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PU82-265471
Region f?l library
Bwfranmental Protection flgen$rlc.iL acvtew of Water Quality and
Dita fro:s Chesapeake Say with Eraphvsis
^^ on Effects of Enrichment
by
•Donald R. Heinle1
m Christopher F. O'Elia
Jay L. TaftZ
-John S. Wilson * '
I Marthe Cole-Jones
Aiica 8. Caplins?
T. - F11 « rt t * -a f' f -\ n i n *^
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I
L,. Eugcna Cronin"1
University of Maryland
Center for Environmental and Estuarine Studies
Chesapeake Biological Laboratory
Soloraons, Maryland 20688
^Present Address: O12M Hill, 1500 114t!l Avenue S.E., Bellevue, Washington
98004
I^The Johns Hopkins University, Chesapeake Bay Institute, Baltimore, Maryland
21218
•^Present Address: Spe-ry Univac Corporation, Route 4, Box 424V, Great Mills
Road, Lexington Par'*;, Maryland 20653
""Chesapeake Research Consortium, Inc., 1419 Forcit Drive. Suite 207,
Annapolis, Maryland 21403
Grant )?R306189010
Project Officer
Thomas Pheiffer
U.S. Environmental Protection Agency
Chesaneake Bay Program '
2083 West Street . •
Annapolis, Maryland 21401
Chesapeake Research Consortium, Inc. Publication No. S4.
1980
UMCEES Ref. No. 80-15CBL
NATIONAL TECHNICAL
INFORMATION SERVICE
US MrM'JIlKI Or CCHtlOCE
EPA Report Collection
Information Resource Center
US EPA Region 3
Philadelphia, PA 19107
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TECHNICAL REPORT DATA
S ACCESS'::••*
F.PA 600/3-82-083
September, 1982
Historical Review of Water Quality & Climatic Data
from Chesapeake Bay with Enphasiu on Lfleets of
Enrichment
OHGAiNiZAT IN CCC'C
Donals^R. Heinle, Christopher F. D'Elia, Jay L. Taft,
John S. Wilson, Marthe Cole-Jones, Alice B. Caplins, | CBP-TR-002E
1^)-, -fefl on % C.r o n i ij r
3 PERFORM l rjGO^GA.MZAT'»,N S S P D K -
NAME A.\,C A33SSSS
hO PROGRAM ELEMENT MO.
University of Maryland, Center for Environmental &
Estuarine Studies, Chesapeake biological Laboratory,
Solomons, Maryland 20688
111. CONTHACT/G3ANT .\C
R806189010
2. SfCNaQSING AGcNC'' NAMii A.MC ACO=
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>^/> ' 1~oA V
«^,v_ - "*~>°<'4C
f-^^^i^^ T&-- —S."1-; 3"<:
J ^-^^y^ iT^V^
• •• . ^-^"Y*^
Frontispiece. The Chesapeake Bay and its major tributaries.
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TABLE OP CONTENTS
Summary
Introduction 2
Chapter A, Climatic Variation 4
Chapter B, Nutrient Inputs 14
Current Inputs ^
Historical Trends 20
Pesticides 26
Chapter C, Historical Changes in Water QuaUty 31
introduction 31
Methods, Comparability, and Liraits of Detection 32
Quality assurance and the historical data record 32
Analytical Methods 33
Chronology of coloriraetric detection device use 38
Upper Chesapeake Bay 3d
Middle Chesapeake Bay 45
Lower Chesapeake Bay 56
Chop tank., Chester and "liles Rivers 53
Ma^ot'iy, Severn and South Rivers 61
Patuxent River 62
Potoraac River 81
James River 84
Other Tributaries of the Bay 91
Suanary of Water Quality 93
Chapter D, Comnerclal Fishery Production 99
Chapter E, Current Status of Chesapeake Bay with Respect to Enrichment 10^
References 115
Appendix A, Accessing Environmental Data Base Directory Cli-nalic Data 129
Appendix B, Environmental Data Base Directory 132
Appendix C, Fisheries catch data documentation 221
Appendix D, Unpublished manuscript "Clinalic Factors Influencing Commercial
Seafood Landings in Maryland" by Ulanowicz, tt al. 223
in
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SUMMARY
Review of the available data on water quality iiv Chesapeake Bay ha?
