shelf experiences hypoxia almost annually over a broad area (Rabalais et
aL, 1991), the upper Texas coast is affected infrequently. Monitoring of a brine disposal site off
254
-------
27° -
20

100

120

140
NITRATE (ygatm N03-N/I)

43 2
CHLOROPHYLL (jjg/lj
TEXAS
20

100

120

140
LOUISIANA

-------
96'00' . 95'30'
10 ' 20 30 40 50
DISTANCE OFFSHORE
10 20 30 40 50
60 70 80
(km)
60 70 80

"0.64
~0.76

_^_J-_0.64_

_^ "0 .6 7

+0.50
-*- + 0.64
— ** • • • • w-
+

•»- +0.68
" *T
;•". . . . *.°-6.8 «J
^
"0.85
Mississippi
Galveston

Brazos Complex

Aransas Complex

Rio Grande
Figure T19. Map of study area of south Texas outer continental shelf and correlation analysis
between chlorophyll a, salinity and freshwater sources (from Flint and Rabalais,
1981a).

Freeport revealed a hypoxic event between May and July 1979 in 15- and 20-m water depths
(Figure T20) (Harper et al., 1981, 1991). Macroinfaunal sampling at the sites showed that
abundances of benthic organisms declined precipitously during the event. Divers inspecting the
study areas during the hypoxia observed mats of sulfur-oxidizing bacteria covering large areas of
the bottom and numerous bodies of dead benthic invertebrates. This hypoxic event was also
responsible for sharply reduced abundance and elimination of both fishes and shrimps in trawl
catches (Pavela et al., 1983). Hypoxia was also recorded at this site in June 1983, and possibly
occurred in June 1982 and 1984 (Harper et al., 1991). Harper and Guillen (1989) suggest that the
high runoff of the Atchafalaya River, reduced salinities, transported nutrients and associated
phytoplankton blooms together with the appropriate meteorological conditions cause hypoxia along
the upper Texas coast These events, however, are infrequent, short-lived and limited in extent

Two blooms of the toxic dinoflagellate, Gonyaulax monilata, occurred in the offshore coastal
waters of Texas at Galveston in August 1971 and August 1972 (Wardle et al., 1975). Similar
numbers of dead and moribund marine organisms were collected from the beachfront on days
following peak cell counts of 1.2 to 1.8 X 106 cells/1. The organisms consisted of coelenterates,
annelids, molluscs, crustaceans, echinoderms and fishes, all of which were either sessile,
sedentary or weakly motile, suggesting that the more mobile species were able to avoid the area of
the bloom before accumulating lethal amounts of the toxin. Despite extensive monitoring in late
July and August of 1973, no G. monilata cells were noted in the offshore area of Galveston Island.
Wardle et al. (1975) suggested that the absence of red tides during 1973 was related to relatively
low salinities and temperatures in the Galveston Bay drainage area during the month of August.
256
-------
>t
Sf
•ti
O a
in a
m f,
-H i
1
CD .
Julian Day

§
•g &
525-
Julian Day
Figure T20. Dissolved oxygen levels in bottom waters at the Bryan Mound 10-mile (upper panel)
and 5-mile (lower panel) site in 1979 (from Rabalais et al., 1985).
257
-------
A bloom of the dinoflagellate, Exuviella baltica, which was extensive in the Galveston Bay system
during the winters of 1972-1973 and 1976-1977 also occurred along the Galveston beachfront in
offshore coastal waters (Zotter, 1979).

Another dinoflagellate, Gymnodinium splendens, was implicated in extensive mortalities of
demersal fish and bentiiic invertebrates during the summer of 1984 off Galveston in nearshore
coastal waters (Harper and Guillen, 1989). The authors .suggested that the high runoff of the
Atchafalaya River, reduced salinities, transported nutrients and associated blooms were
concentrated along the Louisiana shore by winds and then driven alongshore into Texas by the
strong alongshore wind component in May. The decomposition of the phytoplankton that had
settled to the bottom, reduction in oxygen concentrations, and the production of hydrogen sulfide
were the causes of the mortalities of organisms.

Blooms of the dinoflagellate, Gymnodinium breve, were implicated in fish kills in the nearshore
coastal waters of the lower Texas coast off Port Isabel and the Rio Grande in .1955; these fish kills
extended along the coast of the Mexican State of Tamaulipas for at least 120 miles below the Rio
Grande. Other infrequent occurrences of this dinoflagellate have been reported in Texas waters
(Lund, 1935; Wilson and Ray, 1956; cited in Trebatowski, 1988).

The report by Trebatowski (1988) documents an extensive, long-lived and highly toxic bloom of
G. breve which occurred in Texas waters in 1986. Similar to the outbreaks of red tide on the
southwestern Florida coast (see Section F-15.1), the red tide bloom originated in offshore waters
then moved inshore. The bloom was first reported on 27 August 1986 in Gulf of Mexico waters
near Galveston Island. In subsequent weeks the bloom progressed southward along the coastline
and into Matagprda Bay. By mid-September, virtually all of Matagprda Bay and parts of Lavaca
Bay and Espiritu Santo Bay contained red tide. While the red tide continued to impact the
Matagorda Bay area, it also progressed slowly southward until October. During October, the red
tide came ashore as far south as Port Isabel, and into Mexico waters of the State of Tamaulipas,
and also became established in Aransas Bay, Redfish Bay, Corpus Christi Bay and parts of
Laguna Madre (northern end) and Copano Bay. Although the bloom had virtually abated by late
October; localized, and at times dense, concentrations were encountered through January 1987
(Trebatowski, 1988). Nutrient analyses conducted on red tide water did not reveal a strong
nitrogen and phosphorus correlation with cell count and supports the view that G. breve is not
nutrient limited. The Texas Parks and Wildlife Department estimated 126 species of fish reported
killed by red tide and 22.2 million vertebrates and invertebrates killed during the red tide. These
estimates were considered conservative by Trebatowski (1988). (See also sections G-21, G-22, G-
23, G-24, G-25, G-26.1).

The diatom, Nitzchia pungensf. multiseries, has been found recently in the Galveston, Texas area
of the Gulf of Mexico (Fryxell, 1990). This diatom is responsible for a 1987 outbreak of
neurotoxic domoic acid in an area of maricultured blue mussels in Prince Edward Island, Canada,
which resulted in several human deaths and disabilities.

Other algal blooms have been documented for the lower Texas coast: Chaetoceros sp., a diatom
(Gunter and Lyles, 1979), and Trichodesmiwn sp., a blue-green alga (Van Baalen and Brown,
1969; work of C. Van Baalen, University of Texas Marine Science Institute, deceased).
REFERENCES: G-27

Atwood (1981)
Benefield etal (1983)
Boesch and Rabalais (1991a)
Casserly etal (1982)
Churgin and Halminsta (1974)
Parker and Bailey (1979)
Parker etal. (1979)
Pavelaetal. (1983)
Pokryfki (1985)
Pokryfki and Randall (1987)
258
-------
Cons. Perm. Int. Exp. Mer (1936)
Dennis etal. (1984)
Dinnel (1984)
Dinnel and Wiseman (1986)
El-Sayed etal. (1972)
Flint and Kamykowski (1984)
Flint and Rabalais (1981a,b)
Gazey etal. (1982)
Gunter (1979)
Gunter and Lyles (1979)
Harm etal. (1984)
Hann and Randall (1980-1983)
Harper and Guillen (1989)
Harper and McKinney (1982a,b)
Harper era/. (1981,1991)
Leming and Stuntz (1984)
Mauer and Parker (1972)
Rabalais et al. (1991a)
Ray (1981)
Renaud (1985,1986b)
Richards and Redfield (1954)
Sackett and Brooks (1976)
Sackett et al. (1977,1979)
Seadock (1974)
Shaw etal. (1988)
Stetson (1953)
Stuntz et al. (N.D.)
Temple etal. (1977)
Thompson and Bane (1986a,b)
Thompson et al. (1988)
Trask (1953)
Wardleetal. (1975)
Wilson and Ray (1956)
Zein-Eldin and Renaud (1986)
259
-------
Appendix A. Terms and Conversions
Table Al. Definitions of terms.

Alkalinity - acid-neutralizing capacity of water measured as calcium carbonate equivalent

Biochemical Oxygen Demand (BOD) - measure of the quantity of dissolved oxygen, in mg/1,
necessary for the decomposition of organic matter by micro-organisms, such as bacteria.

Chemical Oxygen Demand (COD) - measure of chemically oxidizable material in water and
furnishes an approximation of the amount of organic and reducing material present

Color Unit - produced by 1 mg/l of platinum in the form of chloroplatinate ion. Color is expressed
in units of the platinum-cobalt scale. In surface waters and effluents, the most important
materials that contribute color are humic acids and tannic acids. These substances are typically
from the microbiological breakdown of plant and/or animal material.

Conductance (also Specific Conductance) - measure of the ability of a water to conduct an electrical
current and depends on the presence of ions, their total concentration, mobility, valence, and
relative concentration, and on the temperature of the measurement. Expressed in
microhmos/cm at 25°C; used to estimate the dissolved solids concentration of a water sample.

Cubic feet per second (cfs) - rate of discharge; equivalent to 7.48 gal/sec or 646.3 gal/d, or
0.02832 m3/s.

Dissolved Inorganic Nitrogen (DIN) - usually refers to nitrate + nitrite + ammonia.

Dissolved Oxygen (DO) - amount of oxygen dissolved in water; concentrations expressed in mg/1.

Dissolved Oxygen Percent Saturation - ratio of the measured dissolved oxygen to the solubility in
water at the temperature, pressure and salinity at the time of the measurement.

EPA - U.S. Environmental Protection Agency

Fecal coliform bacteria - gram-negative, nonspore-forming, rod shaped bacteria found in the
intestinal tract of warm-blooded animals. Concentrations are reported as the Most Probable
Number (MPN) per 100 ml of sample. Total coliform bacteria are characterized as aerobic and
facultative anaerobic, gram-negative, nonspore-forming, rod-shaped bacteria which ferment
lactose with gas formation within 48 h at 35°C; also reported as MPN.

GCRL, FAM - Gulf Coast Research Laboratory, Fisheries Assessment Monitoring program,
Ocean Springs, Mississippi.

Hardness - of water is^a physical-chemical characteristic that is commonly recognized by the
increased quantity of soap required to produce lather. It is due primarily to the presence of
calcium and magnesium. Concentrations reported as mg/1 CaCO3-

MMS - U.S. Minerals Management Service.

MRGO - Mississippi River Gulf Outlet, dredged channel through Breton Sound that links the inner
harber of New Orleans East to the Gulf of Mexico.
260
-------
NOAA - National Oceanic and Atmospheric Administration.

pH - negative base-10 logarithm of the hydrogen ion activity in M/l. pH is a measure of whether a
solution is acidic or basic and can range from near 0 (acidic) up to 14 (basic) with normal
measurements ranging from 6 to 9 standard units (SU).

Salinity - concentration of dissolved solids in a kg of water, units are ppt (parts per thousand).

SAV - submerged aquatic vegetation

Secchi Disk - disk, 20-cm in diameter, painted black and white in alternate quadrants, used to
measure, semi-quantitatively, the passage of light through water. Secchi Disk Depth (SDD)
values usually given in m.

STORET - computerized data base utility maintained by EPA for the STOrage and RETrieval of
parametric data pertaining to the quality of the waterways within and contiguous to the United
States. The data are collected by a variety of federal, state, interstate, and local government
agencies. The STORET system contains:

- geographical, political, and descriptive information concerning sites where data have been
collected.

- measurements of the physical characteristics and chemical composition of water, fish tissue,
or sediment sampled at these sites, i.e. the Water Quality System.

- counts and descriptions of living organisms found at these sites, i.e. the Biological Field
Surveys.

- stream flow data, obtained from the U.S. Geological Survey, i.e. the "daily values" system.

TDWR - Texas Department of Water Resources (was Texas Water Development Board).

TKN - Total Kjeldahl Nitrogen, forms of nitrogen quantified in a Kjeldahl test, usually the sum of
total ammonia-N and organic N, excludes nitrate-N and nitrite-N,

Total Dissolved Solids (TDS) - amount of solid material dissolved in water, commonly expressed
as mg/1.

Total N - usually refers to TKN + nitrate + nitrite

Total Organic Carbon (TOC) - indication of the relative amount of organic material dissolved and
suspended in water, expressed in mg/1.

Total Suspended Solids (TSS) - amount of solid material suspended in water, expressed in mg/1.

Turbidity - optical property of a suspension with reference to the extend to which the penetration of
light is inhibited by the presence of insoluble material and is a function of both the
concentration and particle size of the suspended material. Turbidity is reported in
nephelometric turbidity units (NTU).

USFWS - U.S. Fish and Wildlife Service

USGS - U.S. Geological Survey.
261
-------
ts
•a
.a
g
ej"
W
f
9
§
S
0
5

J!
o 2
II 1,
Us
e s
T—t r-*

uivalents
S"
1
E
-££
en
*
S
ia
as
oo o
r^ o
II II

TO O
1 8
o c3
TO ts«
OO N— '

1
II
03
*
VO
oo
en
0
II
!
r- «

en
|
g
0
7
If

S
0
ra
S
g 8
o »
01 T-.
T— i r^*
T? (N

_o
1
.S
•o
1

•i
8
1
C
i
1
13
<4-l
o
*•»
•a
o «
£ *
3. o
» S
S i
=«-«2
0
1
U3
II
S s
oo ob
'i >s
|ig/l div. by mol. '
mole=molecular A

12
JS
oo
'S
&
£
s
A
O
u
e
i
QJ
°1
ij1
g
J-
"33
i
"3
4_»
J3
00
'S
U
a*
s
QJ
>
«
u
~
JL
§
0
es

S
oo
molecular wei

nitrate=NO*3

nitrate NO*3
t~
00
oo
ON
1-H
VO

7
1
2

CN
*
i
a
'2
t-~
Tt
ON
ON
iri

T-l
C
>1
><
O

%
nitrogen
NH*4 ammon
r- t—
VO <^N
o en
T-l T-l

•
,_,
*
en.
"+"
i
Tt
en
1

.| 3?
en ex •!«
* g S
r- •* vo
oo I-H en
en r~ oo
O ON O
06 Tt eN
i-< ON ON

fl" ^ 0
«^J.
7—1

2
• •s
w
f
u
, 1

C '3 "O
g "3 '>
S S =5
en
^^

^_^
en
•K
O
2
1
2
•w
15
s.
J^
^^
"S<
•s
s
S
p ON
Tt T-l
T-l VO

** .2?
£« ^
'§ Js
is |
•- ?
1 "3
CQ G

fli >
s --3

•— ^
^
S
•s
1
u
00
Q
en
*
g
4«*
"o
>,
45
>,
1
9
e
S
t-H

en
*
i
4_)
1
>»
X>
S
w
cU
S
•8
>
s
T^
O
Tt
T-l

2
CM
O
Js
nic weig
i
>>
£>
>>
I1
9'
S'

Tt
#
Q
K
3
>
§,
4-J
s=
«
oo
2
?
0
C>0
4-1
&
3
S
^
*j
9
S
s
oo
CN

^
*
4^
&
3
c/5
S
«j
ea
"*^S
>»
Xi
u
>
o
•s
*J
9
S
S S

1
'S
I3

<5
s
3
I3
s are a cone.
-------
Appendix B. Data Bases
FLORIDA

Florida's literature base
1988 reports of ALL Florida
estuaries. Trend Reports only have
what STORET has in them
and are an indication of the lack
of long term available data in many
of the bays.

Tampa Bay
1974-1990
ASCI files
1974-86 can be used in SAS
1986-1990 need to be reformatted for
use with SAS
Perdido Bay
dBase files, vertical profiles
of temperature, salinity, DO,
nutrients; worked with ADEM for
this project
1988
Hydrographic data, seston,
chla. Unpublished data.
Perdido hydrological data
paper copy
ALABAMA

Monitoring data collection,
submission to data management group
at Gulf Shores, AL
Mark Freidmann
Florida DepL of Environmental Regulation
2600 Blair Stone Rd
Twin Towers Office Bldg.
Tallahassee, FL 32399-2400
904-487-0505
Richard Boler
Melvin T. Geloneck
Hillsborough County
Environmental Protection Commission
1900 9th Ave.
Tampa, FL 33605
813-272-5960

Steve Schropp
State of Florida
Department of Environmental Regulation
2600 Blair Stone Road
Twin Towers Office Bid
Tallahassee, FL 32399-2400
904-488-6221

David A. Flemer
EPA
Environmental Research Laboratory
Sabine Island
Gulf Breeze, FL 32561-5299

Robert J. Lord
EPA Region IV
Water Quality Management Branch
345 Courtland St.» NE
Atlanta, GA 30365
404-347-2126
Steve Heath
Alabama Dept. Conservation and Natural
Resources
Dauphin Island, AL 36528
205-861-2882
263
-------
Temperature, Salinity, DO
1983 - 1989
bottom measurments
ASCI files, clearly marked
Water column monitoring
In Symphony, need to convert Lotus to
move into ASCI or dBase
Paper copy of various parts
Mobile Bay
1989 cruises, nutrient and
hydrological data;
paper copy
MISSISSIPPI

Estuarine Inventory
Stations 1973 - 1986
dBase files;
maps of stations
Dr. Henry G. "Skip" Lazauski
Alabama Dept. Conservation and Natural
Resources
Alabama Marine Resources Division
P.O. Drawer 458
Gulf Shores, AL 36542

Gary Halcomb. Brad Gane. John Carlton
Alabama Dept Environmental Management
(ADEM)
2204 Perimeter Road
Mobile, AL 36615
205-479-2336

Dr. John Pennock
Dauphin Island Sea Lab
Marine Environmental Sciences Consortium
Dauphin Island, AL 36528
205-861-2141
James "Tut" Warren. Dick Waller.
Harriet Perry
Gulf Coast Research Laboratory
Ocean Springs, MS 39564
601-875-2244
Ambient water quality data
submitted to STORET
305(b) reports
Pascagoula Bay
Dredging report;
Information on streamflow
project in the Gulf
LOUISIANA

Louisiana Dept. of Environmental
Quality data, along with other agencies,
entry to the STORET system
Mr. Robert Sevfarth
Mississippi Bureau of Pollution Control
P. O. Box 10385
Jackson, MS 39209

Dr. Susan Ivyster-Rees
205-690-2724
Larry Land
USGS
8011 Cameron Rd.
Austin, TX 78753
512-832-5791
Stephanie Braden
Louisiana DepL of Environmental Quality
Office of Water Resources
Water Pollution Control Division
P. O. Box 82215
Baton Rouge, LA 70884-2215
504-295-0547
264
-------
Lake Pontchartrain
the LPBF is relativelynew
and has no data per se but
is setting up an Information Resources
Project
TEXAS

hydrological/meteorological
data from resource monitoring
programs, 1976 -1990;
ancillary data for Coastal Fisheries
Surveys
Water quality monitoring and freshwater
inflow assessment studies
only monitors every six months
availability of Texas data provided
to STORET for Texas; contains Coastal
Data System of Texas Water Development
Board; USGS data
Red tide data base
INNER CONTINENTAL SHELF

SEAMAP
From cruises 1982-1988
inside 200 meters;
ASCI files
Michael Conroy
Steve Gorin
Lake Pontchartrain Basin Foundation
Lakeway I, 3900 N. Causeway Blvd., Suite 621
P. O. Box 6965
New Orleans, LA 70009-6965
504-836-2215
Charles D. Travis. Executive Director
Maury Osborn
Texas Parks and Wildlife Department
4200 Smith School Road
Austin, TX 78744
512-389-4647

Gary Powell
Texas Water Development Board
Austin, TX 78711-3231
512-463-7979

Charlotte Schwartz
Texas Natural Resources Information System
P. O. Box 13231
Austin, TX 78711-3231
512-463-8337

Jim Bowman
(previously Dave Jensen)
Texas Water Commission
Corpus Christi, TX
RickMinkler
Ken Savastano
NOAA/NMFS
Southeast Fisheries Center
Mississippi Laboratories
Pascagoula Facility
P. O. Drawer 1207
Pascagoula, MS 39568-1207
601-762-4591
265
-------
Appendix C. Information Resources

NATIONAL and/or GULF OF MEXICO REGIONAL

Dr. Robert Dickey
U.S. Food and Drug Administration
P. O. Box 158
Dauphin Island, AL 36528
Public health issues in the Gulf of Mexico, toxic or noxious algal blooms

Dr. Bernard L. Griswold, Co-Chair
NOAA COP/RID
c/o Marine Advisory Service
National Sea Grant College Program
Office of Oceanic and Atmospheric Research, NOAA
Silver Spring Metro Center Bldg. 1, Room 5216
1335 East-West Highway
Silver Spring, MD 20910
301-427-2431, -2799 (Fax)

Kenneth R. Hinga
University of Rhode Island
Graduate School of Oceanography
Narragansett, RI02882
401-792-6851
Principal Investigator, NOAA's
National Estuarine Eutrophication Project

Mr. Larry Land
U.S. Geological Survey
8011 Cameron Road
Austin, TX 78753
STORETdata

Dr. Donald Stanley
Institute for Coastal and Marine Resources
East Carolina University
Greenville, NC 27858
analysis of long-term data sets, Pamlico River, Houston Ship Channel, Galveston Bay

Strategic Assessment Branch
Ocean Assessments Division
Office of Oceanography and Marine Assessment
National Ocean Service, NOAA
11400 Rockville Pike
Rockville, MD 20852
301-443-0453
Daniel T. Basta
Dan Farrow
Charles John Klein *
Ms. Jamison A. Lowe, NOAA's Fish Kill Inventory
Danielle T. Lucid, National Estuarine Eutrophication Project
266
-------
EMAP State Contacts

Alabama
Florida
Louisiana
Mississippi
Texas
FLORIDA
Mr. John Carlton
Alabama Dept, of Environmental Management
Field Operations Div. - Mobile Branch
2204 Perimeter Road
Mobile, AL 33615
205-479-2336

Mr. Tom Swihart
Florida Dept of Environmental Regulation
Standards and Monitorint Section
Twin Towers Office Bldg.
2600 Blair Stone Road
Tallahassee, FL 32399-2400
904-487-0505

Ms. Emelise Cormier
Louisiana Dept of Environmental Quality
Office of Water Resources
P. O. Box 82215
Baton Rouge, LA 70884-2215
504-765-0634

Mr. Jeff Thomas
Mississippi Office of Pollution Control
Surface Water Division
Water Quality Monitoring Branch
P. O. Box 10385
Jackson, MS 39287-0385
601-961-5157

Mr. Bruce Smith
Texas General Land Office
State/Federal Project Coordinator
Stephen F. Austin Bldg., Room 730
1700 North Congress
Austin, TX 78701-1495
512-463-5055
Apalachicola River National Estuarine Research Reserve
Woodard Miley n, Mgr.
261 7th Street
Apalachicola, FL 32320
904-653-8063

Center for Marine Science
University of South Florida
140 7th Ave. S
St. Petersburg, FL 33701
813-893-9512
Dr. Gabriel A. Vargo, 813-893-9130, nutrient studies of Little Manatee, Tampa Bay
267
-------
Sid Flannery
Southwest Florida Waier Management District
2379 Broad Street .
Brooksville, FL 34609-6899
904-796-7211

Dr. Robert J. "Skip" Livingston
Center for Aquatic Research and Resource Management
Department of Biological Sciences
Florida State University
Tallahassee, FL 32306-2043
904-644-1466
long-term data sets, Apalachicola Bay, Perdido Bay, Choctawhatchee Bay

Rookery Bay National Estuarine Research Reserve
Gary Lytton, Mgr.
10 Shell Island Road
Naples, FL 33942
813-775-8845 '

Karen Steidinger
Florida Marine Research Institute
100 Eighth Avenue, S.E.
St. Petersburg, FL 33701

U.S. Environmental Protection Agency
Environmental Research Laboratory
Gulf Breeze, FL 32561-5299
Dr. David A. Flemer, Perdido Bay studies
Dr. Bill Kruczynski
Dr. Kevin Summers, Gulf of Mexico EMAP Coordinator

ALABAMA

Marine Environmental Sciences Consortium
Dauphin Island Sea Lab
Dauphin Island, AL 36528
205-861-2141 . . A1 •
Mr. Mike Dardeau, estuarine and continental shelf ecology; involved in many studies in Alabama
Dr. Tom Hopkins, benthic studies
Dr. John Pennock, nutrients, nutrient cycling, Mobile Bay studies
Dr. Will Schroeder, physical oceanography; hypoxia studies, Mobile Bay, Weeks Bay and
continental shelf ,

Weeks Bay National Estuarine Research Reserve
10936-B U.S. Hwy. 98
Fairhope.AL 36532
205-928-9792
268
-------
MISSISSIPPI

Gulf Coast Research Laboratory
Ocean Springs, MS 39654
601-875-2244
C. Eleuterius
H. Perry
K. Stuck
RC. Sutler
R. Waller
T. Warren

LOUISIANA

Dept. of Biology
University of Southwestern Louisiana
Lafayette, LA 70504
318-231-6748
Dr. Robert Twilley, nutrient cycling

Dr. Gary Gaston
Dept. of Biology
University of Mississippi
University, MS 38677
601-232-7162
(formerly McNeese State University, Lake Charles, Louisiana, hypoxia inner continental shelf of
Louisiana)

DepL of Oceanography and Coastal Sciences
c/o Wetland Resources Bldg.
Louisiana State University
Baton Rouge, LA 70803
504-388-6307
Dr. John Day, nutrients, estuarine ecology
R. Eugene Turner, nutrients, phytoplankton biology, hypoxia
William J. Wiseman, Jr., physical oceanography, hypoxia

Louisiana Dept of Environmental Quality
Office of Water Resources
Water Pollution Control Division
Planning and Assessment Section
P. O. Box 82135
Baton Rouge, LA 70884-2135
Ms. Jan Boydstun, 504-295-0559
Mr. Dugan Sabins, 504-295-0510

Louisiana Universities Marine Consortium
Louisiana Universities Marine Center
8124Hwy. 56
Chauvin, LA 70344
504-851-2800
Dr. Nancy N. Rabalais, hypoxia, benthic ecology
Quay Dortch, phytoplankton biology and systematics
269
-------
Lake Pontchartrain Basin Foundation
P.O. Box 6965
1 Lakewood Center, Suite 821
Pontchartrain Causeway
MetaMe, LA 70009-6965
504-836-2215

Mr. Kerry St. P6
Louisiana Dept. of Environmental Quality
Office of Water Resources
302 Barataria Street
Lockport,LA 70374

Dr. Steve Mathies, Director
Barataria-Terrebonne National Estuary Program
Program Office
Nicnolls State University
P.O. Box 2663
Thibodaux,LA70310
504-447-0868,-0870 (Fax), 1-800-259-0869
Administrative Office
c/o Louisiana Dept of Environmental Quality
11720 Airline Highway
Baton Rouge, LA 70817
504-295-8936

TEXAS

Mr. Jim Bowman
(previously Dave Jensen)
Texas Water Commission
Corpus Christi, TX .
noxious and toxic algal bloom inventory

Dr. Greta A. Fryxell
Department of Oceanography
Texas A&M University
College Station, TX 77843-3146
phytoplankton taxonomy, noxious and toxic algal blooms

Galveston Bay National Estuary Program Office
Dr. Frank Shipley, Director
BayPlazal
711 Bay Area Blvd., Suite 210
Webster, TX 77598
713-332-9937, -8590 (Fax)
Proceedings from 1991 Galveston Bay Characterization Workshop (Shipley and Kiesling, 1991)
270
-------
Dr. Larry McKinney
Resource Protection Division
Texas Parks and Wildlife Department
4200 Smith School Road
Austin, TX 78744
512-389-4864
Convened 1991 Brown Tide Symposium in Port Aransas, Texas

Mr. Gary Powell
Texas Water Development Board
Austin, TX
Oxygen criteria for Texas estuaries, salinity, freshwater inflow needs

Texas A&M University at Galveston
Galveston,TX 77553-1675 ,
Dr. Donald E. Harper, Jr., hypoxia on the inner Texas continental shelf; estuarine-level studies in
several Texas bays
Dr. Peter H. Santschi and colleagues, nutrient cycling studies in Trinity River estuary and
Galveston Bay, trace metal studies
Dr. Frederick C. Schlemmer n, hydrographic data analysis for Galveston Bay

Texas Water Commission
P. O. Box 13087
Austin, TX 78711
noxious or toxic algal bloom inventory

The University of Texas at Austin
Marine Science Institute
Port Aransas Marine Laboratory
Port Aransas, TX 78373
512-749-6711
Several estuarine characterization studies completed or in progress with some of the following
investigators:
Dr. Terry Whitiedge
Dr. Paul Montagna
Dr. Dean Stockwell
Dr. EdBuskey
Dr. Ron Beriner
Mr. RickKalke

Mr. Robin Wilson
Lower Colorado River Authority
P. O. Box 220
Austin, TX 78767
271
-------
Appendix D. Bibliographies

Compiled by

Nancy N. Rabalais
R. V. Bates
A. Neville
J. Riley
Organization
Bibliography I includes those references that were used for the identification of eutrophication
indicators; it is named GOMBIB.DAT in the ProCite software. Annotations to this bibliography
are a short description of the manuscript and codes that identify the estuary or coastal area of
concern. Details of the manuscript, especially where relevant to the identification of eutrophication
indicators, are included in the text of the report. A list of the estuarine codes and maps that identify
the coastal areas of the five Gulf of Mexico states are provided in Table 8 and Figures 19-23.

Bibliography n lists useful references; it is named PROBIB.DAT in the ProCite software.

Use of Bibliographies with ProCite Software

Diskette copies of both bibliographies in ProCite software have been submitted to the EPA Gulf of
Mexico Program Office for inclusion on the Gulf of Mexico Program Data Base. Details of using
ProCite are given in the manual for the software (ProCite, Version 1.4. 1988. Personal
Bibliographic Software, Inc., Ann Arbor, Michigan); however, a few useful hints can make use of
the bibliographies easier.

Searching
i
- Simple searches using single term or phrase in full-text or selected fields.
- Complex searches using Boolean logic in full-text or selected fields.
- Search Only software offered by ProCite that enables the user to search databases and print
bibliographies.

Creating Bibliographies

- Choice of several punctuation styles, including user-defined. (The NNR.PCT specific style for
production of manuscript word document was used for the bibliographies and is part of database
submitted.)
- Create subject bibliographies using index terms.

Other Features

- Preview citations before sending to diskette or printer.
- Sort records in variety of ways.
- Import and export capabilities.
- Merge with other ProCite databases.
272
-------
BIBLIOGRAPHY I.

FOR
IDENTIFICATION OF EUTROPHICATION INDICATORS
Abbott, B. C. 1975. Marine Pollution Hazards. Final Report, Contract No. N00014-67-A-0269-
0017. UCLA Allan Hancock Foundation, Los Angeles, California, 24 p. (not in hand)
G-2

Red tides around our coastline are due mainly to blooms of dinoflagellates. Those in colder northern waters are
due mainly to Gonyaulax sp. which produces the paralytic shellfish poison saxitoxin, a neurotoxin. In the
Gulf of Mexico off Florida, red tides, due to Gymnodinium breve, kill millions of fish during a bloom.

Abston, J. R., S. P. Dinnel, W. W. Schroeder, A. W. Shultz and W. J. Wiseman, Jr. 1987.
Coastal sediment plume morphology and its relationship to environmental forcing: Main Pass,
Mobile Bay, Alabama. Pages 1989-2005 ia Coastal Sediments '87. Vol. n. Proceedings of
a Conference, May 12-14,1987, New Orleans, Louisiana. WW Div./ASCE, New York.
G-2, G-2.1

Landsat multispectral scanner imagery has been used to determine the variability of the surface morphology of
Mobile Bay effluent plumes. The plume characteristics derived from the imagery are area, orientation and rate
of spreading. These characteristics are in turn related to external environmental forces. The observed
relationships between the environmental parameters and the plume morphology are discussed. Estimates of
suspended sediment transport based on limited field data of plume hydrography and total suspended solid loads
are offered. Finally, the authors speculate on the role the plume plays in dispersal of Mobile Bay sediments on
the adjacent continental shelf.

Adkins, G. and P. Bowman. 1976. A Study of the Fauna in Dredged Canals of Coastal
Louisiana. Tech. Bull. No. 18, Louisiana Wildlife and Fisheries Commission, New Orleans,
Louisiana, 72 p.
G-ll

In attempts to investigate biological and hydrological parameters now associated with artificial wetland
features, samples were made in four environment types: 1) open, unaltered areas, 2) open canals, 3) semi-open
canals, 4) closed canals. Sampling was accomplished by using various gear over a 2-yr period. Water
chemistry reflected a trend of fluctuation dependent upon freshwater and saltwater intrusion. Peak levels of
most nutrients were recorded following freshwater flooding conditions or storm surges caused by the passage of
hurricanes.

Ambler, J. W. 1982. Influence of Natural Particle Diets on Egg Laying and Hatching Success of
Acartia tonsa in East Lagoon, Galveston, Texas. Ph.D. Dissertation, Texas A&M
University, College Station, Texas.
G-17

Experiments were conducted on copepod (Acartia tonsa) egg hatching at low oxygen concentrations. Although
oxygen concentrations had to fall below 0.4 ppm to affect hatching success, reduced oxygen concentrations
well above this level probably affected the metabolism of the A. tonsa females. Oxygen profiles for East
Lagoon, Galveston Bay, are presented for April, May, July, August and November 1982. In East Lagoon, the
metabolism of A. tonsa would probably be decreased if they resided in the poorly oxygenated deeper waters,
which were present especially during the summer. If the duration of the hypoxic events is not too long, egg
viability should not be greatly affected. The frequency and duration of hypoxic events are unknown for East
Lagoon, but probably occur during the summer when winds are low.
273
-------
Anon. 1984. Low bottom oxygen observed offshore. Marine Briefs 13(8): 1/3.
G-2.3, G-5.1

Personnel of the Laboratory fisheries monitoring and assessment project report that average water temperature
in Mississippi Sound increased in July. Average salinity increased over the last month and was considerably
greater than that recorded last year at this time. Hydrological data from the western-most stations showed low
oxygen levels and cooler temperatures near the bottom. Hypoxic, or low-oxygen, conditions have been
reported for this area in past years.

Anon. 1981. Shrimp posdarvae taken in samples. Marine Briefs 10(3): 1.
G-2.3

The first brown shrimp postlarvae of the year were noted in the Biloxi estuary, indicating that the offshore
spawning of this species had begun. Inshore samples were dominated by catches of young-of-the-year
menhaden. Average temperature was within the seasonal norm. Salinities at monitored stations were high
initially but decreased sharply with increased rainfall during the latter part of the month. Areas of discolored
water have been investigated. Samples of the water contained large numbers of a dinoflagellate tentatively
identified as Prorocentrum minimum.

Armstrong, N. E. 1987. The Ecology of Open-Bay Bottoms of Texas: A Community Profile.
Biological Report No. 85(7.12), U.S. Dept. of the Interior, Fish and Wildlife Service,
Research and Development, National Wetlands Research Center, Washington, D.C., 104 p.
G-16, G-17, G-21, G-22, G-23, G-24, G-26

Open-bay bottoms represent one of the most extensive habitats in any estuarine system, especially in the
northwestern Gulf of Mexico estuaries of Texas. The structure and function of the benthic communities in
these Texas estuaries are examined by reviewing and integrating data from a number of past and ongoing
studies. The key functions of the benthic system are production of biomass as food resources for higher
trophic levels; bioturbation, which enhances nutrient regeneration; and nutrient regeneration itself. Benthic
nutrient regeneration in the shallow water of Texas estuaries may play a key role in regulating primary
production in the estuaries.

Armstrong, N. E. and A. Goldstein. 1975. Determination of Effects of Dow Chemical Company
Discharge on Organisms of the Lower Brazos River. Final Report to the Dow Chemical Co.,
Texas Division, Freeport, Texas. Center for Research in Water Resources, University of
Texas, Austin, Texas, (not in hand)
G-18

Association of State and Interstate Water Pollution Control Administrators. 1984. America's
Clean Water: The States' Evaluation of Progress, 1972-1982. Appendix. Association of
State and Interstate Water Pollution Control Administrators, Washington, D.C.
F-9 through G-27

The information in this report was drawn from 56 reports submitted by State, interstate and territorial water
pollution control agencies. Respondents used a standardized format and instructions to compile and display
their findings about water quality. These submittals were prepared between June and October 1983. The last
section of this appendix is the instruction package used by the States in completing their reports; it includes
the definitions specifically developed for this effort to promote national consistency.

Atwood, D. K. 1981. Environmental Research Needs in the Gulf of Mexico (GOMEX). Vol. I:
Executive Summary and Panel Reports. Vol. DA: Summary Papers. Vol. IIB: Summary
Papers. Vol. EC: Summary Papers. Proceedings of a Symposium, September 30 - October
5, 1979, Key Biscayne, Florida. U.S. Dept. of Commerce, National Oceanic and
Atmospheric Administration, Environmental Research Laboratories. Atlantic Oceanographic
274
-------
and Meteorological Laboratories, Miami, Florida, 769 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

From September 30 to October 5, 1979, a group of U.S. and Mexican economists, marine scientists, and
environmental managers met at Key Biscayne, Florida to discuss the needs for marine-related environmental
research in the Gulf of Mexico during the next decade. As working papers for this workshop, the participants
had at their disposal a series of NOAA contracted summary documents on the status of our present knowledge
of the physics, chemistry, geology, and biology of the Gulf and the socioeconomic pressures on the Gulf. All
indications are that uses of the Gulf of Mexico and its coastline will continue and increase. Unless these uses
are adequately managed, severe aesthetic and economic loses could result Several research objectives and tasks
were specified as the result of workshop deliberations.

Baldauf, R. J., J. Van Conner, H. W. Holcombe and F. M. Truesdale. 1970. A Study of
Selected Chemical and Biological Conditions of the Lower Trinity River and Upper Trinity
Bay. Research Project Completion Report. Project No. A-007-TEX. February 1, 1966 -
June 30, 1969. Tech. Rept. No. 26, Water Resources Institute, Texas A&M University,
College Station, Texas, 168 p.
G-17

Hydrographic samples and nekton from trawls, marsh nets, and seines for semimonthly samples from March
1966 through May 1968. Water samples were for temperature, salinity, dissolved oxygen, total dissolved
Kjeldahl nitrogen and total phosphorus.

Bancroft, K., E. T. Nelson and G. W. Childers. 1988. The microbiological and chemical quality
of Lake Maurepas. The La. Environmental Professional 5(l):53-66.
G-7

The water quality of Lake Maurepas was monitored from July 1986 to June 1987. Seventeen physical and
chemical parameters and four microbiological parameters were monitored monthly. Seasonal trends in physical
and chemical parameters were found for all locations. The highest values for turbidity, suspended solids,
dissolved organic carbon, dissolved oxygen, nitrate and nitrite were recorded in the winter. Dissolved solids,
total solids, ammonia, conductivity and salinity were highest in the summer. Seasonal trends were also found
for bacteria with densities highest in the winter. All concentrations of bacterial indicators of pollution were
found to be greater than those observed during 1983-1984, indicating a significant decrease in the water quality
of Lake Maurepas. Based on fecal coliform and fecal streptococci ratios, the pollution appeared to be primarily
of human origin.

Barrett, B. B., J. O. Merrell, T. P. Morrison, M. C. Gillespie, E. J. Ralph and J. F. Burden.
1978. A Study of Louisiana's Major Estuaries and Adjacent Offshore Waters. Tech. Bull.
No. 27, Louisiana Dept. of Wildlife and Fisheries, New Orleans, Louisiana, 197 p.
G-8, G-8.1, G-10, G-ll, G-ll.l, G-13, G-15

Seven of Louisiana's major estuaries and adjacent offshore waters were sampled monthly from October 1974
through September 1976. In each of these seven areas, four stations yielded samples that were analyzed in
terms of physical properties, water chemistry, nekton, zooplankton, and chlorophyll a. When evident,
correlations and interrelationships among the various parameters are presented along with tabular information
on all measurements made during the study. Variability of the parameters sampled were primarily the result of
one or more of the following factors: amount of freshwater introduction, season, and proximity to oceanic
waters.

Barrett, B. B. and E. J. Ralph. 1976. 1976 Environmental Conditions Relative to Shrimp
Production in Coastal Louisiana. Tech. Bull. No. 21, Louisiana Wildlife and Fisheries
Commission, New Orleans, Louisiana, 20 p.
G-7.1
275
-------
Shrimp catch data are presented along with environmental factors which influence Louisiana's shrimp harvest
Environmental data for the first four months of 1976, particularly in the Barataria-Caminada Bay area, are
compared with previous years. Relationships between shrimp harvest and river discharge, rainfall, salinity,
water temperatures and the available amount of nursery area are presented.

Basta, D. JM B. T. Bower, C. N. Ehler, F. D. Arnold, B. P. Chambers and D. R. G. Farrow.
1985. The National Coastal Pollutant Discharge Inventory. U.S. Dept. of Commerce,
National Oceanic and Atmospheric Administration, Ocean Assessments Division, Office of
Oceanography and Marine Assessment, National Ocean Service, Rockville, Maryland, 18 p.
F-9 through G-27

The National Coastal Pollutant Discharge Inventory is a database and computational framework being
developed by the Strategic Assessment Branch of the Ocean Assessments Division, National Ocean Service,
National Oceanic and Atmospheric Administration. When completed, the NCPDI will include all point,
nonpoint, and riverine sources of pollutant discharges into estuarine, coastal, and oceanic waters of the
contiguous U.S. (excluding the Great Lakes), extending landward to the head of estuaries and seaward to the
boundary of the Exclusive Economic Zone.

Bault, E. I. 1972. Hydrology of Alabama Estuarine Areas - Cooperative Gulf of Mexico
Estuarine Inventory. Ala. Mar. Resour. Bull. 7:1-36.
G-l, G-2, G-2.2 , .

Twenty-one hydrological stations in five Alabama estuarine areas were sampled monthly from January 1968
through March 1969. Nitrite-nitrogen, nitrate-nitrogen, orthophosphate-phosphorus, total phosphorus, pH,
dissolved oxygen, temperature, turbidity and salinity were determined for each station. Bimonthly isohalines
and isotherms and graphical representations of micronutrients and chemophysical parameters are presented. All
data are presented in tables or graphs and comparisons are made among the estuarine areas.

Bechtel, T. J. and B. J. Copeland. 1970. Fish species diversity indices as indicators of pollution
in Galveston Bay, Texas. Contrib. Mar. Sci. 15:103-132.
O-17

Fish species diversity indices (natural bels/individual) calculated for both fish weights and numbers from trawl
collections were found to be useful indicators of environmental and pollution stress in Galveston Bay, Texas.
Sampling throughout the system indicated that the fish populations could be divided into somewhat separate
communities, each structured as a response to environmental and pollution stress.

Bedinger, Jr., C. A., R. E. Childers, J. W. Cooper, K. T. Kimball and A. Kwok. 1981. Part 1 -
Background, program organization and study plan. In C. A. Bedinger, Jr. (ed.), Ecological
Investigations of Petroleum Production Platforms in the Central Gulf of Mexico. Vol. 1 -
Pollutant Fate and Effects Studies. Report to Bureau of Land Management, New Orleans
OCS, Contract AA551-CT8-17. SwRI Project No. 01-5245, Southwest Research Institute,
San Antonio, Texas, 53 p.
G-7.1

Twenty-four sites on the continental shelf of the Louisiana coast have been studied for long-term cumulative
effects of petroleum production in the region of offshore platforms. Sampling and analysis included
hydrography and hydrocarbons of the water column; sediment physical characterization, hydrocarbons, trace
metals, and contamination with depth; and population of the meiofauna, macroinfauna, macroepifauna,
demersal fishes and species associated with the "artificial reef" brought about by the platform. Bottom studies
extended from 100 to 2000 m away from platforms and were therefore indicative of regional as opposed to
localized contamination. Results confirm widespread, chronic contamination with hydrocarbons and metals
with some apparent incorporation of pollutants into biota found at platforms. Over the entire study area
276
-------
absolute amounts of contaminants vary widely showing a general concentration in the nearshore and eastern
portions where the Mississippi River apparently contributes more contaminants than petroleum production
platforms.

Bednar, G. A. 1978a. Quality of Water and Dye Dispersion Characteristics in Jourdan River and
St. Louis Bay, Hancock and Harrison Counties, Mississippi. Open-File Report No. 78-584,
U.S. Dept. of the Interior, Geological Survey, and Mississippi Air and Water Pollution
Control Commission, Jackson, Mississippi, 63 p.
G-5

Jourdan River is one of two major streams supplying fresh water to St. Louis Bay. As this fresh water moves
through the bay into the Mississippi Sound it mixes with and measurably dilutes the very saline waters
entering the bay from the Gulf of Mexico. The concentrations of dissolved oxygen, nutrients, and the
biochemical oxygen demand, as well as the other water quality parameters examined, were within limits that
might be expected under the hydrologic conditions that existed during this study. However, fecal coliform and
fecal streptococci bacteria were excessive and in proportions indicative of human enteric wastes. The
movement of dye from Jourdan River through St. Louis Bay was traced during a 50-hr time-of-travel study. It
was determined from this study that a soluble pollutant discharged into St. Louis Bay of into the tidal reach of
Jourdan River would likely remain in the Bay for many days before being diluted and dispersed by inflow to the
Bay.

Bednar, G. A. 19785. Quality of Water and Dye Dispersion Characteristics in the Back Bay of
Biloxi, Harrison County, Mississippi. Open-File Report No. 78-908, U.S. Dept. of the
Interior, Geological Survey, and Mississippi Air and Water Pollution Control Commission,
Jackson, Mississippi, 62 p.
G-4

The quality of water characteristics of the estuarine system is complex, and is, to a large extent, dominated by
the interactions of opposing tides. The Biloxi and Tchoutacabouffa Rivers contribute the majority of
freshwater inflow. As the fresh water moves through the Bay it mixes with and dilutes the saline water of
Gulf tides. During this study, the Gulf waters penetrated the entire length (about 10 miles) of the study area
and freshwater inflow was low. The dissolved oxygen content of the water in the bay was generally at
concentrations that would support aquatic life, and at some sites the water was supersaturated with dissolved
oxygen at low tide. Dissolved oxygen concentrations were highest near the surface and the mean dissolved
oxygen concentration of the water at each sampling site was greater than 7.0 mg/1 at low tide and decreased to
less than 7.0 mg/1 at high tide as the Gulf waters moved through the Bay.

Bednar, G. A. 1978c. Quality of Water in Pascagoula and Escatawpa Rivers, Jackson County,
Mississippi. Open-File Report No. 78-913, U.S. Dept. of the Interior, Geological Survey,
and Mississippi Air and Water Pollution Control Commission, Jackson, Mississippi, 91 p.
G-3

The chemical and physical properties and the range of concentrations of most constituents in water in these
rivers during the period May 17-19,1977, varied rapidly between high and low tides, primarily as the result of
interactions of freshwater inflow with highly mineralized Gulf waters. There was evidence of oxygen
deficiency (less than 3.0 mg/1) at many sites in deep pools where there is little circulation and mixing of the
more dense saltwater. Dissolved oxygen concentrations ranged from 2.1 to 8.2 mg/1.

Bednar, G. A. 1979. Quality of Water in Bayou Casotte and Bayou Chico, Jackson County,
Mississippi. Open-File Report No. 79-1059, U.S. Dept. of the Interior, Geological Survey,
and Dept. of Natural Resources, Bureau of Pollution Control, Jackson, Mississippi, 36 p.
G-3
277
-------
A short-term water quality study was conducted on July 25-27,1978. The results of the study indicated that
the chemical and physical properties and range of concentrations of several dissolved constituents in both
estuaries varied during a tide cycle primarily as the result of the interaction of freshwater and wastewater inflow
with the saline Gulf waters. The water quality condition of both estuaries generally was good and the low 5-d
biochemical oxygen demand in the estuaries indicated that excessive oxygen demand was not exerted during the
study. The 5-d biochemical oxygen demand generally was less than 3.5 mg/1. Dissolved oxygen
concentrations decreased with depths and the lowest concentrations occurred below 30-ft depths in Bayou
Casotte. Oxygen levels at shallow depths generally were less in Bayou Chico than in Bayou Casotte.
Dissolved oxygen concentrations in Bayou Casotte ranged from 0.7 to 7.7 mg/1 at high tide and from 2.5 to
8.2 mg/1 at low tide.

Benefield, R. L., T. J. Cody, B. E. Fuls and P. C. Hammerschmidt. 1983. Monitoring of
Coastal Shellfish Resources, January - December 1982. Management Data Series No. 55,
Texas Parks and Wildlife Dept., Coastal Fisheries Branch, Austin, Texas, 75 p.
G-17, G-21, G-22, G-24, G-26.1, G-26.2

Trends in relative abundance and size of brown shrimp (Penaeus aztecus), white shrimp (P. setiferus), pink
shrimp (P. duorarum) and blue crabs (Callinectes sapidus) in Texas bay systems and the Gulf of Mexico
(shrimp only) were monitored from January-December 1982. Shorelines and deeper portions of bays were
sampled in Galveston, Matagorda, San Antonio, Aransas and Corpus Christi Bays and upper and lower Laguna
Madre. Passes were sampled in Galveston, Matagorda, Aransas and Corpus Christi Bays and the lower Laguna
Madre and Gulf samples were collected along the central coast. Data summarized in this report represent the
initiation of a program that will yield long-term trends in abundance and stability of shellfish in Texas waters.
Improved information on trends will result as the peaks of seasonal abundance are identified through time in
the different areas sampled.

Bien, G. S., D. E. Contois and W. H. Thomas. 1958. The removal of soluble silica from fresh
water entering the sea. Geochim. Cosmochim. Acta 14:35-54.
G-7.1

Determinations of soluble silica and chlorosity of water samples collected in and around the east Mississippi
Delta showed that most of the soluble silica was removed from river water by some process other than dilution
with seawater. While biological uptake by diatoms can account for part of this removal, it is more likely that
a major portion is removed by inorganic precipitation. Laboratory experiments with river water and sea water
showed that both suspended matter from the river and electrolytes in sea-water are necessary for maximum
inorganic precipitation. It is concluded that this process is an adsorption of soluble silica on suspended matter
as it comes in contact with electrolytes, rather than a simple formation of salts with electrolytes. The
inorganic removal can increase by a maximum of 4-5 % the weight of sediment in the water that may be
expected to reach the bottom.

Blanton, W. G., T. J. Culpepper, H. W. Bischoff, A. L. Smith and C. J. Blanton. 1971. A
Study of the Total Ecology of a Secondary Bay (Lavaca Bay). Final Report. Texas
Wesleyan College, Fort Worth, Texas, 306 p.
G-21 .

A large-scale multidisciplinary ecological study of the bay systems has been initiated as follows: 1) Chemical
and physical parameters were monitored throughout the Lavaca Bay system. 2) Biological parameters were
compiled with regard to: a) species survey of phytoplankton, zooplankton, and nekton; b) population
dynamics; c) species diversity. 3) Surface sediments with their corresponding water columns were analyzed
with regard to: a) microbiological studies (bacterial count and diversity); b) benthonic studies (benthos count
and diversity); c) sediment type. 4) Laboratory studies of the effects of various concentrations of fluoride on a
variety of organisms. 5) Toxicity of fluoride on fish and phytoplankton.
278
-------
Blaylock, D. A. 1983. Choctawhatchee Bay: Analysis and Interpretation of Baseline
Environmental Data. Technical Paper No. 26, University of West Florida, Pensacola,
Florida, (not in hand)
F-26

Boenig, D. L. 1990. Hypoxia and Its Effect on Bottom-Dwelling Macrofauna Distribution.
Student Report, Louisiana Universities Marine Consortium, Chauvin, Louisiana, 10 p.
G-7.1

It has been established that the largest, most severe, and most persistent zone of hypoxia (defined by oxygen
levels of <2 mg/1) in the United States is found in the northern Gulf of Mexico on the continental shelf off of
Louisiana. Numerous theories have been presented as to the cause of hypoxia. The purpose of this paper is to
show the changes in bottom-dwelling macrofauna distribution as it is affected by the depleted oxygen
abundance during the summer months (April through July) off the coast of Cocodrie, Louisiana.

Boesch, D. F. 1982. Causes and effects of shelf oxygen depletion: Lessons from the 1976 New
York Bight episode. Abstr. for Proceedings of the Third Annual Gulf of Mexico Information
Transfer Meeting, August 24-26,1982, New Orleans, Louisiana. U.S. Dept. of the Interior,
Minerals Management Service, Outer Continental Shelf Office, New Orleans, Louisiana.
G-7.1

Severe depletion of dissolved oxygen in open continental shelf waters is known from only very few areas in
the world, mostly regions of pronounced coastal upwelling. Hypoxic or anoxic bottom water on the inner
shelf of the north-central Gulf of Mexico is apparently a regular occurrence, although it is scarcely reported in
the formal literature and has been little studied. Unusual and widespread oxygen depletion of bottom waters in
the New York Bight occurred during the summer of 1976 and was relatively well studied because of the
substantial ongoing research programs in the area. The findings of these studies are reviewed with regard to the
environmental conditions and biological phenomena that caused oxygen depletion and resulting effects on
benthic organisms. Development of hypoxia in continental shelf waters depends on 1) intense stratification
which reduces eddy diffusivity and, consequently, oxygenation of bottom waters, and 2) an ample supply of
labile organic material resulting from ungrazed phytoplankton production, rather than from inputs of fluvial
organic material.

Boesch, D. F. 1983. Implications of oxygen depletion on the continental shelf of the northern
Gulf of Mexico. Coastal Ocean Pollution Assessment News 2(3):25-28.
G-7.1

The brief review describes what is known about the spatial and temporal extent of the bottom-water oxygen
depletion phenomenon in the Gulf, considers whether the phenomenon has recently increased in extent or
severity, evaluates the potential causes and whether they are related to human activities, and considers
consequences of the phenomenon.

Boesch, D. F., J. W. Day, Jr. and W. H. Conner. 1989. Barataria-Terrebonne Estuarine
Complex. Governor's Nomination and Request for a Management Conference under the
National Estuary Program. Office of the Governor, State of Louisiana, Baton Rouge,
Louisiana, 109 p.
G-10,G-11

The Barataria-Terrebonne Estuarine Complex consists of an extensive array of estuarine wetlands and
waterbodies filling the basins between the two active distributary systems of the Mississippi River, the lower
Mississippi River proper and the Atchafalaya River. The principal environmental problems faced by the
Barataria-Terrebonne Estuarine Complex are hydrological modification, habitat loss and modification,
eutrophication, changes in living resources, toxic substances, and pathogen contamination. The environmental
quality problems center more around physical deterioration of habitats and non-point or diffuse sources of
279
-------
pathogens, nutrients and toxicants than large discharges of toxic materials and biostimulants. In addition, the
pervasive influence of oil and gas production activities, both in terms of hydrologic and habitat alterations
resulting from associated dredging and operational discharges which affect water quality, presents a unique
management challenge.

Boesch, D. F. and N. N. Rabalais (eds.). 1989a. Produced Waters in Sensitive Coastal Habitats:
An Analysis of Impacts, Central Coastal Gulf of Mexico. OCS Report/MMS 89-0031, U.S.
Dept. of Interior, Minerals Management Service, Gulf of Mexico OCS Regional Office, New
Orleans, Louisiana, 157 p.
G-10, G-ll

The objectives of this study were to 1) quantify the location and characteristics of outer continental shelf
(OCS) produced waters discharged into coastal environments of the Gulf of Mexico and 2) provide an
assessment of the environmental fate and effects of selected discharges. An inventory of produced water
discharges based on records of regulatory agencies in Texas and Louisiana was compiled. The other Gulf states
(Mississippi, Alabama and Florida) do not permit the discharge of produced water into surface waters. A field
assessment provided a general delimitation of the scope and nature of the impacts.

Boesch, D. F. and N. N. Rabalais (eds.). 1989b. Environmental Impact of Produced Water
Discharges in Coastal Louisiana. Proceedings of Report prepared for The Louisiana Division
of the Mid-Continent Oil and Gas Association. Louisiana Universities Marine Consortium,
Chauvin, Louisiana, 287 p.
G-10, G-12

In response to concerns about the effects of the discharge of produced waters (oilfield brines) in estuarine and
wetland environments of coastal Louisiana, a three-part study was conducted to 1) determine the potential that
the numerous brine discharges in the coastal zone may have on the salinity regime, 2) assess the effects of
produced water discharges on wetlands based on analysis of aerial photographs, 3) assess the hydrological,
chemical, and biological effects in field studies. The field studies documented the effects of the brine discharge
in near-bottom waters with regards to elevated salinities to some distance from the discharge, depending on the
volume discharged and the characteristics of the receiving environment In two locations, low dissolved
oxygen concentrations were documented in near-bottom waters where there was a strong salinity stratification
of the overlying water column.

Boesch, D. F. and N. N. Rabalais. 1991. Effects of hypoxia on continental shelf benthos:
Comparisons between the New York Bight and the Northern Gulf of Mexico. Pages 27-34 in
R. V. Tyson and T. H. Pearson (eds.), Modern and Ancient Continental Shelf Anoxia.
Geological Society Special Publication No. 58, The Geological Society, London, 470 p.
G-7.1, G-27

Depletion of dissolved oxygen to a point inducing mortality of bottom-dwelling organisms (hypoxia) occurs in
several continental shelf environments in Europe and North America and may have increased as a result of
nutrient overenrichment from human activities. Hypoxia in coastal waters develops as a result of decomposing
plankton and density stratification of the water column, which hinders the oxygenation of bottom waters.
Mass mortalities of benthic organisms have occurred as a result of extensive hypoxia on the inner continental
shelves of the New York Bight and the northern Gulf of Mexico off Louisiana and Texas. In the New York
Bight, extensive hypoxia is rare and recovery of the benthic communities from the catastrophic 1976 hypoxia
to previous conditions was not complete over 2 yr later. On the Louisiana-Texas shelf, large-scale hypoxia
occurs virtually very year, and recovery from this disturbance is rapid, because the community is kept in an
early successional state by the annually recurring hypoxia.

Boler, R. (ed.). 1987. Water Quality 1986-1987, Hillsborough County, Florida. Hillsborough
County Environmental Protection Commission, Tampa, Florida, 207 p.
F-15
280
-------
Sampling has been conducted routinely by the Environmental Protection Commission of Hillsborough
County in Tampa Bay since 1972, when only mid-depth samples were collected. Starting in 1975, samples
for selected parameters have been collected at surface, mid-depth, and bottom. Fresh waters have been sampled
routinely since 1973. These data, obtained during 1972-1987, may provide useful background for eventual
development, revision and enforcement of regulations, standard effluent limitation plans, or programs
established under the Federal Water Pollution Control Act of 1972.

Brent, C. R. N.D. Effect of Mississippi River flood plume on dissolved oxygen, April - July,
1973. Memorandum, University of Southern Mississippi, Hattiesburg, Mississippi, 4 p.
G-7.1

Salinity measurements during April 1973 indicate a surface layer of fresher water having a salinity depression
of some 33% from waters below it extending to a depth of about 10 m. The salinity gradient in April was
rather uniform from the surface to a depth of 10 m, indicating uniform mixing to that depth. The isolation of
waters deeper than 7 m by an extensive, low density Mississippi River plume allowed oxygen demand from a
variety of natural, manmade and unseasonable sources to overtake oxygen resupply mechanisms on the
continental shelf off Timbalier Bay. No one factor seems to dominate the causes of this phenomenon except
the presence of Mississippi plume overlying and isolating the water below it

Breuer, J. P. 1969-70. A biological survey of the tidewater areas of the Rio Grande. Project CF-
2-1 (Job No. 2). Pages 127-136 in Coastal Fisheries Project Reports 1969-1970. Texas
Parks and Wildlife Dept., Austin, Texas.
G-26.3

Hydrographic and biological sampling stations were established on the Lower Rio Grande every 4 mi from the
mouth upstream to Mile 28. These were sampled 15 times in 1969 and 1970. Hydrographic samples included
water temperatures, pH, turbidity, surface and bottom salinities, and surface and bottom dissolved oxygen.
Biological samples were taken principally with a 12-ft otter trawl. Results of sampling were tabulated and
analyzed.

Breuer, J. P. 1957. An ecological survey of Baffin and Alazan Bays, Texas. Publ. Inst. Mar.
Sci. Univ. of Texas 4(2):134-155.
G-25

In the summer of 1950, the Texas Game and Fish Commission began an extensive long-term ecological study
of the Laguna Madre of Texas, a 130-mi long hypersaline bay on the South Texas coast. One of the three
areas of study was the Baffin-Alazan Bay area. Field work in this area was started in June 1951 and was
continued until May 1953. This paper is a portion of a final report to the Texas Game and Fish Commission
on this study.

Breuer, J. P. 1962. An ecological survey of the Lower Laguna Madre of Texas, 1953-1959.
Publ. Inst. Mar. Sci. Univ. of Texas 8:153-183.
G-26.2

Hydrographic data and annotated comments on the distribution and habits of species are presented for the Lower
Laguna Madre of Texas, a shallow, hypersaline marine bay extending 76 miles north of the Rio Grande delta.
In summer, waters of the Gulf move northward through the lagoon with increasing salinity due to evaporation.
The variety of species in the plankton and bottom communities diminish with distance from the pass. In
winter, flow is southward. Some ecological effects of manmade changes are described, including the effects of
opening Port Mansfield Pass, the isolation and silting of South Bay due to spoil, and the management of the
Rio Grande River during floods. Movements of year classes of game fishes are described.
281
-------
Breuer, J. P. 1972. Ecological survey of the Brownsville ship channel - 1971-1972. Pages 93-
131 in Coastal Fisheries Project Reports. Texas Parks and Wildlife Dept., Austin, Texas.
G-26.2

The objective of the ecological survey was to determine the value of the Brownsville ship channel to the area
marine fishery. Monthly biological samples were taken by trawl and water chemistry was analyzed at 14
stations in the Brownsville ship channel and surrounding areas from August 1971 to December 1972.
Monthly rainfall varied from 0.74 in in August 1971 and December 1972 to 10.78 in in September 1972.
Surface and bottom temperatures ranged from 12 *C to 30 "C during the study, and no significant difference
was found between surface and bottom temperatures. Overall salinities ranged from 0.5 ppt to 33.9 ppt.
Bottom dissolved oxygen ranged from 1.8 to 9.0 ppm. pH ranged from 6.8 to 8.7.

Brooks, J. M. 1980. Vol. Ill - Determine Seasonal Variations in Inorganic Nutrients
Composition and Concentration in the Water Column. In W. B. Jackson and G. M. Faw
(eds.), Biological/Chemical Survey of Texoma and Capline Sector Salt Dome Brine Disposal
Sites off Louisiana, 1978-1979. NOAA Tech. Memo. NMFS-SEFC-32, NOAA/NMFS
Final Report to DOE. U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, National Marine Fisheries Service, Galvestoh, Texas, 31 p.
G-7.1

Seawater samples were analyzed for ammonium nitrogen, nitrate nitrogen, nitrite nitrogen, phosphate
phosphorus, and dissolved silicate at the West Hackberry (Texoma) and Weeks Island (Capline) Strategic
Petroleum Reserve brine disposal sites. The nutrient concentrations were typical of the nearshore environment
from which the samples were taken. High ammonia, phosphate, and silicate concentrations were observed in
some near-bottom samples correlating with low oxygen concentrations. Nitrate showed a negative correlation
with salinity suggesting freshwater inputs as a source of this nutrient

Brooks, J. M. and G. A. Wolff (eds.) 1991. Mississippi-Alabama Continental Shelf Ecosystem
Study Data Summary and Synthesis. Vol. HI: Appendices, Part 1 (Appendices A-D). OCS
Study MMS 91-0064. U.S. Dept. of the Interior, Minerals Management Service, Gulf of
Mexico OCS Regional Office, New Orleans, Louisiana, 1001 p.
G-2.1, G-5.1, G-7.1

Browder, J. A., L. N. May, Jr., A. Rosenthal, R. H. Baumann and J. G. Gosselink. 1987.
Utilizing Remote Sensing of Thematic Mapper Data To Improve Our Understanding of
Estuarine Processes and Their Influence on the Productivity of Estuarine-Dependent
Fisheries. Fourth Semiannual Progress Report to the National Aeronautics and Space
Administration on the TM Project. Center for Wetland Resources, Louisiana State
University, Baton Rouge, Louisiana.
G-9, G-10, G-ll

A stochastic spatial computer model addressing coastal resource problems in Louisiana is being refined and
validated using thematic mapper imagery. This research consists of two major activities: 1) Measuring land
(or emergent vegetation) and water and the length of the interface between land and water in thematic mapper
imagery of selected coastal wetlands (sample marshes); 2) Comparing spatial patterns of land and water in the
sample marshes of the imagery to those in marshes simulated by the computer model. This report discusses
the accomplishments in modeling by the NMFS group and in digital processing of thematic mapper data by
the LSU group. Planned future work is briefly discussed in a final section.

Brown, Jr., L. F., L. L. Brewton, J. H. McGowan, T. J. Evans, W. L. Fisher and C. G. Groat.
1976. Environmental Geologic Atlas of the Texas Coastal Zone - Corpus Christi Area.
Bureau of Economic Geology, University of Texas, Austin, Texas, 123 p.
G-23, G-24
282
-------
A series of maps presents data on land and water. The basic environmental geology map delineates and depicts
in detail resource units of first-order environmental significance. The accompanying series of eight special-use
maps outline physical properties and land use suitability, current land use, active physical processes, mineral
and energy resources, topographic and bathymetric configurations, natural and artificial water systems, and
climate. A descriptive text explains the data presented, their utility, and means of extrapolating for other
special uses.

Brown, Jr., L. F., L. L. Brewton, J H. McGowan, T. J. Evans, C. G. Groat and W. L. Fisher.
1980. Environmental Geologic Atlas of the Texas Coastal Zone - Brownsville-Harlingen
Area. Bureau of Economic Geology, University of Texas, Austin, Texas, 140 p.
G-26, G-26.2

See Brown et al. (1976).

Brown, Jr., L. F., J. H. McGowan, T. J. Evans, C. G. Groat and W. L. Fisher. 1977.
Environmental Geologic Atlas of the Texas Coastal Zone - Kingsville Area. Bureau of
Economic Geology, University of Texas, Austin, Texas, 131 p.
G-26
See Brown et al. (1976).

Bryan, C. E. 1971. An ecological survey of the Arroyo Colorado, Texas, 1966-1969.
Parks and Wildlife Dept. Tech. Ser. 10:1-28.
G-26.2
Texas
The lower portion of the Arroyo Colorado is one of very few brackish water areas in the Lower Laguna Madre
of Texas and provides a nursery ground for marine species of the region. Data on biological and hydrographic
conditions prior to and following a major flood were obtained. Salt water reached Mile 25 before the flood and
the entire area was fresh following it It took one year for hydrographic conditions to approximate pre-flood
status. During a major portion of the year, there was little or no oxygen on the bottom from Mile 7 to Mile
25. There was an inverse relationship between encroaching high salinity water and low dissolved oxygen
readings, indicating high organic content and poor water circulation.

Buck, J. D. and R. H. Pierce. 1989. Bacteriological aspects of Florida red tides: A revisit and
newer observations. Estuarine Coastal Shelf Sci. 29(4):317-326.
F-14

A brief review is presented of the literature involving the occurrence of bacteria in red tides caused by the
dinoflagellate Ptychodiscus brevis. Both quantitative and qualitative studies were made on outbreaks along the
Florida Gulf coast in 1982 and 1987 and a bloom along the North Carolina coast in 1987. Non-bloom waters
in both areas were sampled in 1988. Members of the genera Aeromonas, Alteromonas/Pseudomonas and
Vibrio were frequently isolated from the three blooms studied as well as from non-bloom waters.

Burchfield, H. P., R. J. Wheeler and W. Subra. 1974. Nutrient analysis of water and sediment
in Timbalier Bay, Louisiana (August 1973 - January 1974). Pages 54-57 in Abstracts,
Summaries, and Conclusions from the Offshore Ecology Investigation, 1972-74. Gulf
Universities Research Consortium (GURC), Galveston, Texas.
G-ll

Seasonal variations were apparent for the nutrients within the study area. Nutrient values were highest in
October 1972 for total alkalinity, dissolved silica and orthophosphate and sediment total alkalinity, dissolved
silica and total phosphate. Elevated values occurred in October 1973 but were not comparable with the
October 1972 values. The ammonia nitrogen and nitrite plus nitrate nitrogen contents of waters and the
Kjeldahl nitrogen contents of sediments were elevated during the winter months and lowest from early spring
283
-------
to late fall. The values for the winter of 1972-1973 were much greater than the values for the 1973-1974
winter. Variations around oil company structures were observed and attributed to effects of the physical
structure.

Burchfield, H. P., R. J. Wheeler and W. Subra. 1979. Nutrient concentrations in Timbalier Bay
and the Louisiana oil patch. Pages 223-233 in C. H. Ward, M. E. Bender and D. J. Reish
(eds.), The Offshore Ecology Investigation. The Effects of Oil Drilling and Production in a
Coastal Environment. Rice University Studies 65(4&5).
G-ll

Water samples along a transect in eastern Timbalier Bay were taken in August 1972 through January 1974 and
analyzed for total alkalinity, dissolved silica, orthophosphate, ammonia nitrogen, and nitrate and nitrite
nitrogen. Sediments were analyzed for total alkalinity an dissolved silica of the interstitial water and for total
Kjeldahl nitrogen and total phosphate in bulk sediments. Seasonal variations were shown for all of the
nutrients studied. During any collection period, no significant differences were shown among study areas.

Burrage, D. (ed.). 1989. Public Health Issues in the Gulf of Mexico. Proceedings of a
Mississippi Sea Grant Advisory Service Workshop, November 14-15, 1989. Publ. No.
MASGP-90-002, Mississippi-Alabama Sea Grant Consortium, Ocean Springs, Mississippi,
29 p.
F-9 through G-27

Sections of this report include an Introduction, Pathogen Exposure via Molluscan Shellfish, Human Exposure
to Pathogens in Seawater, Marine Biotoxins and Associated Public Health Risks in the Gulf of Mexico,
Summary and Recommendations, and a List of Participants.

Butts, G. L. 1983. Dissolved Oxygen Survey of Upper Perdido Bay. Memorandum, State of
Florida, DepL of Environmental Regulation, Pensacola, Florida, 4 p.
F-28, G-l

On July 14,1983, L. W. Doneland and G. L. Butts sampled Perdido Bay utilizing a model 6D Hydrolab. The
data recorded are included in the memorandum.

Caffrey, J. M. and J. W. Day, Jr. 1986. Control of the variability of nutrients and suspended
sediments in a Gulf coast estuary by climatic forcing and spring discharge of the Atchafalaya
River, Estuaries 9(4A):295-300.
G-12

Water column nutrients (nitrate, ammonium, soluble reactive phosphate, total Kjeldahl nitrogen, and total
phosphorus) and suspended sediments were measured during one 44-h and two 28-h periods in March 1982 at
two stations in Fourleague Bay, Louisiana, which is located at the mouth of the Atchafalaya River, a
distributary of the Mississippi River. River water (a source of nitrate, total Kjeldahl nitrogen, total
phosphorus, and suspended sediments to Fourleague Bay) flows into the upper reaches of the Bay during high
tide and frontal overrunning conditions with northerly and westerly winds. During one sampling period,
decreasing wind speed and the rising tide resulted in Atchafalaya River water inundating the Bay and nitrate
concentrations in the upper Bay increasing from 30-70 uM to 90-118 uM. Significant variations in nutrients
associated with the movement of water masses from the river, marshes, and Gulf of Mexico occurred over
several different time scales. Tidal transport occurred over 25-h periods, while frontal passages occurred at 3-d
to 5-d intervals. Variability in nutrient and suspended sediment concentrations over these relatively short time
scales can be as great as seasonal variability in the bay.

Cahoon, D. R. and C. G. Groat (eds.). 1990. A Study of Marsh Management Practice in Coastal
Louisiana. Vol. I. Executive Summary, Vol. II. Technical Description, Vol. III. Ecological
Evaluations. Final Report to U.S. Dept. of Interior, Minerals Management Service, New
284
-------
Orleans, Louisiana. Contract No. 14-12-0001-30410. OCS Study/MMS 90-0073,90-0074,
90-0075, 36 p, 309 p., 423 p.
G-ll, G-13, G-14

Cardinale, T. and R. Boler. 1984. Environmental Quality: 1982-1983, Hillsborough County,
Florida. Hillsborough County Environmental Protection Commission, Tampa, Florida, 242
p. (not in hand)
F-15 .

Casserly, D. M., M. Vecchione, R. S. Maples, R. Ilg, G. R. Gaston, D. Weston, J. Beck and J.
Lascara. 1982. Biological attributes of the West Hackberry brine disposal site. Abstr. for
Oceans '82 Conference Record: Industry, Government, Education - Partners in Progress
September 20-22, 1982. Washington, D.C.
G-27

A Strategic Petroleum Reserve brine disposal site is located 11.4 km off the southwest coast of Louisiana. A
grid of stations centered at the brine diffuser was monitored monthly for biological attributes during a 12-mo
period. Temporal and spatial distributions in species abundances and diversity were measured for: 1)
macrobenthic invertebrates, 2) fishes and nektonic macrocrustaceans, 3) plytoplankton, and 4) zooplankton.
These assemblages were studied relative to physical and chemical variations occurring in the study area. The
marine fauna and flora of the diffuser area are characteristic of coastal assemblages of the northwestern Gulf
coast. Population fluctuations were attributed to seasonal and hypoxic conditions. The macrobenthic
community was dominated by polychaetes and phoronids; the nekters were typical of the white shrimp
community; the phytoplankton community was dominated by estuarine and neritic species; and the
zooplankton community was dominated by copepods with Penaeus spp. and Brevoortia spp. common in the
area.

Center for Wetland Resources. 1970. Louisiana Wild Life and Fisheries Commission, Water
Chemistry Survey Data, Louisiana Estuaries, 1968-1969. Report to Dept. of the Army, New
Orleans District, Corps of Engineers. Hydrologic and Geologic Studies of Coastal Louisiana
Report No. 7, Coastal Resources Unit, Center for Wetland Resources, Louisiana State
University, Baton Rouge, Louisiana, 91 p.
G-7, G-8, G-9, G-10, G-ll, G-12, G-13, G-14, G-15

This report contains a summary of chemical and physical parameters of mainly the saline waters of coastal
Louisiana. Data were collected by the Louisiana Wild Life and Fisheries Commission at stations located
throughout the coastal wetlands during the period December 1967 through June 1969. At most of the stations
water samples were taken once every month. Recorded parameters are: temperature, salinity, oxygen, turbidity,
nitrate, nitrite, reactive phosphorus, total phosphorus. For each parameter, the mean, maximum, and
minimum value for the year 1968 are given. In addition, seasonal means are presented for those parameters for
which monthly values were available for more than 4 months during winter-spring and/or summer-autumn of
1968 and/or winter-spring of 1969.

Chambers, G. V. and A. K. Sparks. 1959. An ecological survey of the Houston Ship Channel
and adjacent bays. Publ. Inst. Mar. Sci. Univ. of Texas 6:213-250
G-17

An ecological survey of the Houston Ship Channel and adjacent bays was initiated in the summer of 1957
with data collected at frequent regular intervals. This report includes the comparison of data on temperature,
chlorinity, dissolved oxygen, and related quantities with data on fish, shrimp, and crabs caught in trawls. Data
are also given on currents, bottom cores, and organic content of sediments. In the ship channel, a dissolved
oxygen gradient existed from a low dissolved oxygen concentration in the upper channel to near normal
concentrations at the lower boundary of the survey area. The dissolved oxygen in the ship channel below the
285
-------
mouth of the San Jacinto River is greatly influenced by the flow rate of the river which is, in turn, controlled
largely by rainfall.

Childers, D. L. and J. W. Day, Jr. 1990a. Marsh-water column interactions in two Louisiana
estuaries. I. Sediment dynamics. Estuaries 13(4):393-403.
G-10, G-12

Throughflow marsh flumes were used to measure total sediment exchanges between the marshes and water
column of two Louisiana estuaries. Comparisons were made between the Barataria Basin estuary which is
isolated from significant riverine sediment input and the Fourleague Bay estuary which receives large sediment
inputs from the Atchafalaya River.

Childers, D. L. and J. W. Day, Jr. 1990b. Marsh-water column interactions in two Louisiana
estuaries, H. Nutrient dynamics. Estuaries 13(4):404-417.
G-10, G-12

The exchange of dissolved nutrients between marshes and the inundating water column was measured using
throughflow marsh flumes built in two microtidal Louisiana estuaries: the Barataria Basin estuary and
Fourleague Bay. Comparisons were made between the two systems in relation to the deltaic successional stage
of the estuary.

Childers, R. E. 1981. Part 8 - Summary data set. In. C. A, Bedinger, Jr. (ed.), Ecological
Investigations of Petroleum Production Platforms in the Central Gulf of Mexico. Vol. 1 -
Pollutant Fate and Effects Studies. Report to Bureau of Land Management, New Orleans
OCS, Contract AA551-CT8-17. SwRI Project No. 01-5245, Southwest Research Institute,
San Antonio, Texas, 794 p.
G-7.1

See Bedinger etal. (1981).

Childress, U. R. 1966. Hydrographic and Meteorological Study of the San Antonio Bay System.
Pages 447-475 in Coastal Fisheries Project Reports 1964. Texas Parks and Wildlife Dept.,
Austin, Texas, (not in hand)
G-22

Childress, U. R., E. Bradley, E. Hagen and S. Williamson. 1975. The Effects of Freshwater
Inflows on Hydrological and Biological Parameters in the San Antonio Bay System, Texas.
Texas Parks and Wildlife Dept., Coastal Fisheries Branch, Austin, Texas, 190 p.
G-22

The San Antonio Bay system is an oligohaline system that supports substantial populations of economically
important fish and shellfish. The anticipated construction of flow-control structures such as dams and
diversion canals on the Guadalupe and San Antonio Rivers, as well as on other rivers that drain into Texas'
coastal waters, prompted a study of the composition and extent of freshwater flow into and the corresponding
effects on the San Antonio Bay system. This system was chosen for the study because it was an area of high
volume river inflow having little industrialization and few restrictions on the flow of incoming fresh water.

Christmas, J. Y. (ed.). 1973. Cooperative Gulf of Mexico Estuarine Inventory and Study,
Mississippi. Phase I: Area Description. Phase II: Hydrology. Phase HI: Sedimentology.
Phase IV: Biology. Mississippi Marine Conservation Commission, Gulf Coast Research
Laboratory, Ocean Springs, Mississippi, 434 p.
G-2.3, G-3, G-4, G-5, G-6
286
-------
The Mississippi portion of the Gulf of Mexico Estuarine Inventory and Study with attention primarily to the
physical and environmental properties of estuaries, but also economic, developmental, and political factors
associated with them. The major goal of the inventory is related to management of coastal resources.

Christmas, J. Y. and C. K. Eleuterius. 1973. Phase H: Hydrology. Pages 75-121 in J. Y.
Christmas (ed.), Cooperative Gulf of Mexico Estuarine Inventory and Study, Mississippi.
Mississippi Marine Conservation Commission, Gulf Coast Research Laboratory, Ocean
Springs, Mississippi.
G-2.3, G-3, G-4, G-5, G-6

Salinity, temperature, pH and dissolved oxygen concentration were measured at 5-ft intervals through the water
column at 51 stations in Mississippi inshore estuarine waters. Micronutrient concentrations were determined
from surface and bottom water samples. Monthly stream flow was documented. Sampling was accomplished
monthly or oftener. Salinity was closely correlated with stream flow, providing drastic seasonal and area!
variations. Temperature followed a seasonal pattern with spring and fall reversal of offshore clines. Saltwater
wedges were described. Average isohalines and isotherms for Mississippi Sound were constructed. General
micronutrient levels in the study area were established. Concentrations were closely related to adjacent human
population density.

Chuang, W.-S. and E. M. Swenson. 1981. Subtidal water variations in Lake Pontchartrain,
Louisiana. J. Geophys. Res 86:4198-4204. (not in hand)
G-7

Churgin, J. and S. J. Halminsta. 1974. Key to Oceanographic Records Documentation No. 2.
Temperature, Salinity, Oxygen, and Phosphate in Waters off United States. Vol. II. Gulf of
Mexico. U.S. Dept. of Commerce, National Oceanic and Atmospheric Administration,
Environmental Data Service, Washington, D.C., 117 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

Comiskey, C. E. and T. A. Farmer (eds.). 1981. Characterization of Baseline Oceanography for
the Texoma Region Brine Disposal Sites. Vol. I. Contract No. DEAC01-77US08788. Final
Report to DOE, Strategic Petroleum Reserve Office, Washington, D.C., 130 p. (not in hand)
G-7.1

Committee on Merchant Marine and Fisheries. 1988. Coastal Waters in Jeopardy: Reversing the
Decline and Protecting America's Coastal Resources. Oversight Report. Serial No. 100-E,
Committee on Merchant Marine and Fisheries, Washington, D.C., 47 p.

This report culminates the efforts of the Committee, through the course of nine oversight hearings, to amass a
comprehensive record covering every major aspect of the coastal pollution problem, from direct discharges of
pollutants into coastal waters to surface runoff to atmospheric deposition to sediment leaching. The heart of
the report is the recommendations section.

Connell, C. H. and J. B. Cross. 1950. Mass mortality of fish associated with the protozoan
Gonyaulax in the Gulf of Mexico. Science 112(2908):359-363.
G-17

This is the first reported observation of the concurrent appearance of a red tide, luminescent water, and
immense numbers of the dinoflagellate protozoan, Gonyaulax, with mass mortality of fish on the eastern coast
of North America. The episode occurred in the summer of 1949 in a saltwater lagoon known as Offatts Bayou
along Gaiveston Island.
287
-------
Conner, W. H. and J. W. Day, Jr. (eds.). 1987. The Ecology of Barataria Basin, Louisiana: An
Estuarine Profile. Biological Report No. 85(7.13), U.S. Dept. of the Interior, Fish and
Wildlife Service, Washington, B.C., 165 p.
G-10

This estuarine profile is one of a series of publications concerning estuarine areas of the U.S. Its purpose is to
synthesize existing information on the basin. It is one the interdistributary sub-estuaries of'the Mississippi
deltaic plain. Habitats in the basin vary from swamp forest to marine open water. Chapters are entitled:
Description of the Basin; Physical Variables; Chemistry and Nutrient Dynamics; Vegetation: Composition and
Production; Zooplankton; Benthos; Nekton; Wildlife; Review of Modeling Studies in the Barataria Basin;
Management Issues; Synthesis.

Conseil Permanent International pour 1'Exploration de la Mer. 1936. Bulletin hydrographique
rxjurl'anne'e 1935 (Series Bl), 105 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

Provides oxygen, phosphate, and nitrate profiles at numerous locations in the Gulf of Mexico during 1935.

Craig, N. J., J. W. Day, Jr., A. M. Seaton, P. Kemp and W. G. Smith. 1977. Part 1 -
Eutrophication. la N. J. Craig and J. W. Day, Jr. (eds.), Cumulative Impact Studies in the
Louisiana Coastal Zone. Final Report to Louisiana State Planning Office. Center for Wetland
Resources, Louisiana State University, Baton Rouge, Louisiana.
G-7, G-10, G-ll, G-12, G-15

This publication consists of two parts. Part 1 recognizes that eutrophication is a widespread problem
throughout the coastal zone of Louisiana. It leads to poor water quality, development of nuisance algal
blooms, decline in desirable commercial and sports fishery species, and diminished recreational usefulness of
water bodies. The major cultural sources of nutrients leading to eutrophication are urban runoff, domestic
sewage, and agricultural runoff.

Crance, J. H. 1971. Description of Alabama estuarine areas - cooperative Gulf of Mexico
estuarine inventory. Ala. Mar. Resour. Bull. 6:1-85.
G-l, G-2, G-2.2

The physical characteristics of Alabama estuarine areas are presented as part of a cooperative Gfulf of Mexico
estuarine inventory. The importance of estuaries as nursery areas for marine species and for other uses is
discussed, and the early history of the exploration and development of the Gulf of Mexico and the coastal area
of Alabama is reviewed. Maps are presented to show the Alabama estuarine study area and the surface sediment
types, pollution sources, oyster beds, isotherms, isohaline and certain economic characteristics of the area.
Data on climate, tides, open water surface area and average depth, tidal marsh, stream discharge, domestic and'
industrial wastes, navigation channels, commercial fisheries, and other characteristics of the study area are
presented in tables.

Crozier, G. F. and S. R. Heath. 1974. Mobile Bay Plume Study Cruise Report: A-74-45.
NASA Contract No. NAS 8-30810, Marine Environmental Sciences Consortium, Dauphin
Island, Alabama, 10 p.
G-2

In an effort to define the boundaries and provide some quantitative data for the Mobile Bay "plume" of turbidity
and its effect on the inner continental shelf, an east-west cruise track was utilized, October 9, 1974. NASA
has conducted several types of remote sensing studies which clearly demonstrate the occurrence of the offshore
surface turbid water, but found truth turbidity quantitation has not been available for this particular feature.
The intent of this study was to compare visual observations to optical measurements while providing needed
288
-------
ground truth for satellite photography. In addition, nutrient transfer, usually associated with Bay waters, was
determined.

Cullen, J. J. and R. S. Jones. 1986. Executive summary. la R. S. Jones et al., Studies of
Freshwater Inflow Effects on the Lavaca River Delta and Lavaca Bay, Texas. Final Report to
the Texas Water Development Board, Contract No. 55-61011. Tech. Rept No. TR/86-006,
University of Texas Marine Science Institute, Port Aransas, Texas, 17 p.
G-21

The primary goals of this study were to obtain an environmental assessment of the upper Lavaca Bay after
completion of the Palmetto Bend reservoir project on the Navidad River, and to document the use of the lower
river delta as a nursery area for finfish and shellfish. Systematic sampling provided good records of a large
number of variables over limited temporal (1984-1986) and spatial scales. Individual components of the
project were Nutrients, Hydrographic Parameters and Phytoplankton; Benthic Respiration Rate and
Ammonium Flux; Zooplankton; Benthos; Finfish and Shellfish; and Stable Isotopes.

Cullen, J. J. and R. G. Lane. 1986. Nutrients, hydrographic parameters and phytoplankton,
1984 - 1986. Chapter 2 ia R. S. Jones et al., Studies of Freshwater Inflow Effects on the
Lavaca River Delta and Lavaca Bay, Texas. Final Report to the Texas Water Development
Board, Contract No. 55-61011. Tech. Rept. No. TR/86-006, University of Texas Marine
Science Institute, Port Aransas, Texas, 106 p.
G-21

This component of the study was designed to observe spatial and temporal patterns of nutrients and
phytoplankton in the Lavaca Bay estuary and to interpret the observations with respect to the influence of
freshwater input on primary production. Strong patterns were found, and these could often be related to the
influence of freshwater. Sampling was inadequate to examine properly some relationships such as interannual
correlations of nutrients and salinity. The data allow instructive comparisons between a wet year and a dry year
and between sites along a salinity gradient See also Cullen and Jones (1986).

Culliton, T. J., C. M. Blackwell, D. G. Remer, T. R. Goodspeed and M. A. Warren. 1989.
Selected Characteristics in Coastal States, 1980 - 2000. NOAA's Coastal Trends Series:
Report 1. U.S. Dept. of Commerce, National Oceanic and Atmospheric Administration,
Washington, D.C., 15 p.
F-9 through G-27

This report describes some of the activities and resource uses in coastal states that affect the environmental
quality of our coasts, and provides an overview of conditions existing during the 1980s and that may exist in
the year 2000. Information is presented for land, population, housing, transportation, employment and
business establishments, water withdrawals, energy production and consumption, solid waste, wastewater
treatment plants, and hazardous waste sites.

Cunningham, R. 1980. Report on Atchafalaya-Vermilion Estuarine Complex Studies. Hydraulic
Branch, U.S. Army Corps of Engineers District, New Orleans, Louisiana, (not in hand)
' G-12, G-13

Dagg, M. J. 1988. Physical and biological responses to the passage of a winter storm in the
coastal and inner shelf waters of the northern Gulf of Mexico. Continental Shelf Res.
8(2):167-178.
G-7.1

Hydrographic and biological properties in coastal and inner shelf waters of the northern Gulf of Mexico were
monitored daily over 3 days in February 1984, immediately after the passage of a meteorological front. Strong
northerly and westerly components of the wind resulted in upwelling of high salinity inner shelf water
289
-------
containing low nitrate and chlorophyll concentrations. Low salinity coastal water, with associated high
concentrations of chlorophyll and nitrate, was transported offshore at the surface. The passage of such winter
storms at 3- to 8-d intervals could result in a periodic offshore transport of nutrient- and phytoplankton-rich
water from the coastal boundary layer to the inner shelf regions. Laboratory experiments with the neritic
copepods, Acartia tonsa and Centropagesfurcatus, showed that egg production increases dramatically within a
few hours after an increase in food availability such as might occur in inner shelf waters during upwelling
events. It is possible that winter storms and the associated redistribution of nutrients and phytoplankton have
significant direct biological consequences in the inner shelf waters of the northern Gulf of Mexico.

Dagg, M. J. N.D. Temperature, Salinity, Chlorophyll, and Nutrient Concentrations in
Terrebonne Bay, Louisiana from October 1982 to October 1983. Data Report No. 1,
Louisiana Universities Marine Consortium, Chauvin, Louisiana.
G-7.1, G-ll

Coastal and inshore continental shelf waters of Louisiana are influenced by marsh run-off, the Mississippi
River, and the open Gulf of Mexico. The interactions between freshwater run-off and oceanographic processes,
coupled with meteorological conditions that vary widely over short periods as well as seasonally, result in a
complex hydrography and therefore in a complex biological system. As the preliminary portion of a long-term ,
program designed to analyze and understand these processes, a survey of basic hydrographic, chemical, and
biological parameters was made at monthly intervals over a 1-yr period from October 1982 to October 1983.
Nine stations were occupied, transecting Terrebonne Bay and extending into the Gulf of Mexico. The purpose
of this report is to present the data from this survey.

Dagg, M. J. and T. E. Whitledge. 1991. Concentrations of copepod nauplii associated with the
nutrient-rich plume of the Mississippi River. Continental Shelf Res. 11(11): 1400-1423.
G-7.1

During spring and summer, discharge plumes of the Mississippi River were located visually by water color.
Temperature, salinity, nutrients, chlorophyll a and copepod nauplii were sampled coincidentally in a cross-
plume direction. Plume waters contained high concentrations of nitrate, silicate and chlorophyll during both
spring and summer. Nitrate was depleted before silicate during summer but not during spring. During spring,
concentrations of copepod nauplii (50-1000/1) were similar to those reported in an earlier wintertime study in
this region. Summertime concentrations of nauplii were much higher, sometimes >1000/1. Nauplii were
associated with plume waters.

Danek, L. J. and G. S. Lewbel (eds.). 1986. Southwest Florida Shelf Benthic Communities
Study Year 5 Annual Report. Vol. I - Executive Summary. Vol. II - Technical Discussion.
Vol. HI - Appendices. Contract No. 14-12-0001-30211, U.S. Dept. of the Interior, Minerals
Management Service, Gulf of Mexico OCS Regional Office, New Orleans, Louisiana.
F-15.1

The objectives of this study were to determine the potential impact of outer continental shelf oil and gas
offshore activities on live-bottom habitats and communities, which are integral components of the southwest
Florida shelf ecosystem; to produce habitat maps that show the location and distribution of various bottom
substrates; to classify broadly the biological zonation across and along the shelf, projecting the amount covered
by live/reef bottoms and the amount covered by each type of live/reef bottom; to investigate the biological
process of the southwest shelf that would provide the information needed to better assess potential impacts of
offshore development, to develop a conceptual model and impact assessment of offshore oil development This
was a 6-yr study with the results of the first five years included in this report series.

Dardeau, M. R. 1987. Structure of Soft Bottom Benthic Assemblages in Middle Perdido Bay.
Report to Alabama Dept. of Economic and Community Affairs, Contract No. ADECA-
MESC-CXM-87-5. Marine Environmental Sciences Consortium, Dauphin Island, Alabama.
G-l, F-28
290
-------
The data presented here offer a preliminary examination of community structure of macroinfeunal invertebrates
at four stations in middle Perdido Bay. The patterns of species diversity, dominance and abundance are
examined for evidence of stress and disturbance. Species composition and animal densities are compared to
those of other southeastern estuaries, the effect of benthic community structure on estuarine ecosystem
function is discussed and directions for future research are outlined.' The water column in the Bay may be
strongly stratified with the potential for hypoxic events in late summer and early fall.

Darnell, R. M. 1991. Summary and Synthesis. Chapter 15 in L M. Brooks (ed.), Mississippi-
Alabama Continental Shelf Ecosystem Study Data Summary and Synthesis. Vol. II: Technical
Narrative. OCS Study MMS 91-0063. U.S. Dept. of Interior, Minerals Management
Service, Gulf of Mexico OCS Regional Office, New Orleans, Louisiana, 862 p.
G-2.1, G-5.1, G-7.1

Includes a synthesis of the physical environment of the Mississippi and Alabama continental shelf, including
water masses and circulation, standard CTD profiles, bottom water dissolved oxygen, and water column
dissolved nutrient concentrations.

Dauer, D. M. 1984. High resilience to disturbance of an estuarine polychaete community. Bull.
Mar. Sci. 34(1): 170-174.
F-15

Massive reductions in the population densities of the polychaetous annelids of an estuarine, intertidal habitat
were quantified. Anaerobic conditions as a result of the deposition of large volumes of the green alga, Ulva
lactuca L., resulted in an 89 % decrease in the density of the 10 most common polychaete species, while only
two of the 10 species became locally extinct. One month after the peak reduction in total density, all 10
species were present, and the total polychaete community density reached the second highest value for the
study. The high resilience of the polychaete community was explained by 1) the presence of numerous
opportunistic species, 2) the possibility of adult immigration, 3) the spatial extent of the disturbance and 4)
the intensity of the disturbance.

Dauer, D. M. and J. L. Simon. 1976. Repopulation of the polychaete fauna of an intertidal habitat
following natural defaunation: Species equilibrium. Oecologia(Berl.) 22:99-117.
F-15

During summer 1971, a massive outbreak of red tide resulted in defaunation of a previously characterized
sandy, intertidal habitat in upper Old Tampa Bay, Tampa, Florida. Repopulation of the polychaete fauna was
studied from August 1971 to July 1973. A transect composed of four stations running from just below mean
high water to just below mean low water was quantitatively sampled each month for species composition,
densities of individual population, biomass, and distribution of age classes. The community is viewed as a
system in which species composition is determined primarily by the physical attributes of the area, and the
density dominance of any species is dampened by the vagaries of adult dispersal and larval settlement Such a
system could be used to explain the relatively large number of species that belong to the same trophic type and
yet occupy the same habitat.

Dauphin Island Sea Lab. 1983. Analysis of an Environmental Monitoring Program, Theodore
Ship Channel and Barge Channel Extension, Mobile Bay, Alabama. Vol. I and n. Prepared
for Mobile District Corps of Engineers, Contract No. DACW01-80-C-0264. Technical
Report No. 83-003, Dauphin Island Sea Lab, Dauphin Island, Alabama.
G-2

Environmental assessment for the impacts from spoil island construction west of the Mobile Ship Channel
and south of Hollingers Island Channel to provide access to the Theodore Industrial Park.
291
-------
Day, Jr., J. W., D. D. Culley, Jr., R. E. Turner and A. J. Mumphrey, Jr. (eds.). 1979.
Environmental Conditions in the Louisiana Coastal Zone. Proceedings of the Third Coastal
Marsh and Estuary Management Symposium, March 6-7, 1978, Baton Rouge, Louisiana.
Division of Continuing Education, Louisiana State University, Baton Rouge, Louisiana, 511
P-
G-7 through G-15

This volume is the third in a series concerned with marsh and estuary management. The impression that one
gets from this volume is that there are serious environmental problems in coastal Louisiana. Further, it seems
that these problems are not isolated from each other. Most of them are connected in indirect and cumulative
ways. What are isolated and fragmented are the causes of these problems as well as many of the attempts to
address them. We must realize that man and estuary in South Louisiana are part of a single unified system.
Unless environmental problems are addressed within this context, it seems likely that we will achieve, at best,
partial solutions. The most important changes that must take place are social, ethical and philosophical
changes.

Degrove, B. D. 1980. Caloosahatchee River Intensive Survey Documentation. Water Quality
Technical Series Vol. 1, No. 32, Southwest Florida Regional Planning Council, Ft. Myers,
Florida, (not in hand)
F-12

Delfino, J. J., D. L. Frazier and J. L. Nepshinsky. 1984. Contaminants in Florida's Coastal
Zone: A Review of Present Knowledge and Proposed Research Strategies. A Summary of a
Workshop held April 5-6, 1984 in Gainesville, Florida and a Literature Review. Rept. No.
62, Sea Grant Project No. IR-83-13, Florida Sea Grant College, University of Florida,
Gainesville, Florida, 176 p.
F-9 through F-28

The objectives of this project were two-fold: to hold a workshop to discuss research issues and priorities with
representatives from Florida's scientific, regulatory and private organizations; and to conduct a literature review
for research related to the topic of contaminants in Florida's coastal zone. Both of these objectives were met,
and the results of the efforts expended in meeting them appear in this report. A list of recommendations are
included.

Dennis, G. D., T. J. Bright and C. A. Shalan. 1984. Offshore Oceanographic and Environmental
Monitoring Services for the Strategic Petroleum Reserve. Annotated Bibliography of
Hypoxia and Other Oxygen-Depleted Literature on the Marine Environment Final Report to
DOE, Strategic Petroleum Reserve Project Management Office, Contract No. DOE-AC96-
83PO10850. Texas A&M University, Texas A&M Research Foundation, College Station,
Texas, 46 p.
F-15, G-2, G-7.1, G-15, G-16, G-17, G-27

The references compiled herein were acquired principally through Automated Information Retrieval Service
(AIRS) at the Sterling C. Evans Library of Texas A&M University, College Station, Texas. All references
were reviewed for their content pertaining to the subject of hypoxia. Most annotations are the journal abstract
of the paper with additional information pertinent to hypoxia. Papers without abstracts are summarized with
special reference to their hypoxia information content.

DeRouen, L. R., R. W. Hann, Jr., D. M. Casserly and C. P. Giammona. 1982. West Hackberry
Brine Disposal Project Pre-Discharge Characterization. Final Report to DOE, Strategic
Petroleum Reserve Project Management Office, Contract No. DOE-AC96-80P01288.
McNeese State University, Lake Charles, Louisiana. Texas A&M University, Texas A&M
Research Foundation, College Station, Texas.
G-7.1, G-15, G-16
292
-------
Environmental baseline monitoring of the southwestern Louisiana continental shelf off Holly Beach in the
vicinity of the proposed brine discharge for the West Hackbeny site of the Dept. of Energy Strategic Petroleum
Reserve. Data are for February, March and April 1981.

DeRouen, L. R., R. W. Harm, Jr., D. M. Casserly, C. P. Giammona and V. J. Lascara (eds.).
1983. West Hackberry Strategic Petroleum Reserve Site Brine Disposal Monitoring. Vol. I:
Executive Summary. Vol. II: Physical and Chemical Oceanography. Year 1 Report. Final
Report to DOE, Strategic Petroleum Reserve Project Management Office, Contract No. DOE-
AC96-80P010288. McNeese State University, Lake Charles, Louisiana. Texas A&M
University, Texas A&M Research Foundation, College Station, Texas.
G-7.1

Data from monthly hydrographic surveys of the coastal waters off Holly Beach, Louisiana in conjunction with
monitoring of the DepL of Energy Strategic Petroleum Reserve brine disposal from West Hackberry. Field
data cover January 1981 through April 1982.

Diener, R. A. 1975. Cooperative Gulf of Mexico Estuarine Inventory and Study - Texas: Area
Description. NOAA Technical Report NMFS CIRC-393, U.S. Dept of Commerce, National
Oceanic and Atmospheric Administration, National Marine Fisheries Service, Seattle,
Washington, 128 p.
G-16 through G-26

Seven Texas estuarine areas are described in terms of their dimensions; major vegetation types; geology and
geological history; drainage basins and stream discharge records; hydrological, biological and benthic
properties; populations and economic development; pollution; and navigation projects. These areas include the
Sabine Lake, Galveston Bay, Matagorda Bay-Brazos River Delta, San Antonio Bay, Copano-Aransas Bay,
Corpus Christi Bay, and the Laguna Madre. A list of pertinent literature is also presented.

Dinnel, S. P. 1984. Distribution and Residence Time of Freshwater on the West Louisiana and
Texas Continental Shelves. M.S. Thesis, Louisiana State University, Baton Rouge,
Louisiana, 89 p.
G-7.1, G-27

Hydrographic data collected on monthly cruises over the West Louisiana and Texas Shelves during 1963-1965
were analyzed, and the volume of fresh water relative to a reference salinity computed for each cruise. The
freshwater volume on this shelf system exhibits an annual cycle that is dominated and initiated by the spring
floods of the Mississippi and Atchafalaya Rivers. The shelf freshwater volume is largest one to two months
after peak spring discharge and gradually decreases throughout the rest of the year to the annual low freshwater
volume just prior to the next spring flood. The distribution of fresh water on the shelf is described in a series
of maps made for individual cruises. Distribution patterns are present in each of the study years, but the
magnitude of the spring flood discharge determines the strength of the distribution patterns.
Dinnel, S. P. and W. J. Wiseman, Jr. 1986.
Continental Shelf Res. 6(6):765-784.
G-7.1, G-27
Fresh water on the Louisiana and Texas shelf.
Hydrographic data collected on monthly cruises over the West Louisiana and Texas shelf from 1963 to 1965
were analyzed and the volume of fresh water on the shelf was estimated for each data set. The freshwater
volume exhibits an annual cycle that is dominated by the spring flood of the Mississippi and Atchafalaya
Rivers. During the winter, shelf freshwater content is low, with the highest content appearing as a
discontinuous band along the inner,shelf, hi summer an isolated high-content region is present in the center of
the shelf. This high-content region dissipates and the pattern migrates toward the southeast in the late
summer. By late fall the winter distribution is again present
293
-------
Donohoe, R. and W. Calhoun. 1982. Synopsis of the Mobile Bay - Mississippi Sound Research
Review. Proceedings of a Conference, February 4-5, 1982, Mobile, Alabama. Publ. No.
MASPG-81-026, Mississippi-Alabama Sea Grant Consortium, Ocean Springs, Mississippi,
19 p.
G-2, G-2.2, G-2.3

To open avenues of communication between researchers, the Mississippi-Alabama Sea Grant Consortium, in
conjuction with the Alabama Sea Grant Advisory Service, sponsored a workshop for researchers of the Mobile
Bay Mississippi Sound Region. Investigators had the opportunity to review the current status of other
projects, .to determine what data were presently available from other researchers, and to discuss areas in which
work still is needed to be done. This review is a significant effort to define status of knowledge in selected
disciplines and geographic areas of this dynamically developing resource.

Dooris, P. M. and G. M. Dooris. 1985. Surface flows to Tampa Bay: Quantity and quality
aspects. Pages 88-106 in S. F. Treat, J. L. Simon, R. R. Lewis, III and R. L. Whitman, Jr.
(eds ) Proceedings of the Tampa Bay Area Scientific Information Symposium, May 1982.
Sea Grant Project No. IR/82-2. Grant No. NA80AA-D-00038. Florida Sea Grant College,
Report No. 65, Burgess Publishing Co., Minneapolis, Minnesota.
F-15

The streams discharging to the Bay are discussed with respect to their flow characteristics and chemical quality.
Emphasis is placed on well-defined surface water bodies, leaving undiscussed other flows such as sewage plant
effluent and stormwater runoff. There are 20 named rivers and streams with discharge to Tampa Bay. Long-
term data on discharge and chemical quality are available for some, such as the Hillsborough, Alafia, and Little
Manatee Rivers. Other streams, particularly those entering the Bay from Pinellas County have scanty or non-
existent data.

Doyle, L. J. 1985. A short summary of the geology of Tampa Bay. Pages 27-32 in S. F. Treat,
J. L. Simon, R. R. Lewis, HI and R. L. Whitman, Jr. (eds.), Proceedings of the Tampa Bay
Area Scientific Information Symposium, May 1982. Sea Grant Project No. IR/82-2. Grant
No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65, Burgess Publishing
Co., Minneapolis, Minnesota.
F-15

From the body of data, the refereed literature (where there is surprisingly sparse representation), the grey
literature, and from a series of seismic lines and vibracores that have been obtained, the author has distilled this
summary of the geology of Tampa Bay.

Dragovich, A., J. H. Finucane and B. Z. May. 1961. Counts of red tide organisms,
Gymnodinium breve, and associated oceanographic data from Florida west coast, 1957-59.
U.S. Fish and Wildlife Service, Special Scientific Report-Fisheries No. 369. U.S. Dept. of
the Interior, Fish and Wildlife Service, Washington, D. C., 175 p.
F-9, F-10, F-10.1, F-ll, F-12, F-13, F-14, F-15, F-15.1

During the period this report covers, two outbreaks of red tide occurred. The first, from the end of September
through December 1957, occurred chiefly in coastal waters and bays from Anclote Key south to the Shark
River in the Florida Everglades. The second outbreak occurred September through December 1959 in the
coastal area between St. Petersburg Beach and Cape Romano. Both outbreaks caused heavy fish mortalities.

Dragovich, A., J. H. Finucane, J. A. Kelly, Jr. and B. Z. May. 1963. Counts of Red-Tide
Organisms, Gymnodinium breve, and Associated Oceanographic Data from Florida West
Coast, 1960-61. U.S. Fish and Wildlife Service Special Scientific Report-Fisheries No.
455. U.S. Dept. of the Interior, Fish and Wildlife Service, Washington, D. C.
F-15, F-15.1
294
-------
This report presents counts of the red-tide organism, Gymnodium breve, and associated oceaaographic data for
the period January 1960 to August 1961. During this period two minor outbreaks of red tide occurred. The
first was in March 1960 and the second during July and August of the same year. Both of these outbreaks were
confined mainly to an area from the mouth of Tampa Bay to 35 miles offshore, and no fish mortality was
observed.

Dragovich, A., J. A. Kelly, Jr. and J. H. Finucane. 1966. Hydrographic Observations of Tampa
Bay, Charlotte Harbor, Pine Island Sound, Florida, and Adjacent Waters of the Gulf of
Mexico, February 1964 through February 1965. Data Report No. 13, U.S. Dept. of the
Interior, Fish and Wildlife Service, Washington, D.C., 72 p.
F-13, F-15, F-15.1

See Saloman (1974).
Drake, T. 1982. Oxygen depletion as influenced by the Mississippi River outflow. Abstr. for
Proceedings of the Third Annual Gulf of Mexico Information Transfer Meeting, August 24-
26, 1982, New Orleans, Louisiana. U.S. Dept of the Interior, Minerals Management
Service, Outer Continental Shelf Office, New Orleans, Louisiana.
G-7.1
This paper characterizes the lower Mississippi River with respect to oxygenation and reoxygenation, reviews
historical and future trends, describes effects of dredging, and outlines the U.S. Army Corps of Engineers
project to deepen and make other navigational improvements to the river. Conclusions as to the possible
effects of this project and conclusive chemical/biochemical analysis of the water cannot be made until further
information on the interaction of physical and chemical forces is gathered. Samples are chiefly from the
Venice, Louisiana gauging station.

Drew, R. D., N. S. Schomer and S. H. Wolfe, (in review). An Ecological Characterization of the
Tampa Watershed. Biological Report No. 87, U.S. Dept. of the Interior, Fish and Wildlife
Service, Washington, D.C. (not in hand)
F-15

Dugan, P. J. and R. J. Livingston. 1982. Long-term variation of macroinvertebrate assemblages
in Apalachee Bay, Florida. Estuarine Coastal Shelf Sci. 14(4):391-403.
F-22

Trawlable epibenthic macroinvertebrates were sampled monthly from June 1972 to May 1979 to compare
invertebrate assemblages in polluted (Fenholloway drainage) and unpolluted (Econfina drainage) portions of
Apalachee Bay. Decapod crustaceans comprised 95 % of the total number of individuals collected. The relative
abundance of dominant species and species richness in the two estuaries were similar, although the number of
individuals collected in the Econfina area was always at least twice that taken in the Fenholloway. This
difference was attributed to the greater seagrass biomass in the Econfina estuary. Comparisons of the
constancy of species composition over the 7-year period and species rank changes following a pollution
abatement program in the Fenholloway system indicated enhanced species persistence in the unpolluted area.
Overall, despite considerable seasonal variability of physico-chemical and biological characteristics, there was
long-term stability of key invertebrate populations in the unpolluted estuarine system.

Dugas, R. J. 1975. Variation in Day-Night Trawl Catches in Vermilion Bay, Louisiana. Tech.
Bull. No. 14, Louisiana Wildlife and Fisheries Commission, New Orleans, Louisiana, 13 p.
G-13

A total of 1733 organisms, representing 22 species, was taken in trawl samples collected periodically over a
24-h period, on five different occasions near the State Wildlife Refuge on Fearman Bayou, Vermilion Bay,
Louisiana. Simultaneously, the environmental factors of dissolved oxygen, surface temperature, salinity, light
295
-------
intensity, turbidity and pH were recorded; tank observations were conducted on several of the captured animals.
Differences between day-night ratios for several species are presented.

Dugas R J J W Tarver and L. S. Nutwell. 1974. The Mollusk Communities of Lakes
Pontchartrain and Maurepas, Louisiana. Tech. Bull. No. 10, Louisiana Wild Life and
Fisheries Commission, New Orleans, Louisiana, 13 p.
G-7

Densities and distribution of the brackish-water mollusk communities of Lake Pontchartrain and Lake
Maurepas, Louisiana, are outlined. Lakes Pontchartrain and Maurepas were divided into 99 3-mi2 grids with
two Peterson grab samples taken in each grid. The results of these 198 samples, including 10 molluscan
species, are reported, as well as some apparent trends in the two lakes.

Ehler C. N., D. J. Basta and T. F. LaPointe. 1985. Gulf of Mexico Coastal and Ocean Zones
Strategic Assessment: Data Atlas. U.S. Dept. of Commerce, National Oceanic and
Atmospheric Administration, National Ocean Survey, Washington, D.C.
F-9 through G-27

El-Saved, S. Z., W. M. Sackett, L. M. Jeffrey, A. D. Fredericks, R. P. Saunders, P. S. Conger,
G A Fryxell, K. A. Steidinger and S. A. Earle. 1972. Folio 22. Chemistry, primary
productivity, and benthic algae of the Gulf of Mexico. Pages 1-29 in V. C. Bushnell (ed.),
Serial Atlas of the Marine Environment. American Geographical Society, New York.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

This folio sammarizes the knowledge of the chemistry of seawater, its primary production, and the pelagic and
benthic flora of the Gulf of Mexico based on various programs of the Dept. of Oceanography of Texas A&M
Univ. The sections summarize the physical and chemical constituents of the Gulf, the primary production and
standing crop of phytoplankton, and the species composition of two of the main primary producers (the
diatoms and dinoflagellates). Checklists of all species known to occur in the Gulf are given in appendices. A
final section summarizes benthic algae.

Elder, J. F. and H. C. Mattraw, Jr. 1982. Riverine transport of nutrients and detritus to the
Apalachicola Bay estuary, Florida. Water Resour. Bull. 18(5):849-856.
F-24

Fifteen percent of the area is a dense bottom-land hardwood forest that is periodically flooded. The annual leaf-
Jitter fall from the flood-plain trees is a potential source of nutrients and detritus that eventually can flow into
the Bay. Transport of such material is dependent on the periodic inundation of the flood plain. Flood
characteristics, such as prior hydrologic conditions, extent, and timing, are important in determining the
amount and forms of materials transported. Nutrient concentration varied little with discharge in the 1980
spring flood, but it accounted for 53,60,48, and 56 % of the annual flux of total organic carbon, paniculate
organic carbon, total nitrogen, and total phosphorus, respectively. In 1980, the flood peaks, rather than the
rise or recession, accounted for maximum nutrient and detritus transport.

Elder, J. F., S. D. Flagg and H. C. Mattraw, Jr. 1986. Hydrology and Ecology of the
Apalachicola River, Honda: A Summary of the River Quality Assessment. Water-Supply
Paper No. 2196-D, U.S. Dept. of the Interior, Geological Survey, Tallahassee, Florida, 46
P-
F-24

During 1979-1981, The U.S. Geological Survey conducted a large-scale study of this river, which emphasized
interrelations among hydrodynamics, the flood-plain forest, and the nutrient-detritus flow through the river
system to the estuary. This report summarizes major findings of the study. Data on accumulation of toxic
substances in sediments and benthic organisms in the river were also collected. Water and nutrient budgets
296
-------
based on data collected during the river assessment study indicate the relative importance of various inputs and
outputs in the system. Whatever management decisions are made, they should take into account the impact on
the natural flooding cycle. Permanent, substantial changes in the natural flooding cycle would likely induce
concomitant changes in the flood-plain environment and in the nutrient and detritus yield to the estuary.

Eleuterius, C. K. 1976a. Mississippi Sound. Salinity Distribution and Indicated Flow Patterns.
Sea Grant Publ. No. MASGP-76-023, Mississippi-Alabama Sea Grant Consortium, Gulf
Coast Research Laboratory, Ocean Springs, Mississippi, 128 p.
G-2.3, G-3, G-4, G-5, G-6

This study of the circulation and salinity regime of Mississippi Sound describes the general patterns of flow
indicated by the horizontal distribution of salinity at selected depth levels and the variability of salinity through
the year. An appendix containing tables of salinity is included. Particular attention was given to certain areas
or situations that the author felt warranted it in view of various activities planned or ongoing in the Sound,
including those associated with disposal of domestic waste, dredging, fisheries, heavy industry and biological
studies.

Eleuterius, C. K. 1976b. Mississippi Sound. Temporal and Spatial Distribution of Nutrients.
Sea Grant Publ. No. MASGP-76-024, Mississippi-Alabama Sea Grant Consortium, Gulf
Coast Research Laboratory, Ocean Springs, Mississippi, 48 p.
G-2.3

In a general manner, the levels of nutrients declined and became less erratic westward through Mississippi
Sound. In addition, with one exception, there was a seaward decline in the nutrient levels. The primary
sources of nutrients in the Sound are Pascagoula River, Bayou Casotte, Biloxi Bay and Pearl River. To
properly monitor and manage the estuarine waters of Mississippi Sound, a comprehensive study of the Sound's
chemistry is necessary. The emphasis in such a study should be on those parameters that are known to have a
sizable effect on the biota.

Eleuterius, C. K. 1978a. Classification of Mississippi Sound as to estuary type by vertical
salinity structure. J. Miss. Acad. Sci. 23:23-32.
G-2.3
To classify Mississippi Sound as to estuarine type based on vertical salinity structure, 2421 surface-bottom
pairs of salinity measurements made at 90 stations within the Sound during 4 April 1973 through 12 April
1977 were used. Ratios were obtained for surface to bottom salinity for all paired-observations at all stations.
The station data were then sorted by depths at mean low water into four groups: < 5 ft; 5 ft < depth < 10 ft; 10
ft < depth < 15 ft; > 15 ft. The first group of stations showed considerable variability during the period
January through June. From July through December, the range in ratios became much smaller, and the values
approached 1 reflecting a more uniform water column with decreasing river flow. A greater variability was
noted in the second, third and fourth groups than in the first; however, the same trend was present. Although
the data verified that the Sound does become locally stratified, the preponderance of observations showed that it
generally fluctuates between a partially mixed and well-mixed estuary.
Eleuterius, C. K.
6(2):179-181.
G-2.3
1978b. Geographical Definition of Mississippi Sound. Gulf Res. Rep.
Boundaries for Mississippi Sound are determined by application of definitions, established surveying practices
and observations of the physical processes of the area. U.S. Coast and Geodetic charts 1266 (1972 edition),
1267 (1972 edition) and 1268 (1974 edition) were used in ascertaining the boundaries. These boundaries
provide a formal geographical definition for Mississippi Sound.
297
-------
Eleuterius C. K. 1979. Hydrology of Mississippi Sound North of Petit Bois Pass. Prepared for
Mississippi Marine Resources Council. Project No. CO-ST-78-016, Gulf Coast Research
Laboratory, Ocean Springs, Mississippi, 54 p.
G-2.3

The objective of this study was to determine the seasonal norms and variations in levels of several parameters
for the period of sampling. The parameters measured were water temperature, salinity, pH, dissolved oxygen,
nitrite-nitrogen, nitrate-nitrogen, orthophosphate and total phosphate. The hydrology of the area is highly
variable. Water temperatures approach uniformity areally and throughout the water column during summer. In
late summer and fall, salinity reaches maximum levels with minimum variation. Mean levels of pH were
found highest in winter and lowest in late summer and early fall. Dissolved oxygen was highest in whiter and
lowest hi summer. Nitrite-nitrogen was at lowest levels during winter and summer with the maximum
occurring in the spring. Nitrate-nitrogen was highest in winter and spring with summer and fall levels being
much lower. Orthophosphate was highest during spring and summer. Total phosphate reached maximum
levels in summer with fall and winter showing the lowest levels.

Eleuterius, C. K. and S. L. Beaugez. 1981. Mississippi Sound: A Hydrographic and Climatic
Atlas. Publ. No. MASGP-79-009, Mississippi-Alabama Sea Grant Consortium, Gulf Coast
Research Laboratory, Ocean Springs, Mississippi, 135 p.
G-2.1, G-2.2, G-2.3

Eleuterius, L. H., H. M. Perry, C. K. Eleuterius, J. Warren and J. Caldwell. 1981. Causative
analysis on a nearshore bloom of Oscillatoria erythraea (Trichodesmiwn) in the northern Gulf
of Mexico. Northeast Gulf Sci. 5(1):1-11.
G-2.1, G-2.2, G-2.3

Physical, chemical, and biological characteristics that preceded and caused a bloom of Oscillatoria erythraea
(commonly known as trichodesmium) hi coastal waters of Mississippi and adjacent waters of the Gulf of
Mexico are described. This is the first report of the blue-green alga occurring in high density near the mainland
and in a predominantly estuarine area of the northern Gulf of Mexico. The alga occurred in patches with the
greatest concentration near the surface. Some entrapment of zooplankton in the dense algal mass was
observed, but most of the zooplankton was diverse and unharmed. Harmful effects of the algal bloom on larger
animals were not observed nor believed to have occurred.

Environmental Protection Agency. 1978. National Water Quality Inventory. 1977 Report to
Congress. Publ. No. EPA-440/4-78-001, U.S. Environmental Protection Agency, Office of
Water Planning and Standards, Washington, D.C.
F-9 through G-27

A national overview of water quality as reported by the individual State reports for Section 305(b) of PL 92-
500.

Environmental Protection Agency. 1984. National Water Quality Inventory. 1982 Report to
Congress. Publ. No. EPA-440/2-84-006, U.S. Environmental Protection Agency, Office of
Water Planning and Standards, Washington, D.C.
F-9 through G-27

A national overview of water quality as reported by the individual State reports for Section 305(b) of PL 92-
500.

Environmental Protection Agency. 1988. Sediment Deficit and Saltwater Intrusion in Barataria
Basin, Louisiana. Draft Report to Office of Marine and Estuarine Protection. EPA, Region
VI, Dallas, Texas.
G-10
298
-------
Coastal Louisiana wetlands are vanishing at a rate of 40-60 mi^ each year. The losses arise from a
combination of natural processes and human activities that include flood control practices, impoundment,
dredging, channelization, subsidence, erosion, and sea level rise. The end result of these compounding
influences has been a tremendous reduction of sediment and freshwater allocations into Barataria Basin. The
fresh water is being channeled largely put the Mississippi River passes and the river's heavy load of sediments
is being funneled into deep waters in the Gulf of Mexico. As a result, the swamps and marshes in the delta
plain are experiencing a sediment deficit and pathways are opened for the inland advance of saline waters. As
the substrate subsides and the vegetation is stressed, the wetlands are converted to open water. Management
strategies are being developed to restore these wetlands by altering the flow of the water and sediments that feed
and fuel the estuary.

Environmental Protection Agency. 1990. Draft Environmental Impact Statement for the
Designation of an Ocean Dredged Material Disposal Site Located Offshore Pascagoula,
Mississippi. EPA, Region IV, Atlanta, Georgia, 464 p.
G-5.1

The proposed Ocean Dredged Material Disposal Site (ODMDS) will encompass part or all of the former
interim disposal site and an adjacent charted former disposal site. The need for this ocean disposal is primarily
based on the lack of economically, engineeringly, and environmentally feasible alternatives for the disposal of
the projected quantities of dredged material. The Pascagoula ODMDS is restricted to the disposal of dredged
material from the Mississippi Sound area that meets the Ocean Dumping Criteria. No grain size restrictions
have been applied to the proposed ODMDS.

Estabrook, R. H. 1973. Phytoplankton Ecology and Hydrography of Apalachicola Bay. M.S.
Thesis, Florida State University, Tallahassee, Florida, 163 p.
F-24

A year-long study of phytoplankton was conducted from October 1972 to September 1973, with preliminary
studies beginning in July 1972. Productivity, yielding 371 gC/m2/yr, generally followed water temperature,
although peaks occurred in the late spring and fall. Average chlorophyll a was about 7 mg Chi a/m^. Nitrate
values varied greatly over the year. Ammonia concentrations were fairly constant Orthophosphate values
were generally low. Silicate values ranged from 400 to 2500 ug/1 in response to seasonal salinity changes.
Diatoms were generally dominant throughout the year in the netplankton. Bioassays indicated that nutrients
were generally in sufficient quantities for most of the year, but during times of quiescent water in the late
summer, phosphate could be limiting.

Estevez, E. D. (ed.). 1989. Tampa and Sarasota Bays: Issues, Resources, Status, and
Management. Proceedings of a Seminar, December 10, 1987, Washington,, D.C. NOAA
Estuary-of-the-Month Seminar Series No. 11, U.S. Dept. of Commerce, National Oceanic
and Atmospheric Administration, Estuarine Programs Office, Washington, D.C., 215 p.
F-14.F-15

A series of seminars presented as part of the Estuarine Programs Office of the National Oceanic and
Atmospheric Administration as part of the continuing series held with the objective of bring to public
attention the important research and management issues of the Nation's estuaries. Participants presented
historical and scientific overviews of the study area, followed by an examination of management issues.

Estevez, E. D. and J. Merriam. 1989. Resource status and management issues of Sarasota Bay,
Florida. Pages 186-206 in E. D. Estevez (ed.), Tampa and Sarasota Bays: Issues,
Resources, Status, and Management. Proceedings of a Seminar, December 10, 1987,
Washington, D.C. NOAA Estuary-of-the-Month Seminar Series No. 11, U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, Estuarine Programs Office,
Washington, D.C.
299
-------
F-15

The Sarasota Bay area is experiencing rapid population growth, although most of its development having
adverse environmental impact has occurred in the last 50 years. Barrier islands are completely developed as
residential, light commercial, and tourist areas. Nearly the entire upland watershed of Sarasota Bay is also
developed, mostly as suburban residential and commercial areas. There are no heavy industries in the
watershed.'and the amount of agricultural land is low and decreasing due to urbanization. The Bay supports an
extensive recreational industry and is showing signs of overuse.

Estevez E D., J. Miller and J. Morris. 1984. Charlotte Harbor Estuarine Ecosystem Complex
and The Peace River. Vol. I. A Review of Scientific Information. Southwest Flonda
Regional Planning Council, Ft. Meyers, Florida, 370 p.
F-13

The purposes of this review are to: 1) compile information on these areas as a ready reference for local,
regional and state governments; 2) develop the first composite description of the Peace River and the Charlotte
Harbor complex of estuaries; and 3) identify information needs useful in resource management and provide
recommendations for future study.

Fagerburg T L. 1990. Mississippi River - Gulf Outlet, Louisiana. Field Data Report. Final
Report. Tech. Rept. No. HL-90-7, U.S. Army Engineers District, New Orleans, Louisiana,
172 p.
G-8.1

Water levels, current speeds and directions, salinities, and suspended sediment concentrations were measured in
the Mississippi River-Gulf Outlet Canal, New Orleans, Louisiana, in October and November 1988. The
prototype data were collected as part of a study to incorporate these data in a numerical model for determination
of shoaling rates. This report describes the equipment and procedures used in the data acquisition and presents
tables, plots, and summaries of all the data collected. Attempts to correlate ground truth suspended sediment
data with satellite data were unsuccessful due to cloud cover during the periods data were obtained.

Fanning, K. A. and L. M. Bell. 1985. Nutrients in Tampa Bay. Pages 109-129 in S. F. Treat, J.
L. Simon, R. R. Lewis, m and R. L. Whitman, Jr. (eds.), Proceedings of the Tampa Bay
Area Scientific Information Symposium, May 1982. Sea Grant Project No. IR/82-2. Grant
No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65, Burgess Publishing
Co., Minneapolis, Minnesota.
F-15

Several nutrients are considered in this review. They were chosen because they are necessary for growth of
most autotrophs or heterotrophs and because they might occasionally be in short supply. Members of the
nitrogen system are the most interesting in the Bay, particularly ammonia. Also considered are nitrate and
nitrite. Phosphate must be discussed because of its abundance in the Bay. Dissolved silica is found in the
Bay, as in many estuaries, although there is little evidence that it is ever limiting. However, diatoms are
significant components of the Bay phytoplankton.

Fanning, K. A., K. L. Carder and P. R. Betzer. 1982. Sediment resuspension by coastal waters:
A potential mechanism for nutrient re-cycling on the ocean's margins. Deep Sea Res.
29(8A):953-965.
G-2.1, G-5.1, G-7.1, F-15.1

Nutrient profiles from the continental shelf of the northeastern Gulf of Mexico indicated considerable near-
bottom enrichment in silica and nitrate above coarse sediments east of the Mississippi delta. In contrast, near-
bottom waters of the carbonate-rich West Florida shelf showed no such enrichments. Most of the nutrient
increase appeared to come from previously deposited sediments in the early stages of resuspension. Using the
300
-------
ratios of nutrients released to sediments resuspended, calculations indicate that resuspension of as little as 1
mm of shelf sediment could intermittently augment overlying productivity by as much as 100 to 200 %.
Thus, resuspension may accelerate nutrient recycling on continental margins.

Farrell, D. H. 1974. Benthic Ecology of Timbalier Bay, Louisiana, and Adjacent Offshore Areas
in Relation to Oil Production. Ph.D. Dissertation, Florida State University, Tallahassee,
Florida, 164 p.
G-7.1, G-ll

This investigation examines species diversity, faunal similarities, and biomass relations of benthic
communities in Timbalier Bay and offshore Louisiana. A marked oxygen diminuation occurred in the offshore
region during July 1973 and was apparently limiting to most benthic species. The low dissolved oxygen
levels apparently resulted from natural causes and probably were caused by the unusually high Mississippi
River flood during the previous spring. Sampling was designed to examine possible long-term deleterious
effects of oil platforms on the benthic environment, and no abnormal environmental stress could be attributed
to the petroleum structures.

Federal Water Pollution Control Administration. 1970. Effects of Pollution on Water Quality,
Perdido River and Bay, Alabama and Florida. U.S. Dept. of the Interior, Federal Water
Pollution Control Administration, Southeast Water Laboratory, Technical Services Program,
Athens, Georgia, 33 p.
G-l, F-28

An investigation of waste sources and a detailed study of the Bay and its major tributaries were conducted
during September 9-17,1969. This report presents an evaluation of the data collected during this study. The
inadequately treated waste effluent from the St. Regis Paper Company at Cantonment, Florida is the major
cause of the low dissolved oxygen, unsightly foam, excessive sludge deposits, and increased lignin in Perdido
Bay and River, as well as degraded water quality in Eleven Mile Creek. Water quality problems in the mouth
of Bayou Marcus are caused by the collective discharges to the Bayou from six small treatment facilities, the
most significant of which are the Mayfair, Montclair, and Avondale plants.

Fehring, W. K. 1985. History of the port of Tampa. Pages 512-524 in S. F. Treat, J. L. Simon,
R. R. Lewis, in and R. L. Whitman, Jr. (eds.), Proceedings of the Tampa Bay Area
Scientific Information Symposium, May 1982. Sea Grant Project No. IR/82-2. Grant No.
NA80AA-D-00038. Florida Sea Grant College, Report No. 65, Burgess Publishing Co.,
Minneapolis, Minnesota.
F-15

The Port of Tampa has served as a vital transportation link for the west central Florida region since the early
19th century. It evolved initially as a gateway for agricultural products flowing to and from Cuba.
Improvements to the natural harbor began with the discovery of phosphate in the region and the first
Congressional authorization in the l-880s. During the past 100 years, channel dimensions have repeatedly
been enlarged, the size of ships calling on the port has increased, and the annual tonnage transiting the Port has
increased from 1 million tons in 1920 to SO million tons in 1980. The several separate private and public
improvement projects which have culminated in the current 43-ft project are traced, including some analysis of
disposal strategies.

Fernald, E. A. (ed.). 1981. Atlas of Florida. Florida State University Foundation, Tallahassee,
Florida, 276 p.
F-9 through F-28

Fernald, E. A. and D. J. Patton (eds.). 1984. Water Resources Atlas of Florida. Institute of
Science and Public Affairs, Florida State University, Tallahassee, Florida, 291 p.
F-9 through F-28
301
-------
Knucane, J. H. 1964. Distribution and Seasonal Occurrence of Gymnodiwn breve on the West
Coast of Florida, 1954-57. U.S. Fish and Wildlife Service, Special Scientific Report--
Fisheries No. 487. U.S. Dept. of the Interior, Fish and Wildlife Service, Washington, D. C.
F-9, F-10, F-10.1, F-ll, F-12, F-13, F-14, F-15, F-15.1

The distribution and seasonal occurrence of Gymnodinium breve was recorded for a 4-yr period in estuarine and
neritic waters along the Florida west coast G. breve was found throughout the year in the area from Tarpon
Springs south to the Florida Everglades. Blooms of this dinoflagellate occurred mainly from September
through December in 1954 and 1957. Essentially, both 1955 and 1956 were not red-tide years.

Finucane, J. H. and A. Dragovich. 1966. Hydrographic Observations in Tampa Bay, Florida,
and the Adjacent Gulf of Mexico - 1963. Data Report No. 14, U.S. Dept. of the Interior,
Fish and Wildlife Service, Washington, D.C., 80 p.
F-15, F-15.1

See Saloman (1974).

Fitzhugh, J. K. 1983. Factors Determining the Distribution and Abundance of Polychaetous
Annelids on the Central North Gulf of Mexico Continental Shelf. M.S. Thesis, Texas A&M
University, Galveston, Texas, 286 p.
G-7.1

Polychaete samples (830 total) collected on the Louisiana continental shelf during the Central Gulf Outer
Continental Shelf study were reanalyzed. Stations were located around four primary platforms, 16 secondary
platforms and four control sites. The objectives of this study were to determine factors regulating polychaete
distribution and if effects from petroleum-related activities were present No indication was seen of polychaete
distribution being determined by production platform presence. The major trophic group on the shelf are
motile deposit-feeders. The lack of a more diverse trophic structure is probably due to the fine nature of
sediments and their unstable nature.

Hannery, M. S. 1989. Tampa and Sarasota Bays' watersheds and tributaries. Pages 18-48 in E.
D. Estevez (ed.), Tampa and Sarasota Bays: Issues, Resources, Status, and Management.
Proceedings of a Seminar, December 10, 1987, Washington, D.C. NOAA Estuary-of-the-
Month Seminar Series No. 11, U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, Estuarine Programs Office, Washington, D.C.
F-14, F-15

In this paper, the status of tributaries to Tampa and Sarasota Bays is reviewed. Emphasis is placed on water
quality and seasonal quantities of flow and how these characteristics are related to land use and other human
impacts on the watersheds. A brief synopsis of regional meteorological conditions affecting runoff is also
presented.