revealed changes over recent decades caused by enrichment with nutrients. In
the upper and middle Bay, and several tributaries, concentrations of algae
present during the summer months have increased since the raid 1960's. There
have been decreases in the clarity of the water associated with increased
algal stocks. Nutrient concentrations have also increased, phosphorus .nore
notably so than nitrogen. In some of the tributaries, such as the Patvxent
for which we have the most historically complete data, increased algal
production has led to reduced concentrations of oxygen below the halocline in
the middle part of the estuary. The variations in concentration of oxygen
are now more extreme in surface waters than in the early 1950's in the
Patuxent. Oxygen concentrations in th-j open Bay have not changed greatly,
with the possible exception of extreme conditions, as during periods of
extensive ice cover.
There have been historical variations in the abundance of comaercial
fishery stocks that are closely related to climatic variations. Since 1969
or 1970, however, stocks of many anadrotnous species and marine spawners
repre=. iting higher trophic levels have declined to new long-time lows. The
principal exceptions are menhaden (marine-spawning planktivorous fish) and
bluefish (marine spawning top predators). That name tine interval has,
however, been a period of above average rainfall and corresponding reduced
salinities in the Bay, making conclusions concerning effects of enrichment
difficult to achieve.
Thera Is evidence for progression of the effects of enrichment down the
Bay with time. Increased inputs of nutrients may ultimately lead to major
changes in the lower Bay, similar to those already observed in the
tributaries and upper and middle Bay.
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INTRODUCTION
There has been growing concern in recent years over the effects c>f
excessive enrichment of coastal waters. That concern has led to at least
three workshops at the national Ivvel (Glendening aid Curl. 1978; Curl, et
al., 1978; Goldberg, 1930) in which processes and effects of excessive
enrichment have been discussed, r.rid general research and uonitoring needs
have been recommended. Concern for effects of enrichment has not been
restricted to the United States. Excessive enrichment is considered a threat
to some parti of the Mediterranean Sea (United Nations Environnent Programme,
1977) and several other coastal areas around the world (Curl, et al., 1978).
The first conrerns about sewage enrichment in Chesapeake Bay noted in
the literature focused on the health hazards of untreated or primary treated
sewage (Cunning, 1916; Cubing, Purdy and Ritter, 1916). In the early 1900's
outbreaks of typhoid fever were relatively corauon, often as a result of
contact with, or drinking of, contaminated water, and sometimes from eating
shellfish (Cunning, 1916; Gumming, et al. 1916). Nonetheless, the biological
oxygen demand of untreated or partially treated sewage was recognized to
decrease concentrations of oxygen in heavily polluted areas such as the upper
Potomac River (CuiMr.ng, et al., 1916) and Baltimore Harbor (Gumming, 1916).
With the development of sewerage in urban areas and as the use of
secondary treatment increased, it became apparent that the ultimate oxygen
demand caused by decaying algae which bloomed as a result of increased
nutrients in the water could be as great as the direct oxygen demand of
untreated sewage (Wolman and Geyer, 1957; Jaworski, Lear and Villa, 1971,,
1972). It has be^n estimated that the decomposition of the algae represented
by a chlorophyll concentration of 100 ug 1~1 would require about 12 mg 1~1 of
dissolved oxygen, varying sonewhat depending on the amount of refractory
organic matter (Bain, 1967; Jewell and McCarty, 1968).
Stimulated production of algae is often accompanied by other changes
which are less direct. Changes in species composition may result. In waters
of low salinity, nitrogen-fixing blue-green algae often become the most
abundant forms, to the detriment of higher aquatic organisms and other algae.
Blue-green, algae also can produce conditions considered offensive to humans,
such as fouled beaches and noxious odors. blue-green algae were observed in
the upper Potomac estuary as early as 191.J (Cumraings, et al., 1916), but did
not become a serious nusiance until the middle to late 1960"s (Jaworski, et
al., 1971, 1972). Problem quantities of blue-grean algae were noted in
tributaries to the upper Bay during 1. 70 and 1971 coincident with increases
in the concentrations of nutrients in the same area (Clark, Donnelley and
Villa, 1973).