Fleeger, J. W., W. B. Sikora and J. P. Sikora. 1983. Spatial and long-term temporal variation of
meiobenthic-hyperbenthic copepods in Lake Pontchartrain, Louisiana. Estuarine Coastal
Shelf Sci. 16(4):441-453.
G-7

The distribution and abundance of the meiobenthic-hyperbenthic copepods of Lake Pontchartrain were
characterized monthly from August 1978 to August 1979. Ten stations, all with water depth >2 m, were
established and sampled quantitatively by removing four benthic subsamples (containing as much as 25 cm
overlying water) from replicated box cores. Averaged across stations over time, total copepod densities ranged
from 31-89 X 10 cm"2. Only 15 copepod species were identified from benthic samples. The copepod
assemblage in Pontchartrain differs from all other known benthic assemblages in that the species composition
302
-------
is dominated by species that are often associated with the water column; true infaunal species are rare or found
in reduced abundance. Four species comprised 90 % of all individuals collected. Cluster analysis reveals
diffuse seasonal grouping of stations for all seasons except fall, with spatial groupings from the central and
western sides. Physical processes appear to dictate the community structure of benthic-hyperbenthic copepods
in the lake.

Flemer, D. A. 1989. Perdido Bay as a Long-Term Gulf Estuarine Ecosystem Verification
Template. Publ. No. EPA/600/X-89/162, U.S. Environmental Protection Agency,
Environmental Research Laboratory, Office of Research and Development, Gulf Breeze,
Florida, 72 p.
G-l, F-28

Functional integration of monitoring and research is described for Perdido Bay, a representative northern Gulf
of Mexico bayou-type estuary. The research strategy is tiered. Tier 1 includes base-line monitoring in a long-
term time series (e.g., monthly) for hydrographic, climatic and ecological variables. Tier 2 provides special
field studies that require a sampling regime incompatible with a monthly sampling frequency. Emphasis is
placed on analysis of factors such as storms or extreme tides that control the strength of the pycnocline,
hypoxic events, and larval and postlarval recruitment Tier 3 focuses on laboratory and field experiments and
field manipulation. Tier 4 includes conceptual, statistical, and process mathematical modeling.

Flint, R. W. 1983. Freshwater inflow and estuarine dynamics as characterized by benthic
processes. Pages 3-20 in R. J. Varnell (ed.), Water Quality Wetland Management.
Proceedings of a Conference, August 4-5,1983, New Orleans, Louisiana.
G-24.

Using a south Texas estuary, an attempt was made to identify environmental changes that affect an estuary,
isolate specific processes for measurement that lead to a holistic view of ecosystem function, and develop a
simple predictive model of ecosystem dynamics that can serve as a basic tool in decision-making processes.
The results suggested a new perception of the function of south Texas estuaries, relative to freshwater input
Furthermore, with a holistic approach to understand ecosystem function, sound environmental management
balancing ecosystem preservation with societal needs can be performed.

Flint, R. W. 1984. Phytoplankton production in the Corpus Christi Bay estuary. Contrib. Mar.
Sci. 27:65-83.
G-24

The Texas Gulf coast is characterized by a number of subtropical estuaries that have great economic and
ecologic value in that they support important regional fisheries through production of new organic matter by
phytoplankton photosynthesis. One of these estuaries, the Corpus Christi Bay ecosystem, was studied for a 3-
yr period to define temporal and spatial variability in its primary production and to elucidate environmental
factors important in regulating production. It was concluded from the study results that long-term maintenance
of primary production in this estuary is accomplished through nutrient recycling while acute changes from
both meteorologic and hydrologic forcing cause short-term increases in production that sustain steady-state and
replenish lost materials to the system.
Flint, R. W. and R. D. Kalke. 1985.
Contrib. Mar. Sci. 28:33-53.
G-24
Benthos structure and function in a south Texas estuary.
The Corpus Christi Bay estuary in the northwestern Gulf of Mexico was investigated for spatial and temporal
variation of benthos community structure and function. Four stations were sampled quarterly for 2.S years to
investigate for macroinfaunal species assemblage changes as well as changes in benthic metabolism and
nutrient regeneration. Cluster analysis of species assemblages illustrated that community structure changed for
the riverine-influenced end of the estuary to the oceanic-influenced end.
303
-------
Flint, R. W. and R. D. Kalke. 1986. Biological enhancement of estuarine benthic community
structure. Mar. Ecol. Prog. Sen 31(l):23-33.
G-24

Benthos in south Texas estuaries are normally concentrated in the top 3 to 4 cm where the sediment is well-
oxygenated and less compact Where larger infauna such as enteropneusts, ophiuroids, or echiurans occur in
the sediments bioturbation by these infauna oxygenates and redistributes normally uninhabited deeper
sediments. A natural disturbance to Corpus Christi Bay benthos by these larger infauna could increase density
and expansion of infaunal populations into deeper regions of the sediments, as well as enhance colonization by
new infaunal species.

Flint, R. W. and D. Kamykowski. 1984. Benthic nutrient regeneration in south Texas coastal
waters. Estuarine Coastal Shelf Sci. 18(2):221-230.
G-27

Because of the variable, unpredictable nature of many potential nutrient sources for coastal phytoplankton
primary production needs in the northwestern Gulf of Mexico, benthic regeneration was investigated as a more
constant source of nutrients to this ecosystem. Water column ammonia profiles taken at several locations on
the south Texas inner-shelf in the past 7 years showed peak concentration in bottom waters. Benthic chamber
measurements verified the presence of ammonia fluxes at the mud-water interface in south Texas coastal
waters. These fluxes were related to benthic faunal activity as measured by sediment metabolism. Laboratory
experiments, designed to test the effect of benthic faunal removal on nutrient regeneration, suggested that the
fauna play a role in regulating this process. How this regulation may occur is discussed.

Flint, R. W., G. L. Powell and R. D. Kalke. 1986. Ecological effects from the balance between
new and recycled nitrogen in Texas coastal waters. Estuaries 9(4A):284-294.
G-24

Benthic nutrient recycling is a significant source of dissolved nitrogen for south Texas coastal waters in the
region of the Corpus Christi Bay estuary. Studies indicate that 90% of the dissolved nitrogen supply for
phytoplankton production is derived from sediments in the upper-estuary, whereas benthic regeneration
supplies only 33 % of the dissolved nitrogen required for primary production outside the barrier island in
coastal waters (IS m depth). It is suggested that combined effects from new and recycled nutrient sources
buffer south Texas coastal productivity against long periods of low nutrient input from fluvial flow. The
comparison of biological responses at several trophic levels to temporal variability in nitrogen recycling and
fluvial flow indicated the importance of freshwater nitrogen input in stimulating primary production.
Freshwater nitrogen input also appeared to sustain long-term productivity by replacing nutrients lost from the
system by extended reliance upon recycling.

Flint, R. W. and N. N. Rabalais. 198la. Environmental Studies of a Marine Ecosystem. South
Texas Outer Continental shelf. University of Texas Press, Austin, Texas, 240 p.
G-27

This study of the south Texas outer continental shelf was conducted on behalf of the Bureau of Land
Management (now Minerals Management Service) of the U.S. DepL of the Interior. The overall program
included information on: 1) geology and geophysics by the U.S. Geological Survey, 2) fisheries resources and
ichthyoplankton populations by the National Marine Fisheries Service, and 3) biological and chemical
characteristics of selected topographic features in the northern Gulf of Mexico by Texas A&M university. The
data resulting from this investigation represent the environmental background existing before major petroleum
exploration and development commence in the area. The central goal of these and other environmental quality
surveys of continental shelf areas is the characterization and protection of the living marine resources.
304
-------
Flint, R. W. and N. N. Rabalais. 1981b.
hypothesis. Fish. Bull. 79(4):737-748.
G-27
Gulf of Mexico shrimp production: A food web
The desire to better understand the dynamics of commercial shrimp populations which support an important
regional fishery on the south Texas outer continental shelf stimulated us to investigate an extensive data base
for links in the various ecosystem components that related to these dynamics. A correlational model was
developed that suggested relationships between pelagic and benthic components of the south Texas marine
ecosystem. Utilizing tracers, such as nickel concentrations in biota, sediment, and water, we identified
pathways of natural transfer between zooplankton, the benthos, and coastal shrimp populations. These results
stimulated us to develop a theoretical food web for the shrimp populations, focusing on transfer of carbon.
The results of this exercise indicated that the majority of the primary production (approximately 80 %) is
diverted to the benthos. Furthermore, it appeared that the secondary production of benthic infauna was not
sufficient to alone support the coastal shrimp populations. We concluded that at at least part of their nutrition
was derived from the detritus pool which was maintained by the excessive amount of primary production
diverted to the benthos.

Flint, R. W. and J. A. Younk. 1983. Estuarine benthos: Long-term community structure
variations, Corpus Christi Bay, Texas. Estuaries 6(2):126-141.
G-24

A study of the benthic communities in Corpus Christi Bay was carried out between 1974 and 1979 to identify
both natural and human-induced variations in community dynamics of the benthos over a long period of
monthly sample collection. General results of the investigation were comparable to previous shorter-term
studies of this estuary in respect to species list of dominant fauna, total densities and species diversity
measures. The results of this long-term study illustrated the resilience of benthic communities to disturbance.
They also provided supportive evidence to hypotheses concerning the high resistance of communities to
disturbance in inconstant environments and the source of colonists in these environments after a major
disturbance to the bottom.

Florida Board of Conservation. 1966. Observations of an Unusual Red Tide. A Symposium.
Florida Board of Conservation, Professional Papers Series, No. 8. Florida Board of
Conservation, Marine Laboratory, St. Petersburg, Florida, 84 p.
F-22, F-23, F-24, F-24.1

Results from studies initiated during a red tide in the general vicinity of Apalachee Bay from July 29 through
August 15, 1964.

Florida Department of Natural Resources. 1975. Proceedings of the Florida Red Tide
Conference, 10-12 October 1974, Sarasota, Florida. Florida Marine Research Publications,
Number 8. Florida Dept. of Natural Resources, Marine Research Laboratory, St. Petersburg,
Florida.
F-9 through F15.1

Florida Department of Environmental Regulation. 1989. Perdido Bay Interstate Study. A Report
on Physical and Chemical Processes Affecting the Management of Perdido Bay. Provisional
Results from March 1988 - February 1989. Florida Department of Environmental
Regulation, Pensacola, Florida, 125 p. (not in hand)
F-28, G-l

Foote, K. 1982. Observations of oxygen depletion in Louisiana offshore waters. Abstr. for
Proceedings of the Third Annual Gulf of Mexico Information Transfer Meeting, August 24-
26, 1982, New Orleans, Louisiana. U.S. Dept. of the Interior, Minerals Management
305
-------
Service, Outer Continental Shelf Office, New Orleans, Louisiana.
G-7.1

Low dissolved oxygen concentrations were found yearly in Louisiana offshore waters from 1978 through 1982.
Samples were taken from the coastline to 20 fathoms between Grand Terre Island and Timbalier Island.
Concentrations of dissolved oxygen were found in July and September 1978; June, July, August and
November 1979; June, July and August 1980; May through October 1981; and May through August 1982.
Catches of demersal nekton, near-bottom zooplankton and benthos, were significantly lower during periods of
low bottom dissolved oxygen. The relationships of seasonally and salinity stratification to bottom dissolved
oxygen concentration were shown hi an empirical model developed by stepwise multiple regression with log-
log transformed water chemistry and temperature data. Bottom, dissolved oxygen concentration was inversely
related to water temperature, conductivity, the difference between bottom and surface salinities, and
concentrations of ammonium, orthophosphate, and silicates.

Fotheringham, N. and G. Weissberg. 1979. Some causes, consequences and potential impacts of
oxygen depletion in the northern Gulf of Mexico. Proceedings, 11th Annual Offshore Tech.
Conf. OTC 4(3611):2205-2208.
G-7.1

Biological and water quality changes in the Gulf of Mexico off the central Louisiana coast have been examined
during a seasonal period of stratification and oxygen depletion in the water column. Probable cause, observed
effects, and potential impacts on the timing of ocean discharges and dumping and onsite selection for offshore
industries are described. Apparently an annual phenomenon of variable intensity resulting from a large
discharge of low salinity, organic-laden water from the Mississippi and Atchafalaya Rivers at a time of
minimal vertical mixing, the midsummer event may be intensified and prolonged by the intrusion of high
salinity bottom water from a Loop Current eddy. The temporal and geographic distribution of this condition
and its environmental consequences should be recognized by industries engaged in fishing, offshore petroleum
production, and offshore dumping and by government agencies providing leases and permits for these activities.
Fox, L. E., F. Lipschultz, L. Kerkhof and S. C. Wofsy.
Mississippi estuary. Estuaries 10(1):1-12.
G-7.1
1987. A chemical survey of the
A "snapshot" survey of the Mississippi estuary was made during a period of low river discharge, when the
estuarine mixing zone was within the deltaic channels. Concentrations of H+, Ca2+, inorganic phosphorus
and inorganic carbon suggest that the waters of the river and the low salinity portion of the estuary are near
saturation with respect to calcite and sedimentary calcium phosphate. The concentrations of dissolved NH4+
and O2, over most of the estuary, appeared to be influenced by decomposition of terrestrial organic matter in
bottom sediments.

Fox, L. E., S. L. Sager and S. C. Wofsy. 1985. Factors controlling the concentrations of soluble
phosphorus in the Mississippi estuary. Limnol. Oceanogr. 30(4):826-832.
G-9
Sediments from the Mississippi River estuary were suspended in solutions with a range of salinities and
various initial concentrations of phosphate. After 42 days, the suspensions had nearly uniform values for the
ion activity product of calcium times biphosphate, [Ca2+] [HPO^'] approx. 10"^ M^. Similar values were
observed for this ion product in the Mississippi River and in the upper estuary, suggesting that the
concentration of soluble phosphorus may be controlled by an equilibrium with sedimentary material.
Phosphorus levels in the lower estuary are controlled primarily by dilution with low-nutrient waters from the
Gulf of Mexico.
306
-------
Fraser, T. H. 1985. Long-Term Water-Quality Characteristics of Charlotte Harbor, Florida.
U.S. Geological Survey Water-Resources Investigations Report No. 86-4180, U.S. Dept. of
the Interior, Geological Survey, Tallahassee, Florida, 43 p.
F-13

Water-quality data for nine constituents collected from January 1976 through March 1984 in upper Charlotte
Harbor were examined for evidence of trend (change) with time. Average seasonal patterns and moving
averages were described to aid initial descriptions of variation. Evidence suggested an increasing trend for
temperature and orthophosphate and decreasing trend for near-surface dissolved oxygen. The temperature trend
was related to low winter temperatures early in the period. The orthophosphate trend was related to a major
source, the Peace River. The source of the dissolved oxygen trend was not identified, but a relation with
primary producers (phytoplankton) was likely.

Freeberg, L. R., A. Marshall and M. Heyl. 1979. Interrelationships of Gymnodinium breve
(Florida red tide) within the phytoplankton community. Pages 139-144 in D. L. Taylor and
H. H. Seliger (eds.), Toxic Dinoflagellate Blooms. Proceedings of the Second International
Conference on Toxic Dinoflagellate Blooms, October 31 - November 5,1978, Key Biscayne,
Florida. Developments in Marine Biology - Vol. 1, Elsevier North Holland, New York.
F-15.1, F-24.1

Medium, preconditioned by prior growth of G. breve, has been bioassayed with 28 species of phytoplankters
recently isolated in axenic cultures. Growth in 18 of the 28 species tested was significantly inhibited in the
preconditioned medium. Sensitivity to the apparent growth inhibitor is species-specific and variable within
those species affected. The population levels, as indicated by in vivo chlorophyll a for four diatom, one
flagellate, and four dinofiagellate species, only slightly exceeded the inoculum levels, while the inocula of two
dinoflagellate species lysed. Crude extracts of G. breve toxin(s) tested for growth inhibition with 12 algal
species-resulted in the total arrest of growth for four diatom and four dinoflagellate species. Partial purification
of the toxin extract employing column chromatography techniques did not appear to separate properties of the
algal inhibition from the ichthyotoxicity.

Frey, H. R., M. W. Szabados and L. E. Hickman. 1981. National Ocean Survey Strategic
Petroleum Reserve Support Project: Final Report. Vol. I - Oceanography on the Louisiana
Inner Continental Shelf. U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, National Ocean Survey, Washington, D.C.
G-7.1

The Dept of Energy proposes to store crude oil for the National Strategic Petroleum Reserve in subterranean
storage caverns that are produced by solution-mining salt deposits. This NOS project is directed toward
characterizing the physical oceanography of two proposed brine disposal sites along the coast of Louisiana.
Planning for the project began in August 1977, and the mobilization for the field effort began in November
1977. Time series data being obtained with fixed recording instruments include current, speed and direction,
water temperature and conductivity, water levels, waves, air speed and direction, barometric pressure and air
temperature. Conductivity/temperature/depth, vertical profiles and water samples are obtained on a monthly
basis. The water samples are analyzed for salinity and dissolved oxygen. Registered hydrographic surveys
have been conducted at each site on a cooperative basis. A rigorous data quality assurance task is being carried
out Data quality acceptance and rejection levels have been established for each sensor, and a field check
system has been installed on the NOAA Ship Ferrel to monitor instrument performance.

Friedemann, M. and J. Hand. 1989. Typical Water Quality Values for Florida's Lakes, Streams
and Estuaries. Standards and Monitoring Section, Florida Bureau of Surface Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida, 23 p.
F-9 through F-28
307
-------
Over the last 20 years, approximately five million water quality measurements have been taken in Florida
waters. Information has been collected from all of Florida's major lakes, streams, and estuaries and the data
have been placed in "STORET", EPA's water quality database. This document presents the range of typical
values that have been sampled. Values are shown for the conventional water quality constituents, including
water temperature, nutrients, bacteria, oxygen, oxygen demanding substances, water clarity, pH, and biological
diversity indices.

Fryxell, G. A., M. E. Reap, D. L. Roelke, L. A. Cifuentes and D. L. Valencia. 1991. Confirmed
presence of neurotoxin-producing diatom around Galveston, Texas. Pages 153-154 in F. S.
Shipley and R. W. Kiesling (eds.), Proceedings. Galveston Bay Characterization Workshop,
February 21-23, 1991. Galveston Bay National Estuary Program Publication GBNEP-6,
220 p.
G-17

See Shipley and Kiesling (1991).

Fryxell, G. A. 1990. More on Nitzschia pungens. Phycological Newsletter 26(1): 1.
G-17

In 1987, an outbreak of neurotoxic domoic acid, observed after an extended diatom bloom in an area of a,
mariculture shellfish project on Prince Edward Island, Canada, resulted in several human deaths and disabilities;
this event is the first time that a diatom has been documented as the source of a neurotoxin. This same
diatom, Nitzschia pungens f. multiseries Hasle, has just been found in the Galveston, Texas area of the Gulf of
Mexico, and Jinhae Bay, Korea. It is difficult to distinguish from the common coastal diatom, Nitzschia
pungens Grunow, and thus is little known and rarely recorded anywhere, although indications now are that it is
widespread.

Fuller, D. A., R. E. Condrey, J. P. Geaghan and B. B. Barrett. 1990. An analysis of long-term
salinity patterns in the Louisiana coastal zone. Northeast Gulf Sci. 11(1):11-17.
G-7.1

Saltwater intrusion is believed to be one of the greatest threats to Louisiana's fishery and wildlife resources.
The Louisiana Department of Wildlife and Fisheries has maintained salinity recording stations throughout the
State's coastal marshes since the 1960s. We applied several different analytical approaches to the salinity data
from 17 stations to determine whether this database could be used to detect and quantify long-term salinity
trends in coastal Louisiana. We did not detect a large-scale, consistent trend over time in coastal salinities
across the State. For the data to be useful in monitoring salinity trends in coastal marshes, especially with
respect to saltwater intrusion, stations should be added in fresh and intermediate marshes. In addition, the
relationships our study revealed between short- and long-term data indicate that records covering less than a
decade are insufficient to denote long-term salinity changes, barring some major modification of the hydrologic
regime.

Gael, B. T. and C. S. Hopkinson, Jr. 1979. Drainage density, land-use and eutrophication in
Barataria Basin, Louisiana. Pages 147-163 ia J. W. Day, Jr., D. D. Culley, Jr., R. E.
Turner and A. J. Mumphrey, Jr. (eds.), Environmental Conditions in the Louisiana Coastal
Zone. Proceedings of the Third Coastal Marsh and Estuary Management Symposium, March
6-7, 1978, Baton Rouge, Louisiana. Division of Continuing Education, Louisiana State
University, Baton Rouge, Louisiana.
G-10

A multiparametered index has been used to describe the trophic state of water bodies in the Barataria Basin
Hydrologic Unit in Louisiana. Drainage density is significantly correlated with the trophic state index. High
drainage densities serve to move water directly and rapidly from high nutrient loading areas such as urban and
agricultural areas to lakes, effectively preventing overland flow through wetlands in the process. Highest
308
-------
drainage densities were found along upland areas and had concomitantly highest trophic state indexes. Further
increases in drainage density and upland development are projected to further exacerbate the eutrophication
problem in coastal Louisiana.

Gallaway, B. J. 1982. Defining and obtaining management information related to oxygen
depletion. Abstr. for Proceedings of the Third Annual Gulf of Mexico Information Transfer
Meeting, August 24-26, 1982, New Orleans, Louisiana. U.S. Dept. of the Interior, Minerals
Management Service, Outer Continental Shelf Office, New Orleans, Louisiana, 4 p.
G-7.1

Development of hypoxic conditions off the Louisiana coast, together with some major biological changes in
the northwestern Gulf, suggest the need to quantitatively define the oxygen dynamics of the shelf for the
purpose of assessing impacts and planning management strategies. This paper surveys the historical data
associated with changes in the Mississippi River waters, summarizes reports of hypoxia and major biological
changes in Gulf water, and suggests development of an assimilative capacity model for the Texas-Louisiana
shelf ecosystem through a series of modeling workshops.

Gallaway, B. J. 1981. An Ecosystem Analysis of Oil and Gas Development on the Texas-
Louisiana Continental Shelf. Biological Services Program Publ. FWS/OBS-81/27, U.S.
Dept. of the Interior, Bureau of Land Management, Fish and Wildlife Service, Washington,
D.C., 89 p.
G-7.1

Observed effects of oil and gas development activities and effluents are described. Data from most field studies
indicate that direct effects are limited in space, but the effects over time are unknown. One of the major
problems has been separating effects of oil and gas development-related activities and other man-induced
variations from natural changes. Particular concern is expressed relative to increased organic loading of the
system and the apparently related low dissolved oxygen levels characteristic of some parts of the system during
warm seasons.

Garrison, C. R. 1982. Water-Quality of the Barataria Unit, Jean Lafitte National Historical Park,
Louisiana (April 1981 - March 1982. Open-File Report No. 82-691, U.S. Dept. of the
Interior, Geological Survey, Baton Rouge, Louisiana.
G-10

Surface-water samples were collected monthly for April 1981-March 1982 from six sites within the Barataria
Unit of the Jean Lafitte National Historical Park, Louisiana. The sites were located on Bayou Segnette, Kenta
Canal, and Millaudon Canal. Biological, chemical, and physical analyses were performed. Three of the sites
were sampled quarterly for additional parameters including pesticides, metals, algal growth potential,
phytoplankton, benthic macroinvertebrates, and grain size of bed material. The results of the analyses are
presented without interpretation.

Gaston, G. R. 1985. Effects of hypoxia on macrobenthos of the inner shelf off Cameron,
Louisiana. Estuarine Coastal Shelf Sci. 20(5):603-613.
G-7.1

The effects of hypoxic bottom water, an annual event, were documented on the inner shelf off Cameron,
Louisiana during the summer of 1981. Populations of most species of macrobenthos were dramatically
reduced. In an area of fine sediment that was numerically dominated by polychaetous annelids, the most
severely affected populations were those of tube-dwelling and surface-feeding species. Burrowing species were
less influenced by the hypoxia.
309
-------
Gaston, G. R., Rutledge. Philip A. and M. L. Walther. 1985. The effects of hyppxia and brine
on recolonization by macrobenthos off Cameron, Louisiana. Contrib. Mar. Sci. 28:79-93.
G-7.1 ;•••..'

Screened defaunated sediment containers were placed on racks 100 m downcurrent and 10 km upcurrent of a
Dept. of Energy brine diffuser located in the nearshore Gulf of Mexico 20 km southwest of Cameron,
Louisiana. Samples were periodically collected from both racks over a period of 14 weeks to assess
recolonization by the macrobenthos. A disparity in dissolved oxygen levels of the two sites, led to a disruption
of recolonization at one site, and a subsequent dissimilar temporal pattern there. This difference in
recolonization of the two sites was apparent in analyses of numerically dominant species and feeding groups
until the tenth week of the study. By the end of the study, however, differences between diffuser and control
sites were limited to earliest colonizers (surface deposit feeders and suspension feeders) and carnivores, and did
not occur in the subsurface deposit feeders that colonized after the severe hypoxia.

Gazey, W. J., B. J. Gallaway, R. C. Fechelm, L. R. Martin, L. A. Reitsema, K. F. Bennry, R.
Schroeder and D. Chester. 1982. Shrimp mark release and port interview sampling survey
of shrimp catch and effort with recovery of captured tagged shrimp. la W. B. Jackson (ed.),
Shrimp Population Studies: West Hackberry and Big Hill Brine Disposal Sites off Southwest
Louisiana and Upper Texas Coasts, 1980-1982. Vol. H. Final Report to DOE. U.S. Dept.
of Commerce, National Oceanic and Atmospheric Administration, National Marine Fisheries
Service, Washington, D.C., 306 p. (not in hand)
G-7.1, G-27
Geyer, R. A. 1955. Effect of the Gulf of Mexico and the Mississippi River on hydrography of
Redfish Bay and Blind Bay. Publ. Inst. Mar. Sci. Univ. of Texas 4(1): 154-168.
G-9

A hydrographic survey was conducted in Redfish and Blind Bays, on the southern edge of the Mississippi
Delta, and in the adjoining areas in the Gulf of Mexico. Almost 1100 observations were made at 49 locations
during an 8-wk period in the spring of 1953. Information was obtained on salinity, temperature, and current
conditions. These data are summarized and evaluated with emphasis on the effect of the Mississippi River and
the Gulf of Mexico on the hydrography of Redfish and Blind Bays. A correlation exists between the stage of
the Mississippi River and the salinity and temperature characteristics of these bays and their adjoining Gulf
areas. Similarly, the diluting effect during high stages of the Mississippi River is evident over an area
extending several miles into the Gulf. It was noted that islands in Redfish Bay are wasting away.

Geyer, R. A. 1950. The occurrence of pronounced salinity variations in Louisiana coastal waters.
J. Mar. Res. 9(2): 100-110.
G-7.1

The chloride-ion contents of more than 700 sea water samples from the coastal waters of western Louisiana
were converted to salinity values and were used in a study of the salinity characteristics. These data were
gathered from seven drilling platforms during a period of 14 months in a zone paralleling the coast for about
60 miles, approximately 6 to 8 miles offshore and in depths varying between 40 and 50 ft. The chloride-ion
content was determined by the standard chemical titration method in connection with quality control of salt
water drilling mud used in the drilling of offshore oil wells. The analysis of the chloride-ion concentration data
clearly demonstrates the existence of a wide salinity variation in any one area. The variations may be
classified into long seasonal and shorter daily and even hourly types. A well defined correlation exists between
the seasonal variations in salinity and the variations in the amount of water discharged by the Mississippi
River. These data demonstrate that this is the major factor in determining the long-term salinity characteristics
of this area. However, available information also indicates that salinity variations in a given area are affected
as well by local drainage patterns and current characteristics.
310
-------
Gillard, R. M. 1974. Distribution, Abundance, and Species Diversity of Macrobenthic and
Meiobenthic Invertebrates in Relation to Houston Ship Channel Pollution in Upper Galveston
Bay and Tabbs Bay, Texas. M.S. Thesis, Texas A&M University, College Station, Texas,
174 p.
G-17

Benthic collections were made with a modified Ekman dredge over a period of 18 months from August 1970
through January 1972 at 17 stations in Tabbs Bay and upper Galveston Bay, Texas. A total of 87 species,
including 24 polychaete worms, 10 gastropod snails, 11 pelecypod clams, and 26 crustaceans, were collected.
The total number of species, number of individuals, and the Shannon and Weaver species diversity index were
used as benthic community parameters in relation to the environmental parameters of sediment composition,
temperature, salinity, dissolved oxygen, seasonal, areal, and pollution effects.

Gilmore, G., J. Dailey, M. Garcia, N. Hannebaum and J. Means. 1976. A Study of the Effects
of Fresh Water on the Plankton, Benthos, and Nekton Assemblages of the Lavaca Bay
System, Texas. Tech. Rept. to the Texas Water Development Board, January, 1973 - June,
1975. Texas Parks and Wildlife Dept, Coastal Fisheries Branch, Austin, Texas, 113 p.
G-21

This study was typified by above normal freshwater inflow. The average inflow into the Lavaca Bay system
during this 30-mo study was about 59 % above normal. A total of 1S6 phytoplankton taxa representing six
divisions were identified. Phytoplankton taxa diversities generally declined with increased freshwater inflow.
A total of 201 zooplankton taxa representing 14 phyla were identified. No significant correlations were found
between zooplankton standing crops or taxa diversity and freshwater inflow. A total of 169 benthos taxa
representing nine phyla were identified. Benthos taxa diversity was positively related to bottom salinity and
negatively related to bottom turbidity and nutrients. A total of 70 nekton taxa representing three phyla were
identified from trawl samples. Nekton populations appeared to be affected more by water temperature than by
freshwater inflow.

Gosselink, J. G., R. R. Miller, M. Hood and L. M. Bahr, Jr. (eds.). 1975. Environmental
Assessment of a Louisiana Offshore Oil Port and Appertinent Storage and Pipeline Facilities.
Vol. II - Technical Appendices. Appendix V - The Offshore Ecology Study. Prepared for
Louisiana Offshore Oil Port, Inc., New Orleans, Louisiana.
G-7.1

As part of the LOOP, Inc. environmental assessment, an offshore study was carried out to describe the marine
chemistry and biology in the vicinity of the proposed single-point mooring terminal and offshore pipeline.
The study was accomplished through both a literature search and a field study of 1-yr duration. Contents
include the following sections: 1) Geological and Geographical Description of Louisiana Coast; 2) Hydrology;
3) Offshore Physical Oceanography; 4) Nearshore Oceanography; 5) Marine Biology; 6) Onshore Ecology
Study; 7) Economic Impact of Superport in Lafourche and Terrebonne Parishes, Louisiana; 8) Archeology.

Graham, H. W>, J. M. Amison and K. T. Marvin. 1954. Phosphorus Content of Waters along
the West (Coast of Florida. U.S. Fish and Wildlife Service, Special Scientific Report-
Fisheries No. 122. U.S. Dept. of the Interior, Fish and Wildlife Service, Washington, D.
C, 43 p.
F-12, F-13, F-14, F-15.1

The high values of total phosphorus found in the bloom of Gymnodinium breve in 1947 have yet to be
satisfactorily explained. Nowhere in the Gulf of Mexico or in Charlotte Harbor at any time during this
investigation were phosphorus concentrations found corresponding to high values which occurred in the red tide
of 1947 except in a bloom of Trichodesmium.
311
-------
Griffin, G. M. and B. J. Ripy. 1974a. Horizontal and vertical distribution of turbidity on the
Louisiana shelf south of Timbalier Bay-August 1972-July 1973. In Offshore Ecology
Investigation, 1974. #3453, C.I.R. files, Gulf Universities Research Consortium (GURC),
Galveston, Texas.
G-7.1

The study was designed to determine whether or not the intensive petroleum exploration activities on the
continental shelf off Timbalier Bay have significantly affected the turbidity of surrounding waters. The report
concluded no increase in surface turbidity over the ambient background level of the region could be detected
around any of the production platforms examined.

Griffin, G. M. and B. J. Ripy. 1974b. Turbidity, suspended sediment concentrations, clay
mineralogy of suspended sediments, and the origin of the turbid near-bottom water layer--
Louisiana shelf south of Timbalier Bay-August 1972-January 1974-with comments on a
process model for turbid layer transport. Pages 75-79 ia Abstracts, Summaries and
Conclusions from the Offshore Ecology Investigation, 1972-74. Gulf Universities Research
Consortium (GURC), Galveston, Texas.
G-7.1

See Griffin and Ripy (1974a).

Groover R. D. and T. S. Sharik. 1974. A Report on the Ecology of the Lower Colorado River -
Matagorda Bay Area of Texas: June 1973 through July 1974. Docket No. STN 50-498, STN
50-499, U.S. Atomic Energy Commission, Washington, D.C. (not in hand)
G-20, G-21

Gulf Universities Research Consortium. 1979. The Alabama Coastal Zone Ecology and Water
Quality Data Information Sources Existing Benthic Data Evaluation. Final Report to the
Marine Environmental Sciences Consortium, Dauphin Island, Alabama, Agreement MESC-9-
90060. GURC Report No. 170, Gulf Universities Research Consortium, Galveston, Texas,
21 p. (not in hand)
G-2

Gunning, G. E. and R. D. Suttkus. 1986. A comparative study of pH levels in the Sabine, Red,
Mississippi, Pearl, Alabama and Perdido Rivers of the southern United States. The La.
Environmental Professional 3(1):4-20.
F-28 and G-l, G-6, G-9

Six rivers of the southern United States exhibited the following pH ranges: 6.1-7.7, Sabine; 6.8-8.6, Red; 6.7-
8.7, Mississippi; 5.6-7.7, Pearl; 6.3-9.0, Alabama; and 4.8-8.5, Perdido. Of the six rivers, the Sabine showed
the least variation, the Red and Mississippi showed similar pH ranges, the Pearl was properly characterized as
an acid stream, and the Alabama and Perdido showed the greatest range of variation in pH, the former due to
influence of a dam upstream, and the latter due to effects of Perdido Bay. Levels of pH were generally within
the 5.0-9.0 range recommended by biologists for fully developed freshwater fisheries.

Gunter, G. 1979. Notes on sea beach ecology. Food sources on sandy beaches and localized
diatom blooms bordering Gulf beaches. Gulf Res. Rep. 6(3):305-307.
G-27

Of relevance is the description of a type of plankton bloom that occurs along the Texas coast composed of the
diatom Chaetoceros sp. Blooms of 16 miles extend from the water's edge along Mustang Island for 15 or 20
yards. The parallel coincidence of blooms following rains and calm weather is suggested.
312
-------
Gunter, G. 1942. Offatts Bayou, a locality with recurrent summer mortality of marine organisms.
Am. Midi. Nat. 28(3):631-633.
G-17

Discussion of mortalities of marine organisms in Offatts Bayou which opens to West Galveston Bay. Events
occur primarily in the summer and are related to decomposition of organic materials of anthropogenic origin.

Gunter, G. and G. E. Hall. 1965. A biological investigation of the Caloosahatchee estuary of
Florida. Gulf Res. Rep. 2(1): 1-72.
F-12

The scope and purpose of this work was to: a) review the history of the Caloosahatchee River and analyze the
problems concerned with discharges into the estuary; 2) present biological data from investigations of the
estuary made at different times during the years 1957 to 1960, inclusive; 3) determine the biological effects of
operation of Moore Haven and Ortona Locks, and the planned lock and dam at Olga with reference to important
indicator species within the lower river and estuary; and 4) determine operation procedures, practicable within
specific operational requirements of the project, which would be either beneficial or of least damage to
estuarine fishes and fishing.

Gunter, G. and C. H. Lyles. 1979. Localized plankton blooms and jubilees on the Gulf coast.
Gulf Res. Rep. 6(3):297-299.
G-27

The writers describe various small types of plankton blooms such as those occurring hi boat slips, the head of
a large bayou and a strip-type bloom of Chaetoceros on the Gulf beach. Oyster kills from "poison water"
draining off of marshes are said to be caused by plankton bloom. Small "jubilees" are said to be caused by
localized blooms, and one of these is described as it occurred.

Hackney, C. T. 1978. Summary of Information: Relationship of Freshwater Inflow to Estuarine
Productivity along the Texas Coast. Publ. FWS/OBS-78/73, U.S. Dept. of the Interior, Fish
and Wildlife Service, Washington, D.C. (not in hand)
G-16 through G-26.3

Haddad, K. D. and K. L. Carder. 1979. Oceanic intrusion: One possible initiation mechanism of
red tide blooms on the west coast of Florida. Pages 269-274 in D. L. Taylor and H. H.
Seliger (eds.), Toxic Dinoflagellate Blooms. Proceedings of the Second International
Conference on Toxic Dinoflagellate Blooms, October 31 - November 5,1978, Key Biscayne,
Florida. Developments in Marine Biology - Vol. 1, Elsevier North Holland, New York.
F-24.1

Upwelling and intrusion of Loop Current water onto the west Florida shelf is suggested as a mechanism that
resuspends Gymnodinium breve resting cysts and provides conditions for excystment and growth.

Hahl, D. C. and K. W. Ratzlaff. 1970. Chemical and Physical Characteristics of Water in
Estuaries of Texas, September 1967 - September 1968. Prepared by the U.S. Geological
Survey. Rept. No. 117, Texas Water Development Board, Austin, Texas, 91 p.
G-16, G-20, G-21, G-22, G-23, G-24

In September 1967, the USGS and the TWDB began a water-resources investigation of the principal estuaries
along the Texas coast except Galveston Bay and the Rio Grande. The objectives of the investigation are to
determine: 1) the occurrence, source, and distribution of nutrients; 2) current patterns, directions, and rates of
movement; 3) physical, organic, and inorganic water quality and its variations; 4) the occurrence, quantity and
dispersion of land drainage entering the estuarine systems; and 5) the chemical and physical characteristics of
Gulf water that enters the estuaries.
313
-------
Hahl, D. C. and K. W. Ratzlaff. 1972. Chemical and Physical Characteristics of Water in
Estuaries of Texas, October 1968 - September 1969. Prepared by the U.S. Geological
Survey. Rept. No. 144, Texas Water Development Board, Austin, Texas, 161 p.
G-16, G-18, G-19, G-20, G-21, G-22, G-23, G-24, G-26

See Hahl and Ratzlaff (1970).

Hahl, D. C. and K. W. Ratzlaff. 1975. Chemical and Physical Characteristics of Water in
Estuaries of Texas, October 1970 - September 1971. Prepared by the U.S. Geological
Survey. Rept. No. 191, Texas Water Development Board, Austin, Texas, 153 p.
G-16, G-18, G-19, G-20, G-21, G-22, G-23, G-24, G-26

See Hahl and Ratzlaff (1970). This report represents data collected during the 1971 water year and is the fourth
in an annual series.

Hand, J. and J. Jackman. 1984. Water Quality Inventory for the State of Florida. Florida
Department of Environmental Regulation, Bureau of Water Analysis, Tallahassee, Florida,
235 p. (not in hand)

Hand, J., V. Tauxe and M. Friedemann. 1988a. Apalachicola Bay Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 102, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-24

To assess Florida stream water quality, a Florida stream Water Quality Index (WQI) was developed. It is based
on the quality of water as measured by six water quality categories (water clarity, dissolved oxygen, oxygen
demanding substances, bacteria, nutrients and biological diversity). Each category may have more than one
parameter. Raw (annual average) data are converted into index values that range from 0 to 90 for the six
categories. Index values correspond to the percentile distribution of stream water quality data in Florida. The
overall WQI is the arithmetic average of the six water quality index categories. The index for each category is
determined by averaging its component parameter index values. Missing water quality parameters and missing
water quality categories are ignored in the final calculation. Therefore, the final WQI is based on an average of
anywhere from 1 to 6 water quality index categories.

Hand, J., V. Tauxe and M. Friedemann. 1988b. Caloosahatchee River Basin Technical Report.
An Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 106, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-12

See Hand €M/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988c. Charlotte Harbor Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 107, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-13

SeeHande/a/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988d. Choctawhatchee Bay Basin Technical Report.
An Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 110, Bureau of Surface Water Management, Div. of Water
314
-------
Management, Dept of Environmental Regulation, Tallahassee, Florida.
F-26

See Hand ef a/. (1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988e. Crystal River to St. Petersburg Beach Basin
Technical Report. An Appendix of the 305(b) Water Quality Assessment for the State of
Florida. Standards and Monitoring Technical Rept. No. 112, Bureau of Surface Water
Management, Div. of Water Management, Dept. of Environmental Regulation, Tallahassee,
Florida.
F-16

See Hand «a/. (1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988f. Everglades West Coast Basin Technical Report.
An Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 116, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-10.1

SeeHandefa/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988g. Pensacola Bay Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 131, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
. F-27

SeeHandefa/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988h. Perdido Bay Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 132, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-28

See Hand rt a/. (1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988i. Sarasota Bay Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 135, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-14

SeeHand«a/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988J. St. Andrews Bay Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 137, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-25

See Bander al (1988a).
315
-------
Hand, L, V. Tauxe and M. Friedemann. 1988k. St. Marks River Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 140, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-22

SeeHandefo/.(1988a).

Hand, L, V. Tauxe and M. Friedemann. 19881. Steinhatchee River Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 142, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-20

See Hand e/c/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988m. Tampa Bay Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 145, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-15

SeeHandero/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988n. Waccasassa River Basin Technical Report. An
Appendix of the 305(b) Water Quality Assessment for the State of Florida. Standards and
Monitoring Technical Rept. No. 147, Bureau of Surface Water Management, Div. of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida.
F-18

SeeHandera/.(1988a).

Hand, J., V. Tauxe and M. Friedemann. 1988o. Water Quality Assessment for the State of
Florida. Submitted in Accordance with the Federal Clean Water Act, Section 305(b).
Standards and Monitoring Section, Bureau of Surface Water Management, Division of Water
Management, Dept. of Environmental Regulation, Tallahassee, Florida, 105 p.
F-9 through F-15, F-16 through F-24, F-25 through F-28

SeeHand#a/.(1988a).

Hann, Jr., R. W., C. P. Giommona and R. E. Randall (eds.). 1984a. Offshore Oceanographic
and Environmental Monitoring Services for the Strategic Petroleum Reserve Program. Vol. I,
II and ffl. Annual Report for the Bryan Mound Site, September 1982 - August 1983. Dept.
of Energy Contract No. DE-AC96-83P010850, Texas A&M University, Texas A&M
Foundation, College Station, Texas.
G-27

The DOE's Strategic Petroleum Reserve Program began leaching the Bryan Mound salt dome and discharging
brine into the coastal waters offshore of Freeport, Texas on March 10,1980. This report describes the findings
of a team of Texas A&M University scientists and engineers who have conducted a study to evaluate the effects
of the Bryan Mound brine discharge on the marine environment. The study addresses the areas of physical
oceanography, analysis of the discharge plume, water and sediment quality, nekton, benthos and data
management It focuses on the period from September 1982 through August 1983. Vol. II consists of
supporting data in the form of figures and tables, and Vol. Ill is the Executive Summary.
316
-------
Hann, Jr., R. W. C. P. Giommona arid R. E. Randall (eds.). 1984b. Offshore Oceanographic
and Environmental Monitoring Services for the Strategic Petroleum Reserve Program. Vol. I,
II arid HI. 18-Month report for the West Hackberry Site from May 1982 through November
1983. Dept. of Energy Contract No. DE-AC96-83P010850, Texas A&M University, Texas
A&M Foundation, College Station, Texas.
G-7.1

The purpose of this report is to describe the findings of the project team during the 18 months of postdisposal
study conducted from May 1,1982 through November 14,1983. The areas of investigation are benthos, brine
plume, data management, nekton, physical oceanography, phytoplankton, water and sediment quality and
zooplankton. Vol. II consists of supporting data in the form of figures and tables, and Vol. HI is the
Executive Summary.

Hann, Jr., R. W. and R. E. Randall (eds.). 1980. Evaluation of Brine Disposal from the Bryan
Mound Site of the Strategic Petroleum Reserve Program. Vol. I and n. Final Report of
Predisposal Studies. Dept. of Energy Contract No. DE-FC96-79P010114, Texas A&M
University, Texas A&M Foundation, College Station, Texas.
G-27

The purpose of this report is to describe the environmental conditions found by the principal investigators
during the predisposal study conducted from September 1977 through February 1980 prior to the start of brine
discharge in March 1980. The major areas of investigation are physical oceanography, analysis of the
discharge plume, water and sediment quality, nekton, benthos, phytoplankton, zooplankton, and data
management Vol. II consists of appendices which contain additional supporting data in the form of figures
and tables.

Hann, Jr., R. W. and R. E. Randall (eds.). 1981. Evaluation of Brine Disposal from the Bryan
Mound Site of the Strategic Petroleum Reserve Program. Vol. I and U. Final Report of
Twelve-Month Postdisposal Studies. Dept. of Energy Contract No. DE-FC96-79P010114,
Texas A&M University, Texas A&M Foundation, College Station, Texas.
G-27

From March 1980 through February 1981, a team of scientists and engineers at Texas A&M University
conducted a 12-mo environmental study to evaluate the effects of discharging brine into the coastal waters off
Freeport, Texas. The brine discharge is the result of leaching large storage caverns in an underground salt
dome that is being used for the storage of petroleum products. The study addresses the area of physical
oceanography, analysis of the discharge plume, water and sediment quality, nekton, benthos, phytoplankton,
zooplankton, and data management. Vol. U consists of supporting data in the form of figures and tables.

Hann, Jr., R. W. and R. E. Randall (eds.). 1982. Evaluation of Brine Disposal from the Bryan
Mound Site of the Strategic Petroleum Reserve Program. Vol. I and n. Final Report of
Eighteen-Month Postdisposal Studies. Dept. of Energy Contract No. DE-FC96-79P010114,
Texas A&M University, Texas A&M Foundation, College Station, Texas, (not in hand)
G-27

Hann, Jr., R. W. and R. E. Randall (eds.). 1983. Evaluation of Brine Disposal from the Bryan
Mound Site of the Strategic Petroleum Reserve Program for September 1981 - August 1982
Vol. I, II and III. Dept. of Energy Contract No. DE-FC96-79P010114, Texas A&M
University, Texas A&M Foundation, College Station, Texas.
G-27

See Hann et al. (1984).
317
-------
Harper, Jr., D. E. and G. Guillen. 1989. Occurrence of dinofiagellate bloom associated with an
influx of low salinity water at Galveston, Texas, and coincident mortalities of demersal fish
and benthic invertebrates. Contrib. Mar. Sci. 31:147-161.
G-17, G-27

Low salinity water and an associated dinofiagellate bloom appeared suddenly off Galveston, Texas, in early
June 1984. An aerial survey showed the bloom extended east at least as far as Cameron, Louisiana. High
discharge from the Mississippi-Atchafalaya Rivers between March and late May, and a strong, wind-driven
downcoast current preceded the appearance of low salinity water and its associated bloom. Within a week of
the first appearance of the bloom, demersal fish, numerically dominated by Atlantic threadfin began dying early
in the morning and washing ashore. It is believed the kill was caused by hypoxia and/or hydrogen sulfide
production resulting from nocturnal metabolism of the bloom and anaerobic decay of dead dinoflagellate cells.

Harper, Jr., D. E. and L. D. McKinney. 1982a. Causes and effects of oxygen depletion on the
benthic biota of the upper Texas coast. Abstr. for Proceedings of the Third Annual Gulf of
Mexico Information Transfer Meeting, August 24-26, 1982, New Orleans, Louisiana. U.S.
Dept. of the Interior, Minerals Management Service, Outer Continental Shelf Office, New
Orleans, Louisiana.
G-27

Hypoxia occurring in June 1979 at two sites off Freeport, Texas caused extensive mortalities of soft-bottom
and hard-bottom organisms. Events of this kind, which appear to occur nearly annually off the Louisiana
coast, indicate a need for monitoring leading to predictive modeling. After data have been collected for several
years' it should be possible to define the variable causing hypoxia. From this information, a model could be
constructed. Thereafter, routine monitoring of important variables would provide data to be plugged into the
model, which would estimate both the probability of occurrence and area! extent of hypoxia.

Harper Jr., D. E. and L. D. McKinney. 1982b. Effect of brine disposal on benthic communities
off Freeport, Texas. Abstr. for Oceans '82 Conference Record: Industry, Government,
Education - Partners in Progress, September 20-22,1982. Washington, D.C.
G-27

Brine (250 ppt) derived from solution mining the Bryan Mound salt dome located near Freeport, Texas, was
discharged into the Gulf of Mexico through a series of vertical pipes collectively called the "diffuser."
Disposal of brine had no apparent effect on either bottom-water temperature of dissolved oxygen. However,
salinity of the bottom water and pore water in the vicinity of the diffuser was increased above ambient levels as
much as 3 ppL The brine did not appear to effect a change in numbers of species collected near the diffuser,
nor did the amphipod populations (which are relatively sensitive to pollution) appear to be affected. However,
abundances of organisms may have been altered.

Harper, Jr., D. E., L. D. McKinney, R. R. Salzer and R. J. Case. 1981. The occurrence of
hypoxic bottom water off the upper Texas coast and its effects on the benthic biota. Contrib.
Mar. Sci. 24:53-79.
G-27

Hypoxic bottom water occurred off the upper Texas coast in May-July 1979 after heavy spring runoff and a
diatom bloom. Benthic assemblages at two study sites off Freeport, Texas decreased from spring densities of
3000-4000 individuals per m^ to 300-600 individuals per m*- by late July. Species diversity also decreased and
perturbations occurred in the Shannon-Werner diversity indices. Of the dominant taxa, polychaetes were least
affected by hypoxia and amphipods and echinoderms the most affected. Storm-caused waves in late July
initiated the breakup of hypoxic conditions; these conditions had completely abated by late September. A
short-lived irruption occurred immediately afterward as depopulated bottoms were reinvaded. Diversity and
abundances appeared to be returning to more normal conditions by early 1980.
318
-------
Harper, Jr., D. E., L. D. McKinney, J. M. Nance and R. R. Salzer. 1991. Recovery responses
of two benthic assemblages following an acute hypoxic event on the Texas continental shelf,
northwestern Gulf of Mexico. Pages 49-64 ia R. V. Tyson and T. H. Pearson (eds.),
Modern and Ancient Continental Shelf Anoxia. Geological Society Special Publication No.
58, The Geological Society, London, 470 p.
G-27

A hypoxic/anoxic event occurred in the northwestern Gulf of Mexico between May and July 1979. This event,
associated with warm water temperatures, water column stratification and the decay of a phytoplankton bloom,
led to the production of hydrogen sulfide that moved above the sediment-water interface and into the lower 2 m
of the water column. Regular monthly sampling at two sites off Freeport, Texas showed that abundances of
benthic organisms declined precipitously during the event The assemblage in deeper water apparently
stabilized within 1 yr. The shallower water assemblage, however, underwent a very different recovery process.
Each of the species underwent a "bloom" and constituted the numerical dominant for 1 to 3 mos, and then
declined and was replaced by another species "bloom." This sequential dominance pattern persisted until aboutv
May 1981,2 yrs after the hypoxic event, at which time polychaetes again became numerically dominant

Harris, A. H., J. G. Ragan and R. Kilgen. 1976. Oxygen Depletion in Coastal Waters. Final
Report. Project No. R/BOD-L, Office of Sea Grant, U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, Washington, D.C., 45 p.
G-7.1

Baseline studies were conducted on the southeastern Louisiana continental shelf as part of the environmental
data requirements for the proposed superport Hypoxic waters were found throughout several hundred square
miles of normally highly productive shrimping grounds in the Gulf of Mexico where there were significantly
less fish, crabs, shrimp, and other motile benthic organisms within this area. Hypoxia was found from May
1973 through September 1975 in varying degrees of magnitude, except following hurricanes that affected the
area. Results from nekton, zooplankton and benthic macroinfauna samples are given.

Hausknecht, K. A. 1980. Vol. V - Describe Surficial Sediments and Suspended Paniculate
Matter. la W. B. Jackson and G. M. Faw (eds.), Biological/Chemical Survey of Texoma
and Capline Sector Salt Dome Brine Disposal Sites off Louisiana, 1978-1979. NOAA Tech.
Memo NMFS-SEFC-29, NOAA/NMFS Final Report to DOE. U.S. Dept. of Commerce,
National Oceanic and Atmospheric Administration, National Marine Fisheries Service,
Galveston, Texas, 56 p.
G-7.1

This report summarizes measurements of surficial and suspended sediment characteristics which were made
during four cruises to the West Hackberry and Weeks Island brine disposal sites in June and October 1978 and
January and May 1979. The sites showed significant differences in sedimentology, with the West Hackberry
site being composed predominantly of fine-grained silt and clay (<40 % sand) with characteristically high
levels of total organic carbon averaging 12-15 mg/g. Conversely, sediments at Weeks Island were primarily
silty sand (> 70 % sand) with low levels of organic carbon (5-8 mg/g). Total organic carbon showed a
significant inverse correlation with grain size (total organic carbon increased with decreasing grain size).

Heck, K. L. 1987. The Common Rangia (Rangia cuneatd) in Perdido Bay: An Investigation of
Mass Mortality in October 1986. Report to Alabama Dept. of Economic and Community
Affairs, Contract No. ADECA-MESC-CZM-87-5. Marine Environmental Sciences
Consortium, Dauphin Island, Alabama.
G-l, F-28

The data presented here were gathered to shed light on the circumstances involved in a large mortality of
Rangia observed in the nearshore zone of upper Perdido Bay in early October 1986. At this time large
numbers of adult rangia, but few if any juveniles, were observed to be experiencing mortality by residents of
319
-------
communities along the Perdido Bay shoreline. The aims of the study were to: 1) determine the sizes, and age
and growth rates of clams involved in the October mortality; 2) use this information to assess whether affected
clams grew normally throughout their life, thereby indicating a single catastrophic event as a cause of
mortality, or whether clams had a record of depressed growth up to the time of their death,,suggesting a
lifetime of poor conditions for growth in Upper Perdido Bay; and 3) suggest the most plausible hypotheses to
explain the observed mortality.

Heffernan, T. L. 1970, An ecological evaluation of some tributaries of the Aransas Bay area.
Project No. CE-1-1. Pages 23-125 in Coastal Fisheries Project Reports 1969-1970. Texas
Parks and Wildlife Dept., Austin, Texas.
G-23

Environmental conditions were surveyed in the Copano and St. Charles Bay tributary areas in 1969 and 1970.
The white shrimp (Penaeus setiferus) and blue crab (Callinectes sapidus) habitat in the vicinity of Chiltipin
Creek and Mission River was found to be adversely affected by oilfield brine. Production of commercial
crustaceans in the Aransas River was found to be severely retarded by abnormal salinity and water quality
conditions attributed to oilfield brine from Chiltipin Creek. Tributaries of St Charles Bay had water of very
high quality and were normally very productive. The entire St. Charles Bay system appeared to be prime
habitat for adult and juvenile food and game species. Heavy rainfall alleviated poor conditions in Chiltipin
Creek, the Aransas River and the Mission River, but this relief was short-lived.

Heffernan, T. L. 1972. The effect of oilfield brine on the Mission River, Aransas Bay area.
Pages 37-76 in. Coastal Fisheries Project Reports 1972. Texas Parks and Wildlife Dept.,
Austin, Texas.
G-23

A daily discharge of 1.5 mil gallons of oilfield brine (containing approximately 36 gal of crude oil) into the
Mission River has retarded utilization of the stream by marine organisms and has eliminated the freshwater
fishery in the river below the city of Refugio. Hydrological samples collected from December 1971 to
November 1972 indicated conditions were within the tolerance limits of the marine organisms inhabiting
tertiary environments in the local area and the loss of Mission River as a nursery system was attributed
primarily to oil pollution.

Heffernan, T. L. 1971. Port Bay - An evaluation of the marine habitat. Project No. CE-1-2.
Pages 63-80 in. Coastal Fisheries Project Reports 1971. Texas Parks and Wildlife Dept.,
Austin, Texas.
G-23

Trawl samples taken at weekly intervals from December 1970 through July 1971 in Port Bay, a tertiary bay of
the Aransas Bay system, produced 38 species of fin fish and nine species of Crustacea. A 9-mo period of
below normal rainfall from November 1970 through July 1971 influenced white shrimp, Penaeus setiferus, and
blue crab, Callinectes sapidus, populations by raising salinities above optimum ranges during juvenile
migration periods. In September 1971, rainfall associated with tropical storm "Fern" dropped salinities from
above 30.0 to 0.0 ppL Eight hundred ninety six hydrographic samples collected during the survey were
correlated with population densities to establish the salinity influence on individual species. The parameters
determined for each sample were salinity, temperature, turbidity, pH, dissolved oxygen, calcium, total hardness
and magnesium.

Hegen, H. E. 1983. Monitoring of Coastal Finfish Resources for Sport Fish Management,
October 1981 - September 1982. Management Data Series No. 49, Texas Parks and Wildlife
Dept., Coastal Fisheries Branch, Austin, Texas, 157 p.
G-17, G-19, G-21, G-22, G-23, G-24, G-26.1, G-26.2
320
-------
Trends in relative abundance and size of six economically important saltwater fishes (red drum, spotted
seatrout, black drum, sheepshead, southern flounder and Atlantic croaker) were monitored with gill nets and bag
seines in eight Texas bay systems. Catch-rates and mean total lengths of each type are discussed.

Henley, D. E. and D. G. Rauschuber. 1981. Freshwater Needs of Fish and Wildlife Resources
in the Nueces-Corpus Christi Bay Area, Texas: A Literature Synthesis. Biological Services
Program Publ. FWS/OBS-80/10, U.S. Dept. of the Interior, Fish and Wildlife Service,
Washington, D.C., 410 p.
G-23

The highly variable environment of the Nueces-Corpus Christi Bay system is subject to many extremes,
including the effects of freshwater runoff from rural and urban areas; creeks and rivers; rainfall directly on the
Bay surface; and effluent return flows from various industrial, domestic, and agricultural users. Saline Gulf
water flows into the Bay primarily by way of the Corpus Christi Ship Channel at Port Aransas. Variability of
freshwater inflows results from numerous factors, such as hurricanes, droughts, channelization, and dredge and
fill activities. The objectives of this study were to relate the proposed construction of Choke Canyon
Reservoir and Harbor Island Deep-Water Port on resultant hydrologic effects that these structural features may
have on the biological productivity of the estuarine system.

Hern, S. C., W. D. Taylor, L. R. Williams, V. W. Lambou, M. K. Morris, F. A. Morris and J.
W. Hilgert. 1978. Distribution and Importance of Phytoplankton in the Atchafalaya Basin.
Publ. No. 277544, U.S. Environmental Protection Agency, Environ. Monitor. Support Lab,
Las Vegas, Nevada, (not in hand)
G-12

Hewatt, W. G. 1950. Studies on Dissolved Oxygen Content and Hydrogen Ion Concentration in
the Waters of Barataria Bay, Louisiana, 1945-1947. Project 9. Texas A&M University,
Texas A&M Research Foundation, College Station, Texas, lip.
G-10

Barataria Bay is a relatively shallow embayment on the Gulf coast of Louisiana, west of the mouth of the
Mississippi River. The surface of the Bay and its contiguous waters which are considered in this report is
about 400 square miles. The Bay is the center of a large shrimp and oyster fishing industry. Thirty-eight
sampling stations were selected in the Bay and the adjoining bodies of water. Only the dissolved oxygen and
the hydrogen ion concentration data are considered in the report

Higgins, G. G. and C. K. Eleuterius. 1978. Mississippi Sound: Volume, surface area and
bathymetric statistics. J. Miss. Acad. Sci. 23:39-45.
G-2.3

Area measurements were made of the bathymetry of Mississippi Sound contoured at 1-ft depth intervals using
a Leitz (TM) planimeter. Assuming a level surface, the measurement of surface area at mean low water for the
Sound was 22,915,708,304 ft2 (2,128,869,301 m2). Excluding the Intracoastal Waterway, the Biloxi
approach channels and that portion of the Gulfport and Pascagoula ship channels below the contiguous natural
Sound bottoms, a volume of 223,333,594368 ft3 (63,248,073,920 m3) was obtained at mean low water, with
an average depth of 9.76 ft (2.97 m). Considering the Gulfport and Pascagoula ship channels, the volume is
224,079,602,627 ft3 (63,459,343,424 m3), with an average depth of 9.77 ft (2.98 m) at mean low water. The
distribution of depths is skewed positively but 99 % of the total area has a depth of 20 ft (6.10 m) or less.

Ho, C. L. and B. B. Barrett. 1975. Distribution of Nutrients in Louisiana's Coastal Waters
Influenced by the Mississippi River. Tech. Bull. No. 17, Louisiana Wildlife and Fisheries
Commission, New Orleans, Louisiana, 39 p.
G-10
321
-------
The volume of freshwater introduced into Louisiana's coastal zone during 1973, both by rainfall and river
discharge, was the highest recorded since 1940. Selected nutrients (ammonium-N, [nitrate + nitrite]-N,
phosphate-P, and dissolved silicate), organic-N, and salinity were measured in Louisiana coastal waters from
the mouth of the Mississippi River to Caminada Bay during four sampling trips in 1973. Three of these
sampling trips coincided with high river discharge, and the last sampling effort occurred during low river
discharge. Resultant data showed the tremendous influence of the Mississippi River on nutrient concentrations
in the coastal waters adjacent to the river mouth. Nutrient contribution by the Mississippi River undoubtedly
accounts for the high production of fisheries in this region of the Gulf.

Ho, C. L. and B. B. Barrett. 1977. Distribution of nutrients in Louisiana coastal waters
influenced by the Mississippi River. Estuarine Coastal Mar. Sci. 5:173-195.
G-10

The volume of freshwater introduced into Louisiana's coastal zone during 1973, by rainfall and river discharge,
was the highest in the past 35 years. Water samples were taken from inshore estuarine areas as well as hi the
open Gulf of Mexico during 1973. Three of these sampling trips coincided with high river discharge and the
last trip was made during low river discharge. Analysis of the water samples showed that the nutrient content
of the water within the zone of the Mississippi River influence is directly related to the volume of water
discharged to the Gulf by the river. The high fishery productivity of the water adjacent to the river mouth is a
result of nutrient contribution by the Mississippi River. However, marshes play a key role in providing
organic matter and nutrients to the estuaries which serve as nursery grounds for many marine species.

Holland, J. S., N. J. Maciolek, R. D. Kalke and C. H. Oppenheimer. 1973. A Benthos and
Plankton Study of the Corpus Christi, Copano and Aransas Bay Systems. I. Report on the
Methods Used and Data Collected During the Period September, 1972 - June, 1973. First
Annual Report to the Texas Water Development Board. University of Texas Marine Science
Institute, Port Aransas, Texas.
G-23, G-24

Certain physical and chemical parameters of the water column were investigated in this study. Physical
parameters included air temperature, total depth, water temperature and conductivity. Chemical parameters
investigated included dissolved oxygen, organic nitrogen, nitrate, nitrite, ammonia, total phosphate,
orthophosphate, inorganic carbon and organic carbon. It is quite apparent that these are two very
hydrographically dissimilar estuarine systems. The Copano-Aransas system had, over the period reported, a
classic positive estuary salinity regime. In Corpus Christi Bay the salinity regimes were very confused.

Holland, J. S., N. J. Maciolek, R. D. Kalke and C. H. Oppenheimer. 1974. A Benthos and
Plankton Study of the Corpus Christi, Copano and Aransas Bay Systems. II. Report on Data
Collected During the Period July, 1973 - April, 1974. Second'Annual Report to the Texas
Water Development Board. University of Texas Marine Science Institute, Port Aransas,
Texas.
G-23, G-24

See Holland et al. (1973). Added to the 1973 study were the hydrographic parameter measurement of turbidity
and pH. Dissolved oxygen values followed essentially the same pattern during this study as was initially
observed.

Holland, J. S., N. J. Maciolek, R. D. Kalke, L. Mullins and C. H. Oppenheimer. 1975. A
Benthos and Plankton Study of the Corpus Christi, Copano and Aransas Bay Systems. III.
Report on Data Collected During the Period July 1974 - May 1975. Final Report to the Texas
Water Development Board. University of Texas Marine Science Institute, Port Aransas,
Texas.
G-23, G-24
322
-------
Study an extension of that presented in Holland et al. (1974). Low dissolved oxygen concentrations were
found in bottom waters of the Reynolds Metals Co. turning basin near the La Quinta Channel. Otherwise,
oxygen concentrations were high enough at most sites to not be a limiting factor.

Holland, J. S., N. J. Maciolek and C. H. Oppenheimer. 1973. Galveston Bay benthic
community structure as an indicator of water quality. Contrib. Mar. Sci. 17:169-188.
G-17

The objective of this study was to ascertain water quality through investigation of benthic community
structure. Various methods of community structure analysis including several species diversity indices,
rarefaction curves and a probability of interspecific encounter index were applied to data collected from selected
sites in Galveston Bay, Texas. Hydrographic data and sediment analysis were used in interpreting the results of
the various methods of investigating community structure. The different methods of analysis used in this
study showed very close agreement It is suggested that three of the five investigation sites in Galveston Bay
showed normal estuarine water quality. Two other stations showed evidence of large amounts of stress
probably due to water quality. One of the two was probably stressed due to natural causes, primarily salinity
fluctuations. The other, a channel site near a huge industrial complex, showed intermittent stress possibly due
to manmade pollution.

Hopkinson, Jr., C. S. and J. W. Day, Jr. 1979. Aquatic productivity and water quality at the
upland-estuary interface in Barataria Basin, Louisiana. Pages 291-314 in R. J. Livingston
(ed.), Ecological Processes in Coastal and Marine Systems. Proceedings of a Conference,
April 13-15,1978, Florida State University, Tallahassee, Florida. Marine Science, Vol. 10,
Plenum Press, New York.
G-10

Three fresh- to brackish-water coastal lakes and streams at the upland-estuary interface of Barataria Basin were
studied for a 1-yr period. Measurements of community production and metabolism, chlorophyll a, and water
column nitrogen and phosphorus were used to assess the functional relationship the upland connection has
with the estuary. Spatial distribution of selected water chemistry parameters indicates that artificial drainage
and navigation canals in the estuarine and upland area have changed the hydrologic regime. Nutrient loading
rates and high production values indicate that the area immediately adjacent to the upland is currently
hypereutrophic. Its potential to absorb increasing nutrient loads is in doubt

Hopkinson, Jr., C. S. and J. W. Day, Jr. 1980. Modeling the relationship between development
and storm water and nutrient runoff. Environ. Manage. 4(4) :315-324.
G-10

The EPA Storm Water Management Model was used to model the effects of urban and agricultural
development on storm water runoff from uplands bordering a Louisiana swamp forest Using this model, we
examined the effects of changing land use patterns. By 1995, it is projected that urban land on the uplands
bordering the swamp will increase by 321 %, primarily at the expense of land currently in agriculture.
Simulation results indicate that urbanization will cause storm water runoff rates to be up to 4.2 times greater
in 1995 than in 1975. Nutrient runoff will increase 28 % for nitrogen and 16 percent for phosphorus during
the same period. The environmental effects of these changes in the receiving swamp forest are examined.

Hopkinson, Jr., C. S., J. W. Day, Jr. and B. J. Kjerfve. 1985. Ecological significance of
summer storms in shallow water estuarine systems. Contrib. Mar. Sci. 28:69-77.
G-10

Dissolved oxygen, an integrative community metabolic parameter, was monitored in a shallow, coastal,
estuarine water body in Louisiana on days with and without thunderstorms to ascertain the ecological
importance of periodic meteorological mixing events. A thunderstorm caused complete overturn of stratified
water masses and substantially increased oxygen exchange across the air-water interface. Analysis of storm
323
-------
data for coastal Louisiana indicates a high frequency of occurrence of summer storms of sufficient magnitude to
completely mix shallow estuarine water bodies. Periodic mixing and reaeration of bottom waters may be an
important mechanism that increases the habitat value of shallow water bodies to commercially important
fishery species.

Horn, C. R. 1990. Water quality. Pages 53-62 ia Mobile Bay: Issues, Resources, Status, and
Management Proceedings of a Seminar, November 17, 1988, Washington, D.C. NOAA
Estuary-of-the-Month Seminar Series No. 15, U.S. Dept. of Commerce, National Oceanic
and Atmospheric Administration, Estuarine Programs Office, Washington, D.C.
G-2

Mobile Bay, located at the southern extremity of Alabama, receives drainage through the Mobile and Tensaw
River Systems from over 64 % of the land area of the State. The water use classifications of the bay and
tributary streams are high compared to the average of the remainder of the State due to the coastal nature of the
area and to widespread usage for human contact activities and for shellfish growth and harvesting. The water
quality environment is experiencing considerable stress. The Alabama Dept of Environmental Management
maintains an ambient water quality monitoring capability-at 26 locations in the two-county (Mobile-Baldwin)
area, representing 38 % of the total statewide capability, which is indicative of the high priority and value
assigned to coastal Alabama. Though generally good throughout this area, existing water quality does not
meet the higher standards in certain areas. Recent data suggests strongly, however, that standards are not met
in much of the coastal area due to natural causes.

Housley, H. L. 1976. Distribution, Periodicity, and Identification of the Phytoplankton in the
Bay of St. Louis, Mississippi and the Northeastern Gulf of Mexico. Ph.D. Dissertation,
University of Southern Mississippi, Hattiesburg, Mississippi, 206 p.
G-5

The initial objective of this research was to photograph and describe the commonly occurring species and
construct a dichotomous key using the photographs as illustrations. The study area included the Bay of St.
Louis, Mississippi, and areas east and west of the Mississippi River Delta. The area included a shallow
estuarine bay and extended offshore to the 50-fm isobath. The study was later structured to include the seasonal
periodicity of the planktonic algae in the Bay of SL Louis and the distribution of the plankton in the
northeastern Gulf of Mexico. To achieve these objectives, commonly occurring species of the Bay were
identified and their periodicity and distribution were correlated with chemical and physical parameters.
Huang, T.-C. and H. G. Goodell. 1967.
J. Sediment. Petrol. 37(2):449-474.
F-13
Sediments of Charlotte Harbor, southwestern Florida.
Bottom grab samples and shallow cores from the Charlotte Harbor system have been studied to show the
distribution of its sediments textural and compositional properties. The sediments are relatively uniform in
character throughout the harbor system. The distribution of the sediment properties shows that the sediments
are shifted by the two major tidal circulations of the harbor proper and of San Carlos Bay. Multivariate
nonlinear regression is used to relate the sediment characteristics to their provenance, transportation, and
depositional environments.

Ingham, M. 1982. Distress signals from inner space? Coastal Oceanography and Climatology
News 4(4):47. \
G-7.1

The regularity of reports of dinoflagellate blooms, red tide conditions, or critically low oxygen concentrations
in bottom water masses C'dead areas") in the northwestern Gulf of Mexico leads one to wonder if these episodes
are signals of degrading environmental conditions in recent years .or if observers are just paying closer attention
324
-------
to normal circumstances. Parallels are drawn with the areas of hypoxic or anoxic bottom waters off New
Jersey in the summer of 1976. . ;

Ingle, R. M., A. R. Ceurvels and R. Leinecker. 1955. Chemical and Biological Studies of the
Muds of Mobile Bay. Report to the Division of Seafoods, Alabama Dept. of Conservation.
Wetumpka Printing Co., Wetumpka, Alabama, 14 p.
G-2 •' . ' • •• . -

This study concerns the inorganic and organic nutrients, carbohydrates, fats, and proteins contained in the muds
of Mobile Bay. Presumably, these compounds can appear in the muds either adsorbed on the surface of
individual particles or dissolved or paniculate in the interstitial water. An attempt was also made to determine
if any of the above substances contained toxic components, or if the muds, in suspension, were harmful to fish
life. This report covers studies carried out during the spring and summer of 1954. All sample were obtained
from dredges, or from water, in Mobile Bay. The activity of the dredges was centered about 2 to 3 miles west
of Great Point Clear, Alabama.

Isphording, W. C. 1982. Mis-interpretation of environmental monitoring data—a plague on
mankind! Trans. Gulf Coast Assoc. Geol. Soc. 32:399-411.
G-2

All too often, data collected as part of environmental monitoring, programs are subjected to interpretation by
those unqualified to do so. A recent example involved a study carried out in Mobile Bay where geochemical
data were used to "identify" bottom sediments contaminated by the drilling of an exploratory well. Elevated
barium contents of up to several hundred ppm near the mouth of the Bay were attributed to the spillage of
drilling mud, although all drill cuttings, mud, and effluent from the rig had been pumped directly onto barges
for disposal at sites onshore. Partitioning of the barium in the Mobile Bay sediments disclosed that most was
associated with the various clay mineral phases and substitutional impurities in shell material. Thus, the
barium observed was not the direct result of the drilling operation but rather reflected its common association
with disseminated oxides in the bottom muds, as a chelated form adhering to the clay platelets and as
replacement ions in the lattice of carbonate minerals.

Isphording, W. C., D. Imsand and G. C. Flowers. 1987. Storm-related rejuvenation of a
northern Gulf of Mexico estuary. Trans. Gulf Coast Assoc. Geol. Soc. 37:357-370.
F-24

The massive influx of sediment from the Apalachicola River system has built an extensive delta system at the
river's mouth. In the vicinity of the delta, sedimentation rates up to 10 mm/yr have been measured. Analysis
of bathymetric data, dating back to the mid-1880s disclosed that Apalachicola Bay has been undergoing
exceptionally rapid infilling which persists. The passage of two hurricanes near the Bay in 1985, however,
generated high-velocity currents that scoured some 3.6 billion cubic feet of sediment from the bottom of the
Bay, completely changing the character of the texture, mineralogy, and heavy metal chemistry of the bottom
sediments. Even more remarkable, perhaps, is the fact that over 83 mil tons of sediment was carried by the
currents out through one of the passes into the Gulf of Mexico. The removal of this quantity of sediment has
thus returned the Bay to bathymetric conditions existing in the early 1800s and significantly extended the life
of the Bay.

Isphording, W. C. and G. M. Lamb. 1979. The Sediments of Mobile Bay. Report to. Rept.
No. 80-003 for the Alabama Coastal Area Board, Dauphin Island Sea Lab, Dauphin Island,
Alabama, 24 p.
G-2

Mobile Bay constitutes the primary depositional basin for the sixth largest river system in the U.S., in terms
of area. The mean discharge of the river system through a 25-yr period is over 60,000 ft^/s. This large
325
-------
volume is funneled into a relatively small estuary, creating a unique site for the study of the interactions of a
fluvial-estuarine system. Although new data are constantly being accumulated concerning conditions within
the Bay, there is still a dearth of knowledge. The purpose of this study is to map the sediment distribution
within the bay at the present time. This includes both the distribution of sediments by size, and the
distribution of the various clay minerals included in the sediments. This study is meant to provide a basis for
monitoring future change, and a better understanding of the processes that are taking place within the Bay, so
that more intelligent decisions can be made regarding the management of this environment.

Isphording, W. C. and G. M. Lamb. 1980. The Sediments of Eastern Mississippi Sound. Rept.
No. 80-003 for the Alabama Coastal Area Board, Dauphin Island Sea Lab, Dauphin Island,
Alabama, 17 p.
G-2.2

This study deals with the eastern portion of the Sound, lying largely within Alabama, and an adjacent portion
in Mississippi. The western boundary of the study area is generally from Petit Bois Island, on the south, to
the Grande Batture Islands on the northern side. The purpose of the study is to map the sediment distribution
in the eastern portion of Mississippi Sound. This includes both the distribution of the sediments by size, and
the distribution of the various clay minerals included in the sediments. This study is meant to provide the
basis for monitoring future change, and a better understanding of the processes that are taking place within the
Sound, so that more intelligent decisions can be made regarding the management of this environment.

Johansson, J. O. R. and R. R. Lewis, m. 1991. Recent Improvements of Water Quality and
Biological Indicators in HiUsborough Bay, a Highly Impacted Subdivision of Tampa Bay,
Florida, U.S.A. A manuscript submitted to the International Conference on Marine Coastal
Eutrophication, March 21-24,1990., Bologna, Italy, 16 p. (in press)
F-15

Hillsborough Bay water quality has recently improved in response to reduced nitrogen loading caused primarily
by the conversion of Hooker's Point Wastewater Facility from primary to advanced treatment. Less nitrogen
is now available for phytoplankton growth, and the reduced biomass has apparently allowed for improved water
column light penetration. Evidently, seagrasses and the attached macroalgae Caulerpa have responded to the
increased light penetration by colonizing shallow areas. Although this trend is encouraging, most shallow
areas in Hillsborough Bay still lack macrophyte vegetation.

Johansson, J. O. R., K. A. Steidinger and D. C. Carpenter. 1985. Primary production in Tampa
Bay, Honda: A review. Pages 279-344 in S. F. Treat, J. L. Simon, R. Rr Lewis, III and R.
L. Whitman, Jr. (eds.), Proceedings of the Tampa Bay Scientific Information Symposium,
May 1982. Sea Grant Project No. IR/82-2. Grant No. NA80AA-D-00038. Florida Sea
Grant College, Report No. 65, Burgess Publishing Co., Minneapolis, Minnesota.
F-15 . .

A review of historical primary production data; discussion of methodologies and shortcomings; outline of
future research needs for understanding the carbon cycle of the Tampa Bay system; and discussion of the carbon
cycle in relation to trophic dynamics.

Johnson, Jr., R. B. 1974. Ecological changes associated with the industrialization of Cedar
Bayou and Trinity Bay, Texas. Texas Parks and Wildlife Dept. Tech. Ser. 16:1-79.
G-17

Cedar Bayou (a tributary of Galveston Bay) and Trinity Bay were studied before and after construction and
operation of two industries. Cedar Bayou is the discharge site for U.S. Steel Co., and the intake site for
Houston Lighting and Power Co.'s Cedar Bayou Generating Station. Trinity Bay, near Point Barrow, is the
discharge site for thermal effluents from the power plant Ninety percent of dissolved oxygen values in Trinity
Bay were above 6.0 ppm, reflecting unpolluted conditions. Turbidity values were highest during heavy river
326
-------
discharge. Compared to values in the Trinity Bay, the power plant discharge into Trinity Bay had higher
salinity, higher temperature and lower turbidity. Temperature and dissolved oxygen content of the effluent
decreased after the effluent was diverted through the cooling pond.

Johnson, Jr., R. B. 1977. Fishery survey of Cedar Lakes and the Brazos and San Bernard River
Estuaries. Texas Parks and Wildlife Dept. Tech. Ser. 23:1-65.
G-18

A fishery study of Cedar Lakes and the lower parts of the Brazos and San Bernard Rivers, Brazoria County,
Texas, was conducted during February 1973 to January 1975. Samples were collected at 17 stations each
month to determine hydrological conditions and occurrence of estuarine organisms. Salinity, temperature,
dissolved oxygen values, pH values and turbidity were determined in surface- and bottom-water samples. An
otter trawl was used to sample nekton. Benthos was sampled quarterly at the 17 stations with an Ekman
dredge. Samples were collected at four stations monthly after December 1973 with a minnow seine. Area and
station descriptions are presented. Dissolved oxygen values were highest in winter and lowest in summer.
Values less than 3.0 ppm were recorded in the Brazos and San Bernard Rivers. Effects of pollution are
discussed.

Jones, J. I, R. E. Ring, M. O. Rinkel and R. E. Smith (eds.). 1973. A Summary of Knowledge
of the Eastern Gulf of Mexico, 1973. Publ. No. HE-1 - IJE-50, State University System of
Florida, Institute of Oceanography, St. Petersburg, Florida, 590 p.
F-9 through G-9

This report represents a compilation and evaluation of selected studies of the significant natural and artificial
environmental characteristics of the eastern Gulf of Mexico. It has been prepared by a group of qualified
scientists collectively conversant with the major environmental .aspects of the subject region. The purpose of
this report is to provide an overview of the current status of knowledge and information on past and ongoing
studies which are significant for a more complete understanding of the environment and ecology of this area.
Selected investigations have been utilized by the respective authors, and there has been no attempt to list or
discuss all studies within the area.

Jones, R. S., J. J. Cullen, R. G. Lane, W. Yoon, R. A. Rosson, R. D. Kalke, S. A. Holt, C. R.
Arnold, P. L. Parker, W. M. Pulich and R. S. Scalan. 1986. Studies of Freshwater Inflow
Effects on the Lavaca River Delta and Lavaca Bay, Texas. Final Report to Texas Water
Development Board, Austin, Texas, by The University of Texas at Austin, Marine Science
Institute, Port Aransas, Texas.
G-21.

See Cullen and Jones (1986).

Juneau, Jr., C. L. 1975. An Inventory and Study of Vermilion Bay - Atchafalaya Bay Complex.
Phase I, Area Description. Phase H, Biology. Phase HI, Hydrology and Water Chemistry!
Tech. Bull. No. 13, Louisiana Wildlife and Fisheries Commission, New Orleans, Louisiana
153 p.
G-12, G-13

The Vermilion-Atchafalaya Bay estuarine complex is a vast open water brackish system whose primary sources
of fresh water are the Atchafalaya and Vermilion Rivers. There are approximately 475,000 surface acres within
the system. Vegetation in the complex varies from fresh to brackish, depending on nearness to the mouth of
the Atchafalaya River. Biological sampling was conducted from April 1972 through March 1974 at 12 trawl,
two seine, and four plankton stations in the complex. A total of 63 species of fishes and nine species of
invertebrates were collected. The areal and seasonal distribution of the species are discussed. In the two years
of field sampling, hydrological conditions varied considerably, due to flooding conditions on the river systems.
327
-------
Trends and seasonal changes regarding water temperature, salinity, and various chemical parameters are
discussed; tables and graphs supplement the discussion.

Junot J. A., M. A. Poirrier and T. M. Soniat. 1983. Effects of saltwater intrusion from the toner
Harbor Navigational Canal on the benthos of Lake Pontchartrain, Louisiana. Gulf Res. Rep.
7(3):247-254.
G-7

A study of the benthos of southern Lake Pontchartrain, Louisiana, was conducted from July 1976 to July
1978 Seven offshore stations and three stations in the New Orleans Marina complex were sampled
seasonally. Offshore stations formed a transect from the Lake Pontchartrain Causeway to the Inner Harbor
Navigation Canal (IHNC). A west-to-east gradient of increasing salinity and salinity stratification was evident
Faunal differences among stations were assessed using indices of diversity, biological dominance, pollution,
and station homogeneity. The fauna of the marina stations had a low species diversity and was dominated by
annelids indicative of a stressed environment The fauna of stations near the fflNC were similar to the marina
stations. Moving westward from the IHNC, species diversity increased and the fauna became dominated by
mollusks. Stressful conditions associated with the intrusion of water from the IHNC into Lake Pontchartrain
appeared to be responsible for the faunal differences observed.

Kalke R. D. 1986. Zooplankton. Chapter 4 in R. S. Jones et al, Studies of Freshwater Inflow
Effects on the Lavaca River Delta and Lavaca Bay, Texas. Final Report to the Texas Water
Development Board, Contract No. 55-61011. Tech. Rept. No. TR/86-006, University of
Texas Marine Science Institute, Port Aransas, Texas, 14 p.
G-21

Zooplankton sampling was conducted to monitor the effects of freshwater inflow on the spatial and temporal
distribution of zooplankton at seven stations in upper Lavaca Bay from November 1984 through August 1985
(Year 1) and October 1985 through August 1986 (Year 2). In Year 2, sampling effort was increased to cover
marine input from the lower bay by adding six stations along a transect from state highway 35 causeway south
along the Matagorda Ship Channel to marker 35 and 36. Historical and concurrent stream flow data indicate
that Year 1 was a wet year and Year 2 was a drier year. Zooplankton data reflect these differences. See also
Cullen and Jones (1986).

Kalke R D and P. A. Montagna. 1989. A review: The effect of freshwater inflow on the
benthos of three Texas estuaries. Pages 185-234 in P. A. Montagna (ed.), Nitrogen Process
Studies (NIPS): The Effect of Freshwater Inflow on Benthos Communities and Dynamics.
Final Report to the Texas Water Development Board. Tech. Rept. No. TR/89-011,
University of Texas Marine Science Institute, Port Aransas, Texas.
G-21, G-22, G-24

The effect of freshwater inflow on benthic community structure in three Texas estuaries is the subject of a
literature review. All three estuaries can be divided into marine, estuarine, and freshwater zoogeographic zones.
But the boundaries of the zones are regulated by three factors: 1) location of the estuary, 2) whether the bay has
a direct opening to the Gulf of Mexico, and 3) the interannual variability in rainfall and freshwater inflow. In
an open system, such like the Lavaca-Tres Palacios and Nueces estuaries, biomass and abundance typically
increase near the opening to the Gulf, but in a closed system, such as the Guadalupe Estuary, abundance and
biomass usually decrease toward the marine influenced zone. This indicates that the estuaries must be treated
independently when making management decisions, but that we can develop a generic model which describes
the effect of freshwater inflow on estuarine benthic dynamics.

Kalke, R. D. and P. A. Montagna. 1991. The effect of freshwater inflow on macrobenthos in the
Lavaca River delta and upper Lavaca Bay, Texas. Contrib, Mar. Sci. 32:49-71.
G-21
328
-------
A two year study on the effect of freshwater inflow on macrobenthos at selected sites in the upper portion of
the Lavaca River and Bay was conducted from November 1984 through August 1986. Lowest densities
occurred in lakes, and highest densities occurred in creek deltas. Sediment grain size did not have a significant
effect on spatial distribution. Temporal changes of inflow had a large effect on spatial variability, because
freshwater species had extended ranges during the high-flow year. Temporal variation in the benthic
community during the study was associated with high inflow rates during the first year. Freshwater inflow is
apparently necessary to induce the recruitment of low salinity species in the upper bay.

Kaufmann, P. R., A. T. Herlihy, J. W. Elwood, M. E. Mitch, W. S. Overton, M. J. Sale, J. J.
Messer, K. A. Cougan, D. V. Peck, K. H. Reckhow, A. J. Kinney, S. J. Christie, D. D.
Brown, C. A. Hagley and H. I. Jager. 1988. Chemical Characteristics of Streams in the
Mid-Atlantic and Southeastern United States (National Stream Survey-Phase I). Vol. I:
Population Descriptions and Physico-Chemical Relationships. Publ. No. EPA/600/3-
88/021a, U.S. Environmental Protection Agency, Washington, D.C., 397 p.
F-26, F-27

The objectives of the National Stream Survey-Phase I (NSS-I) were to: 1) determine the percentage, extent
(number, length, and drainage area, location, and chemical characteristics of streams in the Mid-Atlantic and
Southeast that are presently acidic, or that have low ANC and thus might become acidic in the future; 2)
identify streams representative of important classes in each region that might be selected for more intensive
study or long-term monitoring. The basic results of the NSS-I are population descriptions of the location,
number, length, and percentage of streams within referenced ranges of chemical concentrations. The most
important of these descriptions are those concerning ANC and pH. Further data interpretation includes an
examination of regional patterns in the relationships among the chemical constituents within stream waters in
an effort to infer the possible geochemical factors and anthropogenic impacts controlling stream chemistry.
Lastly, a high-interest segment of the stream population with low ANC was examined and classified according
to probable sources of acidity.

Kelly, J. R. (ed.). 1981. Symposium on Mississippi Sound. Proceedings of a Conference, June
25-26, 1981, Biloxi,. Mississippi. Publ. No. MASGP-81-007, Mississippi-Alabama Sea
Grant Consortium, Ocean Springs, Mississippi, 152 p.
G-2.2, G-2.3

A series of publications on the Mississippi Sound estuary, covering flora, fauna, pollutants in coastal waters,
resource management, hydrology, socioeconomics, and geology.

Kennedy, V. S. (ed.). 1982. Estuarine Comparisons. Proceedings of the Sixth Biennial
International Estuarine Research Conference, November 1-6, 1981, Gleneden Beach,
Oregon. Academic Press, New York, 709 p.

This book represents a first in the efforts of the Estuarine Research Federation to compare the knowledge that
they have gained about many of the world's estuaries. It is the first real effort to compare different estuaries.
Such estuarine comparisons are vital to the future of estuaries. All future research, as well as management
concepts, must consider the diversity of estuaries in the world, the various management options available, and
the wealth of information gained by comparing estuaries, to make environmentally effective and economically
workable management decisions.

Keys, V. E. 1975. Management of Florida red tides regarding shellfish harvesting. Pages 483-
488 in. V. R. LoCicero (ed.), Proceedings of the First International Conference on Toxic
Dinoflagellate Blooms. The Massachusetts Science and Technology Foundation, Wakefield,
Massachusetts, 541 p.
F-9 through F-27
329
-------
Historically, red tides have occurred along the Florida west coast from Tarpon Springs to the Everglades.
Since 1963, red tides of public health significance have occurred in areas outside the historical zone. The
northwest coast (Panhandle) of Florida experienced a red tide bloom in the early part of September 1974,
necessitating the closure of these waters for shellfish harvesting.

Khalid R A W H. Patrick, Jr. and R. P. Gambrell. 1978. Effect of dissolved oxygen on
chemical transformations of heavy metals, phosphorus, and nitrogen in an estuarine sediment.
Estuarine Coastal Mar. Sci. 6(l):21-35.
G-10

The effect of dissolved oxygen on the chemical transformations of Fe, Mn, Zn, Cu, Pb, Cd, NH4+-N and P in
an estuarine sediment suspension was investigated under laboratory conditions. The data indicate that
increasing oxygen concentrations in the gas mixture resulted in lower sediment pH and higher oxidation-
reduction potential with time. Changes in redox potential and pH strongly modified the distribution of trace
metals in various chemical fractions. Phosphorus and NH4+-N concentrations decreased sharply with time as a
result of increased redox potential levels in the 2.1 % and 21 % oxygen levels. This indicates that oxidized
sediment conditions may be an important factor in regulating eutrophication by reducing levels of P and N
available for biota.

Kjerfve, B. J. (ed.). 1988. Hydrodynamics of Estuaries. Vol. 1. Estuarine Physics. CRC
Press, Boca Raton, Florida, 165 p.

This volume summarizes many of the prevalent concepts and approaches in the investigation in hydrodynamics
and physical processes of estuaries. Leading scientists in the field were asked to contribute chapters, which are
broadly summarizing in nature. It is intended to be useful to oceanography students, research workers in the
field, and persons charged with the management of our estuarine resource. This volume focuses on estuarine
physics and physical processes and interpretations.

Kierfve, B. J. and J. E. Sneed. 1984. Analysis and Synthesis of Oceanographic Conditions in
the Mississippi Sound Offshore Region. Vol. I and H. Final Report, Contract DACW 01-
83-R-0014. U.S. Army Corps of Engineers District, Mobile, Alabama, 253 p. (not in hand)
G-2.1

Knudson K. and C. E. Belaire. 1975. Causes and probable correctives for oxygen depletion fish
kills in the Dickinson Bayou estuary: A field study and simplified algal assay. Contnb. Mar.
Sci. 19:37-48.
G-17

Frequent oxygen depletion fish kills, caused by dense algal blooms, have occurred during summers in the 6-km
portion of Dickinson Bayou directly upstream from two sewage treatment plants. These plants are the major
contributors of wastes to the bayou. During summer periods of low freshwater inflow, the treatment plant
effluents are carried upstream by tidal action, causing dense algal blooms; algal density is much less above
tidal influence and downstream from the plant outfalls. Algal assays demonstrated that if the plants employed
chemical coagulation to remove phosphorus, the summer algal densities in the critical 6-km portion of the
bayou would be reduced to concentrations corresponding to, or less than, the levels found in the rest of the
bayou. Such treatment would thereby reduce the probability of summer fish kills.

Krutak, P. R. 1978. Holocene Ostracoda of Bay St. Louis, Mississippi, U.S.A.
Micropaleontology 24(3):225-250.
G-5

Forty-three quantitative (100 cm3) bottom samples from Bay St Louis, on the coast of Mississippi, have
yielded 1623 ostracods. Sixteen species of podocopid ostracods occur in these samples, in four discrete
330
-------
sedimentary biotopes of the Bay area: estuaries, marshes, bay, and sound. Comparison of the thanatocoenosis
(total population - live + dead) and biocoenosis (live only) of the 16 species reveals significantly different map
distributions in each of the four sedimentary fades; of the 16 species of the thanatocoenosis only 10 are
present in the biocoenosis. Total ostracod populations (live + dead) vary from none in 17 samples to a
maximum of 464 individuals per 199 cm^ in one. Total populations and relative abundance of individuals is
higher in estuaries and marshes, lower in the Bay and sound. The proportion of living ostracods is higher in
the Bay, marshes, and estuaries than in the sound biotope.

Landry, A. M. and H. W. Armstrong. 1980. Vol. IV - Determine Seasonal Abundance,
Distribution and Composition of Zooplankton. In W. B. Jackson and G. M. Faw (eds.),
Biological/Chemical Survey of Texoma and Capline Sector Salt Dome Brine Disposal Sites
off Louisiana, 1978-1979. NOAA Tech. Memo NMFS-SEFC-29, NOAA/NMFS Final
Report to DOE. U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, National Marine Fisheries Service, Galveston, Texas, 179 p.
G-7.1

Demersal finfishes and macro-crustaceans were trawled from proposed West Hackbeny and Weeks Island brine
disposal sites off Louisiana during summer and fall 1978 and winter and spring 1979. Results indicated that
74 taxa of finfish comprising 41,369 individuals and 25 species of macrocrustaceans representing 31,120
specimens were taken. Overall mean catch at West Hackbeny stations exceeded that for Weeks Island by more
than double.

LaRose, H. R. and B. F. McPherson. 1983. Chemical and Hydrologic Assessment of the
Caloosahatchee River Basin, Lake Okeechobee to Franklin Lock, Florida. U.S. Geological
Survey, Water-Resources Investigations Report 83-4126. Dept. of the Interior, U.S.
Geological Survey, Denver, Colorado, 63 p.
F-12

This report is restricted to the freshwater reaches of the system, but identifies the sources of nutrients.
Contributions of nitrite plus nitrate, orthophosphate and total phosphorus from the basin and the river
substantially exceeded input from Lake Okeechobee, while concentrations of ammonia from the river and basin
were quite small compared to the input from the lake. In most tributaries, concentrations of nitrogen and
phosphorus compounds were lower than those in river.

Lee, J. M., W. J. Wiseman, Jr. and F. J. Kelly. 1990. Barotropic, subtidal exchange between
Calcasieu Lake and the Gulf of Mexico. Estuaries 13(3) :258-264.
G-15

Long-term measurements of flow through Calcasieu Pass, Louisiana, are compared to water level variations
within Calcasieu Lake, Louisiana. Except during periods of freshets driven by local rainfall, the exchange is
shown to be predominantly barotropic. A simple wind-driven model accounts for the observed phase relations
between wind, current, and water level.

Leming, T. D. and W. E. Stuntz. 1984. "Zones of coastal hypoxia revealed by satellite scanning
have implications for strategic fishing. Nature 310(5973): 136-138.
G-7.1, G-27

Hypoxic and occasionally anoxic bottom waters occur along the inner continental shelf of Texas and
Louisiana. Little is known, however, about the spatial and temporal scales of these hypoxic areas. Because
hypoxia appears to be related to surface chlorophyll and temperature, which can both be measured with the
Coastal Zone Color Scanner on board the Nimbus 7 spacecraft, we have tried to determine if conditions
favorable for formation of hypoxia could be detected and monitored from space. A linear discriminant function
successfully identified areas of bottom-water hypoxia detected by research vessels for as many as 10 d after
331
-------
satellite overpass. The discriminant function also successfully predicted hypoxic areas in June 1983 without
resort to research vessel data. Shrimp and finfish were absent in the hypoxic zones; hence, the mapping from
space of conditions favorable for hypoxia development may have significant marine resource implications for
both strategic fishing and management.

Lewis R R III. 1989. Biology and eutrophication of Tampa Bay. Pages 89-112 iaE. D.
Estevez (ed), Tampa and Sarasota Bays: Issues, Resources, Status, and Management.
Proceedings of a Seminar, December 10, 1987, Washington, D.C. NOAA Estuary-of-the-
Month Seminar Series No. 11, U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, Estuarine Programs Office, Washington, D.C.
F-14, F-15

Studies were initiated in response to the problem of blooms of toxic dinoflagellates known as "red tides,"
particularly the massive blooms of 1946-1947. The findings of all studies to date have revealed: 1) a north-to-
south, or head-to-mouth, gradient exists in phytoplankton species numbers; 2) nannoplankton generally are the
dominant size class of the phytoplankton; 3) at least 272 species of phytoplankton occur in the bay; 4) short-
term fluctuations in species composition and standing crop are common; 5) the majority of the bloom species
are resident in the bay but significant blooms occasionally occur due to species which invade from the Gulf of
Mexico; and 6) many of the previous studies utilized analytical procedures which limit the quantitative
comparison of all data; some uniform sampling strategy and analytical procedures are needed to make future
data more usable.

Lewis, R. R., HI and E. D. Estevez. 1988. The Ecology of Tampa Bay, Florida: An Estuarine
Profile. Biological Report No. 85(7.18), U.S. Dept. of the Interior, Fish and Wildlife
Service, National Wetlands Research Center, Washington, D.C., 132 p.
F-15

Tampa Bay is Florida's largest open-water estuary and one of the most highly urbanized. This report
summarizes and synthesizes many years of scientific investigation into Tampa Bay's geology, hydrology and
hydrography, water chemistry, and biotic components. Significant changes occurring as a result of
urbanization and industrialization include significant declines in intertidal wetlands and seagrass meadows,
changes in circulation and flushing, and degradation of water quality. Important management issues include
dredge and fill operations, restoration of fisheries, increasing freshwater flow to the Bay, and eutrophication.

Lind,W B. 1983. Chemical and Physical Characteristics of Water in Estuaries of Texas, October
1975 - September 1976. Prepared by the U.S. Geological Survey. Rept. No. 275, Texas
Department of Water Resources, Austin, Texas, 203 p.
G-16, G-17, G-18, G-19, G-20, G-21, G-22, G-23, G-24, G-26

In September 1967 the USGS and TWDB began a cooperative water-resources investigation of the principal
estuaries along the Texas coast except the Rio Grande estuary. The objectives are to define 1) the occurrence,
source, and distribution of nutrients; 2) the physical, organic, and inorganic water-quality; constituents and their
areal distribution and time variations; 3) the chemico-physical characteristics of Gulf water that enters the
estuaries, 4) the occurrence, quality, quantity, and dispersion of drainage entering the estuarine systems, and 5)
the current patterns, directions, and rates of water movement. This report presents data collected during water
year 1976 and is one of a series of annual data reports.

Lindall, Jr., W. N., W. A. Fable, Jr. and L. A. Collins. 1974. Additional studies of the fishes,
macroinvertebrates, and hydrological conditions of upland canals in Tampa Bay, Florida.
Fish. Bull. 73(l):81-85.
F-15

Hydrological and biological data from a concluding study of upland canals in Tampa Bay, Florida are presented
and compared with those collected the previous year. Critically low levels of dissolved oxygen occurred more
332
-------
frequently and over a longer period in the second year. Most affected were the inland portions of the canal
system where the number of species declined markedly over the previous year. Impoverishment of fauna on or
near the bottom is expected to recur during summer months because of oxygen depletion resulting from a
combination of continuing accumulation of decomposing organic sediment, warm water, and little circulation
in the dead-end canals.

Livingston, R. J. 1986. The Choctawhatchee River-Bay System. Center for Aquatic Research
and Resource Management, Florida State University, Tallahassee, Florida, 1,075 p. (not in
hand)
F-26

Livingston, R. J. 1987. Field sampling in estuaries: The relationship of scale to variability.
Estuaries 10(3): 194-207.
F-24

The spatial/temporal scaling problem (i.e., fitting a given research question to the dimensions of variability of
the study area) is particularly pronounced in highly variable systems such as estuaries. Long-term,
multidisciplinary studies in this system were used to evaluate variation of different physical, chemical, and
biological factors. Specific limitation of weekly, monthly, and quarterly sampling intervals were directly
related to the efficiency of the sampling gear, the range of variation in the study parameters, and specific
biological features (motility, recruitment, natural history) of infaunal macroinvertebrates and epibenthic
organisms. Unless experimental studies and field sampling programs are scaled to the dimensions of the
research problem and the study area in question there will be a continued proliferation of trivial studies at one
end of the continuum and the progressive deterioration of estuarine resources at the other.

Livingston, R. J. 1989. Historical Overview and Data Review, Perdido River Complex,
Elevenmile Creek, Bayou Marcus and the Perdido Bay System. Environmental Planning and
Analysis, Inc., Tallahassee, Florida, 68 p.
F-28,G-l

A review was conducted concerning the historical changes that have taken place in the Perdido Drainage
System. According to various sources, serious changes associated with human activities have taken place in
the basin in recent times. Causative factors are postulated including dredging, timbering activities, agricultural
practices, paper manufacturing processes, municipal development (sewage/septic waste releases and stormwater
runoff), and sports/commercial fishing. Definitive cause-and-effect relationships have not been established by
the existing, somewhat inconsistent scientific data base. Various studies of Elevenmile Creek and the Perdido
estuary are currently being carried out by a variety of private and public agencies and groups. These studies
will address system-wide environmental questions in the Perdido Drainage System. Such data will be used in
the long-term planning and resource management in the region. An appendix consisting of maps, charts,
interview questions, and data is included.

Livingston, R. J. 1991. Historical relationships between research and resource management in
the Apalachicola River estuary. Ecological Applications l(4):361-382.
F-24.

A continuous field research effort has been carried out in the Apalachicola River estuary since March. 1972.
The information generated from this interdisciplinary study has been directly applied to the management of the
Apalachicola resource by means of closs associations among local, state, and federal officials and university
scientists. During 1972-1983, scientific data were instrumental in the prevention of the impoundment of the
Apalachicola River. Other initiatives were carried but that were designed to protect the naturally high
productivity of the river estuary. Since 1983, there has been a gradual reduction in the importance of research
as an integral part of the planning and management process in the Apalachicola system. The author sees this
regional trend as also a national pattern.
333
-------
Livingston, R. J. 1983. Resource Adas of the Apalachicola Estuary. Grant No. NA80AA-D-
00038. Rept. No. 55, Sea Grant Project No. T/P-1, Florida Sea Grant College Program,
University of Florida, Gainesville, Florida, 64 p.
F-24

The Apalachicola Valley has been part of a major experiment to determine if scientific information can indeed
be used to develop a resource management program to meet those needs. The central question remains how to
broaden the existing, relatively narrow economic base while continuing to maintain one of the last naturally
functional big river basins in the country. It is with these challenges in mind that this atlas has been written.

Livingston, R. J. 1984. Trophic response of fishes to habitat variability in coastal seagrass
systems. Ecology 65(4): 1258-1275.
F-22

Shallow coastal areas of the northeast Gulf of Mexico are physically unstable in terms of short-term, seasonal,
and year-to-year changes in temperature, salinity, nutrient concentration, and other water quality features. A 9-
yr comparison was made of two estuaries, one polluted and one in the natural state, to determine the response
of fish assemblages to habitat alteration in space and time. Apparently slight water quality changes due to
pollution, which are outside the evolutionary experience of the biotic components, can cause serious
disruptions of the basic habitat structure, energy flow, and community composition of the grassbed
assemblages at various levels of biological organization.

Livingston, R. J., R. L. Iverson, R. H. Estabrook, V. E. Keys and J. Taylor, Jr. 1974. Major
features of the Apalachicola Bay system: Physiography, biota, and resource management.
Fla. Sci. 37(4):245-271.
F-24

A review was made of various features of the Apalachicola Bay System. Unique physical, chemical, and
biological features of this system combine to make it one of the most productive estuarine areas in the State of
Florida, Primary productivity and secondary productivity are discussed in relation to various forcing functions
(natural and man-induced). Problems associated with development include dredging, sewage effluents,
pesticides and a number of up-river activities such as industrialization, cattle ranching, channelization, and
damming. The Apalachicola Drainage System is viewed as one of the largest relatively unpolluted areas in the
country. However, it is a neglected resource with little management or control; as such it is presently
endangered by a number of activities. It is suggested that critical information necessary for the management
and protection of this system be obtained, and that the impact of watershed alterations be viewed on a regional
basis with coordinated participation of the involved states (Florida, Georgia, and Alabama).

Livingston, R. J., and E. A. Joyce, Jr. (eds.). 1977. Proceedings of the Conference on the
Apalachicola Drainage System, 23-24 April 1976, Gainesville, Florida. Florida Marine
Research Publications, Number 26. Florida Department of Natural Resources, Marine
Research Laboratory, St. Petersburg, Florida, 177 p.
F-24

A compendium of information concerning the intrinsic and extrinsic values of the Apalachicola Drainage
System. The various topics covered are the legal, economic, managerial, and environmental aspects of the
Apalachicola basin with contributions from two state university systems, three departments of state
government, the Florida Bar, one private Florida research facility, and one out-of-state university system.
Papers are presented on geobotany, terrestrial and aquatic fauna, and natural history of the Apalachicola River
and Bay systems. The Apalachicola Valley is shown to be a center of endemism in the southeastern U.S. and
critical to the environmental and economic considerations of a three-state area (Florida, Georgia and Alabama).
334
-------
Livingston, R. J., G. J. Kobylinski, F. G. Lewis, m and P. F. Sheridan. 1976. Long-term
fluctuations of epibenthic fish and invertebrate populations in Apalachicola Bay, Florida.
Fish. Bull. 74(2):311-321.
F-24

A 3-yr study was made concerning seasonal changes in the biota of Apalachicola Bay. The Apalachicola River
causes a temporal progression of changes of various environmental parameters in the bay such as salinity,
turbidity, nutrients, and detritus levels. Fishes were more widespread in their distribution throughout the bay
than invertebrates. This was thought to be related to trophic response and habitat preference. High levels of
relative dominance prevailed for both groups with the top three species of each group accounting for more than
80 % of the total number of individuals taken. The temporal and spatial distribution of estuarine fishes and
invertebrates was associated with species-specific reproductive cycles, trophic relationships, and habitat
preferences. The Apalachicola estuary was viewed as a seasonally stable system, with regular temporal
fluctuations of the biota through each annual cycle.

Livingston, R. J., P. S. Sheridan, B. G. McLane, F. G. Lewis, m and G. G. Kobylinski. 1077.
Pages 75-100 in R. J. Livingston, E. A. Joyce, Jr. (eds.), Proceedings of the Conference on
the Apalachicola Drainage System, 23-24 April 1976, Gainesville, Florida. Florida Marine
Research Publications, Number 26. Florida Department of Natural Resources, Marine
Research Laboratory, St. Petersburg, Florida, 177 p.
F-24

Initiated in 1972, this study is one of a series of publications concerning the long-term fluctuations of the
biota in the Apalachicola Bay system. Previous studies have confirmed that the Apalachicola Bay system has
a relatively high level of primary and secondary production, and that such production depends, to a large degree,
on the Apalachicola River system, the largest of its kind in Florida. This unpolluted shallow coastal estuary
is a river-forced, barrier island system that serves as a major source of sports and commercial fisheries in
Florida.

Loesch, H. 1960. Sporadic mass shoreward migrations of demersal fish and crustaceans in
Mobile Bay, Alabama. Ecology 41(2):292-298.
G-2

At infrequent intervals in Mobile Bay, crabs, shrimp, and several species of fish crowd to the shallow water
where they may be easily taken by anyone on the beach at the time. This phenomenon, locally termed
"Jubilee," has heretofore been unreported in literature. In Mobile Bay, mortalities seldom occur. The theory
has been advanced that these shoreward migrations occur when certain meteorological and oceanographic factors
are in coincidence. These jubilees occur in Mobile Bay most frequently during the dark hours on a rising tide
following a day of east wind. The coincidence of these climatological conditions results in an inshore
movement of water which is low in oxygen because of the rotting of wood debris accumulated from the
Tensaw River runoff from a deep pocket near the eastern shore of the bay. Demersal animals especially move
inshore ahead of this water mass. Changes in tide, wind, or other meteorological conditions result in water
aeration and terminate the jubilee.

Lohrenz, S. E., M. J. Dagg and T. E. Whitledge. 1990. Enhanced primary production at the
plume/oceanic interface of the Mississippi River. Continental Shelf Res. 10(7):639-664.
G-7.1

Mechanistic and empirical models were used to examine relationships between primary production and
environmental variables along the Mississippi River plume/oceanic gradient off Southwest Pass, Louisiana.
Comparison of observed chlorophyll concentrations with those predicted using a steady-state light limitation
model suggested factors in addition to light availability constrained maximum biomass levels in the plume.
Factors which may have contributed to low observed biomass included growth limitation or inhibition by
substances not measured, losses due to grazing and sinking, and a short residence time for plume water, which
335
-------
may have prevented populations from reaching steady state. Nutrient-salinity distribution, in conjunction with
approximate calculations of primary consumption of riverine nutrient sources by phytoplankton, led to the
conclusion that biomass and production were controlled by nutrient supply at salinities above 30.

Longley, W.L. (ed.). 1992. Freshwater Inflows to Texas Bays and Estuaries: Ecological
Relationship and Methods for Determination of Needs. Report of the Texas Water
Development Board and the Texas Parks and Wildlife Department, Austin, Texas, 400 p.
(Not in hand).
G-16 through G-26.3

Lopez, M. A. and R. F. Giovannelli. 1984. Water-Quality Characteristics of Urban Runoff and
Estimates of Annual Loads in the Tampa Bay Area, Florida, 1975-1980. U.S. Geological
Survey Water Resources Investigations Rept. No. 83-4181, U.S. Dept. of the Interior,
Geological Survey, Tallahassee, Florida, 76 p.
F-15

Rainfall, runoff, and water-quality data were collected at nine urban watersheds in the Tampa Bay area of west-
central Florida from 1975 to 1980. Watershed drainage ranged from 0.34 to 3.45 mi^. Land use was mixed.
Development ranged from a mostly residential watershed with 19 % impervious surface to a commercial-
residential watershed with 61 % impervious surface. The flow regression equations of this report were used to
compute 1979 water-year loads of biochemical oxygen demand, chemical oxygen demand, total nitrogen, total
organic nitrogen, total phosphorus, and total lead for the nine Tampa Bay area urban watersheds.

Lord, R. J. (in prep.). Perdido Bay, Honda-Alabama Preliminary Analytical and Field Data, My
1986 through October 1987. Draft Report. U.S. Environmental Protection Agency, Region
IV, Atlanta and Athens, Georgia.
F-28, G-l
Lord, R. J. 1989. Perdido Bay.
Gulfwatch l(5):3/7.
G-l, F-28
A coordinated approach to an environmental problem.
In many ways, Perdido Bay's physical characteristics and environmental problems reflect many of the concerns
about the Gulf coast and its estuaries. Because of this, it was selected as the site of a pilot project under the
EPA Near Coastal Waters Program. This report describes the background, details and hoped-for results of this
project.

Louisiana Continental Shelf System Working Group. 1982. Evaluation of the Brine Disposal
from the West Hackberry Site: The Regional Impact on Menhaden Resources. Vol. I and II.
Final Report to the U.S. Dept. of Energy Strategic Petroleum Reserve Project Management
Office, New Orleans, Louisiana. Center for Wetland Resources, Louisiana State University,
Baton Rouge, Louisiana.
G-7.1

The commercial fishery for the Gulf menhaden is the largest (by weight) in the U.S. Given the value of the
menhaden resource, the history of exploitation of related species, and the general lack of an understanding of
the offshore marine ecosystem of the Louisiana shelf, a study was conducted to assess the impacts of brine
discharge on the spawning of menhaden and shrimp and the possible significance to commercial Louisiana
landings; and assess the impact of brine discharge on the food web, with emphasis on those species critical to
menhaden and shrimp. A summary of the relationships within the shelf ecosystem observed during the year's
study stresses cross-shelf gradients, the importance of the coastal boundary layer, trends in phytoplankton
specific growth rates, trends in phytoplankton and zooplankton biomass, location of fish and, specifically
menhaden, larval densities, and location of menhaden spawning.
336
-------
Louisiana Department of Environmental Quality. 1984. Crab Kill in Gulf of Mexico off Point au
Per Island. Memorandum, Louisiana Department of Environmental Quality, Baton Rouge,
Louisiana, 6 p.
G-7.1

On August 24,1984 an investigation was made of a reported crab kill in the Gulf of Mexico just off Point au
Per Island between the mouth of Oyster Bayou and Point au Per. It was believed that the problem was due to
an offshore rig dumping brine into the Gulf and resulted in crabs dying in traps. Water quality readings were
taken at six locations within the area. Measurements were made at 1-m intervals to a depth of 0.3 m above the
bottom. The readings indicated that high salinities were present Also, it was seen that nearer to the mouth of
the Atchafalaya, salinity stratification was present and resulted in depressed dissolved oxygen levels at or near
the bottom. It was confirmed that low oxygen levels and not the brine discharge was the cause of the crab
mortalities. Future trips are planned to gain a more complete understanding of the area! extent and magnitude
of the stratification and low dissolved oxygen levels.

Louisiana Department of Environmental Quality. 1987. Water Quality Management Plan. Vol. 4-
Basin/Segment Boundaries and Inventories. Vol. 5 - Water Quality Assessment. B. Water
Quality Data Summary. Louisiana Department of Environmental Quality, Office of Water
Resources, Water Pollution Control Division, Baton Rouge, Louisiana.
G-7, G-9, G-10, G-l 1, G-12, G-14, G-15

This volume of the Louisiana Water Quality Management Plan includes descriptions of each water quality
management basin and all segments within each basin. It includes descriptions of the geology, geography,
climatology, and hydrology of the basins. Much of the information was extracted from the 1980 Phase II
Basin Plans. Some of the descriptions identify Major Land Resource Areas included within a basin.

Louisiana Department of Environmental Quality. 1988. Water Quality Management Plan. Vol. 5,
Part A - Water Quality Inventory, 1988. Part B. Water Quality Data Summary. Vol. 6, Part
A - Nonpoint Source Pollution Assessment Report, Louisiana Department of Environmental
Quality, Office of Water Resources, Water Pollution Control Division, Baton Rouge,
Louisiana.
G-7, G-9, G-10, G-l 1, G-12, G-14, G-15

The 1988 Water Quality Inventory assesses water quality data and pollution activities for the years 1986 and
1987. The assessment has two phases involving two categories of information: ambient monitoring data and
evaluative data, which includes pollution sources, citizen complaints, fish kills, and general observations. For
this report, 419 water bodies were assessed. Based upon this assessment, water quality in Louisiana is good;
better than 60 % of the assessed waterbodies are considered to be fully supporting their designated uses.
Among the various pollutants identified as causes for non-support of designated uses, the most frequently cited
pollutants are fecal coliform bacteria, oxygen-demanding substances, nutrients, oil and inorganics, specifically
chlorides and brine. The most commonly cited sources of pollutants impacting the assessed waterbodies are
runoff from unsewered communities, inadequately treated sewage discharges from municipalities, discharges and
spills from petroleum activities, agricultural runoff, and urban runoff. At this time, nonpoint sources appear
to be the predominant sources contributing to water quality problems in the state.

Louisiana Department of Environmental Quality. 1989. Water Quality Management Plan. Vol.5,
Part B - Water Quality Data Summary, 1980-81. Louisiana Department of Environmental
Quality, Office of Water Resources, Water Pollution Control Division, Baton Rouge,
Louisiana.
G-7, G-9, G-10, G-l 1, G-12, G-14, G-15

Data report for water quality stations for 1980-1981.
337
-------
Louisiana Department of Environmental Quality. 1990. Water Quality Management Plan. Vol. 5 -
Water Quality Data Summary, 1988-89. Vol. 5 - Water Quality Inventory, 1990. Louisiana
Department of Environmental Quality, Office of Water Resources, Water Pollution Control
Division, Baton Rouge, Louisiana.
G-7, G-9, G-10, G-ll, G-12, G-14, G-15

Data report for water quality stations for 1988-1989. The Water Quality Inventory assesses water quality data
and pollution control activities for the same years. The assessment has two phases involving two categories
of information: ambient monitoring data and evaluative data. The latter includes pollution sources, citizen
complaints, fish kills, and general observations. For this report, 443 waterbodies were assessed, including
8665 miles of rivers, 5,602,758 acres of lakes, and 4212 miles of estuaries. Based upon this water quality
assessment, covering the years of 1988 and 1989, it is concluded that the overall quality of Louisiana's surface
waters is fair to good, with scattered incidences of toxic contamination in certain areas and widespread incidence
of bacterial contamination in populated areas. Nearly 60% of the assessed waterbodies are considered to be
fully supporting their designated uses, and about 30% of the assessed waters are suffering some degree of
impairment The remaining 10 % are unclassified due to lack of information. It should be noted that the
assessed waters represent only a fraction of the total waters of the State.

Louisiana Wild Life and Fisheries Commission. 1971. Cooperative Gulf of Mexico Estuarine
Inventory and Study, Louisiana. Phase I, Area Description. Phase II, Hydrology, Phase
III, Sedimentology. Phase IV, Biology. Louisiana Wild Life and Fisheries Commission,
New Orleans, Louisiana, 366 p.
G-7 through G-16

Tabular data are presented on water volume, vegetation, stream discharge, commercial fishery operations,
coastal populations, pollution, filled areas, drained areas and navigation channels in Louisiana's estuarine zone.
Comparisons are made between past years' data and recent information.

Lowery, T. A. (ed.). 1987. Symposium on the Natural Resources of the Mobile Bay Estuary.
Publ. No. MASGP-87-007, Alabama Sea Grant Extension Service, Alabama Cooperative
Extension Service, Auburn University, Mobile, Alabama, 208 p.
G-2

Series of extended abstracts from the symposium covering topics of resources; fisheries research and
management; amphibian, reptilian and avian populations; benthic and wetland resources; habitat preservation,
restoration and mitigation, educational efforts; and hydrography, circulation, water quality and pollutants.

Lurry, D. L. 1983. Analysis of Native Water, Bottom Material, Elutriate Samples, and Dredged
Material from Selected Southern Louisiana Waterways and Selected Areas in the Gulf of
Mexico, 1979-81. Open-File Report No. 82-690, U.S. Dept. of the Interior, Geological
Survey, Baton Rouge, Louisiana, 114 p.
G-8.1, G-9, G-10, G-12, G-15

Series of chemical samples on water samples, bottom sediments, elutriate samples and dredged materials from
10 locations in coastal Louisiana. Chemical analyses included sodium, potassium, bicarbonate, carbonate,
alkalinity, sulfate, chloride, various solids, various nitrogen, various phosphorus, various trace metals, oil and
grease, cyanide, chemical oxygen demand, PCBs and related chemicals, DDT and related chemicals, and other
toxic chemicals.

Lysinger, W. R. 1982. An Analysis of the Hydrographic Conditions Found in the Main Pass of
Mobile Bay, Alabama, M.S. Thesis, University of Alabama, University, Alabama, 139 p.
G-2
338
-------
Water quality surveys (temperature, salinity, dissolved oxygen) were made in Main Pass from September 1975
through November 1977. This report summarizes the predominant wind conditions, tidal ranges and mean
river flows associated with each survey. Dissolved oxygen mean saturation levels for the surveys ranged from
56.6 to 127.1 %. In June and July, isolated water parcels with values less than 20 % were observed in bottom
waters greater than 9 m. These low values occurred only on falling tides, suggesting that their origins were in
the Bay.
Lytle, T. F. and J. S. Lytle. 1990.
Estuaries 13(1):98-111.
G-2.2, G-2.3, G-3, G-4, G-5
Contaminants in sediments from the central Gulf of Mexico.
Surface sediment samples at 89 locations and 300-cm cores from 43 sites in the Mississippi Sound were
examined for evidence of pollutant impact upon this coastal environment Chemical variables determined were
total organic carbon, Kjeldahl nitrogen, phenols, and hydrocarbons. Values of these pollutant indicators were
about the same or lower in Gulf of Mexico samples compared to Mississippi Sound sediments and
considerably lower than those from rivers and bays emptying into the sound, indicating limited impact from
sites of pollutant sources into the sound. Concentrations of sedimentary pollutants peaked in the Pascagoula
River where levels of total organic carbon, Kjeldahl nitrogen, phenols, and hydrocarbons exceeded sound values
by one to three orders of magnitude. Analysis of cores shows pollutant intrusion to sediment strata predating
industrial development The level of pollution varies from site to site but fortunately is serious only at
localized sites within the sound.

Lytle, T. F. and J. S. Lytle. 1985. Pollutant Transport in Mississippi Sound. Sea Grant Publ.
No. MASGC-82-038, Mississippi-Alabama Sea Grant Consortium, Gulf Coast Research
Laboratory, Ocean Springs, Mississippi, 124 p.
G-2.3, G-3, G-4, G-5, G-6

Because pollution can have a widespread and longlasting effect on the aquatic environment areas of concern
that must emerge in a scientific investigation of pollution are: 1) the types of pollutants present in the system;
2) where pollutants are found: in water, sediments or biota; 3) current state of pollution in the Sound; 4)
migration or transport of pollutants throughout the Sound; 5) environmental significance of pollution; and 6)
use of scientific data to constructively ameliorate the problem of pollution. The principal investigators began
this study in 1979, cognizant of these concerns, and with overall objectives to characterize pollutants in
Mississippi Sound, clarify those processes responsible for pollutant movement and develop criteria essential
for coastal management based upon sound scientific information.

Madden, C. J. 1986. Distribution and Loading of Nutrients in Fourleague Bay, a Shallow
Louisiana Estuary. M.S. Thesis, Louisiana State University, Baton Rouge, Louisiana, 143
P-
G-12

Synoptic transects in Fourleague Bay showed nitrate and salinity regimes strongly tied to the hydrologic cycle
of the Atchafalaya River. Nitrate peaked in June; lower Bay nitrate profiles followed the upper Bay pattern but
at a 40-90 % lower concentration. Phosphate concentrations decreased away from the river to the lower Bay.
The primary source of nitrate was the Atchafalaya River and strong non-conservative declines in concentration
caused a spatial shift from N:P ratios of over 100:1 in the upper bay to as low as 8:1 in the lower Bay.
Retention of water in the bay was highly dependent on the wind regime.

Madden, C. J., J. W. Day, Jr. and J. M. Randall. 1988. Freshwater and marine coupling in
estuaries of the Mississippi River deltaic plain. Limnol. Oceanogr. 33(4, part 2):982-1004.
G-10, G-12
The estuaries of Louisiana's Mississippi River deltaic plain exhibit sharp physical and biological contrast due
to their different successional stages in delta development A comparison of the Atchafalaya-Fourleague Bay
339
-------
complex and the Barataria Basin estuary offers an excellent opportunity to observe coupling of freshwater and
marine environments at the extremes of their scale of interaction. Despite being at opposite ends of the delta
life cycle, both estuaries are highly productive and perform similar functions as important nursery grounds for
juvenile marine and estuarine fishes.

Mahadevan, S., J. Sprinkel, D. Heatwole and D. H. Wooding. 1984. A Review and Annotated
Bibliography of Benthic Studies in the Coastal and Estuarine Areas of Florida. With a
Selected Compilation of Worldwide Benthic Methodological References and Southeastern
United States Benthic Taxonomic References. Project No. IR-79-10. Grant No. NA80AA-
D-00038. SGR Report No. 66, Florida Sea Grant College Program, University of Florida,
Gainesville, Florida, 576 p.
F-9 through F-28

Over 70 % of benthic information from Florida is in the form of technical reports and unpublished material.
While published information could be easily obtained through library searches, unpublished information is
often difficult to obtain. As a result, a reasonable compilation of the majority of benthic studies conducted in
Florida's waters has not been available to date; this report is an attempt to do so, at least for the coastal and
estuarine areas of Florida. The finished project is a compilation of over 1500 benthic studies.

Main, M. B., D. R. G. Farrow and F. D. Arnold. 1987. The National Coastal Pollutant
Discharge Inventory. Publicly Owned Treatment Works in Coastal Areas of the USA. Draft
Report. U.S. Dept. of Commerce, National Oceanic and Atmospheric Administration, Ocean
Assessments Division, Office of Oceanography and Marine Assessment, National Ocean
Survey, Rockville, Maryland, 42 p.
F-9 through G-27

In addressing the question regarding publicly owned treatment works' (POTW) relative importance as a source
of the pollutants that contribute to water quality problems in estuarine and coastal areas, this report presents
estimates of existing and projected wastewater flows, conventional pollutant loadings, and sludge production
from POTWs in the nation's coastal areas. A comparison is made to the volume of wastewater discharged
from industrial facilities, and the levels of wastewater treatment practiced by POTWs are examined. The
information presented provides insights into the relative importance of POTWs as dischargers to the nation's
estuarine and coastal waters and to the regional differences that must be considered in the further development
and implementation of national pollution control policies.

Maples, R. S., M. D. Cruze and R. Donahoe. 1983. Observations on "red tide" organisms in
coastal waters of southwestern Louisiana. Northeast Gulf Sci. 6(2): 157-160.
G-7.1, G-15

This paper reports the common occurrence of four species of red tide producing organisms in the estuarine
waters of Lake Calcasieu and Calcasieu Pass and offshore locations within 15 km of the pass. Bloom
proportions were recorded for Gonyaulax monilata.

Marine Environmental Sciences Consortium. 1979. Baseline Data Collection Experimental
Monitoring Program, Theodore Ship Channel and Barge Channel Extension, Mobile Bay,
Alabama. October, 1977 - October, 1978. Vol. I. Report to Mobile District Corps of
Engineers, Contract No. DACW01-78-C-0010. Marine Environmental Sciences Consortium,
Dauphin Island, Alabama.
G-2

There is a paucity of coherent field data for the wetlands and Bay area involved with the new ship channels and
disposal island. This created the need for a baseline characterization which may be used in conduction with a
monitoring program to ascertain the actual environmental impact of the proposed construction. The majority
of samples were taken on a quarterly/seasonal basis with the intention of describing the area's sedimentology,
340
-------
benthic biology and hydrography including estimates of "turbidity." The adjacent marshes and submersed flora
were monitored on die same basis. Hydrographic data (temperature and salinity) were also taken on a
continuous basis with recording units while monthly benthic/hydrography sampling was initiated in the spring
of 1978. An intensive investigation of dissolved oxygen levels in Deer River was also pursued. General
categories of the report are: hydrography, turbidity/suspended solids, bay bottom, monthly samples, grass beds,
and Deer River dissolved oxygen.

Martinez, A. R. 1969-1970, 1971, 1972, 1973, 1974, 1975. Coastal hydrographic and
meteorological study. la Coastal Fisheries Project Reports for years stated. Texas Parks and
Wildlife Dept., Austin, Texas.
G-16 through G-26.2

Hydrographic and meteorological data collected in the field and taken from publications are presented in these
reports. Included are yearly reports on the following subjects: rainfall, hurricane damage, tides, water
temperature, salinity patterns, dissolved oxygen, hydrogen ion determinations, turbidity readings, river flow
measurements, commercial landings, habitat modifications, and fish kills.

Mauer, L. G. and P. L. Parker. 1972. The distribution of dissolved organic matter in the near-
shore waters of the Texas coast. Contrib. Mar. Sci. 16:109-124.
G-21, G-22, G-23, G-24, G-25, G-26, G-27

The concentration of dissolved organic matter in the coastal waters of south Texas, estuaries and shelf, was
measured. Zones of high and low concentration were found on the shelf. The concentrations in the estuaries
(2-5.3 mg/1) were higher than those for shelf waters (1-3.7 mg/1). A new analytical method based on persulfate
oxidation and gas chromatographic detection was developed.

May, E. B. 1973. Extensive oxygen depletion in Mobile Bay, Alabama. Limnol. Oceanogr.
18(3):353-366.
G-2

Extensive areas of bottom water in Mobile Bay, Alabama, one of the largest estuaries on the Gulf of Mexico,
suffer oxygen depletion in summer because of salinity stratification in sinks created by shoals in the lower bay
and by spoil from construction of the Mobile Ship Channel. When these water masses low in dissolved
oxygen are occasionally forced against the beach, demersal fishes and crustaceans migrate shoreward in a
depressed or moribund state. In the absence of technical, data these popular occurrences, called "jubilees,"
provide over a century of historical evidence of oxygen depletion. Oxygen depletion and jubilees occurred in
the Bay before man physically modified the basin but the conditions responsible for oxygen depletion are
worse than in the past Because of bathymetric changes and modifications that have restricted water
circulation, Mobile Bay has exceeded its capacity to assimilate its oxygen demand in summer, which has
severely affected the biota of the estuary.

McCoy, E. D. and S. S. Bell. 1985. Tampa Bay: The end of the line? Pages 460-473 ia S. F.
Treat, J. L. Simon, R. R. Lewis, III and R. L. Whitman, Jr. (eds.), Proceedings of the
Tampa Bay Area Scientific Information Symposium, May 1982. Sea Grant Project No.
IR/82-2. Grant No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65,
Burgess Publishing Co., Minneapolis, Minnesota.
F-15

Vertebrate and invertebrate species composition of the Tampa Bay area were examined to determine the
zoogeographical affinities. The authors found little evidence that Tampa Bay serves as a boundary for tropical
species of fishes, decapods, polychaetes, gastropods, or bivalves. However, better data, as well as data from
other locations, may indicate a pattern different from the one found.
341
-------
Mclntyre, H. L. and J. J. Cullen. 1988. Primary Production in San Antonio Bay, Texas:
Contribution by Phytoplankton and Microphytobenthos. Vol. 30. Report to the Texas Water
Development Board. University of Texas Marine Science Institute, Port Aransas, Texas, (not
in hand)
G-22

McNulty, J. K., W. N. Lindall, Jr. and J. E. Sykes. 1972. Cooperative Gulf of Mexico
Estuarine Inventory and Study, Florida: Phase I, Area Description. NOAA Technical Report
NMFS CIRC-368, U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, National Marine Fisheries Service, Seattle, Washington, 126 p.
F-9 through F-28

Newly developed tables and maps depict the dimensions, submerged vegetation, tidal marshes, mangrove
swamps, commercial oyster beds, leased oyster-rearing areas, sources of pollution, drained tidal marshes, and
filled areas of Florida's west coast estuaries. Published and unpublished information on temperature, salinity,
geology, artificial fishing reefs, stream discharge, human population, commercial fishing, and economic
development is presented in new form.

McPhearson, Jr., R. M. 1970. The hydrography of Mobile Bay and Mississippi Sound,
Alabama. J. Mar. Sci. Alabama 1(2): 1-83.
G-2, G-2.2

Forty-nine hydrographic stations were sampled at least bimonthly in Mobile Bay and Mississippi Sound,
Alabama from May 1963 through April 1964. An additional 27 stations were sampled monthly from
November 1965 through October 1966. At 671 sites, temperature and salinity (surface and bottom) and
turbidity data were taken. Data on mean low water levels, tidal range and flushing, currents, and river discharge
are presented and discussed.

McPherson, B. J. and H. R. LaRose. 1982. Algal Conditions in the Caloosahatchee River (1975-
1979), Lake Okeechobee to Franklin Lock, Florida. USGS WRI/81-81, U.S. Geological
Survey, Water Resource Investigations, Tallahassee, Florida, 28 p.
F-12

Melancon, E. and R. Kilgen. 1991. Nicholls State University Trawl Data on Shrimp and
Bottomfish Samples Collected on the Louisiana Continental Shelf from 1975-78. Abstr. for
Proceedings of a Meeting of the Louisiana Chapter of the American Fisheries Society, March
1, 1991, Covington, Louisiana.
G-7.1

During the first year of the study, 1975-1976, eight transects spanning the width of Louisiana's continental
shelf were sampled. Each transect was divided into 10 sampling stations by depth and ranged from 6 to 110 m.
The number of transects was reduced to six in the following year, 1976-1978. All stations were sampled with
a 12-m four-seam semi-balloon trawl with a 4.1-cm stretch mesh. All species of shrimp were collected from
the trawl samples and a random sample of bycatch taken at each station. Temperature, salinity, pH, and
dissolved oxygen were measured at each station. BOD, COD, volatile solids, and some metals were also
examined at selected sites.

Menzel, R. W. and E. W. Cake, Jr. 1969. Identification and Analysis of the Biological Value of
Apalachicola Bay, Florida. Contract No. 14-12-191, Florida Water Pollution Control
Agency, Tallahassee, Florida, (not in hand)
F-24
342
-------
Miller, R. L. 1980. Phytoplankton Production within the Grass Beds off Goose Point, Lake
Pontchartrain, Louisiana. M.S. Thesis, Louisiana State University, Baton Rouge, Louisiana,
138 p.
G-7

Phytoplankton paniculate and dissolved production were measured within the grass beds off Goose Point, Lake
Pontchartrain, Louisiana. Considerable variation was observed; however, all measures of phytoplankton
biomass and production followed the same general seasonal pattern with maximum values occurring during the
winter. Paniculate production rates ranged from 20.93 to 133.59 mgC/m^/h. Chlorophyll a concentrations
ranged from 4.6 to 133.59 g/1. Nannoplankton (<53 um) were the most important component of the
phytoplankton and accounted for 90.9 % of production and 91.7 % of biomass. Estimates of phytoplankton
production and biomass were negatively related to the presence of the grasses.