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Although a number of studies have reviewed Che general effects of
increased production of algae in Chesapeake Bay (e.g., Roberts, et al.,
1975), the extent of the changes in parameters of water quality that have
occurred have not been fully documented. It has thus been difficult to
assess the effects of excessive enrichment on the biota and human uses of the
Bay. In this report we atterupt to document nutrient-related changes that
have occurred in Chesapeake Bay that appear to be related to cultural events,
particularly enrichment by the major nutrients in sewage, nitrogen and
phosphorus.
Inasmuch as the period of some variations in climate, approximately 20
years (Mock and Hibler, 1976; Hibler and Johnson, 1979), is similar to the
duration of the events contributing most to excessive enrichment, the effects
of climate are also considered in this report. In addition, a review of the
extensive documentation of one major storm, tropical storm "Agnes" in 1972,
suggested that short-term (1-2 yr) effects of unusual climatic events are
similar in nany ways to the longer-terra effects of excessive enrichment.
Thus, major storns and annual variations in climate must also be taken into
consideration in interpreting the less cyclic effects of enrichment.
This report is written in several chapters, reflecting not only the
division of labor among the contributors and the topicality of reports
intended for later publication in the refereed literature, but also the
contractual arrangement with E.P.A. agreed to in the scope of the work for
this project. The primary purpose of this report is to describe and document
historical changes that have occurred in Chesapeake Bay. It will contribute
information useful to E.P.A. in compiling the "state of the Bay" report at
the eud of the Chesapeake Bay Program. Related papers that were also
produced as part of the same Chesapeake Research Consortium project and which
complement this report are those by Webb (1980) and Neilson (1980). Webb
discussed the process of eutrophication, and provided conceptual models of
trophic relationships at different levels of enrichment. Neilson discussed
effects of enrichment on ecosystem health. This paper is part of the series
of products of Grant No. R806189010 from the Chesapeake Bay Program of the
U.S. Environmental Protection Agency to the Chesapeake Research Consortium,
Inc. That support and the interest and continued assistance of the staff of
the Program are acknowledged with appreciation.
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CHAPTER A.
CLIMATIC VARIATION
Two major climatic variables have the greatest physical effect on
Chesapeake Say. These are temperature and rainfall, the latter affecting
freshwater flows. A special climatic feature, the tropical storm, sometimes
produces unusual floods. Such storas have catastrophic effects on the biota
of the Bay, some of which are discussed below.
Recent analyses have shown that spatfall of the American oyster,
Crassostrea virginica, is a major determinant of eventual commercial catch
and is closely related to a number of climatic variables (Ulanowicz, Caplins,
and Dunnington, 1980). Commercial catches of striped bass also appear to
vary in a way correlated with climate (Merriman, 1941; Heinle, Fiercer, and
Ustach, 1977). As the amount of variation in catzch that is accounted for by
climatic factors is large (Ulanowicz, Caplins, and Dunnington, 1980), those
factors must be considered in the interpretation later in this report of the
effects of enrichment on Bay biota, particularly those species whose
population size is highly dependent on year-to-year variations in
recruitment.
There is growing evidfince of cyclic variations in global climate that
are closely related to the frequency of solar flares (sun spots) (Mock and
Hibler, 1976; Hibler and Johnson, 1979). The period of the solar cycle
(approximately ?0 yr) appears to be reflected in regional climate (Ulanowicz,
Caplins, and Duanington, 1930). A cycle of about 20 yr seems also to be
present in deviations from average winter air temperatures (Fig. A-l). While
there are exceptions, clearly a cluster of colder than normal winters between
1961 and 1971 was preceeded by a somewhat longer period when winters were
milder than normal (Fig. A-l). Annual mean Bay water temperatures have also
fluctuated in a periodic fashion as shown by Schubel (1972) (Fig. A-2) for a
slightly different time period than that shown in Figure A-l. The data
compiled by Schubel suggest a cycle of approximately 18 to 20 yr imposed on a
longer-term general rise in temperatures in Baltimore Harbor. There are also
cycles with shorter periods. Figure A-3 shows the mean water temperatures
for 1939 through 1977. Extremely cold winters occurred with a frequency of 6
to 8 yr.