Miller, R. L., T. F. Kraemer and B. F. McPherson. 1990. Radium and radon in Charlotte
Harbor Estuary, Florida. Estuarine Coastal Shelf Sci. 31(4):439-457.
F-13

Radium-226 and 222RH activities are greater in the estuarine waters of northern Charlotte Harbor and the lower
tidal Peace and Myakka Rivers, Florida, than in either the freshwater reaches of the rivers or waters of the
lower estuary and the Gulf of Mexico. The source of the high activity of 226^ a^j 222^ js predominantly
ground water inflow. Because of the large ground water input, the contribution of 226^ from suspended and
bottom sediments is a smaller fraction of the total 226]^ mput fl^ m many other estuaries.

Mississippi Department of Natural Resources. 1988. Mississippi Water Quality Report, 1988.
Pursuant to Section 305(b) of the Clean Water Act. Mississippi Department of Natural
Resources, Bureau of Pollution Control, Jackson, Mississippi, 148 p.
G-2.3

The purpose of the 1988 Mississippi Water Quality Report is to identify the status and recent trends of the
quality of the State's waters. The state is divided into nine major stream basins with a total length of streams
in excess of 15,600 miles. It has been estimated that marsh or wetlands cover an area of 642,000 acres (1003
mi2). The southern edge of Mississippi borders Mississippi Sound with 81 total coastal miles. The total area
of estuarine waters is estimated to cover an area of 133 mi2. Surface water quality in Mississippi is generally
good. Most water bodies either meet all applicable water quality standards or fully support their designated
uses.

Monaco, M. E., T. E. Czapla, D. M. Nelson and M. .E. Pattillo. 1989. Distribution and
Abundance of Fishes and Invertebrates in Texas Estuaries. NOAA's Estuarine Living Marine
Resources Project, U.S. Dept. of Commerce, National Oceanic and Atmospheric
Administration, Rockville, Maryland, 107 p.
G-16, G-17, G-18, G-21, G-22, G-23, G-24, G-25, G-26

This report presents information synthesized on the spatial and temporal distribution, relative abundance, and
life history characteristics of 40 fish and invertebrate species in nine estuaries along the Texas coast The
presence, distribution and relative abundance of each species' life history stage, and the time period that it
utilizes each estuary, are shown.

Montagna, P. A. and R. D. Kalke. 1989a. The effect of freshwater inflow on meiofaunal and
macrofaunal populations in San Antonio, Nueces and Corpus Christi Bays, Texas. Pages 97-
148 in P. A. Montagna (ed.), Nitrogen Process Studies (NIPS): The Effect of Freshwater
Inflow on Benthos Communities and Dynamics. Final Report to Texas Water Development
Board. Technical Report No. TR/89-011, University of Texas Marine Science Institute, Port
Aransas, Texas.
343
-------
G-22, G-24

Two estuaries with very different inflow characteristics were compared to test the hypothesis that benthic
productivity is enhanced by freshwater inflow. The Guadalupe estuary had 79 times more freshwater inflow
than the Nueces estuary, and a third of the salt content. The Guadalupe had higher macrofaunal densities and
biomass than the Nueces, and both parameters increase along a decreasing salinity gradient within the
Guadalupe Estuary. Macrofauna density increased with increasing salinity in the Nueces Estuary. Meiofaunal
densities were higher in the Nueces estuary, and decreased along increasing salinity gradients in both estuaries.
These results indicate that macrofauna may be responding to freshwater inflow with increased productivity.
Increased macrofaunal densities appear to be associated with decreasing meiofaunal densities.

Montagna, P. A. and R. D. Kalke. 19895. A synoptic comparison of benthic communities and
processes in the Guadalupe and Lavaca-Tres Palacios estuaries, Texas. Pages 149-183 in P.
A. Montagna (ed.), Nitrogen Process Studies (NIPS): The Effect of Freshwater Inflow on
Benthos Communities and Dynamics. Final Report to Texas Water Development Board.
Technical Report No. TR/89-011, University of Texas Marine Science Institute, Port
Aransas, Texas.
G-21, G-22

Water use planning and management in Texas requires that we understand the effect of freshwater inflow on
ecological processes that control and maintain productivity in our bays and estuaries. However, there is a large
gap in our knowledge. We do not know if generalizations gathered in one estuary are applicable to another.
This is true not only in Texas but in the Nation as a whole. We in Texas are fortunate because, within short
distances we have access to bays that are very different in the amount of freshwater input and salinity. We can
compare parameters across different systems synoptically. Sediment oxygen uptake and nutrient regeneration
are good general measures of benthic community metabolism. An important distinction between these two
particular estuaries is that the Lavaca has direct exchange with the Gulf of Mexico, and the Guadalupe does not.

Montagna, P. A. and W. B. Yoon. 1989. The effect of freshwater inflow on meiofaunal
consumption of sediment bacteria and microphytobenthos in San Antonio Bay, Texas. Pages
1-28 in P. A. Montagna (ed.), Nitrogen Process Studies (NIPS): The Effect of Freshwater
Inflow on Benthos Communities and Dynamics. Final Report to Texas Water Development
Board. Technical Report No. TR/89-011, University of Texas Marine Science Institute, Port
Aransas, Texas.
G-22

Edaphic bacteria and microphytobenthos are known to be food resources for meiobenthic organisms. River
inflow is a source of nutrients in estuaries. If inflow results in concomitant primary and secondary production,
then meiofauna grazing rates should be higher in the freshwater influenced part of the estuary. Meiofauna
grazing rates in San Antonio Bay were 3.S times greater in the freshwater-influenced zone than in the marine-
influenced zone. However, this was due to a predominance of juvenile molluscs in the freshwater zone.
Permanent meiofauna all had higher grazing rates in the marine influenced zone. Production of bacteria and
microalgae in the head of the estuary was advected, resulting in higher biomass in the lower end of the estuary.
Therefore, advection of microbial production from the river is very important in maintaining standing stocks of
benthic meiofauna throughout the estuary.

Montagna, P. A., W. B. Yoon and T. E. Whitledge. 1989. The effect of freshwater inflow and
sediment resuspension on benthic metabolism and nutrient regeneration in the Guadalupe and
Nueces estuaries, Texas. Pages 29-96 in P. A. Montagna (ed.), Nitrogen Process Studies
(NIPS): The Effect of Freshwater Inflow on Benthos Communities and Dynamics. Final
Report to Texas Water Development Board. Technical Report No. TR/89-011, University of
Texas Marine Science Institute, Port Aransas, Texas.
G-22, G-24
344
-------
Current flow has the potential to increase photosynthesis by resuspending large quantities of chlorophyll, and
limiting nutrients into the water column. Resuspension can also enhance the decomposition of sediment
organic matter by making buried organic matter available to aerobes and increasing rates of diffusion of
metabolites, thus "stirring the pot." Increased flow rates do increase flux of sediment, chlorophyll, ammonia,
nitrite, phosphate, and silicate to the water column, but decrease nitrate flux. The nitrate uptake and
chlorophyll resuspension indicate that photosynthesis is probably enhanced by resuspension. However,
increased photosynthesis is mitigated by increased turbidity and because resuspended pigment has low
chlorophyll to phaeophytin ratios. The net effect is that increased current flow does not always result in
increased oxygen consumption, since photosynthesis may be stimulated, but this is counter balanced by
chemical oxidation of reduced ions released from the sediment.

Moon, R. E. 1985. Point source discharge in the Tampa Bay area. Pages 551-556 in S. F. Treat,
J. L. Simon, R. R. Lewis, HE and R. L. Whitman, Jr. (eds.), Proceedings of the Tampa Bay
Area Scientific Information Symposium, May 1982. Sea Grant Project No. IR/82-2. Grant
No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65, Burgess Publishing
Co., Minneapolis, Minnesota.
F-15

A point source inventory was performed describing municipalities, industries and commercial businesses which
discharge effluent into surface waters of the State and the Tampa Bay areas. Data for the inventory were
retrieved from 1980 monthly operating reports required by the State and Federal National Pollutant Discharge
System permits. The reports revealed 59 sources along rivers and sites that discharge into the Bay. In 1980,
these sources contributed 190 billion gallons of water carrying 2.35 and 3.58 million pounds of phosphorus
and nitrogen, respectively, to Tampa Bay. Since 1980, significant reductions in nutrient discharge to the Bay
have resulted from alternative sewage disposal methods including spray irrigation, water reuse, land reclamation
projects and limited Federal funds.

Moshiri, G. A., N. G. Aumen and W. G. Crumpton. 1981. Reversal of the eutrophication
process: A case study. Pages 373-390 in B. J. Neilson and L. E. Cronin (eds.), Estuaries
and Nutrients. Proceedings of an International Symposium on the Effects of Nutrient
Enrichment in Estuaries, May 29-31,1979, Williamsburg, Virginia. Contemporary Issues in
Science and Society, Humana Press, Clifton, New Jersey.
F-27

Bayou Texar, Pensacola, Florida, is a bayou estuary that was advancing toward eutrophy, due to nutrient
loadings from various sources. The occurrence of characteristic symptoms of eutrophication, coupled with the
closing of the bayou for water contact recreation, led to the initiation of an intensive 7-yr study. Initial results
indicated that Carpenter's Creek is a prime source of most nitrogen species and that an exchange exists between
dissolved phosphates and those adsorbed onto sediments. A final study suggested among other things that the
importance of toxins from algal blooms to fish kills may be greater than previously indicated. Specific
recommendations made after the fourth year of the study were implemented in most part and led to a substantial
improvement of water quality and the subsequent opening of the bayou to the public for recreational use.

Moshiri, G. A., N. G. Aumen and W. G. Swann, III. 1980. Water Quality Studies in Santa
Rosa Sound, Pensacola, Florida. Grant No. R-803566, U.S. Environmental Protection
Agency, Research and Development, Environmental Research Laboratory, Gulf Breeze,
Florida, 71 p.
F-27

Water samples were collected from six stations in Santa Rosa Sound and Little Sabine Bay, Florida, every 2
wk between October 1977 and June 1979. The samples, taken at the surface, mid-depth, and bottom of each
station, were analyzed for temperature, salinity, pH, transparency, inorganic carbon, 5-d biochemical oxygen
demand, dissolved oxygen, orthophosphate, poly-phosphate, ammonia, nitrate, and nonvolatile grease and oil;
bacteria were enumerated; phytoplankton were identified and enumerated; and the water column primary
345
-------
productivity was measured. Although there were seasonal changes, there were few intra- or inter-station
differences on each sampling day. However, Little Sabine Bay exhibited lower water transparency, higher
BOD, higher rates of primary production, higher concentrations of nonvolatile grease and oil, and larger
numbers of bacteria and phytoplankton than Santa Rosa Sound.

Moshiri, G. A., D. Brown, P. Conklin, D. Gilbert, M. Hughes, M. Moore, D. Ray and L.
Robinson. 1974. Determination of a Nitrogen-Phosphorus Budget for Bayou Texar,
Pensacola, Florida. Research Project Technical Completion Report. Publication No. 29,
Florida Water Resources Research Center, University of Florida, Gainesville, Florida, 82 p.
F-27

To date, results indicate that there are numerous sources of nutrients into the Bayou, of which Carpenter's
Creek and stormwater runoff are the major contributors. Other sources are runoff from fertilizers applied to
lawns, overflow of inadequate sewer lines, and, to a much lesser extent, from sources such as rainwater and
encroaching Pensacola Bay waters. Ecologically, the Bayou is approaching eutrophicau'on as is evidenced by
highly fluctuating oxygen and primary productivity patterns well correlated with algal cell numbers and
distribution. Recommendations made for the improvement of water quality in the Bayou include 1)
improvement of circulation by the construction of a new channel, 2) improvement of storm water and sewage
facilities, 3) improvement in the Carpenter's Creek channel to alleviate erosion, and 4) selected dredging in
areas of heavy siltation in the Bayou in order to improve flushing and circulation.

Moshiri, G. A., W. G. Crumpton and D. A. Blaylock. 1978. Algal metabolites and fish kills in a
bayou estuary: An alternative explanation to the low dissolved oxygen controversy. J. Water
Pollut. Control Fed. 50:2043-2046.
F-27

Bayou Texar is a shallow bayou estuary that has sustained considerable water quality degradation in recent years
as a result of the growing urban development within its drainage basin. Frequent raw wastewater leaks were
followed by massive algal blooms and extensive fish kills. Fish kills of this nature have usually been
attributed to low concentration of dissolved oxygen in the water, primarily because little information is
available on the biotic aspects of the system at the time of the kill. Consequently, these events presented a
unique opportunity to observe the possible presence of other less obvious causative factors, particularly those
involving certain aspects of physiological changes in the phytoplankton population in respect to specific
physicochemical parameters.

Moshiri, G. A., W. G. Crumpton, N. G. Aumen, C. T. Gaetz, J. E. Allen and D. A. Blaylock.
1978. Water-Column and Benthic Invertebrate and Plant Associations as Affected by the
Physico-Chemical Aspects in a Mesotrophic Bayou Estuary, Pensacola, Florida. Research
Project Technical Completion Report. Publication No. 41, Florida Water Resources Research
Center, University of Florida, Gainesville, Florida, 160 p.
F-27

Water column samples were collected every 2 wk over a 1-yr period from three stations in mesotrophic Bayou
Texar, Pensacola, Florida. The samples were analyzed for -NO3, -NHs, -PO4, and total organic carbon (TOQ
against a background of physical parameters. Phytoplankton and zooplankton populations present during the
study period were identified and enumerated. Benthic core samples were collected to assess the
macroinvertebrate populations; however, analysis indicated a paucity of organisms in general. Data was
subjected to appropriate statistical analysis to indicate possible relationships among aspects studied. Negative
correlations appeared between salinity and nitrates, between ammonia and dissolved oxygen (at some stations),
between Brachionus plicatilus and dissolved oxygen, and between Cryptophytes and dissolved oxygen.
Positive correlations were indicated between TOC and ammonia, between Brachionus and Cryptophytes, and
between Brachionus and Oithona colcarva.
346
-------
Murrell, M. C. 1987. Spatial and Temporal Abundance of Meiofauna on a Gulf of Mexico
Continental Shelf Affected by Hypoxia. M.S. Thesis, Louisiana State University, Baton
Rouge, Louisiana, 54 p.
G-7.1

Meiofauna were sampled in shallow (8-13 m) continental shelf waters off the coast of Louisiana at three
stations on 13 dates from June 1985 through August 1986. Total meiofauna abundances ranged from 525 to
3406 individuals per 10 cm^ with a mean of 1810 individuals per 10 cm^. Peak abundances occurred in late
spring and early summer whereas seasonal lows occurred during late summer and winter. Hypoxic waters
(dissolved oxygen <2 mg/1) develop seasonally on this shelf as a result of water column density stratification
and eutrophication during late spring and summer. Abundances of all taxa declined during the summers of both
years apparently in response to hypoxic conditions. Density declines were seasonally correlated with the onset
of hypoxia, as inshore stations developed hypoxia later and underwent declines later.

Murrell, M. C. and J. W. Fleeger. 1989. Meiofauna abundance on the Gulf of Mexico continental
shelf affected by hypoxia. Continental Shelf Res. 9(12):1049-1062.
G-7.1, G-ll

Meiofauna were sampled in shallow (8-13 m) continental shelf waters off the coast of Louisiana at three
stations on 13 dates from June 1985 to August 1986. Total meiofauna abundances ranged from 525 to 3406
individuals per 10 cm^ with a mean of 1810 individuals per 10 cnA Peak abundances occurred in late spring
and early summer while seasonal lows occurred during late summer and winter. Hypoxic conditions developed
seasonally on this shelf as a result of water column density stratification and eutrophication during late spring
and summer. Abundances of all taxa declined during the summers of both years apparently in response to
hypoxic conditions. A single collection of meiofauna from July 1983 in nearby normoxic Terrebonne Bay at
similar water depths reveals a high density and diversity of copepods, further suggesting the sensitivity of
copepods to hypoxia.

Myers, V. B. 1977. Nutrient Limitation of Phytoplankton Productivity in North Florida Coastal
Systems: Technical Considerations, Spatial Patterns, and Wind Mixing Effects. Ph.D.
Dissertation, Florida State University, Tallahassee, Florida, 61 p.
F-22, F-23, F-24

A reliable short-term nutrient enrichment method was developed for the determination of phytoplankton
nutrient limitation. Nutrient enrichment experiments conducted in nearshore waters of the northeastern Gulf of
Mexico indicated that phytoplankton productivity in these waters was phosphorus-limited. A multiple linear
regression model, with phytoplankton productivity regressed against several nutrient and environmental factors,
emphasized the importance of phosphorus for phytoplankton productivity. These data suggest that the
hypothesis that nitrogen limits phytoplankton productivity in coastal waters is not universally true.
Therefore, water quality planning for the coastal zone is best done on a regional basis.

Myers, V. B. and R. L. Iverson. 1981. Aspects of nutrient limitation of the phytoplankton
productivity in the Apalachicola Bay system. Pages 68-74 in R. J. Livingston and E. A.
Joyce, Jr. (eds.), Proceedings of the Conference on the Apalachicola Drainage System, April
, 23-24, 1976, Gainesville, Florida. Florida Marine Research Publications No. 26, Florida
Dept. of Natural Resources, Marine Research Laboratory, St. Petersburg, Florida.
F-20, F-23, F-24

The quantification of the extent of nutrient limitation in a marine ecosystem is critical for die prediction of the
response of the system to various nutrient related stresses. To make sound environmental policy, the critical
nutrients and the relationships between these nutrients and plant productivity must be known. The nutrient
enrichment and phosphorus uptake experiments presented in this paper suggest that phosphorus is the most
347
-------
critical limiting nutrient in this estuarine system and that a reduction in phosphate level during summer
months could reduce phytoplankton productivity.

Myers, V. B. and R. L. Iverson. 1979. Phosphorus and nitrogen limited phytoplankton
productivity in northeastern Gulf of Mexico coastal estuaries. Pages 569-582 in. B. J.
Neilson and L. E. Cronin (eds.), Estuaries and Nutrients. Proceedings of an International
Symposium on the Effects of Nutrient Enrichment in Estuaries, May 29-31, 1979,
Williamsburg, Virginia. Contemporary Issues in Science and Society, Humana Press,
Clifton, New Jersey.
F-24.1

An understanding of nutrient limitation of estuarine phytoplankton growth is important in making
environmentally sound decisions concerning watershed development and the use of aquatic environments for
waste disposal. Experiments to determine nutrient limitation of phytoplankton productivity were conducted
monthly during the summers of 1975 and 1976 in several shallow north Florida coastal and estuarine systems
by inorganic carbon-14 uptake and phosphorus-32 bioassays. The results of these nutrient enrichment
experiments suggest that phosphorus is frequently more important than nitrogen in limiting phytoplankton
productivity in nearshore northeastern Gulf of Mexico. Nitrogen has been identified as the primary limiting
nutrient for phytoplankton in coastal waters, and it has been proposed that the removal of phosphorus from
marine waste discharges will have little impact on the control of eutrophication. The observation that
phosphorus is important in limiting phytoplankton productivity in these coastal and estuarine areas suggest
that water quality planning for the coastal zone is best done on a regional basis, with consideration given to
local nutrient cycling processes.

National Estuary Study. 1970a. Apalachicola Bay, Florida. Pages 145-186inVol.ni, Appendix
B - Management Studies in Specific Estuaries. U.S. Dept. of the Interior, Fish and Wildlife
Service, Bureau of Sport Fisheries and Wildlife and Bureau of Commercial Fisheries,
Washington, D.C.
F-24

The Apalachicola Bay system is a complex of lagoons and an estuary located behind a line of barrier islands
fronting the prominent cusp of Apalachicola Delta on the northeastern Gulf Coast of the Florida Panhandle.
The Bay system is important oceanographically because it is the only Florida Bay into which a large river
system drains. It is important biologically and ecologically for several reasons. This report describes the
magnitude of commercial and sport fisheries and the uncommon recreational advantages of the Bay. These
values are relatively great because the surrounding area is not heavily populated, the few pollution sources have
low volumes of discharge, and the coastline has not suffered significant damage from hydraulic engineering
projects or other forms of modification. Fish and wildlife values are pronounced in that the economy of all the
area surrounding Apalachicola Bay is closely related to the Bay and is fishery oriented.

National Estuary Study. 19705. Aransas Bay, Texas. Pages 147-214 ia Vol. HI, Appendix B -
Management Studies in Specific Estuaries. U.S. Dept. of the Interior, Fish and Wildlife
Service, Bureau of Sport Fisheries and Wildlife and Bureau of Commercial Fisheries,
Washington, D.C.
G-23
*°
Aransas Estuary, located in Aransas and Refugio Counties, Texas comprises about 111,500 surface acres of
land and water. About 28,700 acres of the estuary are salt flats and marshes. The estuary is connected to the
Gulf of Mexico by Aransas Pass. Most of the saline waters enter from the east through the Gulf Intracoastal
Waterway. The estuary has a well distributed shallow-deep water relationship. Ecological modifications have
occurred in the estuary from reduced freshwater inflows and man-made developments and contributions. The
habitat in the estuary is of great importance.
348
-------
National Oceanic and Atmospheric Administration. 1987. National Estuarine Inventory. Data
Atlas. Vol. 2: Land Use Characteristics. Strategic Assessment Branch, Ocean Assessments
Division, Office of Oceanography and Marine Assessment, National Ocean Service, National
Oceanic and Atmospheric Administration, Rockville, Maryland.
F-9 through G-27

This volume presents area estimates for seven categories and 24 subcategories of land use based on data from
the "Land Use and Land Cover Program" of the U.S. Geological Survey (1971-1984).

National Oceanic and Atmospheric Administration. 1989. Galveston Bay: Issues, Resources,
Status, and Management. Proceedings of a Seminar, March 14, 1988, Washington, D.C.
NOAA Estuary-of-the-Month Seminar Series No. 13, U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, Estuarine Programs Office, Washington, D.C.,
114 p. .
G-17

This seminar was held with the objective of bringing to public attention important research and management
issues of our Nation's estuaries. To this end, participants first presented historical and scientific overviews of
the Bay area, followed by an examination of management issues by scientists and research managers involved
in Galveston Bay.

National Oceanic and Atmospheric Administration. 1990b. Mobile Bay: Issues, Resources,
Status, and Management. Proceedings of a Seminar, November 17, 1988, Washington,
D.C. NOAA Estuary-of-the-Month Seminar Series No. 15, U.S. Dept. of Commerce,
National Oceanic and Atmospheric Administration, Estuarine Programs Office, Washington
D.C., 147 p.
G-2

The articles in this volume closely correspond to the presentations that were given at this seminar. The
contents are: Introduction, Overview, Geological and Geochemical Characterization, Climate and
Oceanography, Water Quality, Estuarine Habitats, Fatinal Components, Natural Resource Conservation,
Economic Aspects, and Coastal Resource Management in Alabama: Past Efforts and Future Needs.

NOAA/EPA Team on Near Coastal Waters. 1990. Susceptibility and Status of Gulf of Mexico
Estuaries to Nutrient Discharges. Draft Report. College of Marine Studies, University of
Delaware, Newark, Delaware and Strategic Assessment Branch, Ocean Assessments
Division, Office of Oceanography and Marine Assessment, National Ocean Service, National
Oceanic and Atmospheric Administration, Rockville, Maryland.
F-9 through G-27

This draft report summarizes the estimated relative susceptibility and estimated status of 23 estuaries in the
Gulf of Mexico with respect to nutrient-related pollution. The assessments are based on estimated estuarine
characteristics and nutrient loadings and do not reflect actual estuarine measurements of nutrient concentration
or documented symptoms of eutrophication.

Oetking, P., R. Back, R. Watson and C. Merks. 1974. Hydrography on the Nearshore
Continental Shelf of South Central Louisiana. Final Report of Offshore Ecology
Investigation for Gulf Universities Research Consortium, Galveston, Texas. SwRI Proj.
No. 03-3720, Southwest Research Institute, Corpus Christi, Texas.
G-7.1

A measure of the salinity, temperature, dissolved oxygen, transmissivity and currents was made on the
nearshore continental shelf of south central Louisiana to develop baseline data and to determine whether
offshore production platforms affect the water column. Data from 10 Offshore Ecology Investigation cruises,
349
-------
between August 1972 and January 1974, were used to determine daily, seasonal and areal trends for each of the
parameters. Graphic sections of each day's findings were constructed to reflect the changes in the water column
caused by geographic position, depth, time, air/sea conditions and offshore production platforms. These
profiles and the season average displays showed large variations in dissolved oxygen, zones of highly turbid
water, multiple layers of current, lenses of brackish water offshore and a few temporary changes in the water
column near offshore structures. Current data included in the daily profile displays are discussed on a seasonal
basis in an ...jcompanying OEI paper.

Olinger, L. W., R. G. Rogers, P. L. Fore, R. L. Todd, B, L. Mullins, F. T. Bisterfeld and L. A.
Wise II 1975. Environmental and Recovery Studies of Escambia Bay and the Pensacola
Bay System, Florida. Publ. No. EPA 904/9-76-016, U.S. Environmental Protection
Agency, Region IV, Atlanta, Georgia.
F-27

The Escambia Bay Recovery Study (EBRS) was established when public concern over the degradation of the
waters of Escambia Bay, Florida prompted a multidisciplinary team of EPA scientists to determine methods of
accelerating the recovery of Escambia Bay over and above reducing waste reductions into the Bay. Goals 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. The report documents pollution sources, hydrodynamics, sediments, water quality and
natural history aspects.

O'Neil, P. E. and M. F. Mettee (eds.). 1982. Alabama Coastal Region Ecological
Characterization: 2. A Synthesis of Environmental Data. Report to U.S. Dept of the Interior,
Fish and Wildlife Service, National Coastal Ecosystems Team. Information Series No. 61,
Geological Survey of Alabama, University, Alabama, 346 p.
G-l, G-2, G-2.1, G-2.2

The purpose of this report is to summarize all available information on the natural resources of coastal
Alabama. Data included will be used by the U.S. Fish and Wildlife Service and Bureau of Land Management,
Outer Continental Shelf office to plan for the development of outer continental shelf oil and gas reserves
offshore of Alabama. The report is divided into two sections. The first section contains a detailed description
of the geology and geography, hydrology, climate, plant and animal life, and threatened and endangered species
of coastal Alabama. The second section of the report (not cited) presents a conceptual model and supporting
text on four natural and two manipulated systems.

Orlando, Jr., S. P., L. P. Rozas, G. H. Ward and C. J. Klein. 1991. Analysis of Salinity
Structure and Stability of Texas Estuaries. Strategic Assessment Branch, NOS/NOAA,
Rockville, Maryland, 97 p.
G-116, G-17, G-18, G-21, G-22, G-23, G-24, G-26

The report for this project refines both the temporal and spatial aspects of salinity as depicted in the original
National Estuarine Inventory, Volume 1, by characterizing both its "structure" and "stability." Salinity
structure refers to its spatial distribution at a given time. The current effort improves over the three previously
established zones by defining salinities at 5-ppt increments for both the surface and bottom layers of the water
column for two seasonal periods reflective of representative high and low salinity conditions. Salinity
stability addresses the temporal variability and characterizes the dominant time scales over which the salinity
structure exhibits its greatest differences due to the frequency, magnitude and duration of events that may
potentially alter this structure.

Otvos, Jr., E. G. 1978. Calcareous benthic foraminiferal fauna in a very low salinity setting,
Lake Pontchartrain, Louisiana. J. Foraminiferal Res. 8(3):262-269.
G-7
350
-------
Lake Pontchartrain is a large, semi-enclosed, shallow, coastal embayment, with bottom salinities commonly
in the 1-5 % range, at certain locations infrequently reaching values of 12-19 %. In addition to the exclusively
agglutinated, brackish fauna, calcareous forms dominate large areas. Indications are strong that the calcareous
forms originated in the Gulf of Mexico and, helped by tidal currents, most of them reached the lake through the
Gulf Outlet Canal. This is confirmed by the absence of calcareous forms in the most saline eastern section of
the lake which is separated from the open Gulf by the brackish waters of Lake Borgne and the western
Mississippi Sound. The patchy distribution of sediments with high percentages of calcareous foraminifera may
be related to a number of factors such as bottom currents and nutrient distribution in the sediment and water.

Pacheco, P. A., D. R. G. Farrow, T. Manuelides and S. O. Rohmann. 1989a. Point Source
Discharges in Coastal Areas of Alabama. A Summary by Estuarine Watershed for 1987.
Draft. The National Coastal Pollution Discharge Inventory Program. U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, Rockville, Maryland, 34 p.
G-l, G-2, G-2.2

This report presents an inventory of the 38 major and 153 minor direct discharging point sources located in the
National Coastal Pollutant Discharge Inventory (NCPDI) study area in Alabama. It also summarizes estimates
of annual wastewater and pollutant discharges from these facilities for 16 pollutants. The estimates reflect
discharges for the period December 1986 through November 1987 (base year 1987), and are organized by the
five estuarine drainage areas in the study area. This report is the first in a series that is being compiled for each
state bordering the Gulf of Mexico, as part of an effort to update and improve the estimates in the NCPDI.

Pacheco, P. A., D. R. G. Farrow, T. Manuelides and S. O. Rohmann. 1989b. Point Source
Discharges in Coastal Areas of Mississippi. A Summary by Estuarine Watershed for 1987.
Draft. The National Coastal Pollution Discharge Inventory Program. U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, Rockville, Maryland, 32 p.
G-2.3, G-4, G-5, G-6

This report presents an inventory of the 24 major and 217 minor direct discharging point sources located in the
National Coastal Pollutant Discharge Inventory study area in Mississippi. It also summarizes estimates of
annual wastewater and pollutant discharges from these facilities for 16 pollutants. The estimates reflect
discharges for the period December 1986 through November 1987 (base year 1987), and are organized by the
two estuarine drainage areas in the study area. This report is the second in a series that is being compiled for
each state bordering the Gulf of Mexico, as part of an effort to update and improve the estimates in the
NCPDI.

Pacheco, P. A., D. R. G. Farrow, T. Manuelides, S. O. Rohmann, M. J. Katz and J. McLepd.
1989c. Point Source Discharges in Coastal Areas of Texas. A Summary by Estuarine
Watershed for 1987. Draft. The National Coastal Pollution Discharge Inventory Program.
U.S. Dept. of Commerce, National Oceanic and Atmospheric Administration, Rockville,
Maryland, 71 p.
G-l6, G-17, G-l8, G-19, G-22, G-23, G-24, G-26

This report summarizes annual wastewater and pollutant discharge estimates for 15 pollutants for 306 major
and 1116 minor direct discharging point sources in the National Coastal Pollutant Discharge Inventory study
area in Texas. The estimates reflect discharges between December 1986 and November 1987 (base year 1987),
and are organized by the eight estuarine drainage areas in the study area. This report is the third in a series for
states bordering the Gulf of Mexico, and is part of an effort to update and improve NCPDI discharge estimates.

Parker, Jr., F. R. and C. M. Bailey. 1979. Massive aggregations of elasmobranchs near Mustang
and Padre Islands, Texas. Tex. J. Sci. 31(3):255-266.
G-27
351
-------
From June 1 to June 4, 1977, large aggregations of elasmobranchs were observed along Gulf of Mexico
beaches in the vicinity of Padre and Mustang Island, Texas. Climatological conditions produced unusually
transparent water allowing observation of the aggregation. Resulting hydrological conditions favored
concentration of prey species in the shallow surf zone. Feeding was observed, evidence of recent birth recorded,
and mating behavior indicated in several species of elasmobranch. All of the species identified have been
previously reported to occur in the Gulf of Mexico.

Parker, R. H., A. L. Crowe and L. S. Bohme. 1980. Vol. I - Describe Living and Dead Benthic
(Macro-Meio-) Communities. M W. B. Jackson and G. M. Faw (eds.), Biological/Chemical
Survey of Texoma and Capline Sector Salt Dome Brine Disposal Sites off Louisiana, 1978-
1979. NOAA Tech. Memo NMFS-SEFC-29, NOAA/NMFS Final Report to DOE. U.S.
Dept. of Commerce, National Oceanic and Atmospheric Administration, National Marine
Fisheries Service, Galveston, Texas, 103 p.
G-7.1

A baseline survey of megabenthic and meiobenthic assemblages near two proposed brine disposal areas was
conducted from June 1978 through May 1979. Temporal changes occurred in species composition and
abundance at both sites. Both sites were characterized by low dissolved oxygen values during the summer
cruise. Little correlation between faunal abundance or diversity and sediment type or bacteria counts was found
at the station, site, or seasonal level, although community composition differed considerably between the two
sites. The inference suggested is that abundance and diversity are random but unique for each overall site,
suggesting sampling pattern or frequency is relatively unimportant in determining average production for the
region only.

Pascale, C. A. and J. R. Wagner. 1982. Water Resources of the Ochlockonee River Area,
Northwest Florida. Water-Resources Investigations Open-File Report No. 81-1121, U.S.
Dept. of the Interior, Geological Survey, Tallahassee, Florida, 114 p.
F-23

The Ochlockonee River area comprises about 1420 square miles in the panhandle of northwest Florida. In
1975, the population of the area was about 48,000. Water use averaged 11.4 mil gal per day; about half was
pumped from wells and half from streams. The area receives 57 in/yr of precipitation on the average. Much of
this water enters the surficial sand aquifer, seeps to streams, or enters the underlying water-bearing zone of the
upper confining unit and the Floridan aquifer. The water-bearing zone of the upper confining unit is used for
rural domestic supplies and is also important because the water it stores is a source of recharge to the
underlying Floridan aquifer.

Paulson, Jr., O. L., G. F. Pessoney, H. Battalora, R. Williams, J. Eastman and G. Pruitt. 1977.
Flushing characteristics of a Mississippi dead-end canal system. Water Resour. Bull.
13(2):341-348.
G-5

A study of a residential canal system on the Mississippi Gulf Coast and adjacent natural water bodies was
conducted to determine the relationship in flushing characteristics between manmade and natural systems. The
comparison was based on measurements of temperature, salinity, conductivity, coliform, pH, transparency,
biological oxidation demand, dissolved oxygen, bathymetry, tides, water velocity, and Rhodamine dye
concentrations. The results indicate that coliform bacteria increase with increasing distance of stations from
SL Louis Bay and dissolved oxygen decreases in a similar manner. Biological oxidation demand was low at all
stations, showing no differences between natural and manmade systems. The other parameters measured
showed little or no differences between natural and manmade systems, but reflect overall seasonal changes.

Pavela, J. S., J. L. Ross and M. E. Chittenden, Jr. 1983. Sharp reductions in abundance of
fishes and benthic macroinvertebrates in the Gulf of Mexico. Northeast Gulf Sci. 6(2): 167-
173.
352
-------
G-27

Natural depletion of dissolved oxygen to hypoxic (<2.0 mg/1) or anoxic levels in bottom waters of the
continental shelf of the northwestern Gulf of Mexico has been recognized since the mid-1930s. Subsequent,
but primarily unpublished, studies suggest this is a recurrent hydrographic feature off Louisiana. Little has
been published about the effects of natural hypoxia on fishes, shrimps and other macroinvertebrates in the
northwestern Gulf despite its apparent frequency and the valuable fisheries in that region. This paper
documents sharply reduced abundance and the elimination of both fishes and shrimps coincident with hypoxia
off Texas and presents general observations about decreases in common benthic macroinvertebrates.

Pechmann, K. B., J. O. Ellis, F. G. Everdale, S. Z. Green, I. C. Sheifer and M. K. Stern. 1986.
Marine Environmental Assessment. Gulf of Mexico. 1985 Annual Summary. U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, Marine Environmental
Assessment Division, Washington, D. C., 114 p.
F-9 through G-27

The 1985 annual assessment presents a synoptic view of several economic sectors and their direction and
indirect relations to the physical and biological aspects of the marine and atmospheric environments. The
geographical area considered is Key West, Florida to Brownsville, Texas. A summary of weather and
oceanographic events during 1985 over the region is presented. Three economic sectors appear in the report:
fisheries, recreation and transportation.

Perry, H. M. 1980. Dinoflagellate blooms occur off Louisiana. Coastal Oceanography and
Climatology News 3(1):3.
G-7.1, G-8.1, G-10

Widespread dinoflagellate blooms were reported off Louisiana in September. A fish kill, attributed to the
presence of this water mass, occurred later in the afternoon. On September 24, areas of red water were noted in
Breton and Chandeleur Sounds. Samples taken west of the Mississippi River contained large numbers of the
toxic dinoflagellate, Gonyaulax monilata.

Perry, H. M. and J. A. McLelland. 198la. Blooms continue to cause red tides in coastal waters
of Mississippi. Coastal Oceanography and Climatology News 4(l):l-2.
G-2.3, G-5.1

While small nearshore plankton blooms have occurred frequently in local waters for many years, large-scale
outbreaks of discolored water in Mississippi Sound and the adjacent Gulf of Mexico were not observed prior to
1974. Since then, several major outbreaks of red tide have occurred. The causative organisms include
Oscillatoria erythraea, Gonyaulax monilata, and Prorocentrum minimum.

Perry, H. M. and J. A. McLelland. 198 Ib. First recorded observance of the dinoflagellate
Prorocentrum minimum (Pavillard) Schiller 1933 in Mississippi Sound and adjacent waters.
Gulf Res. Rep. 7(l):83-85.
G-2.3, G-4, G-5

This paper documents the occurrence of the dinoflagellate Prorocentrum minimum in Mississippi Sound and
adjacent coastal waters. Outbreaks of discolored water are attributed to blooms of P. minimum in February
1977 and in January and February 1981. Data are presented on the seasonally of the organism in St. Louis
Bay. Observations on water appearance and a descriptive analysis of the cells are presented for the 1981
blooms.

Perry, H. M., K. C. Stuck and H. D. Howse. 1979. First record of a bloom of Gonyaulax
monilata in coastal waters of Mississippi. Gulf Res. Rep. 6(3):313-316.
G-2.3
353
-------
Data are presented on a bloom of the toxic dinoflagellate GonyaiUax monilata in coastal waters of Florida,
Alabama, Mississippi and Louisiana. This paper documents the first record of a bloom of this species in
Mississippi Sound and adjacent Gulf of Mexico.

Poinier, M. A. 1979. Epifaunal invertebrates as monitors of water quality in Lake Pontchartrain.
Pages 105-111 in J- W. Day, Jr., D. D. Culley, Jr., R. E. Turner and A. J. Mumphrey, Jr.
(eds.), Environmental Conditions in the Louisiana Coastal Zone. Proceedings of the Third
Coastal Marsh and Estuary Management Symposium, March 6-7, 1978, Baton Rouge,
Louisiana. Division of Continuing Education, Louisiana State University, Baton Rouge,
Louisiana.
G-7

The distribution and abundance of epifaunal invertebrates was investigated as a means of assessing and
monitoring the impact of adverse water quality upon aquatic life. Species zonation along pollution and
salinity gradients in Lake Pontchartrain was studied. Many species occurred in zones along these gradients,
indicating a relationship between water quality and distribution, and, hence, potential as indicator species. As
in other studies, the number of species decreased along pollution gradients and highly polluted habitats were
dominated by tolerant, opportunistic forms. Salinity was found to be the factor most highly correlated with
species distribution. Several species appeared to be good salinity indicators because of changes in abundance
and morphology along salinity gradients.

Poirrier, M. A. 1978. Studies of salinity stratification in southern Lake Pontchartrain near the
Inner Harbor Navigation Canal. Proc. La. Acad. Sci. 41:26-35,
G-7

Stratification was studied at 12 stations located within 10 km of the Inner Harbor Navigation Canal in
Southern Lake Pontchartrain. Surface and bottom measurements of salinity, temperature and dissolved oxygen
were made monthly from July 1976 through June 1977. Salinity stratification occurred in late spring, summer
and fall and mixing occurred in winter. Stratification decreased with distance from the canal, and low bottom
dissolved oxygen concentrations were found at stratified stations.

Poirrier, M. A., J. S. Rogers, M. A. Mulino and E. S. Eisenberg. 1975. Epifaunal Invertebrates
as Indicators of Water Quality in Southern Lake Pontchartrain. Tech. Rept. No. 5, Louisiana
Water Resources Research Institute, Louisiana State University, Baton Rouge, Louisiana, 43
P-
G-7

The distribution and relative abundance of estuarine epifaunal invertebrates can be used to detect water quality
differences. Epifaunal invertebrate associations were affected by salinity and stormwater discharge. Differences
among both biological and physico-chemical stations were related to discharge of more saline water by the
Industrial Canal and quality differences of outfall canal discharge. In 1973, the opening of the Bonnet Carre
Spillway added alkaline nutrient-rich, fresh water from the Mississippi River and affected all water quality
parameters. Gradual changes occurred as the river water was flushed from the Lake. Increased phytoplankton
growth resulted from the addition of nutrients. Epifaunal invertebrates were not greatly affected because 26
predominantly estuarine taxa were present 6 weeks after the spillway was closed.

Pokryfki, L. B. 1985. Measurement and Analysis of Hypoxia in Texas-Louisiana Coastal
Waters. M.S. Thesis, Texas A&M University, College Station, Texas, 130 p.
G-7.1, G-27

Hypoxia, and occasionally anoxia, occur annually in the northern Gulf of Mexico. Significant parameters
preceding and partially causing hypoxia, and the spatial extent of hypoxia, are determined. Temporal trends of
salinity, temperature, sigma-f, bottom dissolved oxygen, and river discharge, off Cameron, Louisiana are
described and statistically analyzed using 4 years (1981-1984) of data obtained from the Strategic Petroleum
354
-------
. Reserve Program. A special cruise was conducted in July of 1984 to measure the spatial extent of hypoxia in
coastal waters from Galveston, Texas to 74 km east of Cameron, Louisiana. A "best-fit" linear model
estimating bottom dissolved oxygen concentration contained the salinity and temperature variables. Time-
series analysis of the SPR data revealed time lags between low bottom dissolved oxygen and peak river
discharge (2-mo lag), and low salinity (1-mo lag). A time-series model more accurately predicted bottom
oxygen concentrations during hypoxic events using the river discharge and density gradient variables.

Pokryfki, L. B. and R. E. Randall. 1987. Nearshore hypoxia in the bottom water of the
northwestern Gulf of Mexico from 1981 to 1984. Mar. Environ. Res. 22(1):75-90.
G-7.1, G-27 :

Hypoxia, and occasionally anoxia, occur annually in the northern Gulf of Mexico. Important physical
properties preceding and partially causing hypoxia and the spatial extent of hypoxia are determined. Temporal
trends of salinity, temperature, sigma-f, bottom dissolved oxygen, and river discharge offshore Cameron,
Louisiana, are described and statistically analyzed using 4 years (1981-1984) of monthly data. A cruise was
conducted in July 1984 to measure the spatial extent of hypoxia in coastal waters from Galveston, Texas, to
74 km east of Cameron, La. A "best-fit" linear model estimating bottom dissolved oxygen concentrations
contained the salinity and temperature variables. Time series analysis of the data revealed time lags between
low bottom dissolved oxygen and peak river discharge (2-mo lag), and low salinity (1-mo kg). The time-
series model using the river discharge and density gradient variables more accurately predicted bottom dissolved
oxygen concentrations during hypoxic events.

Post, Buckle, Schuh and Jernigan, Inc. 1984. Hydrodynamic and Water Quality Analysis of
Caloosahatchee Estuary. Draft Report. Southwest Florida Regional Planning Council, Ft.
Meyers, Florida, (not in hand)
F-12

Price, K. C. 1974. Analysis of Water Quality Data - Timbalier Bay, Louisiana (August, 1972 -
January, 1974). Final Report, Part I. Gulf South Research Institute, New Iberia, Louisiana.
G-ll

Low oxygen concentrations were found at one station in July. All others were greater than 4 or 5 ppm.

Price, K. C. 1979. Onshore hydrography of Timbalier Bay, Louisiana. In C. H. Ward, M. E.
Bender and D. J. Reish (eds.), The Offshore Ecology Investigation. Effects of Oil Drilling
and Production in a Coastal Environment. Rice University Studies, Texas 65(4&5):145-157.
G-ll

Synoptic measurements of salinity, temperature, dissolved oxygen, and transparency were made in Timbalier
Bay, Louisiana, over a 2-yr period (1972-1974) to assess the effects of petroleum-related activities upon these
parameters. A total of 214 stations was sampled. No measurable effects attributable to such activities were
found. Seasonal effects during the study period accounted for the greatest variations observed.

Pulich, Jr., W. M. 1980. Ecology of a hypersaline lagoon: The Laguna Madre. Pages 103-122
in. P. L. Fore and R. D. Peterson (eds.), Proceedings of the Gulf of Mexico Coastal
Ecosystems Workshop, September 4-7, 1979, Port Aransas, Texas. Biological Services
Program Publ. FWS/OBS-80/30, U.S. Dept. of the Interior, Fish and Wildlife Service,
Washington, D.C.
G-26

A coastal Gulf of Mexico ecosystem, the Texas Laguna Madre has long been a fascinating place to scientists
because it represents one of only three oceanic hypersaline lagoons in the world. The purpose of this paper is
to 1) describe the present habitat of the Laguna, pointing out major changes that have occurred in the last
355
-------
decade; 2) present evidence for the probable causes of the evolutionary developments; and 3) outline some
critical ecological questions which require future study if the dynamic Laguna ecosystem is to be preserved.

Pulich, Jr., W. M. and W. A. White, (in press). Decline of submerged vegetation in the
Galveston Bay system: Chronology and relationships to physical processes. J. Coastal Res.
(not in hand)
G-17

Pulich Jr., W., W. A. White, M. Castiglione and R. J. Zimmerman. 1991. Status of submerged
vegetation in the Galveston Bay system. Pages 127-132 in F. S. Shipley and R. W. Kiesling
* (eds.), Proceedings. Galveston Bay Characterization Workshop, February 21-23, 1991.
Galveston Bay National Estuary Publication GBNEP-6,220 p.
G-17

See Shipley and Kiesling (1991).

Pullen E J., W. L. Trent and G. B. Adams. 1971. A Hydrographic Survey of the Galveston
Bay System, Texas, 1963-66. NOAA Technical Report NMFS-SSRF-639, U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, NMFS Biological Laboratory,
Galveston, Texas, 13 p.
G-17

Water temperature and salinity data, taken during 1963-1966, and dissolved organic nitrogen, total phosphorus,
and dissolved oxygen data taken during 1964-1966 from Galveston Bay, Texas were analyzed by area and
habitat (depth strata). Temperatures ranged from 0.4 to 36.0 *C during the study. Salinities ranged from 0.1
to 36.6 ppt Dissolved organic nitrogen concentrations ranged from 1 to 300 ug- at/1. Total phosphorus
concentrations ranged from 0.1 to 47.5 ug at/I. Dissolved oxygen concentration ranged from 0.2 to 13.6 ml/1.
Lowest oxygen "concentrations were in the channels and highest and similar concentrations were in the
peripheral and open-water habitats. Oxygen values were inversely correlated with water temperatures.

Rabalais, N. N. 1987. Oxygen depleted waters on the Louisiana continental shelf. Pages 314-
320 in Proceedings of the Seventh Annual Information Transfer Meeting, Minerals
Management Service, November 4-6, 1986. OCS Study MMS 87-0058, U.S. Dept. of the
Interior, Minerals Management Service, New Orleans, Louisiana.
G-7.1

Rabalais, N. N. 1988. Hypoxia on the continental shelf of the northwestern Gulf of Mexico.
Pages 81-87 in T. Mitchell (ed.), Physical Oceanography of the Louisiana-Texas Continental
Shelf. Proceedings of a Symposium, May 24-26, 1988, Galveston, Texas. OCS Study
MMS 88-0065, U.S. Dept. of the Interior, Minerals Management Service, New Orleans,
Louisiana, 198 p.
G-7.1

In mid-summer of 1985,1986, and 1987, critically depressed dissolved oxygen concentrations below 2 mg/1
occurred over large (ca. 8000 to 9500 km2) areas of the shelf from the Mississippi River delta onto the upper
Texas coast. Stations in 5 to 30 m water depth situated along a transect off Terrebonne and Timbalier Bays
were sampled intensively from June 1985 through 1986. Strong pycnoclines and oxyclines and low oxygen
conditions were persistent through the middle of August 1985, after which the water column was mixed by
waves from a series of tropical depressions and hurricanes. Areas of oxygen deficient bottom waters began to
develop as early as mid-April through late May in 1986 but did not become persistent until mid-June. The
summer of 1986 was an inactive hurricane season, and stratified waters and low oxygen conditions persisted
through mid-October. The zones were persistent, continuous, and intense from mid-June through mid-August
356
-------
Rabalais, N. N.
G-7.1
1990. The Dead Zone. Gulfwatch 2(2): 1,4,7.
Rabalais, N. N. and D. F. Boesch. 1986/87. Extensive depletion of oxygen in bottom waters of
the Louisiana shelf during 1985. Coastal Ocean Pollution Assessment News 3(4):45-47.
G-7.1

Bottom water oxygen data from 1985 on the southeastern Louisiana shelf for June through November and
shelfwide for July are summarized. Hypoxia was present when monitoring began on June 14 and continued
through early August. The extent of oxygen-depleted bottom waters in July covered 8000 km^. A series of
tropical storms and hurricanes mixed the water column from August 14-15 through late October.

Rabalais, N. N., M. J. Dagg and D. F. Boesch. 1985. Nationwide Review of Oxygen Depletion
and Eutrophication in Estuarine and Coastal Waters: Gulf of Mexico. Report to the U.S.
Dept. of Commerce, National Oceanic and Atmospheric Administration, National Ocean
Service, Office of Oceanography and Marine Services, Ocean Assessments Division,
Rockville, Maryland, 60 p.
G-l through G-27 -

Oxygen depletion occurs in the estuaries and continental shelf waters of the northern and northwestern Gulf of
Mexico even though these regions are characteristically shallow and usually subject to wind mixing. Hypoxia
or anoxia is most frequent in disturbed habitats, harbors and channels, or where freshwater runoff can provide a
mechanism for density stratification. Significant oxygen depletion occurs not only in shallow bays and
estuaries where patterns and causes are often identifiable but also in larger areas offshore, especially to the west
of the Mississippi River and the Atchafalaya River, where patterns and causes are less well known. Hypoxia
is observed frequently in many regions, for instance, Wolf and Perdido Bays, Mobile Bay, Mississippi Sound,
Lake Pontchartrain, and the Louisiana inner continental shelf.

Rabalais, N. N., B. A. McKee, D. J. Reed and J. C. Means. 199Ib. Fate and Effects of
Nearshore Discharges of OCS Produced Waters. Vol. I. Executive Summary, Vol. II.
Technical Report, Vol. IH. Appendices. Rept. No. OCS Study/MMS 91-0004,91-0005,91-
0006, U.S. Dept. of the Interior, Minerals Management Service, Gulf of Mexico OCS
Regional Office, New Orleans, Louisiana, 48 p., 337 p., 225 p.
G-9, G-10, G-ll, G-l

Estimates as of March 1991 indicate that 253,994 bbl/d of produced waters originating on the Federal OCS are
piped ashore for treatment and discharge into nearshore waters. This represents 25 % of the produced waters
generated on the Federal OCS and 13% of all produced waters discharged into the coastal waters of the State.
Of the 15 facilities that discharge OCS-generated produced waters into the coastal environments of Louisiana
(as of February 1990), ten discharges in seven areas were studied. The volumes discharged in the study areas
ranged from 3000 to 106,000 bbl/d. The receiving environments of these effluents included die shallow,
nearshore continental shelf; high energy, freshwater distributaries of the Mississippi River delta; and brackish
and saline coastal environments with moderately to poorly flushed waters. Elevated levels of dissolved solids
(salinity), volatile organic hydrocarbons, sulfides, and total radium activities identified the brine effluent in the
waters overlying the sediments. Where the water column was strongly stratified and/or sulfides were present in
near-bottom waters, low oxygen concentrations were measured. Sediments up to 1300 m from the produced
water discharges exhibited evidence of contamination by petrogenic hydrocarbons. Effects on benthic
macroinfauna were demonstrated at most of the study areas. Bioaccumulation studies showed the clear
potential for uptake and accumulation of produced water origin contaminants by oysters, both hi close
proximity to the discharges and at great distances from the discharges.
»
Rabalais, N. N., R. E. Turner, W. J. Wiseman, Jr. and D. F. Boesch. 1986a. Hydrographic,
Biological, and Nutrient Characteristics of the Water Column in the Mississippi River Delta
357
-------
Bight, June, 1985 to December, 1985. Data Report No. 2, Louisiana Universities Marine
Consortium, Chauvin, Louisiana.
G-7.1

In June 1985, a focused study was initiated to assess the spatial and temporal extent, intensity, and potential
causes of oxygen depletion in the northern Gulf of Mexico. Hypoxic bottom waters were studied along two
transects (one off Cat Island Pass near Cocodrie and one off Belle Pass off Port Fourchon) in the Mississippi
River Delta Bight area. Temperature, pH, dissolved oxygen, conductivity, salinity and depth were measured
with a Hydrolab Surveyor II Water Quality Data System at 1-, 2-, or 3-m intervals through the water column.
Water for chlorophyll and nutrient analyses was collected from surface and bottom waters in Niskin bottles.
Selected parameters (dissolved oxygen and sigma-f) are illustrated for each transect on each sample date.
Hydrographic, chlorophyll, and nutrient data for the cruises follow the figures.

Rabalais, N. N., R. E. Turner, W. J. Wiseman, Jr. and D. F. Boesch. 1986b. Hydrographic,
Biological, and Nutrient Characteristics of the Water Column on the Louisiana Shelf, July and
September, 1985. Data Report No. 3, Louisiana Universities Marine Consortium, Chauvin,
Louisiana.
G-7.1

In June 1985, a focused study was initiated to assess the spatial and temporal extent, intensity, and potential
causes of oxygen depletion in the northern Gulf of Mexico. Two shelfwide, quasi-synoptic cruises were
conducted from the Mississippi River to the Texas border during mid-July and early September, 1985.
Temperature, pH, dissolved oxygen, conductivity, salinity and depth were measured with a Hydrolab Surveyor
II Water Quality Data System at 1-, 2-, 3- or 5-m intervals through the water column. Water for chlorophyll
and nutrient analyses was collected from surface, mid-depths, and bottom water in Niskin bottles. Selected
parameters (dissolved oxygen and sigma-r) are illustrated for each transect on each cruise. These and additional
parameters are contoured for the entire shelf. Hydrographic, chlorophyll, and nutrient data for the cruise follow
the figures.

Rabalais, N. N., R. E. Turner, W. J. Wiseman, Jr. and D. F. Boesch. 199la. A brief summary
of hypoxia on the northern Gulf of Mexico continental shelf: 1985-1988. Pages 35-47 in R.
V. Tyson and T. H. Pearson (eds.), Modern and Ancient Continental Shelf Anoxia.
Geological Society Special Publication No. 58, The Geological Society, London, 470 p.
G-7.1

Oxygen-deficient conditions occur from April to October on the inner to middle continental shelf of the
northern Gulf of Mexico and may cover up to 9500 km2 during mid-summer off the Louisiana coast Hypoxic
bottom waters are found in 5-60 m water depth, 5-60 km offshore and extend up to 20 m above the bottom.
Salient forcing functions contributing to hypoxic water formation, maintenance and break-up are presented.
Ragan, J. G., A. H. Harris and J. H. Green. 1978. Temperature, salinity and oxygen
measurements of surface and bottom waters on the continental shelf off Louisiana during
portions of 1975 and 1976. Nicholls State University Prof. Paper Ser. (Biol.) 3:1-29.
G-7.1

The data presented in this 1975-1976 study contribute to the existing hydrographic data base and are unique in
some respects. They exceed the scope of previous efforts in covering a wider range of depth contours (6-110
m) in all geographical regions of the Louisiana Shelf, and includes oxygen as well as temperature and salinity
data for surface and bottom waters. Temperature, salinity and dissolved oxygen were recorded at 1 m above the
bottom and one meter below the surface at each station. Most transects were occupied four to six times
between September 1975 and August 1976. Hydrographic data were taken in conjunction with an effort that
was mainly designed to sample shrimp and fish.
358
-------
Randall, J. M. and J. W. Day, Jr. 1987. Effects of river discharge and vertical circulation on
aquatic primary production in a turbid Louisiana (USA) estuary. Neth. J. Sea Res.
21(3):231-242.
G-12

Aquatic primary production was measured at two sites in Fourleague Bay, a shallow, turbid estuary on the
central Louisiana coast receiving flow from the Atchafalaya River. Riverflow strongly influenced spatial and
seasonal patterns of production. Net production was negatively correlated with seasonal changes in riverflow at
both sites (upper Bay and lower Bay). Maximum production rates occurred at intermediate salinities. At low
salinities in the upper Bay, production was apparently limited due to turbidity; at higher salinities in the lower
Bay, production declined despite greater water clarity, apparently due to nitrogen limitation.

Ray, S. M. 1981. Areas of low dissolved oxygen, Gulf of Mexico. Pages 16-17 in P. F.
Sheridan and S. M. Ray (eds.), Report of the Workshop on the Ecological Interactions
between Shrimp and Bottomfishes, April, 1980. NOAA Technical Memo. NMFS-SEFC-63,
U.S. Dept. of Commerce, National Oceanic and Atmospheric Administration, National
Marine Fisheries Service. Southeast Fisheries Center, Galveston Laboratory, Galveston,
Texas.
G-7.1, G-27

Comments on the occurrence of low oxygen waters on the southeastern Louisiana shelf during 1973-1974, the
central Louisiana shelf in 1978, and the upper Texas coast in 1979. Hypoxic bottom waters on the continental
shelf may seriously affect annual recruitment, migration, population distribution, food supply, and mortality
of the shrimp and bottomfish. Consideration of this phenomenon would seem to be of critical importance,
since the shelf region of the northern Gulf of Mexico that is most likely to be affected by hypoxic conditions
related to influx of fresh water coincides with major areas of shrimp and bottomfish production.

Reitsema, L. A. 1980. Vol. n - Determine Seasonal Abundance, Distribution and Composition of
Zooplankton. la W. B. Jackson and G. M. Faw (eds.), Biological/Chemical Survey of
Texoma and Capline Sector Salt Dome Brine Disposal Sites off Louisiana, 1978-1979
NOAA Tech. Memo NMFS-SEFC-29, NOAA/NMFS Final Report to DOE. U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, National Marine Fisheries
Service, Galveston, Texas, 133 p.
G-7.1

Five stations were sampled for zooplankton at each of two sites offshore Louisiana during four collection
periods during 1978 and 1979. A bongo net and neuston net were deployed three times at each station during
four seasons. Each site is a proposed location for the offshore disposal of brine for the Strategic Petroleum
Reserve Program. The purpose of this study was to characterize the sites in terms of the seasonal and spatial
zooplankton and ichthyoplankton communities. The two sites were similar in terms of dominant taxa and the
density of planktonic organisms. Cluster analyses indicated greater differences between collecting dates than
between sites in terms of the taxa collected and their densities.

Renaud, M. L. 1985. Annotated Bibliography on Hypoxia and its Effects on Marine Life, with
Emphasis on the Gulf of Mexico. NOAA Technical Report NMFS-21, U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, National Marine Fisheries
Service, Seattle, Washington, 9 p.
G-2, G-6 through G-15, G-17, G-27

This bibliography contains 73 annotated references from publications and reports concerning hypoxia, <2.0
ppm dissolved oxygen concentration, in the Gulf of Mexico. Instances of hypoxia from similar habitats and
the effects of low oxygen levels on marine or estuarine organisms are also included.
359
-------
Renaud M L. 1986a. Detecting and avoiding oxygen deficient sea water by brown shrimp,
Penaeus aztecus (Ives), and white shrimp Penaeus setiferus (Linnaeus). J. Exp. Mar. Biol.
Ecol. 98:283-292.
G-7.1

Detection and avoidance of oxygen deficient sea water (<3.0 ppm dissolved oxygen) by white shrimp Penaeus
setiferus (Linnaeus), and brown shrimp, Penaeus aztecus (Ives), was measured under laboratory conditions.
Shrimp were acclimated to control salinity (22 %) and temperature (22 'Q for a minimum of 2 days and to the
test chamber for 1 h before recording data. White shrimp detected and significantly avoided intruding water
containing £1.5 ppm dissolved oxygen. Brown shrimp were more sensitive and avoided water having
dissolved oxygen concentration <2.0 ppm. Hypoxia along coastal Louisiana, west of the Mississippi River
Delta, could markedly affect shrimp stocks by increased natural mortality through 1) physiological stress, 2)
increased interspecific and conspecific competition, and 3) increased predation.

Renaud M L 1986b. Hypoxia in Louisiana coastal waters during 1983: Implications for
fisheries. Fish. Bull. 84(1): 19-26.
G-7.1, G-27

Hypoxic bottom water (<2.0 ppm dissolved oxygen) was present in shallow (9-15 m) waters south of central
Louisiana in June and July 1983. It was patchy in distribution from south of Barataria Pass to south and west
of Marsh Island. Data suggested that bottom water hypoxia did affect the abundance and distribution of shrimp
and bottomfish. Offshore bottom water dissolved oxygen was significantly correlated with 1) combined
catches of brown and white shrimp (r = -0.56, P < 0.002), 2) fish biomass (r = 0.56, P < 0.001), and 3)
vertical density gradient (r = -0.73, P < 0.001). Several hypoxic stations were in regions designated as
potentially hypoxic through a posteriori analysis of satellite data

Reyer, A. J., C. L. Holland, D. W. Field, J. E. Cassells and C. E. Alexander 1988. The
Distribution and Areal Extent of Coastal Wetlands in Estuaries of the Gulf of Mexico.
National Coastal Wetlands Inventory. Strategic Assessment Branch, Ocean Assessments
Division, Office of Oceanography and Marine Assessment, National Ocean Service, National
Oceanic and Atmospheric Administration, Rockville, Maryland, 18 p.
F9-G27

This report describes the area! extent and distribution of coastal wetlands in Texas, Louisiana, Mississippi,
Alabama, Florida, and a small section of Georgia that drain into the Gulf of Mexico. The wetlands data are
based entirely on an evaluation of National Wetland Inventory maps produced by the U.S Fish and Wildlife
Service.

Rice K W., L. W. McEachron and P. C. Hammerschmidt. 1988. Trends in Relative Abundance
and Size of Selected Finfishes in Texas Bays: November 1975 - December 1986.
Management Data Series No. 139, Texas Parks and Wildlife Dept., Coastal Fisheries Branch,
Austin, Texas, 192 p. ^^^
G-16, G-17, G-19, G-21, G-22, G-23, G-24, G-26.1, G-26.2

Trends in relative abundance and size of red drum, spotted seatrout, black drum, sheepshead, southern flounder,
Atlantic croaker, sand seatrout, gafftopsail catfish, Gulf menhaden, hardhead catfish, pinfish, spot, and striped
mullet have been monitored since 1975 using a standardized fishery independent gill net and bag seine
sampling program in Texas bay systems. The 1986 data continue to show that the impacts of management
decisions based on optimum sustained yield, effects of catastrophic events, and stock recruitment relationships
can be measured by using estimates of relative abundance based on the fishery independent monitoring
program.

Richards, F. A. and A. C. Redfield. 1954. A correlation between the oxygen content of sea water
and the organic content of marine sediments. Deep Sea Res. 1:279-281.
360
-------
G-7.1, G-27

There is considerable opinion but little direct evidence that the oxygen content of overlying water masses is
important in determining the organic content of marine sediments. Data now available from the northwestern
Gulf of Mexico indicate a clearcut inverse relationship between the organic content of the sediments and the
oxygen content of the overlying waters. The zones of maximum organic content and minimum oxygen
correspond well, and closely follow the edge of the continental shelf. It is probable that in this region, the
high organic content of the sediments is due to the presence'of water of low oxygen content immediately above
the bottom, and the smaller oxygen diffusion gradient available to provide oxygen to the subsurface layers of
sediment

Riley, C M., S. A. Holt, G. J. Holt, E. J. Buskey and C. R. Arnold. 1989. Mortality of larval
red drum (Sciaenops ocellatus) associated with a Ptychodiscus brevis red tide. Contrib. Mar.
Sci. 31:137-146.
G-23

Historically, the occurrence of red tides in Texas coastal waters has not been well documented. The most
recent bloom of the red tide organism Ptychodiscus brevis occurred during October and November 1986, a time
of year when many species of commercially important fish spawn and their larvae are abundant in local
estuaries. Peak density of P. brevis averaged 7000 cells/ml at monitoring sites but transient patches of
extremely high concentrations (10,000-47,680 cells/ml) were commonly found in the bays near Port Aransas
during the entire month of October. Hatch rates of laboratory spawned red drum eggs were unaffected by all red
tide concentrations tested. However, once hatched, larvae were negatively affected by all concentrations >40
cells/ml, based on dilution experiments with natural populations of P. brevis.
Riley, G. A. 1937. The significance of the Mississippi River drainage for biological conditions in
the northern Gulf of Mexico. J. Mar. Res. l(l):60-74.
G-2.1, G-5.1, G-7.1
This study is summarized as follows: 1) The Mississippi River carries large quantities of nutrient salts in the
Gulf of Mexico. The quantity of phosphate per unit volume is approximately four times as much as the
amount found in the sea water of the surrounding region. 2) In the Gulf there is a superficial zone of high
phosphorus content around the mouth of the Mississippi, extending from Mobile Bay westward to longitude
91'W. There is a zone of high phytoplankton content near the river which roughly coincides with the area of
high phosphorus. 3) It is suggested on purely theoretical grounds that some other nutrient which is discharged
from the Mississippi in the same manner as phosphate is a limiting factor in the region. 4) A few notes are
presented on the distribution of copper in the Gulf. It was present in all samples analyzed in both soluble and
combined form.

Roberts, B. S. 1979. Occurrence of Gymnodiniwn breve red tides along the west and east coasts
of Florida during 1976 and 1977. Pages 359-383 ia D. L, Taylor and H. H. Seliger (eds.),
Toxic Dinoflagellate Blooms. Proceedings of the Second International Conference on Toxic
Dinoflagellate Blooms, October 31 - November 5, 1978, Key Biscayne, Florida.
Developments in Marine Biology - Vol. 1, Elsevier North Holland, New York.
F-15.1

The occurrence of a Gymnodiniwn breve red tide off southwest Florida from September to December 1976
provided further evidence the Florida red tides develop in a predictable progression of initiation, support and
maintenance.

Robison, D. E. 1985. Variability in the vertical distribution of ichthyoplankton in lower Tampa
Bay, Florida. Pages 359-383 in S. F. Treat, J. L. Simon, R. R. Lewis, III and R. L.
Whitman, Jr. (eds.), Proceedings of the Tampa Bay Area Scientific Information Symposium,
May 1982. Sea Grant Project No. IR/82-2. Grant No. NA80AA-D-00038. Florida Sea
361
-------
Grant College, Report No. 65, Burgess Publishing Co., Minneapolis, Minnesota.
F-15

Previous studies have demonstrated that many zooplankton taxa are able to effect landward transport into, and
retention within, positive estuaries by regulating their vertical distribution. The present study was undertaken
to determine whether or not ichthyoplankton in lower Tampa Bay exhibit such regulatory abilities. An
evaluation of the net nontidal flow over four tidal cycles revealed that, during the summer rainy season, a
sufficient degree of density stratification occurred so as to result in a tidally averaged, two-layered circulation
pattern. From this information it is concluded that larval fish have a greater probability of achieving landward
transport and/or estuarine retention by remaining near the bottom during all tidal phases.

Rucker, J. B., R. P. Stumpf and W. W. Schroeder. 1990. Temporal variability of remotely
sensed suspended sediment and sea surface temperature patterns in Mobile Bay, Alabama.
Estuaries 13(2): 155-160.
G-2

Distribution patterns of suspended sediments and sea surface temperatures in Mobile Bay were derived from
algorithms using digital data from the visible, near-infrared, and infrared channels of the advanced very high
resolution radiometer (AVHRR) on the NOAA-TIROS-N satellite. Closely spaced AVHRR scenes for January
20,24, and 29,1982, were compared with available environmental information taken during the same period.
A complex interaction between river discharge, winds, and astronomical tides controlled the distribution
patterns of suspended sediments. These same variables, coupled with air temperatures, also governed the
distribution patterns of sea surface temperatures.

Russell, J. L. and J. A. Baskin. 1989. Baffin Bay, Texas. Pages 31-38 in J. A Baskin and J.
S Prouty (eds.), South Texas Clastic Depositional Systems. Guidebook Published by the
Corpus Christi Geological Society of the Annual Meeting of the Gulf Coast Association of
Geological Societies, Corpus Christi, Texas.
G-25

Baffin Bay in Kleberg and Kenedy Counties, Texas is a unique coastal plain estuary in the U.S., because it is
commonly hypersaline, with reverse estuarine circulation. Only ephemeral streams drain into the Bay. It is
commonly recognized as one of the few large hypersaline bays in the world. The hypersalinity is the result of
reverse estuarine circulation caused by evaporation, with natural inflow of fresh water associated only with
heavy rains of tropical storms. The only permanent sources of water entering the Bay are from sewage
outfalls, a large pertrochemical plant, and disposal of brines from oil and gas production.

Russell, M. 1977. Apparent effects of flooding on distribution and landings of industrial
bottomfish in the northern Gulf of Mexico. Northeast Gulf Sci. 1 (2) :77-82.
G-2.1, G-5.1, G-7.1

River discharge possibly affected bottomfish distribution from January - June 1972 and 1973. Normal
commercial concentrations of industrial bottomfish were not seen on the inshore grounds from Mobile Bay,
Alabama to Trinity Shoal, Louisiana during peak flood periods in 1973. Comparison between river runoff and
annual bottomfish landings for the last 17 years indicates that flooding may be beneficial to annual production
by increasing availability of nutrients and extending the estuarine nursery boundaries.

Sackett, W. M., J. M. Brooks, B. B. Bernard and C. R. Schwab. 1979. Low-molecular-weight
hydrocarbons and hydrographic project. Chapter 3 in P. L. Parker (ed.), Environmental
Assessment of the South Texas Outer Continental Shelf, Biology and Chemistry. Vol. I.
Final Report for 1977 to Bureau of Land Management. Contract No. AA550-CT7-11,
University of Texas Marine Science Institute, Port Aransas Marine Laboratory, Port Aransas,
Texas.
G-27
362
-------
This report contains a comprehensive tabulation and analysis of all low-molecular-weight hydrocarbon,
dissolved oxygen, and nutrient data taken as part of the BLM South Texas Outer Continental Shelf program in
1977. The above mentioned parameters were measured at Stations 1-3, on the four transects during the three
seasonal sampling periods (winter, spring and fall). Oxygen values are controlled throughout most of the year
in the upper 50 to 70 m of the STOCS area by physical processes. Nutrient concentrations were typically
low, being representative of open Gulf surface water. Nitrate was limiting to productivity and disappeared
during the summer and early fall. Phosphate and silicate were affected by the spring increase in productivity
but were generally regenerated by fall. Increased continental runoff during the spring months was reflected by
high silicate values at nearshore stations.

Sackett, W. M. and J. M. Brooks. 1976. Productivity and low-molecular weight hydrocarbons
project. Pages 331-373 in P. L. Parker (ed.), Environmental Assessment of the South Texas
Outer Continental Shelf, Chemical and Biological Survey Component for 1975. Report to
Bureau of Land Management. Contract No. 08550-CT5-17, University of Texas Marine
Science Institute, Port Aransas Marine Laboratory, Port Aransas, Texas.
G-27

This report contains a comprehensive tabulation of all the analyses of samples for the BLM-South Texas OCS
area during 1975. This includes analyses of 1) methane, 2) ethene, 3) ethane, 4) propene, 5) propane, 6)
dissolved oxygen, 7) nitrate, 8) phosphate, 9) silicate, 10) temperature and 11) salinity for three depths at each
of the 12 stations during each of the seasonal sampling periods. In addition, this report contains hydrographic
and hydrocarbon data obtained in the South Texas OCS region during 1975 that were not taken as part of the
South Texas OCS contract This includes: 1) more sampling depths on the 12 stations during the August-
September sampling period; 2) 5 stations with methane, nutrient and hydrographic data; and 3) hydrocarbon
"sniffer" data across part of the South Texas OCS area during a cruise in early October.

Sackett, W. M., J. M. Brooks and B. B. Bernard. 1977. Selected water column measurements:
Low-molecular-weight hydrocarbons, nutrients and dissolved oxygen. Chapter 15 in P. L.
Parker (ed.), Environmental Assessment of the South Texas Outer Continental Shelf, Biology
and Chemistry. Vol. II. Final Report for 1976 to Bureau of Land Management. Contract
No. AA550-CT6-17, University of Texas Marine Science Institute, Port Aransas Marine
Laboratory, Port Aransas, Texas.
G-27

Data for the baseline monitoring of the South Texas Outer Continental Shelf for winter, spring and fall of
1975 for the entire study area and along transect II off Port Aransas for monthly monitoring. Data are for
dissolved oxygen, phosphate, nitrate, silicate, temperature, salinity, and low-molecular-weight hydrocarbons in
water samples.

Sager, D. R. 1976. Temporal and Spatial Distribution of Phytoplankton in the Lower Atchafalaya
River Basin, Louisiana. M.S. Thesis, Louisiana State University, Baton Rouge, Louisiana,
158 p.
G-12

In a survey of the phytoplankton and physiochemical characteristics in this basin, 76 genera representing
Chlorophyta, Euglenophyta, Chrysophyta, Pyrrophyta, and Cyanophyta were identified. Swamp, lacustrine
and riverine habitats were distinguished on the basis of their distinctive phytoplankton assemblages and water
quality. The majority of taxa peaked during low water (summer and fall) when habitats were differentiated,
rather than during flood periods when the entire basin was inundated.

Sale, M. J., P. R. Kaufmann, H. I. Jager, J. M. Coe, K. A. Cougan, A. J. Kinney, M. E. Mitch
and W. S. Overton. 1988. Chemical Characteristics of Streams in the Mid-Atlantic and
Southeastern United States (National Stream Survey-Phase I). Vol. II: Streams Sampled,
363
-------
Descriptive Statistics, and Compendium of Physical and Chemical Data. Publ. No.
EPA/600/3-88/021b, U.S. Environmental Protection Agency, Washington, D.C., 595 p.
F-26, F-27

This second volume of the National Stream Survey-Phase I report presents basic data and provides
supplemental analyses of populations that are not included in Volume I (see Kaufmann et al. 1988). Separate
tables are presented for the following groups of variables: major cations and anions; acid neutralizing capacity,
pH, and related variables; aluminum, other metals, and dissolved organic carbon; and nutrients and other water
quality variables.

Saloman, C. H. 1973a. Hydrographic Observations in Tampa Bay, Florida - 1970. Data Report
No. 77, U.S. Dept. of Commerce, National Oceanic and Atmospheric Administration,
National Marine Fisheries Service, Seattle, Washington, 246 p.
F-15

Hydrographic data include water temperature, salinity, total phosphorus, total Kjeldahl nitrogen, pH, dissolved
oxygen, turbidity, water transparency, chlorophyll a, b and c, astacin and nonastacin carotenoids, and primary
productivity based on chlorophyll a. Also included are hourly observations of rainfall, air and water
temperature, and wind direction and velocity for October through December. Methods of collecting and
analyzing samples are indicated. Tables summarize data collected from 30 permanent stations by mean, range,
and number of observations according to month and area. Other tables summarize the mean, range, and
number of observations of samples taken twice daily at the laboratory dock.

Saloman C H. 1973b. Hydrographic Observations in the Gulf of Mexico off Pinellas County,
Florida (November 1970 - January 1972). Data Report No. 78, U.S. Dept. of Commerce,
National Oceanic and Atmospheric Administration, National Marine Fisheries Service,
Seattle, Washington, 228 p. (not in hand)
F-15.1

Saloman, C. H. 1974. Hydrographic and Meteorological Observations from Tampa Bay, and
Adjacent Waters - 1971. Data Report No. 84, U.S. Dept. of Commerce, National Oceanic
and Atmospheric Administration, National Marine Fisheries Service, Seattle, Washington,
554 p.
F-15, F-15.1

See Saloman (1973a).

Saloman, C. H., J. H. Finucane and J. A. Kelly, Jr. 1964. Hydrographic Observations of
Tampa Bay, Florida, and Adjacent Waters, August 1961 through December 1962. Data
Report No. 4, U.S. Dept. of the Interior, Fish and Wildlife Service, Washington, D.C., 112

F-15, F-15.1

See Saloman (1973a).

Saloman, C. H. and J. L. Taylor. 1968. Hydrographic Observations in Tampa Bay, Florida, and
the Adjacent Gulf of Mexico, 1965-66. Data Report No. 41, U.S. Dept. of Commerce,
National Oceanic and Atmospheric Administration, National Marine Fisheries Service,
Biological Laboratory, St. Petersburg, Florida, 393 p. (not in hand)
F-15, F-15.1

Saloman, C. H. and J. L. Taylor. 197 la. Hydrographic Observations in Tampa Bay and the
Adjacent Gulf of Mexico - 1967. Data Report No. 55, U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, National Marine Fisheries Service, Biological
364
-------
Laboratory, St. Petersburg, Florida, 67 p. (not in hand)
F-15, F-15.1

Saloman, C. H. and J. L. Taylor. 1971b. Hydrographic Observations in Tampa Bay and the
Adjacent Gulf of Mexico - 1968. Data Report No. 63, U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, National Marine Fisheries Service, Biological
Laboratory, St. Petersburg, Florida, 208 p. (not in hand)
F-15, F-15.1

Santos, S. L. and J. L. Simon. 1980. Response of soft-bottom benthos to annual catastrophic
disturbance in a south Florida estuary. Mar. Ecol. Prog. Ser. 3(4):347-355.
F-15

A portion of Hillsborough Bay, part of the Tampa Bay estuary, undergoes annual summer defaunation,
presumably due to hypoxia. Dissolved oxygen levels are very low (<1.0 mg/1) at the times of the
defaunations. In the ensuing period between defaunations, recolonization occurs. Monthly samples for 42
consecutive months were collected by Scuba-diver-operated, handheld PVC cores and screened through a 0.5-
mm sieve. Eight species, Mysella planulata, Ampelisca abdita, Streblospio benedicti, Grandidierella
bonnieroides, Mulinia lateralis, Mediomastus calif orniensis, Cyclaspis sp. and Nereis succinea were
numerically dominant, accounting for more the 95 % of the total density during the entire period. These eight
species are all classified as r-strategists and utilize several dispersal mechanisms to attain large populations
rapidly. Circumstantial evidence is presented which indicates that Ampelisca abdita, although classified as an
r-strategist, may be an effective interference competitor.

Santschi, P. H. and J. O. Samuell. 1991. The cycling of nutrients in Galveston Bay: Factors
regulating their concentrations. Pages 105-106 in F. S. Shipley and R. W. Kiesling (eds.),
Proceedings. Galveston Bay Characterization Workshop, February 21-23, 1991. Galveston
Bay National Estuary Program Publication GBNEP-6,220 p.
G-17

See Shipley and Kiesling (1991).

Schomer, N. S. and R. D. Drew. 1982. An Ecological Characterization of the Lower Everglades,
Florida Bay and the Florida Keys. Biological Services Publ. FWS/OBS-82/58.1, U.S. Dept.
of the Interior, Fish and Wildlife Service, Washington, D.C., 246 p.
F-9, F-10

A conceptual model of the study area identifies four major ecological zones: 1) terrestrial and freshwater
wetlands, 2) estuarine and saltwater wetlands, 3) Florida Bay and mangrove islands, and 4) the Florida Keys.
These zones are delineated by differences in basic physical-chemical background factors which in turn promote
characteristic ecological communities.

Schroeder, W. W. 1976. Physical Environmental Atlas of Coastal Alabama. Publ. No. MASGP-
76-034, Mississippi-Alabama Sea Grant Program. G. C. Marshall Space Flight Center,
National Aeronautics and Space Administration and Marine Science Programs, University of
Alabama System, Dauphin Island Sea Lab, Dauphin Island, Alabama.
G-l, G-2, G-2.1, G-2.2

Schroeder, W. W. 1979. The dissolved oxygen puzzle of the Mobile Estuary. Pages 25-30 in H.
A. Loyacano, Jr. and J. P. Smith (eds.), Symposium on the Natural Resources of the Mobile
Bay Estuary, Alabama. Alabama Coastal Area Board, Mississippi-Alabama Sea Grant
Consortium and U.S. Fish and Wildlife Service. U.S. Army Corps of Engineers District,
Mobile, Alabama.
G-2
365
-------
The dissolved oxygen system in the Mobile Estuary remains essentially unknown. Some information is
available on the quantitative annual cycle and macro-scale distribution patterns during oxygen depletion
periods. Recent unpublished research has provided the first look at oxygen-consuming processes. Virtually
nothing is known about oxygen-producing processes, environmental factors responsible for the on-set,
maintenance and termination of oxygen depletion periods or meso- to micro-scale distribution patterns during
oxygen depletion periods.

Schroeder, W. W., J. R. Abston, S. J. Parker and A. W. Schultz. 1988. Annotated Bibliography
of Selected Geological Oceanography References and a Bibliography of Related Material, East
Louisiana, Mississippi, Alabama, and Northwest Florida Continental Shelf. Project R/ER-
16, Contract No. NA85AA-D-SG005, Mississippi-Alabama Sea Grant Consortium, Dauphin
Island Sea Lab, Dauphin Island, Alabama, 27 p.
F-24.1, G-2.1, G-5.1, G-7.1

Schroeder W. W. and G. F. Crozier. 1974. Hydrographic and current structure on the western
continental shelf of the northeastern Gulf of Mexico. Pages 395-404 in R, E. Smith (ed.),
Marine Environmental Implications of Offshore Drilling in the Eastern Gulf of Mexico.
Proceedings of a Conference, January 31 - February 2, 1974, University of South Florida,
St. Petersburg, Florida. State University System of Florida, Institute of Oceanography, St.
Petersburg, Florida.
G-2.1, G-5.1

The interest developing in the offshore areas of Mississippi and Alabama stimulated a series of cruises in 1973
by personnel from the Marine Environmental Sciences Consortium. The Alabama Estuarine and Continental
Shelf Oceanographic Survey has been concerned with the relationship of Mobile Bay to Mississippi Sound and
the continental shelf, as well as the areas involved in the possible "superport." Recent support of the
University of South Alabama will extend these activities to the east toward Panama City. Development of the
program has led to the establishment of several standard cruise tracks.

Schroeder, W. W., S. P. Dinnel and W. J. Wiseman, Jr. 1990. Salinity stratification in a river-
dominated estuary. Estuaries 13(2): 145-154.
G-2

Analysis of salinity data from Mobile Bay indicates that stratification-destratification events within this broad,
shallow estuary are not uncommon. These events are related to the strength of the winds, through their
influence on wave generation and subsequent bottom drag coefficient increase, and to the strength of river
discharge. They do not appear to be due to the strength of tidal currents, as has been observed elsewhere.
Furthermore, river flow appears to be the dominant control, the winds being important only in the absence of
large freshwater discharges. The annual spring freshet can flush most of the salt from the Bay. During other
times of the year the relative strengths of river discharge and wind stress change the bay from highly stratified
to nearly homogeneous and back on a variety of time scales ranging from daily to seasonal.

Schroeder, W. W. and W. R. Lysinger. 1979. Hydrography and circulation of Mobile Bay.
Pages 75-94 in H. A. Loyacano, Jr. and J. P. Smith (eds.), Symposium on the Natural
Resources of the Mobile Bay Estuary, Alabama. Alabama Coastal Area Board, Mississippi-
Alabama Sea Grant Consortium and U.S. Fish and Wildlife Service. U.S. Army Corps of
Engineers District, Mobile, Alabama.
G-2

Mobile Bay's salinity regime ranges from Bay-wide influence of high salinity Gulf of Mexico waters during
extended periods of low river discharge to dominance by freshwater under flooding river conditions. However,
no set seasonal salinity pattern exists because of the river system's high degree of variability on day-to-day,
month-to-month and year-to-year scales. On the other hand the Bay's thermal regime has a well defined
seasonal structure directly linked to atmospheric temperatures. Circulation is poorly understood. It appears to
366
-------
be a two-layer system even though the Bay is very shallow. Surface drogue studies suggest a highly variable
system in the lower Bay.

Schroeder, W. W., W. J. Wiseman, Jr., A. Williams, Jr., D. C. Raney and G. C. April. 1990.
Climate and oceanography. Pages 27-51 in Mobile Bay: Issues, Resources, Status, and
Management. Proceedings of a Seminar, November 17, 1988, Washington, B.C. NOAA
Estuary-of-the-Month Seminar Series No. 15, U.S. Dept. of Commerce, National Oceanic
and Atmospheric Administration, Estuarine Programs Office, Washington, D.C.
G-2

Despite long periods of repetitious weather, especially during the summer, the climate of the Mobile Bay
region is quite variable. During severe weather, systems often dissipate or strengthen when approaching the
coast A monitoring program, consisting of both land and buoy observation stations, should be developed to
allow prediction of the impacts of meso- and micro-scale systems, particularly on economically important
aspects of the area.

Schroeder, W. W. and W. J. Wiseman, Jr. 1988. The Mobile Bay estuary: Stratification, oxygen
depletion, and jubilees. Pages 41-52 ia B. J. Kjerfve (ed.), Hydrodynamics of Estuaries.
Vol. II. Estuarine Case Studies. CRC Press, Boca Raton, Florida.
G-2

Jubilees, mass migrations of estuarine organisms to the shores of Mobile Bay, have been presumed to be
induced by hypoxic bottom waters. A review of new and historic data sets corroborates this hypothesis and
elucidates the processes causing hypoxia. Hypoxia may be frequent and widespread during the summer,
stratified season, whereas the winter climatology appears generally to preclude its occurrence. Interactions of
the Bay's geomorphology, water column structure, circulation, biological activity, and man-made
modifications result in oxygen depletion zones. These, in turn, elicit a movement response from certain
estuarine biota. The relationships between these factors are the subject of this paper. During summer months,
strong haline stratification isolates the bottom waters of Mobile Bay from direct air-sea interaction. High
temperatures increase metabolic rates and benthic consumption reduces near-bottom dissolved oxygen content
of the water column to values that are stressful to the biota. This hypoxic water is advected by tides and wind-
driven baraclinic motions. This movement appears to be responsible for the jubilee phenomenon in the Bay.

Schropp, S. J., F. D. Calder, G. M. Sloane, K. O. Swanson, J. C. Carlton, G. L. Halcomb, H.
L. Windom, F. Huan and R. B. Taylor. 1991. A Report on Physical and Chemical
Processes Affecting the Management of Perdido Bay. Results of the Perdido Bay Interstate
Project. Alabama Dept of Environmental Management, Mobile, Alabama and Florida Dept.
of Environmental Regulation, Coastal Zone Management Section, Tallahassee, Florida, 323
P-
F-28, G-l

Objectives of this study were to describe physical and chemical processes affecting dissolved and paniculate
nutrient and suspended solid transport in the Perdido River basin and the fate of these materials in Perdido Bay.
The results show that the bay receives nutrients from anthropogenic sources, dominated during this study by
materials delivered by Elevenmile Creek. The results also show that physical conditions controlled by the
natural forces of wind, streamflow, and tide, are such that stratification and hypoxia occur during a major
portion of the year. Summer and early fall months are critical periods when maximum natural stresses
(hypoxia) are imposed on the Bay and its biological communities. The results of sediment studies indicate
that, at present, the Bay does not suffer from acute toxic contamination. There is evidence of some
contamination from urban runoff, but not at the levels encountered in other, more developed, parts of Alabama
and Florida.

Schurtz, M. H. and K. M. St. P€. 1984. Water Quality Investigation of Environmental
Conditions in Lake Pontchartrain. Report on Interim Findings. Louisiana Dept. of
367
-------
Environmental Quality, Water Pollution Control Division, Baton Rouge, Louisiana.
G-7

This study was initiated to address in general the concern of the Louisiana public over the apparently
deteriorating water quality of Lake Pontchartrain, and specifically to further investigate an environmental
situation that resulted in speculation that "dead zones" cover large areas of the lake bottom. A prominent
concern central to the "dead zone" issue was speculation that toxic chemicals may be the cause of the observed
depressed species diversity of bottom dwelling animals in the southeastern part of the lake. The study
determined the occurrence and distribution of chemicals, toxic and otherwise, in the southern portion of the
lake that have resulted from anthropogenic origin; and provided an overall water quality assessment to ascertain
any phenomena, in particular water pollution, that may be adversely affecting the ecological balance of the
lake. The evaluation concluded that severe dissolved oxygen depletions in 1980 resulted from salinity
stratification and that there was no evidence that toxic chemicals caused the defaunated areas.
Seadock, Inc. 1974. Environmental Report. Vol. I and
Texas A&M Foundation, College Station, Texas.
G-18, G-21, G-27
Summary. Texas A&M University,
A comprehensive environmental report has been prepared in support of the proposed project. The
environmental study was conducted over a period of a full year. It included both marine and terrestrial field
studies conducted by recognized environmental authorities. The Texas A&M Research Foundation conducted
the marine studies. This summary presents a brief description of the existing environment and an assessment
of the environmental effects of the proposed project.

Seaton, A. M. 1979. Nutrient Chemistry in the Barataria Basin - a Multivariate Approach. M.S.
Thesis, Louisiana State University, Baton Rouge, Louisiana, 124 p.
G-10

A general survey of nutrient chemistry in the fresh and estuarine waterbodies of the Barataria basin was
initiated in winter 1976. Physical, chemical, and biological water quality parameters were sampled quarterly
from February 1976 through August 1977 along a 120-km transect extending the length of the basin. Twenty-
three sampling stations were selected to reflect the range of nutrient conditions and general water quality in the
basin. Multivariate statistical analyses (i.e., cluster and factor analysis) were utilized to create a general
characterization of water quality in both the estuarine and freshwater areas. The parameters selected for the
analysis were: total organic nitrogen, total phosphorus, Secchi disk depth, chlorophyll a and total inorganic
nitrogen. The multivariate analysis clearly documents the change in nutrient dynamics between a dry year
(1976) and a wet year (1977).

Seaton, A. M. and J. W. Day, Jr. 1979. The development of a trophic state index for the
quantification of eutrophication in the Barataria Basin. Pages 113-125 in J. W. Day, Jr., D.
D. Culley, Jr., R. E. Turner and A. J. Mumphrey, Jr. (eds.), Environmental Conditions in
the Louisiana Coastal Zone. Proceedings of the Third Coastal Marsh and Estuary
Management Symposium, March 6-7, 1978, Baton Rouge, Louisiana. Division of
Continuing Education, Louisiana State University, Baton Rouge, Louisiana.
G-10

A systematic investigation of the variability in water parameters in the Barataria Basin was initiated in 1976.
The objectives of this study was to measure changes in a number of physical, chemical, and biological
parameters on a fresh-saline transect and to elucidate reasons for the change. The development of a trophic
state index is the result of the search for appropriate tools to accomplish this objective. It is concluded that: 1)
most of the Barataria Basin above the Gulf Intracoastal Waterway appears to be eutrophic; 2) multivariate
analysis techniques provide a good quantitative approach in examining the eutrophication process; and 3) with
further refinement, these techniques should be able to be applied to the remainder of the coastal zone.
368
-------
Seller, R., G. Guillen and A. M. Landry, Jr. 1991. Utilization of the upper Houston Ship
Channel by fish and macroinvertebrates with respect to water quality trends. Pages 39-45 in
F. S. Shipley and R. W. Kiesling (eds.), Proceedings. Galveston Bay Characterization
Workshop, February 21-23, 1991. Galveston Bay National Estuary Program Publication
GBNEP-6, 220 p.
G-17

See Shipley and Kiesling (1991).

Shampine, W. J. 1971. Chemical, Biological, and Physical Data for the Major Lakes and
Reservoirs in Louisiana. Basic Records Report No. 5, U.S. Dept. of the Interior, Geological
Survey, Water Resources Division, Louisiana District. Louisiana Dept. of Public Works,
Baton Rouge, Louisiana, 98 p.
G-7, G-ll, G-ll.l, G-14

Includes data on Lake Boudreaux, Lake Calcasieu, Lake De Cade, the Grand Lake complex. Lake Maurepas,
Lake Mechant, and Lake Pontchartrain. The lowest dissolved oxygen value was for Lake Mediant (3.3 mg/1);
no others were below 4.5 mg/1.

Shaw, J. K., P. G. Johnson, R. M. Ewing, C. E. Comiskey, C. C. Brandt and T. A. Farmer.
1982. Benthic Macroinfauna Community Characterizations in Mississippi Sound and
Adjacent Waters. Contract No. DACW01-80-C-0427. Final Report to U.S. Army Engineer
District, Mobile, Alabama.
G-2, G-2.1, G-2.2, G-2.3, G-5.1
This report presents the results of a study of benthic macroinfauna communities in Mississippi Sound and
adjacent areas. This information will be utilized by the U.S. Army Corps of Engineers in developing a
regional dredging plan for the Mississippi Sound and vicinity. During planning, consideration will be given
to the impacts of removal and placement of dredged material on each of the benthic communities. The
analyses will include: 1) effect of time of dredging operation on the benthos, 2) effect of dredging operation on
benthic community structure, and 3) effect of dredging operations on the abundance and area! distribution of a
community.

Shaw, R. F., B. D. Rogers, J. H. Cowan, Jr. and W. H. Herke. 1988. Ocean-estuary coupling
of ichthyoplankton and nekton in the northern Gulf of Mexico. Am. Fish. Soc. Symp. 3:77-
89.
G-7.1, G-27

Both gulf menhaden Brevoortia patronus and sand seatrout Cynoscion arenarius spawn offshore in the Gulf of
Mexico during winter and spring. After a cross-shelf transit, their larvae later enter estuarine nursery areas.
We have integrated new and existing early life history data on the occurrence of these species in the continental
shelf ichthyoplankton and as late-stage larvae and juveniles in Louisiana estuaries to document this recruitment
process.

Shepard, F. P. and G. A. Rusnak. 1957. Texas bay sediments. Publ. Inst. Mar. Sci. Univ. of
Texas 4(2):5-13.
G-17, G-21, G-22, G-23, G-26

The purpose of the study was to determine differences between sediments in bays of a humid area and those in
areas of semiaridity. The differences in the bays range from over 80 ppt in Laguna Madre to approximately 1
ppt at the mouths of some of the rivers entering the bays on the northern Texas coast Detailed results are
presented for San Antonio Bay and Laguna Madre. Texas bay deposits have such definite environmental
characteristics that these bay fades should be easily recognized in the Tertiary sediments which are now largely
buried by recent deposits along the Texas coast
369
-------
Sheridan, P. F. 1992. Comparative habitat utilization by estuarine macrofauna within the
mangrove ecosystem of Rookery Bay, Florida. Bull. Mar. Sci. 50(l):21-39.
F-ll

Abundance and biomass of juvenile and adult decapods and fishes in adjacent intertidal mangrove, seagrass, and
open water habitats were compared using a quantitative drop sampler in July, September and December 1988
and April 1989. Fish densities were higher in non-vegetated, open waters than in flooded red mangrove prop
roots or mixed seagrass beds. Shrimp densities were higher in seagrass habitats than in open waters or among
mangrove prop roots. On a monthly basis, among-habitat differences in density or biomass of major taxa did
not exhibit any patterns, with the exception of shrimp which were always significantly more numerous in
seagrasses than in one or both alternate habitats. Flooded red mangroves were, at times, utilized by both
resident and transient fishes and crabs (but not by shrimps) at densities similar to those in seagrasses and open
waters.

Shew, D. M., R. H. Baumann, T. H. Fritts and L. S. Dunn. 1981. Texas Barrier Islands Region
Ecological Characterization: Environmental Synthesis Papers. Biological Services Program,
Publ. FWS/OBS-81/32. National Coastal Ecosystems Team, Biological Services Program,
U.S. Fish and Wildlife Service, Washington, D.C., 413 p.
G-17 through G-27

The report is a synthesis of selected environmental literature for the Texas Barrier Islands Region and is a part
of the Texas Barrier Islands Region Ecological Characterization Study. The region includes the coastal
counties and extends 64 km inland and offshore for 9 nautical miles, or the State-Federal demarcation. The
papers address the geology, climate, hydrology and hydrography, and the biology of each of six drainage basins
along the Texas coast: Galveston, Matagorda-Brazos, San Antonio, Copano-Aransas, Corpus, Christi and
Laguna Madre, as well as the marine system offshore.
Shiller, A. M. and E. A. Boyle. 1991. Trace elements in the Mississippi River Delta outflow
region: Behavior at high discharge. Geochim. Cosmochim. Acta 55(11):3241-3251.
G-7.1

Samples for dissolved trace element analysis were collected in surface waters of the plume of the Mississippi
River during a period of high discharge. These field data are compared to the results of laboratory mixing
experiments. The studies show that Cu, Ni, and Mo are largely unreactive in the plume. Surprisingly, Fe
also appears to show little reactivity; the pronounced flocculation removal of Fe frequently observed in other
estuaries is not seen in this system. This difference may be a consequence of the alkaline nature of the
Mississippi which results in low dissolved Fe concentrations in the river. Zinc, another particle-reactive
element, also shows little reactivity. The chromium distribution shows apparent non-conservative behavior
indicative of estuarine removal; however, temporal variation in river concentrations is a more likely
explanation for this behavior.

Shipley, F. S. and R. W. Kiesling (eds.). 1991. Proceedings. Galveston Bay Characterization
Workshop, February 21-23, 1991. Galveston Bay National Estuary Program Publication
GBNEP-6, 220 p.
G-17

A compilation of summaries of current status of scientific data concerning multiple aspects of the Galveston
Bay system. Topics include resource agency programs, point and non-point source pollution, the Houston
Ship Channel, toxicants in water, toxicants in aquatic organisms, toxicants in birds, oil spill impacts, oilfield
produced water, nutrients, pollutant transport, habitat studies, ecological surveys, faunal surveys, biological
studies, physical features, inflow and hydrology, salinity, modeling, and information synthesis.

Shirzad, F. F., C. J. Klein, HE and S. P. Orlando, Jr. 1989. Revised Physical and Hydrologic
Characteristics for the Mississippi Delta Region Estuaries. National Estuarine Inventory:
370
-------
Supplement 3. Strategic Assessment Branch, Ocean Assessments Division, Office of
Oceanography and Marine Assessment, National Ocean Service, National Oceanic and
Atmospheric Administration, Rockville, MD, 18 p.
G-8.1, G-9, G-10, G-ll

A supplement to the National Estuarine Inventory Data Atlas of 1985 for the named estuaries. The
supplement divides the Mississippi Delta into four distinct systems: Breton and Chandeleur Sounds,
Mississippi River, Barataria Bay, and Terrebonne and Timbalier Bays. Each system presentation addresses the
physical and hydrologic characteristics, spatial depictions of salinity zones and their variability, tide gauges,
and head of tide. New data, such as volume by salinity zone, and freshwater retention time as an indicator of
flushing, have been added.

Sikora, W. B. and B. J. Kjerfve. 1985. Factors influencing the salinity regime of Lake
Pontchartrain, Louisiana, a shallow coastal lagoon: Analysis of a long-term data set.
Estuaries 8(2A):170-180.
G-7

Lake Pontchartrain, Louisiana, is a 1630 km shallow brackish lagoon with a mean salinity from 1.2 ppt in the
west to 5.4 ppt in the east. The construction of a 120 km long deep-water connection to the Gulf of Mexico
in 1963, was expected to cause a 5 ppt increase in lagoon salinity. However, the actual increase was
everywhere in the lagoon less than 2 ppt Analysis of 31 years of daily salinity and discharge records indicated
that discharge is the most important factor controlling salinity variations in Lake Pontchartrain. Seventy-four
percent of low-frequency salinity variations are explained by freshwater discharge and the completion of the
deep-water canal. Lake Pontchartrain experiences annual variations of salinity as high as 8%. This salinity
signal has remained constant since the beginning of the salinity records in 1946. It appears that the deep-water
canal is not responsible for observed die-back of freshwater swamps and retreat of lagoon shorelines.

Sikora, W. B., J. P. Sikora and A. M. Prior. 1981. Environmental Effects of Hydraulic
Dredging for Clam Shells in Lake Pontchartrain, Louisiana. Report to U.S. Army Engineer
District, New Orleans, Contract No. DACW29-79-C-0099. Coastal Ecology Laboratory,
Center for Wetland Resources Publ. No. LSU-CEL-81-18. Louisiana State Univ., Baton
Rouge, Louisiana, 140 p.
G-7

The results of the experimental shell dredging lead to the following conclusions: 1) bulk density of sediments
is reduced and the conditions persist for long periods, 2) a detrimental effect on the macrofauna and meiofauna
was produced and persisted for two years, 3) benthic biomass production was reduced, 4) seasonal recruitment
was similar but there was differential survival at the dredged site, 5) species diversity did not differ, 6) benthic
community of Lake Pontchartrain has reached an equilibrium with present levels of pollution and consists of a
low number of species characterized as being tolerant of pollution, and 7) the direct impacts of dredging have
the potential to maintain a benthic community of low biomass in the open lake.

Simmons, E. G. 1957. An ecological survey of the Upper Laguna Madre of Texas. Publ. Inst.
Mar. Sci. Univ. of Texas 4(2): 156-200.
G-26.1

Considerable interest has been shown in the Laguna Madre because of its unusual salinity conditions. This
report is concerned with the plant life, invertebrates and vertebrates of the area and the relationship of these to
basic physical and biological factors in the environment
Simon, J. L. 1974. Tampa Bay estuarine system - A synopsis. Florida Scientist 37(4):217-244.
F-15

The tremendous surge in population and development in the area has placed a severe drain on the system which
comprises five contiguous areas -1) Old Tampa Bay, 2) Hillsborough Bay, 3) Tampa Bay, 4) Boca Ciega Bay,
371
-------
and 5) Terra Ceia Bay. The system extends over some 346 square miles and includes 212 miles of shoreline.
Coliform bacteria counts in Old Tampa Bay and Hillsborough Bay have been high enough to justify limiting
contact sports and shellfishing. Water quality is affected by discharges from 55 sewage treatment plants, more
than 90 industries and over 100 marinas. Primary productivity is among the highest in the world. A great
diversity of marine life is present from both temperate and tropical regions. Projects in progress or proposed
threaten every part of the System and a means for proper management must be established to avoid a
degradation of its waters.

Sklar, F. H. and R. E. Turner. 1981. Characteristics of phytoplankton production off Barataria
Bay in an area influenced by the Mississippi River. Contrib. Mar. Sci. 24:93-106.
G-7.1, G-10

Phytoplankton paniculate production was measured in coastal waters along a transect west of the Mississippi
River delta using in situ and light-box techniques. Seasonal changes in light-box surface production (0.2-
155.0 mg C/m3/h), chlorophyll a (1-26 mg Chi a/m3), and assimilation number (0.15-42.0 mg C/mg Chi
a/h) were all correlated with riverflow. Seasonal changes in the riverflow volume altered the nutrient supply,
water color, turbidity and salinity/temperature regimes. Changes in nutrient concentrations were indicative of
nitrogen limitation. Annual particulate phytoplankton production was 290 g C/m^.

Skupien,L. 1989. Stress. A way of life for Mobile Bay. Gulfwatch l(4):2-3/7.
G-2

This article discusses the various forces at work in creating stress on the Mobile Bay area. It describes the
efforts being made to change this pattern.
Smith, C. J. and R. D. DeLaune. 1985. Recovery of added l^N-labelled ammonium-N from
Louisiana Gulf coast estuarine sediment. Estuarine Coastal Shelf Sci. 21(2):225-233.
G-10

The loss of added ^N-labelled NH4+ from bottom sediment was studied in situ in a shallow saline Louisiana
Gulf Coast lake (Airplane Lake in the Barataria estuary). ^N enrichment in the organic N fraction increased
rapidly during the first 15 days of incubation and then increased slowly from 15 to 123 days. After the initial
rapid ^N \oss and the ^N-labelled NH4+ had been immobilized in the organic pool, there was no further
statistically significant loss of ^N from the sediment between 15 and 337 days. Correspondingly low
denitrification rates were measured.

Smith, N. P. 1988. The Laguna Madre of Texas: Hydrography of a hypersaline lagoon. Pages
31-40 in B. J. Kjerfve (ed.), Hydrodynamics of Estuaries. Vol. H Estuarine Case Studies.
CRC Press, Boca Raton, Florida.
G-26

The purpose of this paper is to summarize results of studies that provide insight into the effects of physical
processes acting upon or within the lagoon. Integration of available information reveals a hypersaline lagoon,
reflecting the semiarid climate, but modified by low-frequency meteorologically forced exchanges with adjacent
coastal bays.

Stanley, D. W. 1992. Historical Trends: Water Quality and Fisheries, Galveston Bay. University
of North Carolina Sea Grant College Program Publication UNC-SG-92-03. Institute for
Coastal and Marine Resources, East Carolina University, Greenville, North Carolina, 100 p.
G-17

The overall goal of this study was to prepare a systematic comparison of long-term trends of water quality in
four important U.S. estuaries, and to try to relate the water quality trends to changes in fishery resources. This
372
-------
project had four specific objectives: 1) to document long-term trends in water quality and, where possible,
identify causes, consequences and significance; 2) to assess whether problems are similar or unique to each
estuary; 3) to assess whether progress is being made in improving conditions in water quality and fishery
resources and whether there are examples of success that would be useful for estuarine managers and researchers
elsewhere; 4) to glean examples of the useful integration of research and policy.

Steidinger, K. A. 1973. Phytoplankton ecology: A conceptual review based on eastern Gulf of
Mexico research. CRC Crit. Rev. Microbiol. 3:49-68.
F-15, G-18, G-7.1, G-24

A review based on eastern Gulf of Mexico data that is applicable to many temperate and tropical regions.
Phytoplankton distributions are grouped into estuarine, coastal/open Gulf, open Gulf diatom communities, and
open Gulf dinoflagellate communities. Communities are composed of year-round resident coastal species that
fluctuate in dominance and secondarily "visitors." Diatoms dominate inshore coastal areas while
dinoflagellates and coccolithophores often dominate open Gulf waters. Microflagellates numerically dominate
in eastern Gulf coastal and estuarine environments. Florida red tide ecology is outlined.

Steidinger, K. A. and W. E. Gardiner. 1985. Phytoplankton of Tampa Bay - a review. Pages
147-183 in S. F. Treat, J. L. Simon, R. R. Lewis, m and R. L. Whitman, Jr. (eds.),
Proceedings of the Tampa Bay Area Scientific Information Symposium, May 1982. Sea
Grant Project No. IR/82-2. Grant No. NA80AA-D-00038. Florida Sea Grant College,
Report No. 65, Burgess Publishing Co., Minneapolis, Minnesota.
F-15
This paper contains an introduction to phytoplankton, a description of the Tampa Bay estuary, a historical
account of phytoplankton studies, and a discussion and summary. It includes two tables: 1) number of Tampa
Bay system phytoplankton species/varieties and genera by major grouping, and 2) number of species of
diatoms and dinoflagellates in common between other geographical areas and the Tampa Bay system.

Steidinger, K. A. and E. A. Joyce, Jr. 1973. Florida Red Tides. State of Florida, Department of
Natural Resources, Educational Series No. 17. Marine Research Laboratory, Florida
Department of Natural Resources, St. Petersburg, Florida, 26 p.
F-9 through F-24

The first documented fish kill associated with discolored water in Florida occurred in 1844, but the causative
organism, Gymnodinium breve, was not identified until 1948. Red tides and research results over the period
1953-1973 are discussed and summarized. Red tides are natural phenomena along the Florida Gulf coast, but
major incidents are sporadic.
Stephens, C. F. and C. H. Oppenheimer. 1972.
coast. Contrib. Mar. Sci. 16:99-108.
F-22
Silica contents in the northwestern Florida Gulf
Analyses of the river and bay waters of the northwestern Florida Gulf Coast indicate that weathering of silica is
active and that the fresh waters and runoff are significant sources of silica for the estuarine waters. An eighteen
month study of the distribution of silica in the St. Marks River and Apalachee Bay indicates that active
inorganic processes contribute to the loss of silica as dilution is not entirely responsible for the change.
Silicate content of the surface waters ranged from 240 ug-at/1 in fresh water at 10 miles from the open
Apalachee Bay to less than 1 ug-at/1 in the Bay where salinity is 34 %. The St Marks River has an average
discharge of 1000 cfs which, if containing 200 ug-at Si/1, would have an average discharge of approximately
15.5 metric tons of silica per day. Other areas of the shore estuarine environment show similarly high silica
values and are relative to salinity.
373
-------
Stern, D. H., B. H. Atwell, E. L. Merz and M. J. Vinet 1968. A Summer Limnological Study
of Lake Pontchartrain, Louisiana. Technical Report No. 3, Louisiana Water Resources
Research Institute, Louisiana State University, Baton Rouge, Louisiana, 83 p.
G-7

Basic physical, chemical, and biological data were collected in the summer of 1968 in preparation for future
investigations of the lake. Biweekly samples were collected at 26 during June and July. Field measurements
at each station included the following physical and chemical factors: dissolved oxygen, pH, relative light
transmissions, salinity, Secchi disc visibility, specific conductivity, and total alkalinity. Laboratory analyses
of the lake water included the following factors: aluminum, barium, coliform bacteria, copper, cyanide,
detergents, nitrate-nitrogen, orthophosphate, silica, sodium and chloride ions, sulfate, tannins and lignins, total
hardness, total iron, total nitrogen and turbidity. Plankton tows were made during most station visits, and
bottom sediments were collected from most stations in June. The plankton composition and abundance was
studied, and the pH and organic matter content of the bottom sediments were examined.

Stern, D. H. and M. S. Stem. 1969. Physical, Chemical, Bacterial, and Plankton Dynamics of
Lake Pontchartrain, Louisiana. Technical Report No. 4, Louisiana Water Resources
Research Institute, Louisiana State University, Baton Rouge, Louisiana, 60 p.
G-7

Preliminary and intensive studies from November 1968 to July 1969 showed that the discharge of stormwater
into Lake Pontchartrain affects the water quality and biorhythm of aquatic microorganisms. Especially after
heavy rains in Orleans Parish, the presence of coliforms renders the nearshore water and beaches unsafe for
some water sports. Lake sediments, stirred up by wind waves and during heavy rains, increase the turbidity;
the reduced light available for photosynthesis results in the death of phytoplankton, which add to the bottom
organic materials and subsequently furnish food for more planktonic growth, and thus hastens the filling of the
lake. Recommendations include: counting of fecal coliforms to determine water quality; prohibition or
discouragement of water sports at certain beaches after summer rains; careful regulation of proposed
chlorination of storm water owing to presence of ammonia, which retards the disinfection process, and because
of unreacted chlorine, which will disrupt the natural food chain; and basin-wide cooperation to prevent or reduce
further pollution.

Stetson, H. C. 1953. The sediments of the western Gulf of Mexico. Part I - The continental
terrace of the western Gulf of Mexico: Its surface sediments, origin and development Papers
in Physical Oceanography and Meteorology 12(4): 1 -45.
G-7.1, G-27

During the winter of 1947 the research vessel, Atlantis worked in the western half of the Gulf of Mexico. The
primary purpose of the cruise was to determine the texture and organic content of the surface and near-surface
sediments with their contained foraminiferal fauna, from the shelf, the slope, and the Sigsbee Deep. Surface
samples and cores up to 11 ft were obtained from 551 stations. A number of plankton tows and hydrographic
stations were made and bathythermograph readings were taken to the depth of 100 m every 5 miles. Rock
dredging was carried out on two of the coral capped hills or "bioherms" which are numerous in the vicinity of
the 80-fm curve.

Stone, J. H. (ed.). 1980. Environmental Analysis of Lake Pontchartrain, Louisiana, Its
Surrounding Wetlands, and Selected Land Uses. Vol. I, 581 p. and Vol. II, 1219 p.
Prepared for U.S. Army Corps of Engineers District, New Orleans, Louisiana. Publ. No.
LSU-CEL-80-08, Coastal Ecology Laboratory, Center for Wetland Resources, Louisiana
State University, Baton Rouge, Louisiana.
G-7

A year-long study during 1978-1979 was made of selected ecological components and processes of Lake
Pontchartrain and its surrounding wetlands and of selected land uses in its drainage basin or watershed. A large
374
-------
report with chapters on preliminary modeling of the Lake Pontchartrain ecosystem by computer simulations; a
trophic analysis of Lake Pontchartrain, Louisiana, and surrounding wetland tributaries; computation of drift
patterns; general hydrography of Lake Pontchartrain; general hydrography of the tidal passes; nutrient and
carbon geochemistry; structure and function of the phytoplankton community; the distribution and abundance
of plankton; productivity of the swamps and marshes that surround Lake Pontchartrain; changes in the
submerged macrophytes of the Lake; macrobenthic survey; nekton; aspects of the life history of Anchoa
mitchilli; fish food habits; microplankton movement through the tidal passes; selected commercial fish and
shellfish data; preliminary survey of higher vertebrates; recent land use changes in the watershed; and
urbanization, peak streamflow and estuarine hydrology of Louisiana.

Stuntz, W. E. 1982. Coastal anoxia in the northern Gulf of Mexico. Abstr. for Proceedings of
the Third Annual Gulf of Mexico Information Transfer Meeting, August 24-26, 1982, New
Orleans, Louisiana. U.S. Dept. of the Interior, Minerals Management Service, Outer
Continental Shelf Office, New Orleans, Louisiana.
G-7.1

A large area of low oxygen was found along the coast of Louisiana in June and July of 1982. The anoxia was
restricted to the bottom waters in depths from 46 m shoreward. Bottom trawl samples were taken at each of
the stations. In areas where the oxygen levels were less than 2 ppm, the catches of fish were very low and
were made up mostly of pelagic species. No commercial shrimp were taken in the low oxygen areas. Water
temperatures were very high in the area, which may indicate an area where circulation is limited, at least during
some periods. The biological implications of this situation are of considerable interest, due largely to the
potential impacts on the commercial shrimp species.

Stuntz, W. E., C. E. Bryan, K. Savastano, R. S. Waller and P. A. Thompson. N.D. SEAMAP
Environmental and Biological Atlas of the Gulf of Mexico, 1982. Southeast Area Monitoring
Assessment Program (SEAMAP) of the Gulf States Fisheries Commission, Ocean Springs,
Mississippi, 155 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

In this first of a series of of biological and environmental atlases, the objectives of the 1982 surveys were to
determine distribution and abundance of ichthyoplankton and trawl-caught organisms and to document the
environmental factors that might affect their distribution and abundance.

Stuntz, W. E., N. Sanders, T. D. Leming, K. N. Baxter and R. M. Barazotto. 1982. Area of
hypoxic bottom water found in northern Gulf of Mexico. Coastal Oceanography and
Climatology News 4(4):37-38.
G-7.1

During a recent SEAMAP cruise to assess shrimp and bottomfish distribution and abundance, an area of low
dissolved oxygen was found in bottom water along the coast of Louisiana. The area of low oxygen
concentration was found in depths of 9^46 m along the coast from 89*30.5^ to 91*30.1^. Based on our
data, the area of low oxygen certainly had an impact on demersal fish and invertebrate distribution. Of interest,
especially from the commercial fishing point of view is how the bottom-dwelling species respond to the low
oxygen.

Summers, J. K. and V. D. Engle. 1992. Evaluation of sampling strategies to characterize
dissolved oxygen conditions in northern Gulf of Mexico estuaries. Environ. Monitoring and
Assessment, (in press)
F-27, F-28

Dissolved oxygen was continuously monitored in eight sites of northern Gulf of Mexico estuaries in August
1990. Monte Carlo analyses on subsamples of the data were used to evaluate several commonly used
monitoring strategies. Monitoring strategies which involve single point sampling of dissolved oxygen may
375
-------
often misclassify an estuary as having good water quality. In the case of shallow, often well-mixed estuaries
that experience diurnal cycles, such monitoring often does not occur at night, during the time of lowest
dissolved oxygen concentration. Our objective was to determine the minimum sampling effort required to
correctly classify a site in terms of the observed frequency of hypoxia. Tests concluded that the most
successful classification strategy used the minimum dissolved oxygen concentration from a continuously
sampled 24-h period.

Swingle, H. A. 1971. Biology of Alabama estuarine areas - cooperative Gulf of Mexico estuarine
inventory. Ala. Mar. Resour. Bull. 5:1-123.
G-l, G-2, G-2.2

Twenty trawl stations, five seine stations, and four plankton stations were sampled monthly from January
1968 through March 1969. A total of 162 species of fishes and 44 species of invertebrates were collected from
the estuarine waters of Alabama. Seventy-six species of fishes are documented from other sources. The area!
and seasonal distributions of the species are discussed. Also presented are data on the density of oysters on the
public reefs and historical fisheries statistics.

Swingle, H. A. and D. G. Bland. 1974. A study of the fishes of the coastal watercourses of
Alabama. Ala. Mar. Resour. Bull. 10:17-102.
G-l, G-2, G-2.2

Trawl or seine samples were collected monthly at 23 stations within the brackish water zone of the coastal
watercourses of Alabama. A total of 104 species of fishes and 19 species of invertebrates was collected from
December 1970 through May 1972. Water salinity, temperature and dissolved oxygen values are presented and
are correlated to some extent with species abundance and diversity. The species composition of altered and
unaltered watercourses and the species composition of estuarine waters are discussed. The number of species of
marine, estuarine and freshwater fishes taken was approximately equal, but marine and estuarine individuals
made up 96 % of the total catch. Marine and estuarine species of fishes and invertebrates dominated the
population down to, about 2 ppt. Freshwater species were dominant at salinities below 1 ppt but the number
of individuals was still exceeded by marine and estuarine species.

Tarver, J. W. 1972. Occurrence, Distribution and Density of Rangia cuneata in Lakes
Pontchartrain and Maurepas, Louisiana. Tech. Bull. No. 1, Louisiana Wild Life and
Fisheries Commission, New Orleans, Louisiana, 8 p.
G-7 . . . .

Samples of Rangia cuneata populations were taken with a modified 18-in oyster dredge throughout Lakes
Pontchartrain and Maurepas to determine the occurrence, distribution, and density of clam populations. Depth,
bottom type, salinity, temperature, and turbidity were recorded with each sample. A total of 187 samples
yielded 237,963 Rangia clams. Rangia catches ranged from 0 to 1,517 clams per 3-min tow, and specimen
sizes ranged from 8 to 64 mm, with a mean height of 30.9 mm. Though all the monthly stations reported
that the mean height varied from month to month, the data indicate that Rangia populations were stable,
having no major fluctuations in mean height during the study. The presence of low salinity, high turbidity,
and a substrata of sand, mud and vegetation remnants during the sample period seems to have resulted in a high
clam density and, consequently, a small clam size.

Tarver, J. W. and R. J. Dugas. 1973. A Study of the Clam, Rangia cuneata, in Lake
Pontchartrain and Lake Maurepas, Louisiana. Tech. Bull. No. 5, Louisiana Wild Life and
Fisheries Commission, New Orleans, Louisiana, 97 p.
G-7

Samples of Rangia cuneata were taken by utilizing a Peterson and modified oyster dredge throughout Lakes
Pontchartrain and Maurepas to determine the occurrence, distribution and density of clam populations.
Hydrological, sedimentological and plankton samples were analyzed in an effort to determine some of the
376
-------
factors affecting the distribution, density and growth of R. cuneata. Mortality and the effects of dredging
operations on the environment are briefly discussed. Annual shell production and overfishing factors are
discussed and recommendations to the industry are also proposed.

Tarver, J. W. and L. B. Savoie. 1976a. Phase I - Area Description. Pages 1-6 ia An Inventory
and Study of Lake Pontchartrain-Lake Maurepas Estuarine Complex. Tech. Bull. No. 19,
Louisiana Wildlife and Fisheries Commission, New Orleans, Louisiana.
G-7

The study was initiated to investigate the composition, general distribution, and abundance of commercially or
potentially important fauna inhabiting the Lake Pontchartrain-Lake Maurepas estuarine complex, so that
comparisons with previously Completed wetland research in Louisiana and the northern Gulf of Mexico might
enable administrators to efficiently manage Louisiana's renewable coastal zone resources. Vertebrate and
macroinvertebrate populations were sampled, and molluscan benthic communities were empirically determined.
Zooplankton was estimated. Hydrological and climatological parameters were collected at four stations. Grain
size determinations were made.

Tarver, J. W. and L. B. Savoie. 1976b. Phase m - Hydrology and Water Chemistry. Pages
101-144 ia An Inventory and Study of Lake Pontchartrain-Lake Maurepas Estuarine
Complex. Tech. Bull. No. 19, Louisiana Wildlife and Fisheries Commission, New Orleans,
Louisiana.
G-7

Although there are many interdependent factors to which the hydrology of Lakes Pontchartrain and Maurepas
may respond, probably one of the most significant is wind speed and direction, followed by the discharge of
adjacent rivers. Some authors attribute major hydrological changes to tidal fluctuation, but in the case of these
lakes this factor would seem to have generally less effect than characteristically recognized. Tidal movements
seldom exceed a 1- to 2-ft change. This would seem to precluue the use of tidal stages to explain some
hydrological changes.

Taylor, J. L. 1974(1975). The Charlotte Harbor estuarine system. Fla. Sci. 37(4):205-216.
F-13
The estuary is about 35 by 30 miles at the extremes with more than 200 miles of shoreline and comparatively
little contamination. Vegetation includes salt marsh, mangrove and other peninsular Florida Gulf Coast
communities which are highly productive. Of 246 fish species, 18 produce a harvest with a dockside value of
ca. $3,000,000. Dredging and development have had an adverse effect on more than 1 1,000 acres near Port
Charlotte, Punta Gorda, Cape Coral and Fort Myers. An additional 25300 acres are closed to shellfishing
because of pollution. Further manmade changes threaten the value of the estuary as a fishing ground and
hatchery for commercially valuable marine fishes.
Taylor, J. L. 1970. Coastal development in Tampa Bay, Florida.
1(NS)(10):153-156.
F-15
Mar. Pollut. Bull.
In 1962, a site on Tampa Bay's western shore was selected for the U.S. Bureau of Commercial Fisheries
Estuarine Research Laboratory. The scientific program included biological, chemical and physical studies of
estuaries in the eastern Gulf of Mexico to determine the effects of environmental factors on fisheries in the
Gulf. Tampa Bay was well chosen as a starting point for these investigations because the estuary contains
many unchanged areas as well as areas that have been altered by dredge-fill operations, harbor and channel
construction, and effluents from domestic sewage and industry. Sufficient work has been completed in all
major areas of the bay to show some of the natural features that promote fishery production as well as some
effects of pollution and coastal development
377
-------
Teague, K. G., C. J. Madden and J. W. Day, Jr. 1988. Sediment-water oxygen and nutrient
fluxes in a river-dominated estuary. Estuaries 11(1): 1-9.
G-12

Sediment oxygen uptake and net sediment fluxes of dissolved inorganic and organic nitrogen and phosphorus
were measured at two sites in Fourleague Bay from August 1981 through May 1982. Sediment oxygen uptake
averaged 49 mg/m^/h. On the average, ammonium was released from the sediments and nitrate was taken up.
Very different nitrate fluxes were observed at the two sites, with sediment uptake at the upper, river-influenced,
high nitrate site and release at the lower, marine-influenced, low nitrate site. Phosphate fluxes were low and
often negative. Dissolved organic nitrogen fluxes varied greatly. Total dissolved nitrogen and phosphorus
fluxes indicated the sediments were a nitrogen and phosphorus source at the lower bay, and a nitrogen sink and
phosphorus source in the upper bay.

Temple, R. P., D. L. Harrington and J. A. Martin. 1977. Monthly Temperature and Salinity
Measurements of Continental Shelf Waters of the Northwestern Gulf of Mexico, 1963-65.
NOAA Technical Report NMFS SSRF-707, U.S. DepL of Commerce, National Oceanic and
Atmospheric Administration, National Marine Fisheries Service, Washington, D.C., 26 p.
G-7.1, G-27

Temperature and salinity observations made monthly from January 1963 to December 1965 at 48 stations in
the northwestern Gulf of Mexico are presented. Off the coasts of Louisiana and Texas, monthly average
temperatures of surface and bottom waters at station depths of 7, 14, 28, 46, and 73 m exhibited seasonal
trends that were similar over a 3-yr period. Salinities of surface and bottom waters varied markedly at 7- and
14-m stations, whereas at deeper stations seasonal fluctuations were restricted primarily to surface waters. The
magnitude of yearly salinity fluctuation decreased with an increase in distance offshore.

Texas Department of Water Resources. 1980a. Guadalupe Estuary: A Study of the Influence of
Freshwater Inflows. Rept. No. LP-107, Texas Dept of Water Resources, Austin, Texas.
G-22

In 1975, the 64th Texas Legislature enacted Senate Bill 137, a mandate for comprehensive studies of "the
effects of freshwater inflow upon the bays and estuaries of Texas" Reports published as a part of the effort
were to address the relationship of freshwater inflow to the health of living estuarine resources (e.g., fish,
shrimp, etc.) and to present methods of providing and maintaining a suitable ecological environment The
technical analyses were to characterize the relationships which have maintained the estuarine environments
historically and which have provided for the production of living resources at observed historic levels. Seven
major estuaries on the Texas coast are part of this series.

Texas Department of Water Resources. 1983. Laguna Madre Estuary: A Study of the Influence of
Freshwater Inflows. Rept. No. LP-182, Texas DepL of Water Resources, Austin, Texas.
G-25, G-26, G-26.1, G-26.2

SeeTDWR(1980a).

Texas Department of Water Resources. 1980b. Lavaca-Tres Palacios Estuary: A Study of the
Influence of Freshwater Inflows. Rept. No. LP-106, Texas Dept. of Water Resources,
Austin, Texas.
G-21

SeeTDWR(1980a).
378
-------
Texas Department of Water Resources. 198 la. Nueces and Mission-Aransas Estuaries: A Study
of the Influence of Freshwater Inflows. Rept. No. LP-108, Texas Dept. of Water Resources,
Austin, Texas.
G-23, G-24

See TDWR (1980a).

Texas Department of Water Resources. 198 Ib. Sabine-Neches Estuary: A Study of the Influence
of Freshwater Inflows. Rept. No. LP-116, Texas Dept. of Water Resources, Austin, Texas.
G-16

See TDWR (1980a).

Texas Department of Water Resources. 198Ic. Trinity-San Jacinto Estuary: A Study of the
Influence of Freshwater Inflows. Rept. No. LP-113, Texas Dept. of Water Resources,
Austin, Texas.
G-17

See TDWR (1980a).

Texas Water Development Board. 1973. Coastal Data System User Documentation. Vol. I,
revised Feb. 1977, Storage Reference Manual, 156 p. Vol. n, revised June 1976, Retrieval
Reference Manual, 173 p. Texas Water Development Board, now Texas Department of
Water Resources, Austin, Texas.
G-16 through G-24, G-26

This manual describes the mechanics of estuarine data storage and retrieval for the Texas Coastal Data System.
Information is given for basic data coding methods, data header information, parameter coding, hydrographic
coding, and biological coding. Chemical, physical, and biological data on all of the bays and estuaries along
the Texas Gulf coast. The data were collected in a cooperative effort by several State and Federal agencies at
numerous sampling locations in several bays.

Thayer, G. W., D. R. Colby, W. F. Hettler, L. F. Simoneaux and D. S. Peters. 1985. Alteration
of freshwater inflow patterns can impact the fishery function of estuaries. Coastal Ocean
Pollution Assessment News 3(3):33-34.
F-ll

The upland and wetland areas of coastal Florida have undergone extensive development in the past 20 years, and
concerns have been expressed that this development may be responsible for reductions in sport and commercial
fisheries in some areas. One development was in die area called Golden Gates Estates near the Ten Thousand
Island area in south Florida. The pattern of freshwater inflow into an estuary in the area, Falca Union Bay, was
greatly altered by channelization of the upland drainage basin in the vicinity of Golden Gate Estates in the
1960s. The channelization resulted in a point source discharge of freshwater into Faka Union Bay during the
rainy season rather than the overland flow that normally occurs.

Thomas, W. H. and E. G. Simmons. 1960. Phytoplankton production in the Mississippi Delta.
Pages 103-116 ia F. P. Shepard, F. B. Phleger and T. H. van Andel (eds.), Recent
Sediments, Northwest Gulf of Mexico. Proceedings of a Symposium Summarizing the
Results of Work Carried on in Project 51 of The American Association of Petroleum
Geologists (1951-1958), 1959, Scripps Institute of Oceanography, La Jolla, California. The
American Association of Petroleum Geologists, Tulsa, Oklahoma.
G-7.1, G-8.1
379
-------
At 138 stations in the eastern Mississippi Delta area, measurements were made of phy toplankton produced
(C14 uptake), chlorinity, temperature, suspended solids, Secchi disc depth, inorganic phosphate, soluble silica,
and soluble Kjeldahl nitrogen. In addition, the phytoplankton in the water were identified and enumerated.

Thompson, P. A. and N. Bane (eds.). 1986a. SEAMAP Environmental and Biological Adas of
the Gulf of Mexico, 1983. No. 13. Southeast Area Monitoring Assessment Program
(SEAMAP) of the Gulf States Fisheries Commission, Ocean Springs, Mississippi, 179 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

Overall survey objectives were to assess the distribution and abundance of ichthyoplankton and trawl-caught
organisms, and document environmental factors that might affect their distribution and abundance. This second
in a series of SEAMAP biological and environmental atlases presents resource survey data, in a summarized
form, collected during 1983 surveys.

Thompson, P. A. and N. Bane (eds.). 1986b. SEAMAP Environmental and Biological Adas of
the Gulf of Mexico, 1984. No. 15. Southeast Area Monitoring Assessment Program
(SEAMAP) of the Gulf States Fisheries Commission, Ocean Springs, Mississippi, 171 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

In keeping with the program goal of establishing a coordinated, long-term resource database, it was decided to
continue the same types of survey activities conducted in 1982 and 1983, but in addition, to add a plankton
survey for mackerel in August of 1984.

Thompson, P. A. and T. D. Leming. 1978. Seasonal Description of Winds and Surface and
Bottom Salinities and Temperatures in the Northern Gulf of Mexico, October 1972 to January
1976. NOAA Technical Report NMFS SSRF-719, U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, National Marine Fisheries Service, Washington,
D.C., 44 p.
G-2.1, G-5.1, G-7.1

Seasonal surface and bottom salinities and temperatures in the northern Gulf of Mexico are described. The area
surveyed, from October 1972 to January 1976, was between Mobile Bay, Ala. Gong. 88'00'W), and
Atchalfalaya Bay, La. (long. 91'30'W), from 5 to 50 fm (9 to 91 m).

Thompson, P. A., T. Van Devender and N. J. Sanders, Jr. (eds.). 1988. SEAMAP
Environmental and Biological Atlas of the Gulf of Mexico, 1985. No. 17. Southeast Area
Monitoring Assessment Program (SEAMAP) of the Gulf States Fisheries Commission,
Ocean Springs, Mississippi, 338 p.
F-15.1, F-24.1, G-2.1, G-5.1, G-7.1, G-27

In keeping with the program goal of establishing a coordinated long-term resource database, it was decided to
continue the same types of survey activities conducted in 1982, 1983 and 1984 but with several exceptions.
The offshore plankton survey conducted during April-May 1982, 1983 and 1984 was cancelled due to other
NMFS commitments. A coordinated July-August Squid/butterfish Survey was established for the northern
Gulf of Mexico. The plankton survey for mackeral of August 1984 was not requested in 1985. Finally, a
Shrirnp/Groundfish Survey was added to the survey activities between September and December.

Trask, P. D. 1953. The sediments of the western Gulf of Mexico. Part U - Chemical studies of
sediments of the western Gulf of Mexico. Papers in Physical Oceanography and Meteorology
12(4):47-120.
G-7.1, G-27
380
-------
In 1947, the Woods Hole Oceanographic Institution organized an expedition to investigate the bottom
sediments and oceanography of the northwest Gulf of Mexico. The main objective was to investigate the
environmental conditions of deposition of the sediments in the offshore waters more than 10 fm in depth in
order to throw light on the oceanography of the northwest part of the Gulf of Mexico and to develop ecological
criteria that would benefit geologists in their efforts to determine the condition of deposition of ancient
sediments deposited in the geologic past in adjacent areas.

Treat, S. F., J. L. Simon, R. R. Lewis, HI and R. L. Whitman, Jr. (eds.). 1985. Proceedings of
the Tampa Bay Area Scientific Information Symposium, May 1982. Sea Grant Project No.
IR/82-2. Grant No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65,
Burgess Publishing Co., Minneapolis, Minnesota, (parts in hand)
F-15

Trebatowski, B. 1988. Observations on the 1986-1987 Texas Red Tide (Ptychodiscus brevis).
Rept. No. 88-02, Texas Water Commission, Austin, Texas, 48 p.
G-19 through G-27

From August 1986 through January of 1987, a red tide caused by the unarmored dinoflagellate Ptychodiscus
brevis impacted Texas coastal and Gulf of Mexico waters from Galveston to Port Isabel, Texas and extended
into Mexican waters. The red tide resulted in extensive fish kills, human respiratory and dermal irritation and
closure of shellfish harvesting. This report documents the movement of and area impacted by the red tide,
through plankton and water chemistry samples and boat and aerial surveys. Water chemistry data from samples
taken during the bloom were in agreement with those of other red tide studies but failed to correlate with cell
densities. P. brevis densities ranged to an estimated high of 1.1 million cells per ml (Rockport Harbor).
Vertebrate and invertebrates killed during the event were estimated at greater than 22.2 million.
Trefry, J. EL, S. Metz, R. P. Trocine and T. A. Nelsen.
Mississippi River. Science 230(4724):439-441.
G-9
1985. A decline in lead transport by the
Input of pollutant lead to the Gulf of Mexico from the Mississippi River have declined by about 40 % within
the past decade. This decrease has been determined from annual lead loads of the Mississippi River and from
the lead record in Mississippi Delta sediments. The observed trend is consistent with reduced consumption of
lead in gasoline in the United States. More than 90 % of the riverborne lead is associated with suspended
sediments. Most of this particle-bound lead is deposited within 50 km of the river mouth and is not easily
leached at pH values above 3.

Turner, R. E. and R. L. Allen. 1982a. Bottom water oxygen concentration in die Mississippi
RiverDelta Bight. Contrib. Mar. Sci. 25:161-172.
G-7.1

Bottom-water oxygen concentrations in the Mississippi River Delta Bight are commonly below saturation
values. Hypoxic conditions most often occur in shallow depths, west of the delta during summer. The
hypoxic layer may be only a few meters thick and located on the bottom. An unusual midwater oxygen-
depleted zone was observed south of Mobile Bay. The oxygen-minimum layer from deep water in the Gulf of
Mexico may connect with low oxygen zones at the shelf break. In situ decomposition of material sinking
from the surface layers is the most likely major oxygen consuming process. Lack of vertical mixing due to
stratification probably contributes to the hypoxic summer conditions when oxygen concentration values are
lowest

Turner, R. E. and R. L. Allen. 1982b. Oxygen concentration and plankton respiration in the
Mississippi River Delta Bight. Abstr. for Proceedings of the Third Annual Gulf of Mexico
Information Transfer Meeting, August 24-26, 1982, New Orleans, Louisiana. U.S. Dept. of
381
-------
the Interior, Minerals Management Service, Outer Continental Shelf Office, New Orleans,
Louisiana. .
G-7.1

Bottom oxygen concentrations on seven cruises within the Mississippi River Delta Bight (MRDB) are
observed to be commonly below complete saturation. Hypoxic conditions (less than 3 mg/1) most often occur
in shallow depths, west of the delta, during summer. The hypoxic layer may be only a few meters thick and
located near the bottom. Community plankton respiration rates in the bottom waters of the (MRDB) ranged
from 0.12 to 8 mg oxygen/m3/h in July and in November 1976. Mean values were similar on both cruises,
and between east and west halves of the delta in July. The observed rates are high enough to significantly
influence and possibly dominate factors influencing bottom water oxygen concentration, although benthic
oxygen demand is also a major additional factor.

Turner, R. E. and R. L. Allen. 1982c. Plankton respiration rates in the bottom waters of the
Mississippi River Delta Bight. Contrib. Mar. Sci. 25:173-179.
G-7.1

Community plankton respiration (CPR) rates in the bottom water of the Mississippi River Delta Bight ranged
from 0.12 to 8 mg oxygen/m3/h in July and November 1976. Mean values were similar on both cruises, and
between east and west halves of the delta in July. The observed rates are high enough to influence
significantly and possibly dominate factors influencing oxygen concentrations. In July, CPR was correlated
with variations in chlorophyll a concentrations, thus indicating that phytoplankton sinking is probably a
major factor determining regional variations in CPR.

Turner R. E., R. M. Darnell and J. Bond. 1980. Changes in the submerged macrophytes of
Lake Pontchartrain (Louisiana): 1954-1973. Northeast Gulf Sci. 4(l):44-49.
G-7

The only submerged grasses found in the lake in 1954 were Ruppia maritima and Vallisneria americana. There
was an apparent decline in the abundance of these two species from 1954 to 1973. Much of the loss occurred
in the vicinity of the New Orleans beachfront and near the entrance to the estuary. There is an apparent
decrease in these two species along the shoreline from 1954 to 1973 which amounts to a 25-33 % reduction.
Other species shifts were noted.

Turner, R. E., R. Kaswadji, N. N. Rabalais and D. F. Boesch. 1987. Long-term changes in the
Mississippi River water quality and its relationship to hypoxic continental shelf waters. Pages
261-266 in Estuarine and Coastal Management - Tools of the Trade. Proceedings of the
Tenth National Conference of the Coastal Society, October 12-15, 1986, New Orleans,
Louisiana. The Coastal Society, New Orleans, Louisiana.
G-7.1, G-9

See Turner and Rabalais (1991a) citation for a more thorough treatment of the data.

Turner, R. E. and N. N. Rabalais. 199la. Changes in Mississippi River water quality this
century. Implications for coastal food webs. BioScience 41(3): 140-147.
G-5.1, G-7.1, G-9, G-12

Nitrate concentrations in the largest U.S. watershed, the Mississippi, doubled since the beginning of the
century, primarily since the 1950s. The concentration of silicate has been halved in the same period resulting
in a decrease in the silicate:nitrate atomic ratio from about 4 to 1. Nitrogen loading from the Mississippi and
Atchafalaya Rivers to the continental shelf increased about two times over the past 30 years. The biological
responses in the Mississippi watershed are consistent with the hypothesis that silicon depletion is a
consequence of increased phosphorus supply and results in silicon depletion and a silicon-limited diatom
382
-------
population. These changes in nitrate, phosphate and silicate has almost certainly changed estuarine
phytoplankton communities (especially the diatoms), if not led to increased phytoplankton production. The
effect of the probable decline in diatom abundance, a likely source of the organic matter fueling oxygen
consumption rates in offshore hypoxic zones, may have been compensated for by increased abundances of other
algal types, especially flagellates.

Turner, R. E. and Y. S. Rao. 1990. Relationships between wetland fragmentation and recent
hydrologic changes in a deltaic coast. Estuaries 13(3):272-281.
G-5, G-6, G-9 through G-16

Patterns in coastal wetland loss in the northern Gulf of Mexico were examined using aerial imagery from
1955-1956 and 1978. Canals and their spoil banks are spatially related to wetland-to-water conversion which
is evident up to 2 km away from those manmade features. The indirect impacts of canals and spoil banks vary
regionally, for example, with sediment compaction rates that increase with increasing sediment deposition.
These results are consistent with the hypothesis that canals and spoil banks are a major factor driving wetland
loss rates because they change wetland hydrology.

Turner, R. E., W. W. Schroeder and W. J. Wiseman, Jr. 1987. The role of stratification in the
deoxygenation of Mobile Bay and adjacent shelf bottom waters. Estuaries 10(1): 13-19.
G-2, G-2.1

Oxygen depletion in the shallow bottom waters of Mobile Bay, Alabama, and in adjacent nearshore and
continental shelf waters, is shown to be directly related to the intensity of water column stratification. Low
wind speeds are coincidental with the onset of water column stratification and the occurrence of hypoxic events.
Hourly, daily, and seasonal changes in the relationship between percent oxygen saturation or oxygen
concentration in the bottom waters and surface-bottom density differences indicate that the oxidized materials
are recently formed, and not relic or overwintering carbon sources. The influence of density structure (water
column stratification) in the oxygen-depleted coastal water masses is compared to Mobile Bay.

U.S. Fish and Wildlife Service, (in prep.). An Evaluation of Finfish and Shellfish Resource
Changes in the Perdido Bay Vicinity. Prepared by Division of Ecological Services, Panama
City Field Office. U.S. Dept. of the Interior, Fish and Wildlife Service, Southeast Region,
Atlanta, Georgia, 99 p.
G-l, F-28

The purpose of this report is to identify and document changes in selected finfish and shellfish resources, using
presently available information. No new field or laboratory studies were performed in conjuction with this
report Conclusions based upon the results of 96 statistical analyses performed for this report are included.

U.S. Geological Survey. 1980. Water Resources Data for Louisiana. Vol. III. Coastal
Louisiana. U.S. Geological Survey Water-Data Report No. LA-80-3, Water Year 1980,
U.S. Dept of the Interior, Geological Survey, Baton Rouge, Louisiana, (not in hand)

Van Hoose, M. S. 1988. Biological Assessment of the Perdido Bay System. Report to the
Alabama Department of Economic and Community Affairs. Alabama Marine Resources
Division, Dauphin Island, Alabama.
G-l, F-28

In response to public uneasiness concerning industrial discharge, the Alabama Dept of Economic and
Community Affairs contracted the Alabama Dept of Conservation and Natural Resources to conduct an
extensive sampling survey of the Perdido Bay estuary. Nine trawl samples and six seine stations were taken
monthly throughout the estuary. The survey monitored finfish, commercially important shrimp and crabs, and
hydrographic parameters (dissolved oxygen, temperature, and salinity). This report includes the results of the
survey from April 1987 to March 1988. Samples showed an abundance of fish life throughout Perdido Bay
383
-------
each month. Critically low dissolved oxygen exists in Eleven Mile Creek probably the result of treated paper
mill effluent being dumped there, the condition is confined to the creek as there is no noticeable impact on
finflsh and hydrographic conditions in the upper area of the bay.

Van Sickle, V. R., B. B. Barrett, T. B. Ford and L. J. Gulick. 1976. Barataria Basin: Salinity
Changes and Oyster Distribution. Sea Grant Publ. No LSU-T-76-02. Tech. Bull. No. 20,
Louisiana Wildlife and Fisheries Commission. Center for Wetland Resources, Louisiana
State University, Baton Rouge, Louisiana, 22 p.
G-10

The biology, production, and distribution of the American oyster in the Barataria Basin have been correlated
with environmental factors that determine spatfall, growth, reproduction, and mortality. Mortalities resulting
from predan'on and disease are often associated with increased levels of salinity and temperature. Oysters thrive
in the mixture of fresh and salt water found in many of our estuaries; their distribution is found to be directly
related to salinity. This paper explains the interrelationships that exist between salinity and other
environmental parameters affecting oyster populations.

Van Vleet, E. S. 1985. Hydrocarbons in Tampa Bay - a review. Pages 130-146 ia S. F. Treat,
J. L. Simon, R. R. Lewis, HI and R. L. Whitman, Jr. (eds.), Proceedings of the Tampa Bay
Area Scientific Information Symposium, May 1982. Sea Grant Project No. IR/82-2. Grant
No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65, Burgess Publishing
Co., Minneapolis, Minnesota.
F-15

This paper reviews the extent to which petroleum hydrocarbons and chlorinated hydrocarbons are impacting the
marine environment of Tampa Bay, Florida. The sparse data presently available tend to indicate that most of
the Bay is still much cleaner with respect to petroleum and chlorinated hydrocarbon contamination than many
other anthropogenically impacted estuaries around the U.S. Areas of unusually high concentrations of these
compounds have been reported around the Bay, however.

Waldrop, R. D. 1983. Characteristic seasonal conditions in Barataria Bay waters on the north
shore of Grand Terre Island, Louisiana. Proc. La. Acad. Sci. 46:97-105.
G-10

Cycles of temperature, tidal occurrence, tidal depth, and salinity were analyzed with data obtained from the
Louisiana DepL of Wildlife and Fisheries, Seafood Division. The data were taken from continuous recorders
on the north shore of Grand Terre Island, Louisiana, and were summarized to exemplify seasonal conditions in
adjacent Barataria Bay waters during six week periods in the spring, summer, and fall. Photoperiods were
included to complete each seasonal profile. The limits given for the indicated variables may be useful for
accurate laboratory simulation in studies of seasonal physiology and behavior of aquatic species in lower
Barataria Bay, Louisiana.

Ward, C. H., M. E. Bender and D. J. Reish (eds.). 1979. The Offshore Ecology Investigation.
Effects of oil drilling and production in a coastal environment. Rice Univ. Studies 65:1-589.
G-7.1, G-ll

Ward, Jr., G. H., N. E. Armstrong and the Matagorda Bay Project Teams. 1980. Matagorda
Bay, Texas: Its Hydrography, Ecology and Fishery Resources. Biological Services Program
Publ. FWS/OBS-81/52, U.S. Dept. of the Interior, Fish and Wildlife Service, Washington,
D.C., 230 p.
G-21

The purpose of the report is to present compiled available information on the Matagorda Bay system and to
synthesize the present knowledge of the hydrography and ecology of the system. Chapters cover the
384
-------
hydrography (physiography, circulation, hydrology, sedimentary processes), water quality, inflow and waste
discharges, fish and wildlife resources, species profiles of vegetation, shellfish and finfish, and a preliminary
assessment of perturbations. .

Wardle, W. J., S. M. Ray and A. S. Aldrich. 1975. Pages 257-263 ia V. R. LoCicero (ed.),
Proceedings of the First International Conference on Toxic Dinoflagellate Blooms. The
Massachusetts Science and Technology Foundation, Wakefield, Massachusetts.
G-27

This report documents the occurrence of blooms of the toxic dinoflagellate Gonyaulax monilata in the offshore
coastal waters of Texas at Galveston. Blooms of 1.2 to 1.9 x 10" cells per liter were recorded in August of
1971 and 1972, respectively. Despite extensive monitoring in late July and August of 1973, no G. monilata
were noted in the offshore area of Galveston Island. It was suggested that the absence of the red tides during
these years was related to relatively low salinities and temperatures in the Galveston Bay drainage area during
the month of August.

Weiss, W. R. and T. D. Phillips. 1985. The meroplankton of Tampa Bay. Pages 345-358 in S.
F. Treat, J. L. Simon, R. R. Lewis, HI and R. L. Whitman, Jr. (eds.), Proceedings of the
Tampa Bay Area Scientific Information Symposium, May 1982. Sea Grant Project No.
IR/82-2. Grant No. NA80AA-D-00038. Florida Sea Grant College, Report No. 65,
Burgess Publishing Co., Minneapolis, Minnesota.
F-15

Information on the planktonic, early developmental stages of fish and invertebrates (meroplankton) has been
collected in a variety of studies conducted in the Tampa Bay area over the last 20 years. Early, largely
qualitative investigations documented the importance of the bay system as a spawning site and nursery for
species important to Gulf of Mexico fisheries. More recent studies have provided quantitative estimates of
relative abundance, seasonality, and to some extent, spatial distribution of meroplaktonic organisms in the
estuarine and coastal waters of the area. However, because of "state of the art" limitations to the study of
meroplankton organisms, as well as the restricted areal coverage of the quantitative investigations, additional
data collection is needed before a comprehensive assessment can be made of the relative value of the various
subareas of the bay system as spawning and nursery grounds.

Wells, F. C. and C. R. Demas. 1977. Hydrology and Water Quality of the Atchafalaya River
Basin. Water Resources Technical Report No. 14, Louisiana Dept. of Transportation and
Development, Office of Public Works, Baton Rouge, Louisiana, 53 p.
G-12
Water quality of the Atchafalaya River is controlled by the discharges and chemical quality of the Red, Black
and Mississippi Rivers. The major anion and cation present in the Atchafalaya Basin Floodway are
bicarbonate and calcium, respectively. Chemical quality in the Atchafalaya Basin Floodway is closely related
to the chemical quality of the river at Simmesport. Differences in concentrations in the major ions between
the river at Simmesport and the swamp areas of the floodway are most pronounced during periods of low flow.
Dissolved oxygen concentrations generally exceed 6 mg/1 in the main channel and major distributaries;
however, dissolved oxygen concentrations fall below 4 mg/1 in the floodway during periods of low flow.
Concentrations of nitrogen and phosphorus, heavy metals, and pesticides in the floodway are relatively low.
Nutrient and suspended solid concentrations decrease as distance from the main channel and major distributaries
increases.
Wells, L. and P. N. Froelich. 1982.
Florida (Abstr.). EOS 63(3):56.
F-23
Estuarine nutrient geochemistry in Ochlockonee Bay,
385
-------
Nutrient and related data are being gathered at monthly intervals in the Ochlockonee River and Bay, a simple
"two-end-member," unperturbed estuary in Florida. Samples, taken at intervals of 1-2 ppt over the full salinity
gradient, are analyzed. These data are used in a simple estuarine model to quantify removal and input fluxes.
With the river flow values and seasonal removal patterns, one can then calculate nutrient fluxes to the ocean
from such systems.

Whitledge, T. E. 1985. Nationwide Review of Oxygen Depletion and Eutrophication in Estuarine
and Coastal Waters. Executive Summary. Report to U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, National Ocean Service, Office of Oceanography
and Marine Assessment, Ocean Assessments Division. Brookhaven National Laboratory,
Oceanographic Sciences Division, Upton, New York, 28 p.
F-9 through G-27

This is the executive summary for the Nationwide Review conducted in the northeast, southeast, Florida, Gulf
of Mexico, and west coast. The principal investigator for each area was to assess the health of the estuarine
and coastal environments in the U.S. as indicated by low oxygen concentrations, eutrpphication, or mass
mortalities of organisms. Following the literature compilations, all principal investigators and key personnel
attended a workshop to discuss the results of the respective regional compilations and prepare common
products to represent a nationwide summary. The major product of the workshop was a list of impacts found
in the study representing: 1) priority hypoxia areas, 2) potential hypoxia areas, and 3) areas lacking data but
with potential dissolved oxygen problems.

Whitledge, T. E. 1989. Data Synthesis and Analysis, Nitrogen Processes Study (NIPS), Nutrient
Distributions and Dynamics in Lavaca, San Antonio and Nueces/Corpus Christi Bays in
Relation to Freshwater Inflow. Part I: Results and Discussion. Final Report for Bays and
Estuaries Program, Environmental Systems Section, Texas Water Development Board. Tech.
Rept. No. TR/89-007, University of Texas Marine Science Institute, Port Aransas, Texas.
(whole document not in hand)
G-22

Whitledge, T. E. and W. M. Pulich, Jr. (conveners). 1991. Report, Red Tide Symposium and
Workshop, 15-16 July 1991. Marine Science Institute, The University of Texas, Port,
Aransas, Texas, 44 p.
G-25, G-26

The "brown tide" bloom of an aberrant Chrysophyte sp. phytoplankter occurred for more than 18 months and
extended into both upper and lower Laguna Madre, Texas. Great concern for the Laguna Madre ecosystem was
shown during the brown tide event by local, state and regional groups, but little previous knowledge was
available about this unusual phytoplankton bloom. This report includes the agenda, abstracts of presentations,
and summary of findings by the workshop participants convened to discuss the data and results on brown tide
and other unusual phytoplankton blooms.

Williams, C. D., D. M. Nelson, L. C. Clements, M. E. Monaco, S. L. Stone, L. R. Settle, C.
lancu and E. A. Irlandi. 1990. Distribution and Abundance of Fishes and Invertebrates in
Eastern Gulf of Mexico Estuaries. NOAA's Estuarine Living Marine Resources Project
Report No. 6, National Oceanic and Atmospheric Administration, Strategic Assessment
Branch, National Ocean Survey, Rockville, Maryland, 105 p.
F-9, F-ll, F-12, F-13, F-15, F-19, F-22, F-24, F-25, F-26, F-27, G-l, G-2

This report presents information on the spatial and temporal distribution, relative abundance, and life history
characteristics of 36 fish and invertebrate species in 13 estuaries along the Eastern Gulf of Mexico coast Its
purpose is to disseminate data developed in NOAA's Estuarine Living Marine Resources (ELMR) project. The
objective of ELMR is to develop a consistent data base on the distribution and abundance of selected fishes and
invertebrates in the Nation's estuaries.
386
-------
Williams, H. B. 1956. A Chemical and Bacteriological Survey of the Waters and Muds in a
Western Portion of Lafourche Parish, Louisiana. C.S.I. Contribution No. 56-5, Coastal
Studies Institute, Louisiana State University, Baton Rouge, Louisiana.
G-10

This summary report presents chemical and bacteriological data that resulted from five field trips into the Grand
Bayou Blue section of Lafourche Parish, Louisiana, made from December 1954 to November 1955 and the
correlation and interpretation of those data. The following experimental determinations were made; pH,
temperature, specific gravity, specific conductance, absolute turbidity, differential refractive index, total solids
before and after ignition, chlorinity, dissolved oxygen, biological oxygen demand, sulfate, soluble and
oxidizable forms of sulfur, type of bacteria, bacteriological count, and sulfur content of the muds.

Williams, J. and R. M. Ingle. 1972. Ecological notes on Gonyaulax monilata (Dinophyceae)
bloom along the west coast of Florida, Florida Marine Research Laboratory, Leaflet Series:
Volume I - Phytoplankton, Part 1 (Dinoflagellates) No. 5. Florida Dept. of Natural
Resources, Marine Research Laboratory, St. Petersburg, Florida, 12 p.
F-12, F-13, F-14, F-15, F-15.1

The study documents the first record of Gonyaulax monilata along Florida's west coast, along with associated
fish kills. The bloom was concentrated in early August 1966 in estuaries and offshore waters from Estero
Island to Doctors Pass. Later in August and September, this species was distributed along the coast from
Anna Maria Island to Cape Roman. Following the G. monilata outbreak, a Gymnodinium breve bloom
occurred in late October offshore Tampa Bay.

Wilson, W. B. and S. M. Ray. 1956. The occurrence of Gymnodinium brevis in the western
Gulf of Mexico. Ecology 37(2):388.
G-27

During 1953-55, seawater samples were collected at Galveston, Texas and along the Gulf coast between
Galveston and Florida, but no G. brevis were observed. In September 1955 a fish kill near Port Isabel, Texas
was associated with a bloom of G. brevis. The bloom extended down the coastline of the Mexican state of
Tamaulipas for approximately 200 km.

Windham, C. M., T. L. Bradley, M. H. Schurtz and P. Romanowsky. 1980. Lake Pontchartrain
Crab Kill. Louisiana Department of Wildlife and Fisheries, and Louisiana Department of
Natural Resources, Baton Rouge, Louisiana, 10 p.
G-7

Several reports were received by the Louisiana Dept. of Wildlife and Fisheries during the month of August,
1980 concerning dead crabs in Lake Pontchartrain. A preliminary survey on August 20 indicated that an
oxygen problem existed. A more detailed survey was conducted on August 28 and 29. Twenty-six stations
were sampled during this 2-d period. The data indicates that a dense layer of high salinity anoxic water was
present in the Lake during August 1980. Communication with various crab fishermen indicated that this area
of poor water quality would move depending oh wind and tide. Thus, crabs could enter traps in areas of good
water quality and could not leave the area when water quality conditions became poor. It is probable that this
phenomena was the cause of the crab kill. Subsequent samples taken in September have shown that the water
column is now well mixed and the deoxygenated layer has dispersed.

Windsor, Jr., J. G. 1985. Nationwide Review of Oxygen Depletion and Eutrophication in
Estuarine and Coastal Waters: Florida Region. Project Completion Report to Brookhaven
National Laboratory, Upton, New York and U.S. Dept. of Commerce, National Oceanic and
Atmospheric Administration, National Ocean Service, Office of Oceanography and Marine
Assessment, Ocean Assessment Division, Rockville, Maryland, 177 p.
F-9 through F-28
387
-------
The coastal regions of Florida have been most impacted in recent years by rapid population growth and its
associated burdens. The most significant burden on estuaries and coastal waters of Florida appears to have been
the discharge of untreated or improperly treated municipal sewage. Other impacts are from industrial processes
related to wood, paper and pulping, agriculture, fertilizer mining and processing, and commercial shipping.
Areas with sufficient data to suggest a definite problem with oxygen depletion were listed as Perdido Bay,
Tampa/Hillsborough Bay, and Biscayne Bay. An area with marginal or deteriorating water quality with respect
to oxygen depletion was listed as Pensacola and Escambia Bays. Two areas were placed on the list of
suspicious areas which are either lacking data or have insufficient data to suggest an oxygen problem: Indian
River, Banana River, Mosquito Lagoon systems and the Florida Keys.

Wiseman, Jr., W. J. 1982. Physical processes which may impact the oxygen depletion zone over
the Louisiana shelf. Abstr. for Proceedings of the Third Annual Gulf of Mexico Information
Transfer Meeting, August 24-26, 1982, New Orleans, Louisiana. U.S. Dept. of the Interior,
Minerals Management Service, Outer Continental Shelf Office, New Orleans, Louisiana.
G-7.1

To date, there is no clearly demonstrated relationship between physical processes on the Louisiana shelf and the
oxygen depletion zone found in the same region. One can, though, speculate about quite plausible
interactions. Any process which provides a source of carbon for the inner shelf waters, or which isolates these
waters from processes which renew the dissolved oxygen concentration, will contribute to an oxygen depletion
zone. Three such mechanisms have been observed in the Louisiana Bight, the area immediately west of the
Mississippi River Delta: 1) The effluent from the Mississippi River flowing westward over the mid and inner
shelf; 2) the intrusion of high salinity water along the bottom from farther offshore; 3) a well-mixed bottom
layer often found throughout the Louisiana Bight.

Wiseman, Jr., W. J., W. W. Schroeder and S. P. Dinnel. 1988. Shelf-estuarine water exchange
between the Gulf of Mexico and Mobile Bay, Alabama. Am. Fish. Soc. Symp. 3:1-8.
G-2, G-2.1

One month of current meter data from Main Pass, which connects lower Mobile Bay with the Gulf of Mexico,
demonstrated shelf-estuarine exchange driven by north-south wind stress at periodicities longer than the tide.
Riverine discharge fluctuations may modulate the gravitational circulation over time scales shorter than
seasons. Tidal diffusion, long-period advection, and the mean circulation are of equal importance to dispersion
of water through Main Pass.

Wiseman, Jr., W. J. and E. M. Swenson. 1987. Long-term salinity trends in Louisiana estuaries.
• Pages 101-121 in R. E. Turner and D. R. Cahoon (eds.), Causes of Wetland Loss in the
Coastal Central Gulf of Mexico. Vol. II: Technical Narrative. OCS Study MMS 87-0120,
U.S. DepL of the Interior, Minerals Management Service, Gulf of Mexico OCS Regional
Office, New Orleans, Louisiana.
G-7, G-8, G-9, G-10, G-l 1, G-12, G-13, G-14, G-15

The goal of this study was to analyze existing records of salinity from the Louisiana coastal zone to determine
whether or not they support the notion that significant long-term trends in the estuarine salinity regime have
occurred. These data were analyzed to determine the long-term (30 to 40 years), seasonally adjusted trends.
The authors were primarily concerned with the salinity regime as it relates to both natural and man-induced
factors. Thus, the task had two major objectives; to determine the secular trends (if any) in the salinity regime
and to identify the factors that may be controlling these changes. They were particularly interested to see if the
existing salinity records indicated the occurrence of changes of sufficient magnitude to impact the vegetation.
Wiseman, Jr., W. J., E. M. Swenson and J. Power.
Estuaries 13(3):265-271.
G-7, G-8 through G-15
1990. Salinity trends in Louisiana estuaries.
388
-------
If long-term trends in the character of the estuarine salinity field are contributing to land-loss in coastal
Louisiana, then evidence of the presence of these trends may exist in historical salinity records. Nonparametric
tests for the presence of a trend in the time series of various salinity statistics were performed. The results
appear to be strongly influenced by climatological variations of decadal scale. Statistically significant trends
.were found at many stations. Both increasing and decreasing trends occurred with no apparent underlying
spatial pattern. The observed changes during the time covered by the available records were generally too small
to be lethal to the dominant marsh plants.

Wiseman, Jr., W. L, R. E. Turner,,F. J. Kelly, L. J. Rouse, Jr. and R. F. Shaw. 1986.
Analysis of biological and chemical associations near a turbid coastal front during winter
1982. Contrib. Mar. Sci. 29:141-151.
G-7.1

An intense front separates the waters of the nearshore region from those of the Louisiana inner shelf.
Horizontal salinity gradients often exceed 0.2S ppt km'1. Data from hydrographic cruises and moored
instruments are used to characterize the variability in and around the front during winter/spring, when the
structure is most changeable. A modified empirical orthogonal function analysis explains 88 % of the data
variability with three basic patterns: 1) high nitrate and silicate concentrations are strongly associated with the
low-salinity nearshore waters; 2) an association between high chlorophyll a concentration and low temperature
reflects, we believe, both parameters' relationship with turbid shallow depths rather than a direct interaction; 3)
coincidental high ammonia and zooplankton concentrations are, presumably, due to excretion. In contrast to
oceanic fronts, these shelf fronts do not lead to regional boundary zones of increased biologic activity.

Witzig, A. S. and J. W. Day, Jr. 1983. A Multivariate Approach to the Investigation of Nutrient
Interactions in the Barataria Basin, Louisiana. Final Report to the Louisiana Water Resources
Research Institute. Project - A-047-LA, Coastal Ecology Laboratory, Center for Wetland
Resources, Louisiana State University, Baton Rouge, Louisiana, 36 p.
G-10

A study of nutrient chemistry in the Barataria basin was designed to illustrate seasonal and spatial variability
along a fresh to saltwater gradient and to assess the impact of human induced alterations on the water chemistry
of the system. These impacts include high nutrient loads in runoff from agricultural and urban development
and an extensive network of canals dredged through the wetlands. Twenty-three sampling stations were
sampled quarterly in 1975-1977 along a 120-km transect to reflect the high diversity of water types within the
basin. Parameters measured included total and dissolved organic nitrogen, total phosphorus, nitrate-nitrite
nitrogen, ammonium nitrogen, chlorophyll a, secchi depth, salinity, conductivity, dissolved oxygen and
temperature. Multivariate statistical techniques were used to provide an holistic approach to the interpretation
of chemical data. The analyses suggested that the variation in water chemistry between the upper and lower
basin would be much less with fewer human impacts.

Wolfe, S. H. (ed.) 1990. An Ecological Characterization of the Florida Springs coast:
Pithlachascotee to Waccasassa Rivers. USFWS Biological Report No. 90(21), U.S. Dept. of
the Interior, Fish and Wildlife Service, Washington, D.C. and Minerals Management Service,
New Orleans, Louisiana, 323 p.

Wolfe, S. H. and R. D. Drew (eds.) 1990. An Ecological Characterization of ithe Tampa Bay
Watershed. USFWS Biological Report No. 90(20), U.S. Dept. of the Interior, Fish and
Wildlife Serivce, Washington, D.C. and Minerals Management Service, New Orleans,
Louisiana, 334 p.
F-15
389
-------
Wolfe S H J A Reidenauer and D. B. Means. 1988. An Ecological Characterization of the
Florida'Panhandle. FWS Biological Report No. 88(12), OCS Study MMS 88-0063, U.S.
Dept. of the Interior, Fish and Wildlife Service, Washington, D.C. and Minerals Management
Service, New Orleans, Louisiana, 277 p.
F-23, F-24, F-25, F-26, F-27

The Florida Panhandle is one of the most rapidly developing regions in the entire State. Many Panhandle
commercial interests, especially fishing and tourism, are highly dependent upon the maintenance of relatively
unaltered habitats. Critical decisions on the preservation or economic development of particular areas are often
made without knowledge of the composition, dynamics, and sensitivity of the local habitats and the associated
flora and fauna to perturbations. Additionally, higher level interactions between systems and habitats are often
overlooked. This report is an extensive review and synthesis of available literature on the local physical
setting and ecology and a discussion of important impacts on the habitats within the Panhandle region.
Included are projections of possible future impacts and identification of areas that need further research before
they are permanently altered.

Wright L D. 1970. Circulation, Effluent Diffusion, and Sediment Transport, Mouth of South
Pass, Mississippi River Delta. Technical Report No. 84, Coastal Studies Institute, Louisiana
State University, Baton Rouge, Louisiana, 56 p.
G-9

A study was conducted at the mouth of South Pass, Mississippi River, to ascertain the influence exerted by
interaction between effluent and ambient fluids; tides; waves; winds; bottom topography and channel mouth
geometry; regional coastal currents; horizontal and vertical density gradients; and hydrologic regime of the
Mississippi River. It is concluded that fluid and sediment dissemination at the mouth of South Pass is
associated with an intricately interacting multipurpose system. Patterns cannot be adequately explained in
terms of any single process such as turbulent jet diffusion.

Zein-Eldin, Z. P. and M. L. Renaud. 1986. Inshore environmental effects on brown shrimp,
Penaeus aztecus, and the white shrimp, P. setiferus, populations in coastal waters,
particularly of Texas. Mar. Fish. Rev. 48(3):9-19.
G-27

This discussion compares and contrasts responses of the two species to single factors and their interaction,
giving only limited literature citations. Implications for the two species are then explored. The purposes of
this paper are to 1) provide, in an easily accessed tabular format, representative information and literature
sources relating environmental factors to several inshore life stages of brown and white shrimp and 2) bring
attention to those factors, their interactions, and life stages for which information is lacking.

Zieman, J. C. and R. T. Zieman. 1989. The Ecology of the Seagrass Meadows of the West Coast
of Florida: A Community Profile. Biological Report No. 85(7.25), U.S. Dept. of the
Interior, Fish and Wildlife Service, Research and Development, Washington, D.C., 155 p.
F-15

The greatest losses of seagrass habitat are caused by the effects of physical damage from dredging and the
chronic stresses placed on the plants by suspended sediments and eutrophic algal growth, manifested in the
form of increased turbidity and resultant light reduction.

Zimmerman, M. S. and R. J. Livingston. 1979. Dominance and distribution of benthic
macrophyte assemblages in a north Florida estuary (Apalachee Bay, Florida). Bull. Mar. Sci.
29(1):27-40.
F-22
390
-------
A comparative analysis was made concerning the distribution of benthic macrophyte assemblages in shallow
portions of Apalachee Bay. This included a comparison of areas affected by bleached kraft mill effluents with
appropriate uncontaminated control stations. Meter-square samples of benthic macrophytes were collected
monthly in both areas. Relative dominance was generally high in the unpolluted areas. Four species of red
algae were found at all stations. It was postulated that selective removal of dominant species by bleached kraft
mill effluents allowed recruitment of various "rare" species in areas of chronic impact, thus contributing to
anomalous patterns of community structure when compared to published data from other pollution-stressed
benthic systems.

Zimmerman, M. S. and R. J. Livingston. 1976. Effects of kraft-mill effluents on benthic
macrophyte assemblages in a shallow-bay system (Apalachee Bay, North Florida, USA).
Mar. Biol. 34:297-312.
F-22

A 14-mo study was carried out to determine the impact of kraft-mill effluents on the offshore benthic
macrophyte distribution in a shallow north Florida bay. A polluted river drainage system was compared to an
adjoining (unpolluted) one. The affected area was characterized by elevated levels of color and turbidity. Near-
shore coastal systems in Apalachee Bay were affected by gradients in water quality in addition to natural
(seasonal) fluctuations in key physical and chemical parameters.

Zotter, J. 1979. Exuviella baltica: A bloom organism of the Galveston Bay system. Pages 195-
198 in D. L. Taylor and H. H. Seliger (eds.), Toxic Dinoflagellate Blooms. Proceedings of
the Second International Conference on Toxic Dinoflagellate Blooms, October 31 - November
5, 1978, Key Biscayne, Florida. Developments in Marine Biology - Vol. 1, Elsevier North
Holland, New York.
G-17

This report documents the occurrence of high cell concentrations of the dinoflagellate Exuviella baltica
Lohmann in three different environmental areas of the Galveston Bay System. Data were recorded once every
three weeks from 18 December 1976 through 5 March 1977 during a 12-mo study of live nannoplankton.
Concurrent blooms of Exuviella baltica (to 2.8 X 105 cells/ml), the green alga Chlorella sp. (to 2.0 X 1&
cells/ml), and the blue-green alga Schizothrix calcicola (to 5.2 X 104 cells/ml) were recorded in each of three
different environmental areas in Galveston Bay and adjacent waters during the winter months. Total cell
concentrations of nannoplankton during the apparently non-toxic blooms were from 6.7 x 10^ cells per ml to
4.2 x 105 cells per ml.
391
-------
BIBLIOGRAPHY II.

GENERAL REFERENCES

Aber, J. D., P. Nadelhoffer, P. Streudler and J. M. Malillo. 1989. Nitrogen saturation in
northern forest ecosystems. BioScience 39:378-386.

Aldrich D V. and W. B. Wilson. 1960. The effect of salinity on growth of Gymnodiniwn breve
Davis. Biol. Bull. 119(l):57-64.

Allen R L 1975. Aquatic Primary Productivity in Various Marsh Environments in Louisiana.
M.S. Thesis, Louisiana State University, Baton Rouge, Louisiana, 49 p. (not in hand)

Alpine A E. and J. E. Cloern. 1988. Phytoplankton growth rates in a light-limited environment,
San Francisco Bay. Mar. Ecol. Prog. Ser. 44(2): 167-173.

Anderson, G.F. 1986. Silica, diatoms and a freshwater productivity maximum in Atlantic coastal
plain estuaries, Chesapeake Bay. Estuarine Coastal Shelf Sci. 22(2): 183- iy/.

Andersson, L. and L. Rydberg. 1988. Trends in nutrient and oxygen conditions_within the
Kattegat: Effects of local nutrient supply. Estuarine Coastal Shelf Sci. 26(5).:>:>yo /y.

Arntz WE 1981. Zonation and dynamics of macrobenthos biomass in an area stressed by
oxygen deficiency. Pages 215-225 in G. W. Barrett and R. Rosenberg (eds.), Stress Effects
on Natural Ecosystems. Proceedings of a Special Symposium at the 2nd International
Congress of Ecology, September 10-16, 1978, Jerusalem, Israel. Environmental
Monographs and Symposia Series, John Wiley & Sons, Chichester, England.

Asmus R. 1986. Nutrient flux in short-term enclosures of intertidal sand communities. Ophelia
26:1-18.

Atkinson, M. J., T. Berman, B. R, Allanson and J. Imberger. 1987 Fine-scale oxygen
variability in a stratified estuary: Patchiness in aquatic environments. Mar. Ecol. Prog. ber.
Augusti, S., C. M. Duarte and D. E. Canfield, Jr. 1990. Phytoplankton abundance in Florida
lakes- Evidence for the frequent lack of nutrient limitation. Limnol. Oceanogr. 35(l):18l-
188.

Baden, S. P., L.-O. Loo, L. Pihl and R. Rosenberg. 1990. Effects of eutrophication on benthic
communities including fish: Swedish west coast Ambio 19(3): 11 3- 122.

Baeteman M. and W. Vyncke. 1989. Nutrients in Belgian continental shelf waters: A ten years'
survey (1978-1987). In Cooperative Research Report. International Council for the
Exploration of the Sea (ICES), Copenhagen, Denmark, 1.0 p. (not in hand)

Baillie P W 1987. Diatom size distributions and community stratification in estuarine intertidal
sediments. Estuarine Coastal Shelf Sci. 25(2): 193-209.

Baker, W. 1986. Forms of phosphorus and its accumulation in coastal sediments of Kieler
Bucht. Ophelia 26: 19-35.

Barinaga,M. 1990. Fish, money, and science in Puget Sound. Science 247(4943):631.
392
-------
Barnes, C. A. and E. E. Collias. 1958. Some considerations of oxygen utilization rates in Puget
Sound. J. Mar. Res. 17:68-80.

Bauerfeind, S. 1985. Degradation of phytoplankton detritus by bacteria: Estimation of bacterial
consumption and respiration in an oxygen chamber. Mar. Ecol. Prog. Ser. 21(l/2):27-36.

Bender, M. L. and K. D. Grande. 1987. Production, respiration, and the isotope geochemistry of
O2 in the upper water column. Global Biochem. Cycles l(l):49-59.

Bennekom, A. J. van, W. W. C. Gieskes and S. B. Tijssen. 1975. Eutrophication of Dutch
coastal waters. Proc. R. Soc. Lond. B. 189:359-374.

Bennekom, A. J. van, G. W. Gerger, W. Helder and R. T. P. de Vries. 1978. Nutrient
distribution in the Zaire estuary and river plume. Neth. J. Sea Res. 12(3/4):296-323.

Benovid, A., D. Justic and A. Bender. 1987. Enigmatic changes in the hydromedusan fauna of
the northern Adriatic Sea. Nature 326(61 13):597-600.

Berner, R. A. 1978. Sulfate reduction and the rate of deposition of marine sediments. Earth and
Planetary Science Letters 37:492-498.

Berounsky, V. M. and S. W. Nixon. 1990. Temperature and the annual cycle of nitrification in
waters of Narragansett Bay. Limnol. Oceanogr. 35(7):1610-1617.

Beukema, J. J. and G. C. Cadde. 1986. Zoobenthos responses to eutrophication of the Dutch
WaddenSea. Ophelia 26:55-64.

Billen, G., M. Somville, E. de Becker and P. Servais. 1985. A nitrogen budget of the Scheldt
hydrographical basin. Neth. J. Sea Res. 19(3/4):223-230.

Bird, D. F. and J. Kalff. 1984. Empirical relationships between bacterial abundance and
chlorophyll concentration in fresh and marine waters. Can. J. Fish. Aquat. Sci. 41(7):1015-
Blackburn, T. H. 1986. Nitrogen cycle in marine sediments. Ophelia 26:65-76.

Blair, N. E., C. S. Martens and D. J. Des Marais. 1987. Natural abundances of carbon isotopes
in acetate from a coastal marine sediment. Science 236(4797):66-68.

Bodungen, B. v. 1986. Annual cycles of nutrients in a shallow inshore area, Kiel Bight -
Variability and trends. Ophelia 26:9 1-107.

Boesch, D. F., L. C. Schaffner, M. A. Bowen, J. Van Montfrans and R. C. Swartz. (in press).
Benthos community dynamics following a plankton bloom and hypoxia in the New York
Bight. Estuarine Coastal Shelf Sci.

Bogardi, I. and R. D. Kuzelka (eds.). 1991. Nitrate Contamination. Exposure, Consequence and
Control. NATO ASI Series G: Ecological Sciences, Vol. 30. Springer- Verlag, New York,
520 p.

Borman, F. H. 1982. The effects of air pollution on the New England landscape. Ambio 1 1 :338-
346.
393
-------
Boynton, W. R. and W. M. Kemp. 1985. Nutrient regeneration and oxygen consumption by
sediments along an estuarine salinity gradient. Mar. Ecol. Prog. ber. 23(l):4DOD.

Bradley, P. M. and J. T. Morris. 1990. Physical characteristics of salt marsh sediments:
Ecological implications. Mar. Ecol. Prog. Sen 61(3):245-252.

Bradley, R. S., H. F. Diaz, J. K. Eischeid, P. D. Jones, P. M .Kelly and CM. 9°^ess. 1987.
Precipitation fluctuations over Northern Hemisphere land areas since the mid-19th century.
Science 237(4811):171-175.

Brand, L. E., M. D. Gottfried, C. C. Baylon and N. S Romer.1991 Spatial and temporal
distribution of phytoplankton in Biscayne Bay, Florida. Bull. Mar. Sci. 49(l-2):599-613.

Breitburg D. L. 1990. Near-shore hypoxia in the Chesapeake Bay: Patterns and relationships
among physical factors. Estuarine Coastal Shelf Sci. 30(6):593-609.

Brezonik, P. L. 1972. Nitrogen: Sources and transformations in natural waters. Pages 1-50 in
H. E. Allen and J. R. Krlmer (eds.), Nutrients in Natural Waters. John Wiley & Sons, New
York.

Brinkhurst R. O., K. L. Denman and H. J. Freeland. 1989. Statistical assessment of toe impact
of low oxygen conditions on benthic macrofauna. Meeting on Modern and Ancient
Continental Shelf Anoxia, London, May 17-19, 1989. The Geological Society of London
(abstr.), 1 p-

Brush, G. S. 1984. Stratigraphic evidence of eutrophication in an estuary. Water Resour. Res.
20(5):531-541.

Brzezinsld, M. A., R. J. Olson and S. W. Chisholm. 1990. Silicon availability and cell-cycle
progression in marine diatoms. Mar. Ecol. Prog. Ser. 67(l):83-96.

Bulger, A. J., B. P. Hayden, M. G. McCormick-Ray, M. E. Monaco and DM. Nelson 1990.
A Proposed Estuarine Classification: Analysis of Species Salinity Ranges. NOAA s
Estuarine Living Marine Resources Project No. 5, U.S. Dept. of Commerce, National
Oceanic and Atmospheric Administration, Strategic Assessment Branch, National Ocean
Service, Rockville, Maryland, 28 p.

Burd B. J. and R. O. Brinkhurst. 1984. The distribution of the galatheid crab Munida
auadrispina (Benedict 1902) in relation to oxygen concentrations in British Columbia fjords.
J. Exp. Mar. Biol. Ecol. 81(1):1-20.

Burd, B. J. and R. O. Brinkhurst. 1985. The effect of oxygen depletion on the galatheid craj>
Munida auadrispina in Saanich Inlet, British Columbia. Pages 435-443 m J- S. Gray and M.
E. Christiansen (eds.), Marine Biology of Polar Regions and Effects of Stress on Marine
Organisms. John Wiley & Sons, Chichester, England.

Burton J D. (ed.). 1988. River Inputs to Ocean Systems: Status and Recommendations for
Research. Unesco Technical Papers in Marine Science No. 55, SCOR Working Group 46^
Unesco, Paris, 24 p.

Butman C A. 1986. Sediment trap biases in turbulent flows: Results from a laboratory flume
study. J. Mar. Res. 44(3):645-693.
394
-------
Cade"e, G. C. 1975. Primary Production off the Guyana coast. Neth. J. Sea Res. 9(1):128-143.

Cade"e, G. C. 1978. Primary production and chlorophyll in the Zaire River, estuary and plume.
Neth. J. Sea Res. 12:368-381.

Cade"e, G. C. 1984. Paniculate and dissolved organic carbon and chlorophyll a in the Zaire River,
estuary and plume. Ophelia 17(2-4):426-440.

Cade"e, G. C. 1990a. Increase of Phaeocystis blooms in the westernmost inlet of the Wadden
Sea, the Marsdiep, since 1973. Pages 105-112 in. C. Lancelot, G. Billen and H. Earth
(eds.), Eutrpphication and algal blooms in North Sea coastal zones, the Baltic and adjacent
areas: Prediction and assessment of preventive actions. Water Pollution Research Report
Vol. 12, CEC, Brussels.

Cade"e, G. C. 1990b. Trends in North Sea phytoplankton. Lutra 33:187-189.

Cade"e, G. C. 1990c. Increased bloom. Nature 346(6283):418.

Cade"e, G. C. and J. Hegeman. 1986. Seasonal and annual variation in Phaeocystis pouchetii
(Haptophyceae) in the westernmost inlet of the Wadden Sea during the 1973 to 1985 period
Neth. J. Sea Res. 20(l):29-36.

Cade"e, G. C. and J. Hegeman. 1991. Historical phytoplankton data of the Marsdiep. Hydrobiol
Bull. 24(2): 111-118.

Callender, E. and D. E. Hammond. 1982. Nutrient exchange across the sediment-water interface
in the Potomac River estuary. Estuarine Coastal Shelf Sci. 15(4):395-413.

Cambridge, M. L., A. W. Chiffings, C. Britton and L. M., A. J. Moore. 1986. The loss of
seagrass in Cockburn Sound, Western Australia, n. Possible causes of seagrass decline Aa
Bot. 24(3):269-285. "

Cambridge, M. L. and A. J. McComb. 1984. The loss of seagrasses in Cockburn Sound,
Western Australia. I. The time course and magnitude of seagrass declines in relation to
industrial development. Aq. Bot. 20(3-4):229-243.

Canfield, D. E., Jr. and D. J. Des Marais. 1991. Aerobic sulfate reduction in rnicrobial mats
Science 251(5000):1471-1473.

Carpenter, E. J. and K. Romans. 1991. Major role of the cyanobacterium Trichodesmium in
nutrient cycling in the North Atlantic ocean. Science 254:1356-1358.

Carpenter, J. H., D. W. Pritchard and R. C. Whaley. 1969. Observations of eutrophication and
nutrient cycles in some coastal plain estuaries. Pages 210-221 in Eutrophication: Causes,
Consequences, Correctives. Proceedings of a Symposium, 1967. National Academy of
Sciences, Washington, D.C.

Casey, R., C. Hueni and A. Leavesley. 1981. Brizalina lowmani, a meroplanktonic
foraminiferan useful as an indicator of shelfal circulation and eutrophication (with comments
on biostratigraphy and evolution). Trans. Gulf Coast Assoc. Geol. Soc. 31:249-255.

Cavanaugh, T. M. and W. J. Mitsch. 1989. Water quality trends of the upper Ohio River from
1977 to 1987. Ohio J. Sci. 89(5):153-163.
395
-------
Cederwall H and R. Elmgren. 1980. Biomass increases of benthic macrofauna demonstrates
eutrophication of the Baltic Sea. Ophelia, Suppl. 1:287-304.
CederwaU, H. and R. Elmgren. 1990. Biological effects of eutrophication in the Baltic Sea,
particularly the coastal zone. Ambio 19(3): 109-112.
Charles D. R and J. P. Smol. 1990. The PIRLA H Project: Regional assessment of lake
acidification trends. Verh. Internal. Verein Limnol. 24:474-480.
Cherfas,! 1990. The fringe of the ocean -under siege from land. Science 248(4952): 163-165.
Chittenden W. H. and S. A. Freudberg. 1987. A Dissolved Oxygen Study of the Upper
Potomac Estuary. Executive Summary. Final Report. Dept. of Environmental Programs,
Metropolitan Washington Council of Governments, Washington, D.C., 21 p.
Christensen, P. B., L. P. Nielsen, J. Sorensen and N. P. Revsbech. 1990. Denitriiication in
nitrate-rich streams: Diurnal and seasonal variation related to benthic oxygen metabolism.
Limnol. Oceanogr. 35(3):640-651.
Christian R R J. N. Boyer and D. W. Stanley. 1991. Multi-year distribution patterns of
nuMents whhin the Neuse River Estuary, North Carolina. Mar. Ecol. Prog. Ser. 71(3):259-
274.
Toale K H 1990 Labyrinth of doom: A device to minimize the "swimmer" component in
\M*WUJ.W) A»t **• *-" «^ v« ———^ ^^ C/£.\ 1 O*7£. 1 *2Q 1
sediment trap collections. Limnol. Oceanogr. 35(6):137o-lJ5i.
Cochlan, W. P. 1986. Seasonal study of uptake and regeneration of nitrogen on the Scotian
Shek Continental Shelf Res. 5(5):555-577.
Cochlan, W. P., P. J. Harrison, P. J. Clifford and K. Yin. 1990. Observations on double
chlorophyll maxima in the vicinity of the Fraser River plume, Strait of Georgia, British
Columbia. J. Exp. Mar. Biol. Ecol. 143(1/2): 139-146.
Codispoti, L. A., G. E. Friederich, T. T. Packard, H. E. Glover, P. J. Kelly, R. W. Spinrad R.
T Barber, J. W. Elkins, B. B. Ward, F. Lipschultz and N. Lostaunau. 1986. High nitrite
levels off northern Peru: A signal of instability in the marine denitnfication rate, bcience
233(4769):1200-1202.
Conley, D. J. and S. S. Kilham. 1989. Differences in silica content between marine and
freshwater diatoms. Limnol. Oceanogr. 34(1):205-213.
Corredor, J. E. and J. M. Morell. 1989. Assessment of inorganici nitrogen^fluxes across the
sediment-water interface in a tropical lagoon. Estuanne Coastal Shelf Sci. 28(3):33y-34D.
Cooper S R. and G. S. Brush. 1991. Long-term history of Chesapeake Bay anoxia. Science
254:992-996.
Correll, D. L. 1981. Nutrient mass balances for the watershed, headwaters, intertidal zone, and
basin of the Rhode River estuary. Limnol. Oceanogr. 26:1142-1149.
Correll, D. L. and D. Ford. 1982. Comparison of precipitation and land runoff as sources of
estuarine nitrogen. Estuarine Coastal Shelf Sci. 15:45-56.
396
-------
Cosper, E. M., V. M. Bricelj and E. J. Carpenter (eds.). 1989. Novel Phytoplankton Blooms.
Causes and Impacts of Recurrent Brown Tides and Other Unusual Blooms. Proceedings of a
Symposium, October 27-28, 1988, Stony Brook, New York. Coastal and Estuarine Studies
No. 35, Springer-Verlag, New York, 799 p.

Cosper, E. M., W. C. Dennison, E. J. Carpenter, V. M. Bricelj, J. G. Mitchell, S. H. Kuenstner,
D. Colflesh and M. Dewey. 1987. Recurrent and persistent brown tide blooms perturb
coastal marine ecosystem. Estuaries 10(4):284-290.

Costner, P. and J. Thornton. 1989. We All Live Downstream: The Mississippi River and the
National Toxics Crisis. Greenpeace USA, Washington, D.C., 181 p.

Coutant, C. C. and D. L. Benson. 1990. Summer habitat suitability for striped bass in
Chesapeake Bay: Reflections on a population decline. Trans. Am. Fish. Soc. 119(4):757-
778.

Craig, H. and T. Hayward. 1987. Oxygen supersaturation in the ocean: Biological versus
physical contributions. Science 235(4785): 199-202.

Crema, R., A. Castelli and D. Prevedelli. 1991. Long term eutrophication effects on macrofaunal
communities in northern Adriatic Sea. Mar. PolluL Bull. 22(10):503-508.

Csanady, G. T. 1990. Physical basis of coastal productivity. The SEEP and MASAR
experiments. EOS 71(36):1060-1061/1064-1065.

Culliton, T. J., M. A. Warren, T. R. Goodspeed, D. G. Remer, C. M. Blackwell and J. J.
McDonough, HI. 1990. 50 Years of Population Change along the Nation's Coasts, 1960-
2010. Strategic Assessments Branch, Ocean Assessments Division, Office of Oceanography
and Marine Assessment, National Ocean Service, National Oceanic and Atmospheric
Maryland, 41 p. •

Dame, R. F., T. G. Wolaver and S. M. Libes. 1985. The summer uptake and release of nitrogen
by an intertidal oyster reef. Neth. J. Sea Res. 19(3/4):265-268.

Davies, J. M. 1975. Energy flow through the benthos in a Scottish sea loch. Mar. Biol. 31:353-
362.

DeFur, P. L. 1990. Respiration during ecdysis at low salinity in blue crabs, Callinectes sapidus
Rathbun. Bull. Mar. Sci. 46(l):48-54.

DeFur, P. L., C. P. Mangum and J. E. Reese. 1990. Respiratory responses of the blue crab
Callinectes sapidus to long-term hypoxia. Biol. Bull. 178:46-54.

Devol, A. H. 1991. Direct measurement of nitrogen gas fluxes from continental shelf sediments
Nature 349(6307):319-321.

Ditty, J. 1990. Sediment Chlorophyll Analysis. Student Report, Biological Oceanography, Dept.
of Oceanography and Coastal Sciences, Louisiana State University, Baton Rouge, Louisiana,
16 p.

Dodds, W. K. and J. C. Priscu. 1990. Development and application of a technique for estimating
nutrient deficiency in soft sediments. Hydrobiologia 203(l/2):93-97.
397
-------
Doerine P H C A Oviatt and M. E. Q. Pilson. 1990. Control of nutrient concentrations in the
Teekon^Pro'vidence River region of Narragansett Bay, Rhode Island. Estuaries 13(4):418-
430.

Dolan J. R. and D. W. Coats. 1990. Seasonal abundances of planktonic ciliates and
microflagellates in mesohaline Chesapeake Bay waters. Estuarine Coastal Shelf Sci.
31(2):157-175.

Dortch Q 1990 ITie interaction between ammonium and nitrate uptake in phytoplankton. Mar.
EcoLProg. Ser. 61(1/2):183-201.

Dortch Q. and J. R. Postel. 1989. Biochemical indicators of N utilization by phytoplankton
during upwelling off the Washington coast Limnol. Oceanogr. 34(4):758-773.

Dortch Q andT E Whitiedge. 1992. Does nitrogen or silicon limit phytoplankton production in
the Mississippi River plume and nearby regions? Continental Shelf Res. (in press).

Draxler A. R J., A. Matte, R. Waldhauer and J. E. O'Reilly. 1985. Nugent Distribution for
Georges Bank and Ad acent Waters in 1979. NOAA Tech. Rept. NMFS 32, U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, National Marine Fishenes
Service, Springfield, Virginia, 34 p.

Ducdale R C 1979. Primary nutrients and red tides in upwelling regions. Pages 257-262 ia
Dennis L.' Taylor and Howard H. Seliger (eds.), Toxic Dinoflagellate Blooms. Proceedings
of the Second International Conference on Toxic Dinoflagellate Blooms October 31 -
November 5, 1978, Key Biscayne, Florida. Developments in Marine Biology - Vol. 1,
Elsevier North Holland, New York.

Dundas, I, O. M. Johannessen, G. Berge and B. R. Heimdal 1989. Toxic algal bloom in
Scandanavian waters, May-June 1988. Oceanography 2(1):9-14.

Edler L 1984. A mass development of Ceratium species on the Swedish west coast.
Limnologica (Berlin) 15(2):353-357.

Edler, L., S. Ferno, M. G. Lind, R. Lundberg and P. O Nilsson. 1985. Mortality of dogs
associated with a bloom of the cyanobacterium Nodulana spumigena in the Baltic Sea.
Ophelia 24(2): 103-109.
Edler, L. and P. Olsson. 1985. Observations on diel migration of Ceratium
Prorocentrum micans in a stratified bay on the Swedish west coast. Pages 195-200 m D. M.
Anderson, A. W. White and D. G. Baden (eds.), Toxic Dinoflagellates. Proceedings of the
3rd International Conference of Toxic Dinoflagellates, June 8-12, 1985, St. Andrews, New
Brunswick, Canada. Elsevier Science, New York.

Edmond, J. M., E. A. Boyle, B. Grant and R. F. Stallard. 1981. The chemical mass balance in
the Amazon plume. I: The nutrients. Deep Sea Res. 28A(11): 1339-1374.

Eisma D and J. Kalf. 1984. Dispersal of Zaire River suspended matter in the estuary and the
Angola Basin. Neth. J. Sea Res. 17(2-4):385-411.

Elmgren, R. 1975. Benthic meiofauna as indicator of oxygen conditions in the northern Baltic
proper. Merentutkimuslait Julk/Havsforskningsinst, Skr. 239:265-271.
398
-------
Elmgren, R. 1989. The eutrophication status of the Baltic Sea: Input of nitrogen and phosphorus,
their availability for plant production, and some management implications. BalL Sea Environ.
Proc. 30:12-31. (not in hand)

Emery, K. O. and E. Uchupi. 1972. Western North Atlantic: Topography, Rocks, Structure,
Water, Life, and Sediments. American Assoc. Petroleum Geologists, Tulsa, Oklahoma, 523
P-

Enoksson, V. 1986. Nitrification rates in the Baltic Sea: Comparison of three isotope techniques.
Appl. Environ. Microbiol. 51(2):244-250.

Enoksson, V., F. Sorensson and W. Gran61i. 1990. Nitrogen transformations in the Kattegat.
Ambio 19(3):159-166.

Environmental Protection Agency. 1983. Chesapeake Bay: A Framework for Action. Chapter 2,
EPA, Annapolis, Maryland, 33 p.

Epifanio, C. E., D. .Maurer and A. I. Dittel. 1983. Seasonal changes in nutrients and dissolved
oxygen in the Gulf of Nicoya, a tropical estuary on the Pacific coast of Central America.
Hydrobiologia 101(3):231-238.

Faganeli, J., A. AvCin, N. Fanuko, A. Malej, V. Turk, P. Tusnik, B. VriSer and A. Vukovic.
1985. Bottom layer anoxia in the central part of the Gulf of Trieste in the late summer of
1983. Mar. Pollut. Bull. 16(2):75-78.

Falkowski, P. G., T. S. Hopkins and J. J. Walsh. 19,80. An analysis of factors affecting oxygen
depletion in the New York Bight. J. Mar. Res. 38(3):479-506.

Falkowski, P. G., J. Vidal, T. S. Hopkins, G. T. Rowe, T. E. Whitledge and W. G. Harrison.
1983. Summer nutrient dynamics in the Middle Atlantic Bight: Primary production and
utilization of phytoplankton carbon. J. Plankton Res. 5(4):515-537.

Faust, M. A. and D. L. Correll. 1976. Comparison of bacterial and algal utilization of
orthophosphate in an estuarine environment. Mar. Biol. 34:151-162.

Fenchel, T. M., L. D. Kristensen and L. Rasmussen. 1990. Water column anoxia: Vertical
zonation of planktonic protozoa. Mar. Ecol. Prog. Ser. 62(1/2):1-10.

Fenchel, T. M. and R. J. Riedl. 1970. The sulfide system: A new biotic community underneath
the oxidized layer of marine sand bottoms. Mar. Biol. 7:255-268.

Field, D. W., A. J. Reyer, P. V. Genovese and B. D. Shearer.- 1991. Coastal Wetlands of the
United States. An Accounting of a Valuable National Resource. A Special NOAA 20th
Anniversary Report. Strategic Assessment Branch, Ocean Assessments Division, Office of
Oceanography and Marine Assessment, National Ocean Service, National Oceanic and
Atmospheric Administration, Rockville, Maryland in cooperation with National Wetlands
Inventory, U. S. Fish and Wildlife Service, Washington, D.C. and National Wetlands
Research Center, U. S. Fish and Wildlife Service, Slidell, Louisiana, 59 p.

Fisher, T. R. and R. D. Doyle. 1987. Nutrient cycling in Chesapeake Bay. Pages 49-53 in G.
B. Mackiernan (ed.), Dissolved Oxygen in the Chesapeake Bay: Process and Effects.
Proceedings of a Seminar on Hypoxic and Related Processes in Chesapeake Bay. Maryland
Sea Grant Publication, University of Maryland, College Park, Maryland.
399
-------
Flemer, D. A. 1972. Current status of knowledge concerning the cause and biological effects of
eutrophication in Chesapeake Bay. Chesapeake Sci. 13(suppl):S144-S149.

Flemer, D. A., W. R. Boynton, C. F. D'Elia, W. M. Kemp, M. M. Nichols, R. J. Orth, J. T.
Smullen, J. L. Taft and R. L. Wetzel. 1985. The Chesapeake Bay Program: A summary of
scientific research to address management needs for Chesapeake Bay. Pages 399-438 ia N.
L. Chao and W. W. Kirby-Smith (eds.), Proceedings of the International Symposium on
Utilization of Coastal Ecosystems: Planning, Pollution and Productivity, November 21-27,
1982, Rio Grande, Brazil. Editora da Furg, Rio Grande, Brazil.

Fransz, H. G. and J. H. G. Verhagen. 1985. Modelling research on the production cycle of
phytoplankton in the Southern Bight of the North Sea in relation to riverborne nutrient loads.
Neth. J. Sea Res. 19(3/4):241-250.

Frey, H. 1990. Stratification during periods of oxygen deficiency in the German Bight during
the summers from 1981 to 1983: A comparison with the long-term variation in stratification.
Meeresforschung 32(4):306-328.

Friligos, N. and A. Zenetos. 1988. Elefsis Bay anoxia: Nutrient conditions and benthic
community structure. Mar. Ecol. 9(4):273-290.

Froelich, P. N., M. L. Bender, N. A. Luedtke, G. R. Heath and T. DeVries. 1982. The marine
phosphorus cycle. Am. J. Sci. 282(0002-9599):474-511.

Garber, J. H. 1984. Laboratory study of nitrogen and phosphorus remineralization during the
decomposition of coastal plankton and seston. Estuarine Coastal Shelf Sci. 18(6):685-702.

Garber, J. H. and W. R. Boynton. 1991. Nutrient loading, primary production, and
eutrophication of Chesapeake Bay. Pages 15-18 in K. R. Hinga, D. W. Stanley, C. J. Klein,
D. T. Lucid and M. J. Katz (eds.), The National Estuarine Eutrophication Project: Workshop
Proceedings. Strategic Environmental Assessments Division, Office of Ocean Resources
Conservation and Assessment, National Ocean Service, National Oceanic and Atmospheric
Administration, Rockville, Maryland, 41 p.

Garcia-Soto, C. Madariaga, I. de, F. Villate and E. Orive. 1990. Day-to-day variability in the
plankton community of a coastal shallow embayment in response to changes in river runoff
and water turbulence. Estuarine Coastal Shelf Sci. 31 (3):217-229.

Carlo, E. V., C. B. Milstein and A. E. Jahn. 1979. Impact of hypoxic conditions in the vicinity
of Little Egg Inlet, New Jersey in summer 1976. Estuarine Coastal Mar. Sci. 8(5):421-432.

Garside, C. and T. C. Malone. 1978. Monthly oxygen and carbon budgets of the New York
Bight apex. Estuarine Coastal Shelf Sci. 6:93-104.

Geldermalsen, L. A. van. 1985. Evaluation of seasonal nutrient dynamics in the Oosterschelde
(SW Netherlands). Neth. J. Sea Res. 19(3/4):207-217.

GESAMP. 1990. Review of Potentially Harmful Substances. Nutrients. GESAMP -
IMO/FAO/UNESCO/WMO/WHO/L\EA/UN/UNEP Joint Group of Experts on the Scientific
Aspects of Marine Pollution. Reports and Studies No. 34, United Nations Educational,
Scientific and Cultural Organization, Paris, 43 p.
400
-------
Gieskes, W. W. C. and G. W. Kraay. 1977. Continuous plankton records: Changes in the
plankton of the North Sea and its eutrophic southern bight from 1948 to 1975. Neth. J. Sea
Res. ll(3/4):334-364.

Graham, F., Jr. 1990. Careful orchestration creates harmony on the Sound. Audubon
92(6): 142-143.

Gran&i, E. 1984. Algal growth potential and limiting nutrients for phytoplankton production in
Oresund water of Baltic and Kattegat origin. Limnologica (Berlin) 15(2):563-569.

Graneli, E., W. Graneli and L. Rydberg. 1986. Nutrient limitation at the ecosystem and the
phytoplankton community level in the Laholm Bay, south-east Kattegat Ophelia 26:181-194.

Graneli, E., H. Persson and L. Edler. 1988. Connection between trace metals, chelators and red
tide blooms in the Laholm Bay south-east Kattegat - an experimental approach. Mar. Envir.
Res. 18:61-78. '

Graneli, E. and K. Sundback. 1985. The responses of planktonic and microbenthic algal
assemblages to nutrient enrichment in shallow coastal waters, southwest Sweden. J. Exp.
Mar. Biol. Ecol. 85(3):253-268.

Gran61i, E., B. Sundsrrom, L. Edler and D. M. Anderson (eds.). 1990. Toxic Marine
Phytoplankton. Proceedings of the 4th International Conference on Toxic Marine
Phytoplankton, June 26-30, 1989, Lund, Sweden. Elsevier Science, New York, 554 p.

Graneli, E., K. Wallstrom, U. Larsson, W. Gran€li and R. Elmgren. 1990. Nutrient limitation of
primary production in the Baltic Sea area. Ambio 19(3):142-151.

Graneli, W. and K. Sundback. 1986. Can microbenthic photosynthesis influence below-halocline
oxygen conditions in the Kattegat? Ophelia 26:195-206.

Gray, J. S. and H. Christie. 1983. Predicting long-term changes hi marine benthic communities.
Mar. Ecol. Prog. Ser. 13(l):87-94.

Gunning, G. E. 1985. Biological basis for dissolved oxygen criteria with applications to rivers of
the southern United States. The La. Environmental Professional 2(1): 10-27.

Hagerman, L. and S. P. Baden. 1988. Nephrops norvegicus: Field study of effects of oxygen
deficiency on haemocyanin concentration. J. Exp. Mar. Biol. Ecol. 116(2): 135-142.

Hall, P. O. J., L. G. Anderson, M. M. Rutgers van der Loeff, B. Sundby and S. F. G.
Westerlund. 1989. Oxygen uptake kinetics in the benthic boundary layer. Limnol.
Oceanogr. 34(4):734-746.

Hanson, R. B., C. Y. Robertson, J. A. Yoder, P. G. Verity and S. S. Bishop. 1990. Nitrogen
recycling in coastal waters of southeastern U.S. during summer 1986. J. Mar. Res.
48(3):641-660.

Hansson, S. and L. G. Rudstam. 1990. Eutrophication and Baltic fish communities. Ambio
19(3): 123-125.

Harding, L. W., Jr., B. W. Meeson and T. R. Fisher, Jr. 1985. Photosynthesis patterns in
Chesapeake Bay phytoplankton: Short- and long-term responses of P-I curve parameters to
light. Mar. Ecol. Prog. Ser. 26(l/2):99-lll.
401
-------
Harris, G. P. 1986. Phytoplankton Ecology: Structure, Function and Fluctuations. Chapman
and Hall, New York.

Hawes, S. R. and H. M. Perry. 1978. Effects of 1973 floodwaters on plankton populations in
Louisiana and Mississippi. Gulf Res. Rep. 6(2): 109-124.

Hecky, R. E. and P. Kilham. 1988. Nutrient limitation of phytoplankton in freshwater and
marine environments: A review of recent evidence on the effects of enrichment. Limnol.
Oceanogr. 33(4, part 2):796-822.

Henriksen, K., J. I. Hansen and T. H. Blackburn. 1980. The influence of benthic infauna on
exchange rates of inorganic nitrogen between sediment and water. Ophelia Suppl. 1:249-256.

Hickel, W., E. Bauerfeind, U. Niermann and H. v. Westernhagen. 1989. Oxygen deficiency in
the south-eastern North Sea: Sources and biological effects. Ber. Biol. Anst. Helgoland 4:1-
148.

Hinga, K. R., D. W. Stanley, C. J. Klein, D. T. Lucid and M. J. Katz (eds.). 1991. The
National Estuarine Eutrophication Project: Workshop Proceedings. Strategic Environmental
Assessments Division, Office of Ocean Resources Conservation and Assessment, National
Ocean Service, National Oceanic and Atmospheric Administration, Rockville, Maryland, 41
P-

Hirsch, R. M., J. R. Slack and R. A. Smith. 1982. Techniques of trend analysis for monthly
water quality data. Water Resour. Res. 18(1):107-121.

Hobson, L. 1985. Seasonal variations and spatial gradients of nitrogenous nutrients in waters of
southeastern Vancouver Island, British Columbia, Canada. Neth. J. Sea Res. 19(3/4):251-
256.

Holland, A. F. 1985. Long-term variation of macrobenthos in a mesohaline region of Chesapeake
Bay. Estuaries 8(2A):93-113.

Holland, A. F., N. K. Mountford and J. A. Mihursky. 1977. Temporal variation in Upper Bay
mesohaline benthic communities: I. The 9-m mud habitat. Chesapeake Sci. 18(4):370-378.

Holland, A. F., A. S. Shaughnessy and M. H. Hiegel. 1986. Separation of long-term variation
in benthic organisms into major components. IEEE Trans. Biomed. Eng. 3:1056-1061.

Hooper, F. F. 1969. Eutrophication indices and their relation to other indices of ecosystem
change. Pages 225-235 in Eutrophication: Causes, Consequences, Correctives. Proceedings
of a Symposium, 1967. National Academy of Sciences, Washington, D.C.

Howarth, R. W. and J. J. Cole. 1985. Molybdenum availability, nitrogen limitation, and
phytoplankton growth in natural waters. Science 229(4714):653-655.

Howarth, R. W., J. R. Fruci and D. Sherman. 1991. Inputs of sediment and carbon to an
estuarine ecosystem: Influence of land use. Ecological Applications l(l):27-39.

Howes, B. L., J. W. H. Dacey and G. M. King. 1984. Carbon flow through oxygen and sulfate
reduction pathways in salt marsh sediments. Limnol. Oceanogr. 29(5): 1037-1051.
402
-------
Ignatiades, L., K. Pagou and A. Vassiliou: 1986. Long term response of six diatom species to
eutrophication. Oceanol. Acta 9(4):449-456.

Ittekkot, V. A. and S. Zhang. 1989. Pattern of paniculate nitrogen transport in world rivers.
Global Biochem. Cycles 3(4):383-391.

Jaworski, N. A. 1981. Sources of nutrients and the scale of eutrophication problems in estuaries.
Pages 83-110 in B. J. Neilspn and L. E. Cronin (eds.), Estuaries and Nutrients. Proceedings
of an International Symposium on the Effects of Nutrient Enrichment in Estuaries, May 29-
31, 1979, Williamsburg, Virginia. Contemporary Issues in Science and Society, Humana
Press, Clifton, New Jersey.

Jensen, L. M., K. Sand-Jensen, S. Marcher and M. Hansen. 1990. Plankton community
respiration along a nutrient gradient in a shallow Danish estuary. Mar. Ecol. Prog. Ser.
61(l/2):75-85.

Jensen, M. H., E. Lomstein and J. Sorensen. 1990. Benthic NH4+ and NOs" flux following
sedimentation of a spring phytoplankton bloom in Aarhus Bight, Denmark. Mar. Ecol. Prog.
Ser. 61(l/2):87-96.

Johnson, C., J. Henshaw and G. Mclnnes. 1992. Impact of aircraft and surface emissions of
nitrogen oxides on tropospheric ozone and global warming. Nature 355(2):69-71.

Jonge, V. N. de. 1980. Fluctuation in the organic carbon to chlorophyll a ratios for estuarine
benthic diatom populations. Mar. Ecol. Prog. Ser. 2(4): 345-353.

Jonsson, P., R. Carman and F. Wulff. 1990. Laminated sediments in the Baltic - a tool for
evaluatingnutrientmassbalances. Ambio 19(3): 152-158.

Jordan, T. E., D. L. Correll, J. Miklas and D. E. Weller. 1991. Nutrients and chlorophyll at the
interface of a watershed and an estuary. Limnol. Oceanogr. 36(2):251-267.

J0rgensen, B. B. 1980. Seasonal oxygen depletion in the bottom waters of a Danish fjord and its
effect on the benthic community. Oikos 34(l):68-76.

J0rgensen, B. B. 1990. A thiosulfate shunt in the sulfur cycle of marine sediments. Science
249(4965):152-154.

Juniper, S. K. and R. O. Brinkhurst. 1986. Water-column dark CC>2 fixation and bacterial-mat
growth in intermittently anoxic Saanich Inlet, British Columbia. Mar. Ecol. Prog. Ser.
33(1):41-50.

Justic', D. 1987. Long-term eutrophication of the Northern Adriatic Sea. Mar. Pollut. Bull.
18(6):281-284.

Justid, D. 1988. Trend in the transparency of the northern Adriatic Sea 1911-1982. Mar. Pollut.
Bull. 19(l):32-35.

Justic, D. 1991. Hypoxic conditions in the northern Adriatic Sea: Historical development and
ecological significance. Pages 95-105 in R. V. Tyson and T. H. Pearson (eds.), Modern and
Ancient Continental Shelf Anoxia. Geological Society Special Publication No. 58, The
Geological Society, London, 470 p.
403
-------
Justic, D. 1991. A simple oxygen index for trophic state description. Mar. Pollut. Bull.
22(4):201-204.

Justic, D., T. Legovic and L. Rottini-Sandrini. 1987. Trends in oxygen content 1911-1984 and
occurrence of benthic mortality in the northern Adriatic Sea. Estuarine Coastal Shelf Sci.
25(4):435-445.

Kahru, M. and A. Aitsam. 1985. Chlorophyll variability in the Baltic Sea: A pitfall for
monitoring. J. Cons. IntExplor. Mer 42(2): 111-115.

Kamykowski, D. and S.-J. Zentara. 1986. Predicting plant nutrient concentrations from
temperature and sigma-r in the upper kilometer of the world ocean. Deep Sea Res. 33(1):89-
105.

Kankaala, P., E. Alasaarela and A. Sundberg. 1984. Phytoplankton and zooplankton production
in the northeastern and central Bothnian Bay - a review of studies carried out in 1968-1978.
Ophelia Suppl. 3:69-88.

Kanneworff, E. and H. Christensen. 1986. Benthic community respiration in relation to
sedimentation of phytoplankton in the Oresund. Ophelia 26:269-284.

Karr, J. R. 1991. Biological integrity: A long-neglected aspect of water resource management.
Ecological Applications l(l):66-84.

Keizer, P. D. and D. C. Gordon. 1985. Nutrient dynamics in Cumberland Basin - Chignecto
Bay, a turbid macrotidal estuary in the Bay of Fundy, Canada. Neth. J. Sea Res.
19(3/4):193-205.

Keller, A. A., P. H. Doering, S. P. Kelly and B. K. Sullivan. 1990. Growth of juvenile Atlantic
menhaden, Brevoortia tyrannus (Pisces: Clupeidae) in MERL mesocosms: Effects of
eutrophication. Limnol. Oceanogr. 35(1):109-122.

Kelly, J. R. and S. W. Nixon. 1984. Experimental studies of the effect of organic deposition on
the metabolism of a coastal marine bottom community. Mar. Ecol. Prog. Ser. 17(2): 157-169.

Kelly, M. and M. Naguib. 1984. Eutrophication in Coastal Marine Areas and Lagoons: A Case
Study of "Lac de Tunis." Unesco Reports in Marine Science No. 29, United Nations
Educational, Scientific and Cultural Organization, Paris, 55 p.

Kemp, W. M. and W. R. Boynton. 1980. Influence of biological and physical processes on
dissolved oxygen dynamics in an estuarine system: Implications for measurement of
community metabolism. Estuarine Coastal Mar. Sci. 11(4):407-431.

Kemp, W. M. and W. R. Boynton. 1981. External and internal factors regulating metabolic rates
of an estuarine benthic community. Oecologia (Berlin) 51(l):19-27.

Kemp, W. M., P. A. Sampou, J. M. Caffrey, M. Mayer, K. Henriksen and W. R. Boynton.
1990. Ammonium recycling versus denitrification in Chesapeake Bay. Limnol. Oceanogr.
35(7): 1545-1563.

Kempe, S. 1988. Estuaries-Their Natural and Antropogenic Changes. Pages 251-285 ia T.
Rosswall, R. G. Woodmansee and P. G. Risser (eds.), Scales and Global Change, John
Wiley & Sons, New York.
404
-------
Kennett, D. M. and P. E. Hargraves. 1985. Benthic diatoms and sulfide fluctuations: Upper
basin of Pettaquamscutt River, Rhode Island. Estuarine Coastal Shelf Sci. 21(4):577-586.

Kerr, R. A. 1986. Shaping new tools for paleoceanographers. Science 234(4775) :427-428.

Kircher, J. E., R. J. Gilliom and R. E. Hickman. 1984. Loads and concentrations of dissolved
solids, phosphorus, and inorganic nitrogen at U.S. Geological Survey National Stream
Quality Accounting Network stations. U.S. Geological Survey Water-Supply Paper
2275:61-65. ;

Kjerfve, B. J. (ed.). 1988. Hydrodynamics of Estuaries. Vol. I. Estuarine Physics. CRC Press,
Boca Raton, Florida, 163 p.

Klump, J. V. and C. S. Martens. 1981. Biogeochemical cycling in an organic rich coastal marine
basin - H. Nutrient sediment-water exchange processes. Geochim. Cosmochim. Acta
Kolmel, R. 1980. The annual cycle of macrozoobenthos: Its community structures under the
influence of oxygen deficiency in the Western Baltic. Pages 19-28 in E. Naylor and R. G.
Hartnoll (eds.), Cyclic Phenomena in Marine Plants and Animals. Proceedings of the 13th
European Marine Biology Symposium, September 27 - October 4, 1978, Isle of Man.
Pergamon Press, Oxford, England. ,

Kononen, K. and A. Niemi. 1984. Long-term variation of the phytoplankton composition at the
entrance to the Gulf of Finland. Ophelia Suppl. 3:101-110.

Koop, K., W. R. Boynton, F. Wulff and R. Carman. 1990. Sediment-water oxygen and nutrient
exchanges along a depth gradient in the Baltic Sea. Mar. Ecol. Prog. Ser. 63(l):65-77.

KovaFchuk, L. A. 1986. Asphyxiation phenomena in the northwestern Black Sea. Sov.
Meteorol. Hydrol. 3:62-67.

Kramer, G. L. 1975. Studies on the lethal dissolved oxygen levels for young brown shrimp,
Penaeus aztecus Ives. Pages 157-167 in J. W. Avault, Jr. and R. Miller (eds.), Proceedings
of the Sixth Annual Meeting, World Mariculture Society, January 27-31, 1975, Seattle,
Washington. Division of Continuing Education, Louisiana State University, Baton Rouge,
Louisiana.

Kramer, J. R., S. E. Herbes and H. E. Allen. 1972. Phosphorus: Analysis of water, biomass,
and sediment. Pages 51-100 in H. E. Allen and J. R. Kramer (eds.), Nutrients in Natural
Waters. John Wiley & Sons, New York.

Kristensen, E. and T. H. Blackburn. 1987. The fate of organic carbon and nitrogen in
experimental marine sediment systems: Influence of bioturbation and anoxia. J. Mar. Res.
45(l):231-257.

Krom, M. D. and R. A. Berrter. 1980. The diffusion coefficients of sulfate, ammonium, and
phosphate ions in anoxic marine sediments. Limnol. Oceanogr. 25(2):327-337.

Krstulovic, N. and M. Solid. 1990. Long-term study of heterptrophic bacteria as indicators of
eutrophication of the open middle Adriatic Sea. Estuarine Coastal Shelf Sci. 30(6) :61 1-617.

Kuo, A. Y. and B. J. Neilson. 1987. Hypoxia and salinity in Virginia estuaries. Estuaries
10(4):277-283.
405
-------
Kuparinen, J. 1984. Annual and seasonal fluctuation of primary productivity and overall
respiration in a pelagic plankton community off Tvarminne, sw coast of Finland. Ophelia
Suppl. 3:111-122.

Lancelot, C., G. Billen, A. Sournia, T. Weisse, F. Colijn, M. J. W. Veldhuis, A. Davies and P.
Wassmann. 1987. Phaeocystis blooms and nutrient enrichment in the continental coastal
zones of the North Sea. Ambio 16(l):38-46.

Larsson, U., R. Elmgren and F. Wulff: 1985. Eutrophication and the Baltic Sea: Causes and
consequences. Ambio 14(1):9-14.

Leffler, M. 1990. Reading the hypoxia record: Clues below the bay bottom. Marine Notes
Legovic, T. and D. Justic. 1984. Effects of ecological perturbations on diatom dynamics in the
model of Lake Jezero. Periodicum Biologorum 86(3):277-286.

Legovic, T. and D. Justic. 1985. A model of diatom dynamics in the epilimnion of Lake Jezero
on the island of Krk. Periodicum Biologorum 86(3):269-276.

LeppSnen, J.-M., E. Lahdes and J.-E. Bruun. 1986. Cycling of nitrogen during the vernal
growth period in the northern Baltic proper in 1982. Ophelia 26:293-303.

Levasseur, M. E. and J.-C. Therriault. 1987. Phytoplankton biomass and nutrient dynamics in a
tidally induced upwelling: The role of the NO3:SiO4 ratio. Mar. Ecol. Prog. Ser. 39(1):87-
97.

Lightner, D. V. 1978. Possible toxic effects of the marine blue-green alga, Spirulina subsalsa, on
the blue shrimp, Penaeus stylirostris. J. Invertebr. Pathol. 32:139-150.

Likens, G. E. and H. Bormann. 1979. The role of watershed and airshed in lake metabolism.
Arch. Hydrobiol. 13:195-211.

Lipschultz, F., S. C. Wofsy and L. E. Fox. 1986. Nitrogen metabolism of the eutrophic
Delaware River ecosystem. Limnol. Oceanogr. 31(4):701-716.

LoCicero, V. R. 1975. Proceedings of the First International Conference on Toxic Dinoflagellate
Blooms. The Massachusetts Science and Technology Foundation, Wakefield,
Massachusetts, 541 p.

Lowe, J. A., D. R. G. Farrow, A. S. Pait, S. J. Arenstam and E. F. Lavan. 1991. Fish Kills in
Coastal Waters, 1980-1989. Strategic Environmental Assessments Division, Office of Ocean
Resources Conservation and Assessment, National Ocean Service, National Oceanic and
Atmospheric Administration, Rockville, MD.

Lynch, M. P. and E. C. Krome (eds.). 1988. Understanding the Estuary: Advances in
Chesapeake Bay Research. Proceedings of a Conference, March 29-31, 1988, Baltimore,
Maryland. CRC Publ. No. 129, Chesapeake Research Consortium, Solomons, Maryland,
607 p.

Maclsaac, J. J., G. S. Grunseich, H. E. Glover and C. M. Yentsch. 1979. Light and nutrient
limitation in Gonyaulax. excavata: Nitrogen and carbon trace results. Pages 107-110 in D. L.
406
-------
Taylor and H. H. Seliger (eds.), Toxic Dinoflagellate Blooms. Proceedings of the Second
International Conference on Toxic Dinoflagellate Blooms, October 31 - November 5,1979,
Key Biscayne, Florida. Developments in Marine Biology - Vol. 1, Elsevier North Holland,
New York.

Mackiernan, G. B. 1990. Bay hypoxia - the circulation factor. Marine Notes 7(10): 1-3.

Mackiernan, G. B. 1992. Nutrients and dissolved oxygen hi the Chesapeake: How much is
enough? Marine Notes, March 1992:1-3.

Mackiernan, G. B. (ed.). 1987. Dissolved Oxygen in the Chesapeake Bay: Processes and
Effects. Proceedings of a Seminar on Hypoxia and Related Processes in Chesapeake Bay.
Maryland Sea Grant Publ. No. UM-SG-TS-87-03, Univ. of Maryland, College Park,
Maryland, 177 p.

Mahoney, J. B. and F. W. Steimle, Jr. 1979. A mass mortality of marine animals associated with
a bloom of Ceratium tripos in the New York Bight Pages 225-230 is D. L. Taylor and H.
H. Seliger (eds.), Toxic Dinoflagellate Blooms. Proceedings of the Second International
Conference on Toxic Dinoflagellate Blooms, October 31 - November 5,1979, Key Biscayne,
Florida. Developments in Marine Biology - Vol. 1, Elsevier North Holland, New York.
Makarewicz, J. C. and P. Bertram. 1991.
ecosystem. BioScience 41(4):216-223.
Evidence for the restoration of the Lake Erie
Malone, T. C. 1987. Seasonal oxygen depletion and phytoplankton production in Chesapeake
Bay: Preliminary results of 1985-86 field studies. Pages 54-60 in. G. B. Mackiernan (ed.),
Dissolved Oxygen in the Chesapeake Bay: Processes and Effects. Proceedings of a Seminar
on Hypoxia and Related Processes in Chesapeake Bay. Maryland Sea Grant Publ. No. UM-
SG-TS-87-03, Univ. of Maryland, College Park, Maryland, 177 p.

Malone, T. C. and M. B. Chervin. 1979. The production and fate of phytoplankton size fractions
hi the plume of the Hudson River, New York Bight. Limnol. Oceanogr. 24(4):683-696.

Malone, T. C., M. B. Chervin-Ledman, J. C. Stepien, C. Garside, C. D. Litchfield and J. P.
Thomas. 1985. Synoptic Investigation of Nutrient Cycling in the Coastal Plume of the
Hudson and Raritan Rivers: Plankton Dynamics. Grant No. NA82RBA6074, U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, National Ocean Service,
Stony Brook, New York, 119 p.

Malone, T. C., L. H. Crocker, S. E. Pike and B. W. Wendler. 1988. Influences of river flow on
the dynamics of phytoplankton production in a partially stratified estuary. Mar. Ecol. Prog.
Ser. 48(3):235-249.

Malone, T. C., W. M. Kemp, H. W. Ducklow, W. R. Boynton, J. H. Tuttle and R. B. Jonas.
1986. Lateral variation in the production and fate of phytoplankton in a partially stratified
estuary. Mar. Ecol. Prog. Ser. 32(2/3): 149-160.

Martens, P. 1989. On trends in nutrient concentration in the northern Wadden Sea of Sylt.
Helgol. Meeresunters. 43(3/4) :489-499.

Maryland Sea Grant. 1989. Piecing together the hypoxia puzzle. Marine Notes 7(3): 1-2.

Matthaus,W. 1980. Is the Baltic halocline really rising? Ophelia Suppl. 1:157-163.
407
-------
MatthSus, W. 1984. Variations of the oceanological conditions in the Baltic proper during the last
decades. Ophelia Suppl. 3:151-156.

Mayewski, P. A. and M. R. Legrand. 1990. Recent increase in nitrate concentration of Antarctic
snow. Nature 346:258-260.

Meade R. H. and R. S. Parker. 1985. Sediment in Rivers of the United States. National Water-
Supply Summary 1984. U.S. Geological Survey Water-Supply Paper No. 2275, U.S. Dept.
of the Interior, Geological Survey, Washington, D.C.

Megard, R. O. 1989. Effects of algae on the Secchi transparency of the southeastern
Mediterranean Sea. Limnol. Oceanogr. 34(8): 1640- 1655.

Meybeck, M. 1982. Carbon, nitrogen, and phosphorus transport by world rivers. Am. J. Sci.
282:401-450.

Meybeck, M., G. Cauwet, S. Dessery, M. Somville, D. Gouleau and G. Billen. 1988. Nutrients
(organic C, P, N, Si) in the eutrophic River Loire (France) and its estuary. Estuarine Coastal
Shelf Sci. 27(6):595-624.

Meybeck, M. and R. Helmer. 1989. The quality of rivers: From pristine stage to global pollution.
Palaeogeography, Palaeoclimatology, Palaeoecology (Global and Planetary Change Section)
75:283-309.

Michaels, A. F. and M. W. Silver. 1988. Primary production, sinking fluxes and the microbial
food web. Deep Sea Res. 35(4):473-490.

Milliman, J. D. and R. Meade. 1983. World-wide delivery of river sediment to the oceans. J.
Geol 91:1-21.

Mitsui, A., D. Rosner, A. Goodman, G. Reyes- Vasquez, T. Kusumi, T. Kodama and K.
Nomoto. 1989. Hemolytic toxins in marine cyanobacterium Synechococcus sp. Pages 367-
370 in T. Okaichi, D. M. Anderson and T. Nemoto (eds.), Red Tides. Biology,
Environmental Science, and Toxicology. Proceedings of the 1st International Symposium on
Red Tides, November 10-14, 1987, Takamatsu, Kagawa Prefecture, Japan. Elsevier
Science, New York.

Monahan, R. 1988. National Estuary Program. The Long Island Sound study. TCS Bulletin
Morel, A. and J.-F. Berthon. 1989. Surface pigments, algal biomass profiles, and potential
production of the euphotic layer: Relationships reinvestigated in view of remote- sensing
applications. Limnol. Oceanogr. 34(8): 1545- 1562.

Morris, A. W., R. J. M. Rowland, E. M. S. Woodward, A. J. Bale and R. F. C. Mantoura.
1985. Nitrite and ammonia in the Tamar estuary. Neth. J. Sea Res. 19(3/4):217-222.

Morris, J. T. 1991. Effects of nitrogen loading on wetland ecosystems with particular reference
to atmospheric deposition. Annu. Rev. Ecol. Syst. 22:257-279.

Mortimer, C. H. 1969. Physical factors with bearing on eutrophication of lakes in general and
large lakes in particular. Pages 340-368 ia National Academy of Sciences.Eutrophication:
Causes, Consequences, Correctives. Proceedings of a Symposium, 1967. National Academy
of Sciences, Washington, D.C.
408
-------
Mountford, K., R. Reynolds and N. Fisher. 1989. A telemarketing environmental data buoy in
Chesapeake Bay. Pages 17-22 ia mds '89. Proceedings of a Conference and Exposition on
. Marine Data Systems, April 26-28, 1989, New Orleans, Louisiana. Marine Technology
Society, Gulf Coast Section, Stennis Space Center, Mississippi.

National Academy of Sciences. 1969. Eutrophication: Causes, Consequences, Correctives.
Proceedings of a Symposium, 1967. National Academy of Sciences, Washington, D.C.

National Oceanic and Atmospheric Administration. 1985. National Estuarine Inventory: Data
Atlas, Volume I: Physical and Hydrologic Characteristics. Strategic Assessment Branch,
Ocean Assessments Division, Rockville, Maryland, 103 p.

National Oceanic and Atmospheric Administration. 1990a. Estuaries of the United States. Vital
Statistics of a National Resource Base. Strategic Assessment Branch, Ocean Assessments
Division, Office of Oceanography and Marine Assessment, National Ocean Service, National
Oceanic and Atmospheric Administration, Rockville, Maryland.

National Oceanic and Atmospheric Administration. 1991. Inventory of Fish Kills in Coastal
Waters. Project Description. Strategic Assessment Branch, National Oceanic and
Atmospheric Administration, Rockville, Maryland.

Nehring, D. 1984. The further development of the nutrient situation in the Baltic proper. Ophelia
Suppl. 3:167-179.

Neilson, B. J. and L. E. Cronin (eds.). 1981. Estuaries and Nutrients. Humana Press, Inc.,
Clifton, New Jersey, 643 p.

Newcombe, C. L., W. A. Home and B. B. Shepherd. 1939. Studies on the physics and
chemistry of estuarine waters in Chesapeake Bay. J. Mar. Res. 2(2):87-116.

Nichols, J. A. 1976. The effect of stable dissolved-oxygen stress on marine benthic invertebrate
community diversity. Int. Rev. Gesamten Hydrobiol. 61(6):747-760.

Nielsen, A. and G. iErtebjerg. 1984. Plankton blooms in Danish waters. Ophelia Suppl. 3:181-
188.

Nielsen, E. and S. Mellergaard. 1989. Impact of oxygen deficiency on fish disease levels.
Danish Institute for Fisheries and Marine Research. Research Report No. 353. Danish
Institute for Fisheries and Marine Research, Charlottenlund, Denmark.

Niermann, U., E. Bauerfeind, W. Hickel and H. V. Westernhagen. 1990. The recovery of
benthos following the impact of low oxygen content in the German Bight. Neth. J. Sea Res.
25(l/2):215-226.

Nitrate Coordination Group. 1986. Nitrate in Water. Pollution Paper No. 26, Dept. of the
Environment, Central Directorate of Environmental Protection. HMS Books, London, 104 p.

Nixon, S. W. 1981. Remineralization and nutrient cycling in coastal marine ecosystems. Pages
111-138 ia B. J. Neilson and L. E. Cronin (eds.), Estuaries and Nutrients. Proceedings of
an International Symposium on the Effects of Nutrient Enrichment in Estuaries, May 29-31,
1979, Williamsburg, Virginia. Contemporary Issues in Science and Society, Humana Press,
Clifton, New Jersey.
409
-------
Nixon, S.W. 1986. Nutrient dynamics and the productivity of marine coastal waters. Pages 97-
115 in. R. Halwagy, D. Clayton and M. Behbehanis (eds.), Marine Environment and
Pollution. The Alden Press, Oxford, England.
it
Nixon, S. W., C. A. Oviatt, J. B. Frithsen and B. K. Sullivan. 1986. Nutrients and the
productivity of estuarine and coastal marine ecosystems. J. Limnol. Soc. South. Afr.
12(l/2):43-71.

Noga, E. J., M. J. Dykstra and J. F. Levine. 1989. Fish Diseases of the Albemarle-Pamlico
Estuary. Rept. No. 238, WRRI Project No. 70054, Water Resources Research Institute of
the University of North Carolina, North Carolina State University, Raleigh, North Carolina,
81 P-

Nowicki, B. L. and S. W. Nixon. 1985. Benthic nutrient remineralization in a coastal lagoon
ecosystem. Estuaries 8(2B):182-190.

O'Connor, T. P. 1990. Coastal Environmental Quality in the United States, 1990. Chemical
Contamination in Sediment and Tissues. A Special NOAA 20th Anniversary Report. Coastal
and Estuarine Assessment Branch, Ocean Assessments Division, Office of Oceanography and
Marine Assessment, National Ocean Service, National Oceanic and Atmospheric
Administration, Rockville, Maryland, 34 p.

Office of Technology Assessment. 1987. Wastes in Marine Environments. Summary. Rept.
No. OTA-O-335, Congress of the United States, Office of Technology Assessment,
Washington, D.C., 46 p.

Officer, C. B., R. B. Biggs, J. L. Taft, L. E. Cronin, M. A. Tyler and W. R. Boynton. 1984.
Chesapeake Bay anoxia: Origin, development, and significance. Science 223(4631):22-27.

Officer, C. B. and J. H. Ryther. 1980. The possible importance of silicon in marine
eutrophication. Mar. Ecol. Prog. Ser. 3(1):83-91.

Oviatt, C. A., D. T. Rudnick, A. A. Keller, P. A. Sampou and G. T. Almquist. 1986a. A
comparison of system (O2 and CO2) and C-14 measurements of metabolism in estuarine
mesocosms. Mar. Ecol. Prog. Ser. 28(l/2):57-67.

Oviatt, C. A., A. A. Keller, P. A. Sampou and L. L. Beatty. 1986b. Patterns of productivity
during eutrophication: A mesocosm experiment. Mar. Ecol. Prog. Ser. 28:69-80.

Pace, M. L. and E. Funke. 1991. Regulation of planktonic microbial communities by nutrients
and herbivores. Ecology 72(3) :904-914.

Packard, T. T., H. J. Minas, B. Coste, R. Martinez, M.-C. Bonin, J. Gostan, P. Garfield, J.
Christensen, Q. Dortch, M. Minas, G. Copin-Montegut and C. Copin-Montegut. 1988.
Formation ,of the Alboran oxygen minimum zone. Deep Sea Res. 35(7): 1111-1118.

Paerl, H. W. 1988. Nuisance phytoplankton blooms in coastal, estuarine, and inland waters.
Limnol. Oceanogr. 33(4, part 2):823-847.

Pearson, T. H. 1981. Stress and catastrophe in marine benthic ecosystems. Pages 201-214 in G.
W. Barrett and R. Rosenberg (eds.), Stress Effects on Natural Ecosystems. Proceedings of a
Special Symposium at the 2nd International Congress of Ecology, September 10-16, 1978,
410
-------
Jerusalem, Israel. Environmental Monographs and Symposia Series, John Wiley & Sons,
Chichester, England.

Pearson, T. H., A. B. Josefson and R. Rosenberg. 1985. Petersen's benthic stations revisited. I.
Is the Kattegat becoming eutrophic? J. Exp. Mar. Biol. Ecol. 92(2/3): 157-206.

Pennock, J. R. 1985. Chlorophyll distributions in the Delaware estuary: Regulation by light-
limitation. Estuarine Coastal Shelf Sci. 21(5):711-725.

Pennock, J. 1991. Estuarine nutrient enrichment and phytoplankton production: What factors
regulate the expression of eutrophication? Pages 23-24 in K. R. Hinga, D. W. Stanley, C. J.
Klein, D. T. Lucid and M. J. Katz (eds.), The National Estuarine Eutrophication Project:
Workshop Proceedings. Strategic Environmental Assessments Division, Office of Ocean
Resources Conservation and Assessment, National Ocean Service, National Oceanic and
Atmospheric Administration, Rockville, Maryland, 41 p.

Pennock, J. R. and J. H. Sharp. 1987. Phytoplankton production in the Delaware estuary:
Temporal and spatial variability. Mar. Ecol. 34:143-145.

Persson, L.-E. 1987. Baltic eutrophication: A contribution to the discussion. Ophelia 27(1):31-
42.

Pihl, L., S. P. Baden and R. J. Diaz. 1991. Effects of periodic hypoxia on distribution of
demersal fish and crustaceans. Mar. Biol. 108:349-360.

Pilson, M. E. Q. 1985. Annual cycles of nutrients and chlorophyll in Narragansett Bay, Rhode
Island. J. Mar. Res. 43(4):849-873.

Pollehne, F. 1986. Benthic nutrient regeneration processes in different sediment types of Kiel
Bight Ophelia 26:359-368.

Pomeroy, L. R., L. R. Shenton, R. D. H. Jones and R. J. Reimold. 1972. Nutrient flux in
estuaries. Pages 274-291 in G. E. Likens (ed.), Nutrients and Eutrophication: The Limiting-
Nutrient Controversy. Vol. I. Proceedings of a Symposium, February 11-12, 1971, W.K.
Kellogg Biological Station, Michigan State University, East Lansing, Michigan. Allen Press,
Lawrence, Kansas.

Portman, J. E. 1989. The chemical pollution status of the North Sea. Dana 8:95-108.

Pringle, C. M. 1991. U.S.—Romanian environmental reconnaissance of the Danube Delta.
Conservation Biology 5(4):442-445.

Purdue University. 1991. Sources and Quantities of Nutrients Entering the Gulf of Mexico from
Surface Waters of the United States. Research Report to U.S. EPA Gulf of Mexico Program.
Dept. of Agricultural Economics, Purdue University, West Lafayette, Indiana, 49 p. and
appendices.

Pugkaric, S., G. W. Berger and F. J. Jorissen. 1990. Successive appearance of subfossil
phytoplankton species in Holocene sediments of the northern Adriatic and its relation to the
increased eutrophication pressure. Estuarine Coastal Shelf Sci. 31(2):177-187.

Quick, J. A., Jr. 1975. Evidences of new ichthyointoxicative phenomena in Gymnodinium breve
red tides. Pages 413-422 in V. R. LoCicero (ed.), Proceedings of the First International
411
-------
Conference on Toxic Dinoflagellate Blooms. The Massachusetts Science and Technology
Foundation, Wakefield, Massachusetts, 541 p.

Rachor, E. 1980. The inner German Bight - an ecologically sensitive area as indicated by the
bottom fauna. Helgol. Meeresunters. 33(l-4):522-530.

Rainer, S. F. and R. C. Fitzhardinge. 1981. Benthic communities in an estuary with periodic
deoxygenation. Aust. J. Mar. Freshwater Res. 32(2):227-243.

Raloff, J. 1987. U.S. river quality: Not all signs are good. Science News 131:214.

Redfield, A. C. 1934. On the proportions of organic derivatives in sea water and their relation to
the composition of plankton. James Johnstone Memorial Volume (Liverpool), 176 p.

Redfield, A. C. 1958. The biological control of chemical factors in the environment Amer. Sci.
46:205-221.

Reise, K., E. Herre and M. Sturm. 1989. Historical changes in the benthos of the Wadden Sea
around the island of Sylt in the North Sea. Helgol. Meeresunters. 43(3/4):417-433.

Richardson, K. 1989. Algal blooms in the North Sea: The Good, the Bad and the Ugly. Dana
8:83-93.

Risberg, J. 1990. Siliceous microfossil stratigraphy in a superficial sediment core from the
northwestern part of the Baltic proper. Ambio 19(3): 167-172.

Rizzo, W. M. 1990. Nutrient exchanges between the water column and a subtidal benthic
microalgal community. Estuaries 13(3):219-226.

RSnner, U. and F. Sorensson. 1985. Denitrification rates in the low-oxygen waters of the
stratified Baltic proper. Appl. Environ. Microbiol. 50(4):801-806.

Rosenberg, R. 1976. Benthic faunal dynamics during succession following pollution abatement
in a Swedish estuary. Oikos 27(3):414-427.

Rosenberg, R. 1977. Benthic macrofaunal dynamics, production, and dispersion in an oxygen-
deficient estuary of west Sweden. J. Exp. Mar. Biol. Ecol. 26:107-133.

Rosenberg, R. 1980. Effect of oxygen deficiency on benthic macrofauna in fjords. Pages 499-
514 in. H. J. Freeland, D. M. Farmer and C. D, Levings (eds.), Fjord Oceanography.
Proceedings of the NATO Conference, June 4-8, 1979, Victoria, British Columbia, Canada.
NATO Conference Series: IV, Marine Sciences, Vol. 4, Plenum Press, New York.

Rosenberg, R. 1985. Eutrophication - the future marine coastal nuisance? Mar. Pollut. Bull.
16(6):227-231.

Rosenberg, R. (ed.). 1986. A Review. Eutrophication in Marine Waters Surrounding Sweden.
Rept. No. 3054, The National Swedish Environmental Protection Board, Solna, Sweden,
137 p.

Rosenberg, R. 1990. Negative oxygen trends in Swedish coastal bottom waters. Mar. Pollut.
Bull. 21(7):335-339.
412
-------
Rosenberg, R., W. E. Arntz, E. C. de Flores, L. A. Flores, G. Carbajal, I. Finger and J.
Tarazona. 1983. Benthos biomass and oxygen deficiency in the upwelling system off Peru
J. Mar. Res. 41(2):263-279.

Rosenberg, R., R. Elmgren, S. Fleischer, P. Jonsson, G. Persson and H. Dahlin. 1990. Marine
eutrophication case studies in Sweden. Ambio 19(3): 102-108.

Rosenberg, R., J. S. Gray, A. B. Josefson and T. H. Pearson. 1987. Petersen's benthic stations
revisited. II. Is the Oslofjord and eastern Skagerrak enriched? J. Exp. Mar. Biol. Ecol.
105(2/3):219-251.

Rosenberg, R. and L.-O. Loo. 1988. Marine eutrophipation induced oxygen deficiency: Effects
on soft bottom fauna, western Sweden. Ophelia 29(3) :213-225.

Rosenberg, R. and P. Moller. 1979. Salinity stratified benthic macrofaunal communities and
long-term monitoring along the west coast of Sweden. J. Exp. Mar. Biol. Ecol. 37:175-203.

Rossignol-Strick, M. 1985. A marine anoxic event on the Brittany coast, July 1982. J. Coastal
Res. 1(1): 11-20.

Rounsefeil, G. A. and W. R. Nelson. 1966. Red-Tide Research Summarized to 1964 Including
an Annotated Bibliography. U.S. Fish and Wildlife Service, Special Scientific Report--
Fisheries No. 535. U.S. Dept. of the Interior, Fish and Wildlife Service, Washington, B.C.,
85 p.

Rydberg, L. 1986. Observations on nutrient fluxes through the coastal zone. Rapp. P.-V. Re*un
Cons. Int. Explor. Mer 186:49-59.

Rydberg, L., L. Edler, S. Floderus and W. Grane"lil 1990. Interaction between supply of
nutrients, primary production, sedimentation and oxygen consumption in SE Kattegat
Ambio 19(3):134-141. .;.

Rydberg, L. and J. Sundberg. 1988. An estimate of oxygen consumption and denitrification in
coastal waters of the Swedish west coast, using indirect methods. Estuarine Coastal Shelf
Sci. 26(3):269-284.

Ryther, J. H. 1954. The ecology of phytoplankton blooms in Moriches Bay and Great South
Bay, Long Island, N.Y. Biol. Bull. 106:198-209. |

Ryther, J. H. 1955. Ecology of autotrophic marine dinoflagellates with reference to red water
conditions. Pages 387-414 ia F. H. Johnson (ed.), The Luminescence of Biological
Systems. American Association for the Advancement of Science, Washington, D.C.

Ryther, J. H. and W. M. Dunstan. 1971. Nitrogen, phosphorus, and eutrophication in the coastal
marine environment. Science 171(3975): 1008-1013.

Sakshaug, E., K. Andresen, S. Mkklestad and Y. Olsen. 1983. Nutrient status of phytoplankton
communities in Norwegian waters (marine, brackish, and fresh) as revealed by their chemical
composition. J. Plankton Res. 5:175-196.

Salomons, W., B. L. Bayne, E. K. Duursma and U. Forstner (eds.). 1988. Pollution of the
North Sea: An Assessment. Springer-Verlag, Berlin, 687 p.
413
-------
Sampou P A. 1989. Effects of Eutrophication on the Biogeochemical Cycling of Carbon,
Oxygen, Sulphur and Energy in Coastal Marine Ecosystems. Ph.D. Dissertation, University
of Rhode Island, Kingston, Rhode Island, 236 p.

Sanford, L. P., K. G. Sellner and D. L. Breitburg. 1990. Covariability of dissolved oxygen with
physical processes in the summertime Chesapeake Bay. J. Mar. Res. 48(3):567-590.

Sanford, L. P., K. G. Sellner, M. H. Bundy and M. C. Marsh. 1988. Utility of the Endeco
pulsed d o sensor for estuarine measurements of dissolved oxygen, la K. G. bellner and L.
P Sanford (eds.), Summertime Variability of Dissolved Oxygen Concentrations in the
Mesohaline Chesapeake Bay. Progress Report 1 to the Maryland Sea Grant College
Program, University of Maryland, College Park, Maryland, 31 p.

Sarmiento J. L., T. D. Herbert and J. R. Toggweiler. 1988. Causes of anoxia in the world
ocean. Global Biochem. Cycles 2(2): 115-128.

Sas H. (ed.). 1985. Lake Restoration by Reduction of Nutrient Loading: Expectations,
' Experiences, Extrapolations. Academia Verlag Richarz, St. Augustin, Germany, 497 p.

Savage, N. B. 1976. Burrowing activity in Mercenaria mercenaria (L.) and Spisula solidissima
(DUlwyii) as a function of temperature and dissolved oxygen. Mar. Behav. Physiol. 3:221-
234.

Scharf, E.-M., W. Schnese and G. Schlungbaum. 1984. Short term response of benthic and
pelagic ciliates to artificial eutrophication. Ophelia Suppl. 3:195-200.

Schiedek, D. and U. Schottler. 1990. The energy production of juvenile Arenicola marina
(Polychaeta) under anoxic and hypoxic conditions. Helgol. Meeresunters. 44(2): 135-145.

Schiewer, U., R. Borner, B. Kriiger and F.-K. Evert. 1984. Estuarine phytoplankton response
to nutrient changes in controlled ecosystem enclosures. Ophelia Suppl. 3:201-212.

Seitzinger, S. P. and S. W. Nixon. 1985. Eutrophication and the rate of denitrification and N2O
production in coastal marine sediments. Limnol. Oceanogr. 30(6): 1332-1339.

Seki, H., T. Tsuji and A. Hattori. 1974. Effect of zooplankton grazing on the formation of the
'anoxic layer in Tokyo Bay. Estuarine Coastal Mar. Sci. 2:145-151.

Seliger, H. H. and J. A. Boggs. 1987. Anoxia in the Chesapeake Bay. A turbidity hypothesis.
Coastal Ocean Pollution Assessment News 3(4):47-49.

Seliger H. H., J. A. Boggs and W. H. Biggley. 1985. Catastrophic anoxia in the Chesapeake
Bay in 1984. Science 228(4695):70-73.

Selmer J.-S. 1988. Ammonium regeneration in eutrophicated coastal water of Sweden. Mar.
Ecol. Prog. Ser. 44(3):265-273.

Short, F. T. 1987. Effects of sediment nutrients on seagrass: Literature review and mesocosm
experiment. Aq. Bot. 27:41-57.

Short F. T. 1991. Effects of excessive nutrient loading on the eelgrass community. Pages 25-27
i K. R. Hinga, D. W. Stanley, C. J. Klein, D. T. Lucid and M. J. Katz (eds.), The National
Estuarine Eutrophication Project: Workshop Proceedings. Strategic Environmental
414
-------
Assessments Division, Office of Ocean Resources Conservation and Assessment, National
Ocean Service, National Oceanic and Atmospheric Administration, Rockville, Maryland, 41

P-

Shumway, S. E. 1990. A review of the effects of algal blooms on shellfish and aquaculture. J.
World Aquacult. Soc. 21(2):65-105.

Shumway, S. E., J. Barter and S. Sherman-Caswell. 1990. Auditing the impact of toxic algal
blooms on oysters. Environ. Audit. 2(l):41-56.

Siddall, S., V. M. Bricelj, E. J. Carpenter, A. Chiaraviglio and W. C. Dennison. 1987. Impact
of the 1985 phytoplankton bloom in Long Island's coastal bays. Coastal Ocean Pollution
Assessment News 3(4):49-52.

Sieburth, J. M. 1979. Sea Microbes. Oxford University Press, New York, 491 p.

Simon, N. S. 1989. Nitrogen cycling between sediment and the shallow-water column in the
transition zone of the Potomac River and estuary. II. The role of wind-driven resuspension
and adsorbed ammonium. Estuarine Coastal Shelf Sci. 28(5):531-547.

Skjoldal, H. R. and P. Wassmann. 1986. Sedimentation of particulate organic matter and silicium
during spring and summer in Lindaspollene, Western Norway. Mar. Ecol. Prog. Ser.
30(l):49-63.

Skreslet, S. (ed.) 1986. The Role of Freshwater Outflow in Coastal Marine Ecosystems.
Springer-Verlag, New York, 453 p.

Smayda, T. J. 1989. Primary production and the global epidemic of phytoplankton blooms in the
sea: A linkage? Pages 449-483 M E. M. Cosper, V. M. Bricelj and E. J. Carpenter (eds.),
Novel Phytoplankton Blooms. Causes and Impacts of Recurrent Brown Tides and Other
Unusual Blooms. Proceedings of a Symposium, October 27-28, 1988, Stony Brook, New
York. Coastal and Estuarine Studies No. 35, Springer-Verlag, New York.

Smayda, T. J. 1990. Novel and nuisance phytoplankton blooms in the sea: Evidence for a global
epidemic. Pages 29-40 ia E. Graneli, B. Sundstrom, L. Edler and D. M. Anderson (eds.),
Toxic Marine Phytoplankton. Proceedings of the 4th International Conference on Toxic
Marine Phytoplankton, June 26-30,1989, Lund, Sweden. Elsevier Science, New York.

Smayda, T. 1991. Increasing worldwide frequency of nuisance algal blooms. Pages 41 in K. R.
Hinga, D. W. Stanley, C. J. Klein, D. T. Lucid and M. J. Katz (eds.), The National
Estuarine Eutrophication Project: Workshop Proceedings; Strategic Environmental
Assessments Division, Office of Ocean Resources Conservation and Assessment, National
Ocean Service, National Oceanic and Atmospheric Administration, Rockville, Maryland, 27
P-

Smayda, T. J. and A. W. White. 1990. Has there been a global expansion of algal blooms? If so,
is there a connection with human activities? Pages 516-517 in E. Grandli, B. Sundstrom, L.
Edler and D. M. Anderson (eds.), Toxic Marine Phytoplankton. Proceedings of the 4th
International Conference on Toxic Marine Phytoplankton, June 26-30, 1989, Lund, Sweden.
Elsevier Science, New York.

Smetacek, V. S. 1980. Annual cycle of sedimentation in relation to plankton ecology in western
Kiel Bight. Ophelia Suppl. 1:65-76.
415
-------
Smetacek, V. S., B. v. Bodungen, B. Knoppers, H. Neubert, F. Pollehne and B. Zeitzschel.
1980. Shipboard experiments on the effect of vertical mixing on natural plankton populations
in the central Baltic Sea. Ophelia Suppl. 1:77-98.

Smetacek, V. S., K. v. Brockel, B. Zeitzschel and W. Zenk. 1978. Sedimentation of particulate
matter during a phytoplankton spring bloom in relation to the hydrographical regime. Mar.
Biol. 47:211-226.

Smetacek, V. S. and U. Passow. 1990. Spring bloom initiation and Sverdrup's critical-depth
model. Limnol. Oceanogr. 35(l):228-234.

Smetacek, V. S. and F. Pollehne. 1986. Nutrient cycling in pelagic systems: A reappraisal of the
conceptual framework. Ophelia 26:401-428.

Smith, J. D., E. C. V. Butler, D. Airey and G. Sandars. 1990. Chemical properties of low-
oxygen water column in Port Hacking (Australia): Arsenic, iodine and nutrients. Mar. Chem.
28(4):353-364.

Smith, R. A. and R. B. Alexander. 1984. Trends in concentrations of dissolved solids,
suspended sediments, phosphorus, and inorganic nitrogen at U.S. Geological Survey
National Stream Quality Accounting Network stations. U.S. Geological Survey Water-
Supply Paper 2275:66-73.

Smith, R. A., R. B. Alexander and M. G. Wolman. 1987. Water-quality trends in the nation's
rivers. Science 235(4796):1607-1615.

Smith, S. V. 1981. Responses of Kaneohe Bay, Hawaii, to relaxation of sewage stress. Pages
391-410 in B. J. Neilson and L. E. Cronin (eds.), Estuaries and Nutrients. Humana Press,
Inc., Clifton, New Jersey.

Smith, S. V. 1984. Phosphorus versus nitrogen limitation in the marine environment. Limnol.
Oceanogr. 29(6):1149-1160.

Smith, S. V., J. T. Hollibaugh, S. J. Dollar and S. Vink. 1989. Tomales Bay, California: A case
for carbon-controlled nitrogen cycling. Limnol. Oceanogr. 34(l):37-52.

Soulsby, P. G., D. Lowthion, M. Houston and H. A. C. Montgomery. 1985. The role of
sewage effluent in the accumulation of macroalgal mats on intertidal mudflats in two basins in
southern England. Neth.J. Sea Res. 19(3/4):257-263.

Spencer, C. P. 1985. The use of plant micro-nutrient and chlorophyll records as indices of
eutrophication in inshore waters. Neth. J. Sea Res. 19(3/4):269-275.

Stachowitsch, M. 1984. Mass mortality in the Gulf of Trieste: The course of community
destruction. Mar. Ecol. 5(3):243-264.

Stachowitsch, M. 1986. The Gulf of Trieste: A sensitive ecosystem. Nova Thalassia 8 (Suppl.
3):221-235.,

Stanley, S. O., J. W. Leftley, A. Lightfoot, N. Robertson, I. M. Stanley and I. Vance. 1981.
The Loch Eil project: Sediment chemistry, sedimentation, and the chemistry of the overlying
water in Loch Eil. J. Exp. Mar. Biol. Ecol. 55(2/3):299-313.
416
-------
Steimle, F. W., Jr. 1985. Biomass and estimated productivity of benthic macrofauna in the New
York Bight: A stressed area. Estuarine Coastal Shelf Sci. 21(4):539-554.

Stickle, W. B., M. A. Kapper, L.-L. Liu, E. Gnaiger and S. Wang. 1989. Metabolic adaptations
of several species of crustaceans and molluscs to hypoxia: Tolerance and microcalorimetric
studies. Biol. Bull. 177(2):303-312.

Suess, E. 1980. Particulate organic carbon flux in th oceans: surface productivity and oxygen
utilization. Nature 288:260-263.

Sullivan, T. J., D. F. Charles, J. P. Smol, B. F. Gumming, A. R. Selle, D. R. Thomas, J. A.
Bernert and S. S. Dixit. 1990. Quantification of changes in lakewater chemistry in response
to acidic deposition. Nature 345(6270):54-58.

Summerson, H. C. and C. H. Peterson. 1990. Recruitment failure of the bay scallop, Argopecten
irradians concentricus, during the first red tide, Ptychodiscus brevis, outbreak recorded in
North Carolina. Estuaries 13(3):322-331.

Sun, M. 1986. The Chesapeake Bay's difficult comeback. Science 233(4765):? 15-717.

Sundback, K. 1984.. Distribution of microbenthic chlorophyll-a and.diatom species related to
sediment characteristics. Ophelia Suppl. 3:229-246.

Suttle, C. A. and P. J. Harrison. 1986. Phosphate uptake rates of phytoplankton assemblages
grown at different dilution rates in semicontinuous culture. Can. J. Fish. Aquat. Sci.
43:1474-1481.

Swanson, R. L. and C. A. Parker. 1988. Physical environmental factors contributing to recurring
hypoxia in the New York Bight. Trans. Am. Fish. Soc. 117(l):37-47.

Swanson, R. L. and C. J. Sindermann (eds.). 1979. Oxygen Depletion and Associated Benthic
Mortalities in New York Bight, 1976. NOAA Professional Paper No. 11, U.S. Dept. of
Commerce, National Oceanic and Atmospheric Administration, Washington, D.C., 345 p.

Sykes, J. E. 1965. Bureau of Commercial Fisheries Symposium on Red Tide. U.S. Fish and
Wildlife Service, Special Scientific Report—Fisheries No. 521. U.S. Dept. of the Interior,
Fish and Wildlife Service, Washington, D.C., lip.

Tarazona, J., H. Salzwedel and W. E. Arntz. 1988a. Oscillations of macrobenthos in shallow
waters of the Peruvian central coast induced by El Nino 1982-83. J. Mar. Res. 46(3) :593-
611.

Tarazona, J., H. Salzwedel and W. E. Arntz. 1988b. Positive effects of "El Nino" on
macrozoobenthos inhabiting hypoxic areas of the Peruvian upwelling system. Oecologia
76(2): 184-190.

Taylor, D. L. and H. H. Seliger (eds.). 1979. Toxic Dinoflagellate Blooms. Proceedings of the
Second International Conference on Toxic Dinoflagellate Blooms, October 31 - November 5,
1978, Key Biscayne, Florida. Developments in Marine Biology - Vol. 1, Elsevier North
Holland, New York, 505 p.

Tenore, K. R. 1972. Macrobenthos of the Pamlico River estuary, North Carolina. Ecol.
Monogr. 42(l):51-69.
417
-------
Tett, P 1982. The Lock Eil project: Planktonic pigments in sediments from Loch Eil and the Firth
of Lome. J. Exp. Mar. Biol. Ecol. 56(1): 101-114.

Theede, H. 1973. Comparative studies on the influence of oxygen deficiency and hydrogen
sulphide on marine bottom invertebrates. Neth. J. Sea Res. 7:244-252.

Theede, H., A. Ponat, K. Hiroki and C. Schlieper. 1969. Studies on the resistance of marine
bottom invertebrates to oxygen-deficiency and hydrogen sulphide. Mar. Biol. 2:325-337.

Thorhaug, A. 1985. Large-scale seagrass restoration in a damaged estuary. Mar. Pollut. Bull.
16(2):55-62.

Tolmazin, D. 1985. Changing coastal oceanography of the Black Sea. I: Northwestern shelf.
Prog. Oceanogr. 15(4):217-276.

Townsend, D. W. and L. M. Cammen. 1988. Potential importance of the timing of spring
plankton blooms to benthic-pelagic coupling and recruitment of juvenile demersal fishes.
Biol. Oceanogr. 5(3):215-229.

Tracey, G. A. 1988. Feeding reduction, reproductive failure, and mortality in Mytilus edulis
during the 1985 "brown tide" in Narragansett Bay, Rhode Island. Mar. Ecol. Prog. Ser.
50:73-81.

Tsai, C.-F., M. Wiley and A.-L. Chai. 1991. Rise and fall of the Potomac River striped bass
stock: A hypothesis of the role of sewage. Trans. Am. Fish. Soc. 120(l):l-22.

Tunnicliffe, V. and S. K. Juniper. 1990. Cosmopolitan underwater fauna. Nature
344(6264):300.

Turner, R.E. 1991. Fertilizer and climate change. Nature 349(6309):469-470.

Turner, R. E. and D. F. Boesch. 1987. Aquatic animal production and wetland relationships:
Insights gleaned following wetland loss or gain. Pages 25-39 m D. Hooks (ed.), Ecology
and Management of Wetlands. Croons Helms, Ltd., Beckenham, Kent, United Kingdom.

Turner, R. E. and N. N. Rabalais. 199 Ib. Eutrophication and its effects on coastal habitats.
Coastal Zone '91. Pages 61-74 in, S. H. Bolton (ed.), Coastal Wetlands. Proceedings of the
Seventh Symposium on Coastal and Ocean Management, July 8-12, 1991, Long Beach,
California. American Society of Civil Engineers Press, New York.

Turner, R. E., N. N. Rabalais and Z.-N. Zhang. 1990. Phytoplankton biomass, production and
growth limitations on the Huanghe (Yellow River) continental shelf. Cont. Shelf Res.
10:545-571. .

Tuttie, J. H., T. C. Malone, R. B. Jonas, H. W. Ducklow and D. G. Cargo. 1987. Nutrient-
Dissolved Oxygen Dynamics in Chesapeake Bay: The Roles of Phytoplankton and Micro-
Heterotrophs under Summer Conditions, 1985. Final Report to U.S. Environmental
Protection Agency, Chesapeake Bay Program, Ref. No. UMCEES CBL 86-125a.
Chesapeake Biology Laboratory, Solomons, Maryland, 158 p.

Twilley, R. R., W. M. Kemp, K. W. Staver, J. C. Stevenson and W. R. Boynton. 1985.
Nutrient enrichment of estuarine submersed vascular plant communities. I. Algal growth and
effects on production of plants and associated communities. Mar. Ecol. Prog. Ser.
23(2): 179-191.'
418
-------
Tyson, R. V. and T. H. Pearson. 1991. Modern and ancient continental shelf anoxia: an
overview. Pages 1-24 in R. V. Tyson and T. H. Pearson (eds.), Modem and Ancient
Continental Shelf Anoxia. Geological Society Special Publication No. 58. The Geological
Society of London, 470 p.

U. S. Army Corps of Engineers. 1974. Deep draft access to the ports of New Orleans and Baton
Rouge. Draft Environmental Statement. U.S. Army Corps of Engineers, New Orleans
District, New Orleans, Louisiana.

United Nations. 1981. River Inputs to Ocean Systems. Proceedings of a Review Workshop,
March 30, 1979, Rome, Italy. Unipub, New York, 384 p.

Valiela, I. 1984. Marine Ecological Processes. Springer Verlag, New York.

Van Baalen, C. and R. M., Jr. Brown. 1969. The ultrastructure of the blue-green alga,
Trichodesmium erythraeum, with special reference to the cell wall, gas vacuoles, and
cylindrical bodies. Arc. Microbiol. 69:79-9i.

Vanni, M. J., C. Luecke, J. F. Kitchell, Y. Allen, J. Temte and J. J. Magnuson. 1990. Effects
on lower trophic levels of massive fish mortality. Nature 344(6264):333-335.

Vanni, M. J. and J. Temte. 1990. Seasonal patterns of grazing and nutrient limitation of
phytoplankton in a eutrophic lake. Limnol. Oceanogr. 35(3):697-709.

Varmo, R. and S. Skog. 1980. Relation of macrozoobenthos to pelagic primary production in the
polluted coastal waters off Helsinki. Ophelia Suppl. 1:165-178.

Vaulot, D. and G.-F. Frisoni. 1986. Phytoplanktonic productivity and nutrients in five
Mediterranean lagoons. Oceanol. Acta9(l):57-63.

Veer, H. W. van der, W. v. Raaphorst and M. J. N. Bergman. 1989. Eutrophication of the
Dutch Wadden Sea: External nutrient loadings of the Marsdiep and Vliestroom basin. Helgol.
Meeresunters. 43(3/4):501-515.

Verity, P. G. 1987. Factors driving changes in the pelagic trophic structure of estuaries, with
implications for Chesapeake Bay. Pages 35-56 in M. P. Lynch and E. C. Krome (eds.),
Perspectives on the Chesapeake Bay: Recent Advances in Estuarine Sciences. Chesapeake
Bay Program and Chesapeake Research Consortium, U.S. Environmental Protection Agency,
CRC Publication No. 127, Gloucester Point, Virginia.

Vollenweider, R. A. 1968. Scientific Fundamentals of the Eutrophication of Lakes and Flowing
Waters, with Particular Reference to Nitrogen and Phosphorus as Factors in Eutrophication.
Water Management Research Technical Report. Organization for Economic Cooperation and
Development Directorate for Scientific Affairs, Paris.

Walsh, J. J. 1991. Importance of continental margins in the marine biogeochemical cycling of
carbon and nitrogen. Nature 350(6313):53-55.

Walsh, J. J., E. T. Premuzic and T. E. Whitledge. 1980. Fate of Nutrient Enrichment on
Continental Shelves as Indicated by the C/N Content of Bottom Sediments. Publ. No. BNL-
28659, Brookhaven National Laboratory, Upton, New York, 37 p.
419
-------
Walsh, J. J., G. T. Rowe, R. L. Iverson and C. P. McRoy. 1981. Biological export of shelf
carbon is a sink of the global CO2 cycle. Nature 291(5821):196-201.

Ward, L. G. and R. R. Twilley. 1986. Seasonal distributions of suspended paniculate material
and dissolved nutrients in a coastal plain estuary. Estuaries 9(3): 156-168.

Warsh, C., B. Gottholm, T. E. Whitledge and S. Oakley. 1982. Water quality monitoring in the
Middle Atlantic Bight - A monitoring tool. Pages 1136-1141 in Oceans '82. Proceedings of
a Conference, September 20-22, 1982, Washington, D.C. Marine Technology Society and
IEEE Council on Ocean Engineering, Washington, D.C.

Wassmann, P. 1986. Benthic nutrient regeneration as related to primary productivity in the west-
Norwegian coastal zone. Ophelia 26:443-456.

Watson, P. G., P. E. Prickers and C. M. Goodchild. 1985. A comparison of nutrients in the
interstitial water of reducing (Tamar Estuary) and oxic (Carmarthen Bay) coastal sediments.
Neth. J. Sea Res. 19(3/4):231-239.

Webb, K. L. and C. F. D'Elia. 1980. Nutrient and oxygen redistribution during a spring neap
tidal cycle in a temperature estuary. Science 207(4434):983-985.
Wells, F. C. 1980. Hydrology and Water Quality of the Lower Mississippi River. Water
Resources Technical Report No. 21, Louisiana Department of Transportation and
Development, Office of Public Works, Baton Rouge, Louisiana, 82 p.

Welsh, B. L. and F. Craig Eller. 1991a. Mechanisms controlling summertime oxygen depletion
in western Long Island Sound. Estuaries 14(3):265-278.

Welsh, B. L. 1991b. Anoxia and hypoxia in Long Island Sound, Chesapeake Bay, and Mobile
Bay: A comparative assessment. Pages 35-40 ia K. R. Hinga, D. W. Stanley, C. J. Klein,
D. T. Lucid and M. J. Katz (eds.), The National Estuarine Eutrophication Project: Workshop
Proceedings. Strategic Environmental Assessments Division, Office of Ocean Resources
Conservation and Assessment, National Ocean Service, National Oceanic and Atmospheric
Administration, Rockville, Maryland, 41 p.

Westernhagen, H. v. and V. Dethlefsen. 1983. North Sea oxygen deficiency 1982 and its effects
on the bottom fauna. Ambio 12(5):264-266.

Westernhagen, H. v., W. Hickel, E. Bauerfeind, U. Niermann and I. Kroncke. 1986. Sources
and effects of oxygen deficiencies in the south-eastern North Sea. Ophelia 26:457-473.

White, F. C., J. R. Hairston, W. N. Musser, H. F. Perkins and J. F. Reed. 1981. Relationship
between increased crop acreage and nonpoint-source pollution: A Georgia case study. J. Soil
Water Conservation 36:172-177.

Widbom, B. and R. Elmgren. 1988. Response of benthic meiofauna to nutrient enrichment of
experimental marine ecosystems. Mar. Ecol. Prog. Ser. 42:257-268.

Wolfe, D. A., M. A. Champ, D. A. Flemer and A. J. Mearns. 1987. Long-term biological data
sets: Their role in research, monitoring, and management of estuarine and coastal marine
systems. Estuaries 10(3):181-193.
420
-------
Wolman, M. G. 1971. The nation's rivers. Problems are encountered in appraising trends in
water and river quality. Science 174(4012) :905-918.

Wulff, F. and L. Rahm. 1988. Long-term, seasonal and spatial variations of nitrogen,
phosphorus and silicate in the Baltic: An overview. Mar. Environ. Res. 26(1): 19-37.

Wulff, F., A. Stigebrandt and L. Rahm. 1990. Nutrient dynamics of the Baltic Sea. Ambio
19(3): 126-133.
U.S. GOVERNMENT PRINTING OFFICE: 1993 — 7 19-819' 80085
421
-------
-------
-------
ISBN 0-16-036279-2
90000
9 "780160" 362798"
-------
SV.WK.W. JW \ *A A "• "
•. •K'.ssss v. ^ vi v. w, s s
•.••••*• v ms% -./
^v .v sgfrs •. w ss
* * -. St
VVsw.s ^s ^\^.ss ^ s\ ss
A-AxAA S
MONITORING GUIDANCE FOR THE
NATIONAL ESTUARY PROGRAM

Final
Office of Water
Office of Wetlands, Oceans, and Watersheds
Oceans and Coastal Protection Division
U.S. Environmental Protection Agency
Washington, D.C. 20460
September 1992
-------
-------