Freshwater flow has many effects on the Bay ecosystem (see review by
Snedekar et al., 1977), including effects on nutrient inputs and ration. The
input of nutrients to the Bay is to a large extent proportional to freshwater
flow, and the ratios of nitrogen to phosphorus also are affected (Guide and
Villa, 1972). Ratios of nitrogen to phosphorus in the input also vary
significantly fiom tributary to tributary (Jaworski, 1980). Figures V-18
through V-23 of Guide and Villa (1972) show the excellent linear relationship
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between the logarithm of flow and the logarithm of input of nutrients to the
head of Chesapeake Bay.
There is no apparent cycle in the variations in freshwater flow to the
Bay (Table A-l). The highest annual mean flow shown in Table A-l, for 1972,
was above normal because of tropical storra "Agnes."
Average flows during some years are greatly enhanced by exceptional
storms such as hurricanes (e.g., 1972 in Table A-l). Truitt (1968) reviewed
Table A-l. Annual mean freshwater flows to all of Chesapeake Bay (cubic feet
per second) for 1951-1979.
Bay Annual
Year Average
1951 82,100
1952 94,300
1953 72,800
1954 58,700
1955 73,400
1956 76,000
1957 64,400
1958 81,400
1959 66,400
1960 77,300
1961 78,000
1962 64,800
J963 52,400
1964 61,900
1965 49,000
1966 53,300
1967 77,200
1968 60,100
1969 54,900
1970 77,200
1971 79,000
1972 131,800
1973 95,200
1974 76,900
1975 103,100
1976 84,400
1977 80,100
1978 91,300
1979 113,800
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™£^ -
Che aajor storms affecting Chesapeake Bay and the coastal areas of .'laryland
and Virginia through between 1649 and 1967. Those major storms and two
additional hurricanes are suamarlzed in Table A-2. S>a.e of the reported
hurricanes did not cause heavy rains throughout the region, or Truitt (1963)
in some cases did not sent Ion rainfall. Those that are known to have caused
flooding are noted in Table A-2.
Table A-?. Major recorded storms and hurricanes between 1649 and 1979
(1649-196^ from Truitt, 1963) affecting Chesapeake Say and coastal Maryland
and Virginia. Storms recorded by Truitt which apparently did not seriously
affect Chesapeake Bay were excluded.
Year Type of Scorn Heavy
1649 Extratropical ?
1667 Hurricane ?
1894 Hurricane ?
1904 Hurricane ?
1911 Hurricane ?
1912 Hurricane ?
1933 Hurricane ?
1936 Hurricane Yes
1954 Hurricane Yes
1955 2 Hurricanes Yes
1972 Hurricane Yes
1979 Hurricane Yes
Seller tributary watersheds ire subjected to storms affecting river
flows nore frequently than in the Chesapeake Bay basin as a whole. Scorns
affecting the Patuxent River watershed were summarized by the Philadelphia
Academy of Natural Sciences, Benedict Estuariue Laboratory, and provided for
our use. ineir sunraary is shown in Table A-3 including measured rainfall at
Prince Frederick, Maryland, and sometimes at Solomons. Variations in the
intensity of storns within the Patuxent basin are shown by the three storms
listed for 1969 (Table A-3). Precipitation at a single location does noc
fully predict the hydrograph for a tributary. For example, there was a very
large peak in runoff during September of 1968 in the Patuxent (Fiercer, et
al., 1970) which was not preceded by abnormally heavy rainfall at Prince
FrtaericK. (Table A-3). Since most najor tributaries are now gauged, detailed
records of freshwater flow exist and can be u^ed to calculate nutrient inputs
(e.g., see Guide and Villa, 1972 or Jaworski, 1980).
The salinity of Chesapeake Bay at a fixed point provides a good
integration of short-term variations in freshwater flow and tnas a smoothed
indication of long-term trends. Figure A-4 shows nie.in surface, extrene high
and extreiae j.ow salinities at Solomons, Maryland using data from our data
base (Appentix A). Note that the variability of salinity is somewhat greater
from about 1960 onward than prior to that tine. The 1960's were
characterized by relatively high salinities while the 197u's have been
characterized by relatively low salinities, reflecting the trends in
freshwater flows (Table A-l).
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Table A-3. .Hajor storas in the Pacuxent Xiver ciasin (Prince Frederick Data)
Coartesy of the Philadelphia Academy of Matural Sciences.
1961
1962
1963
1966
19o7
1964
1969
1970
1971
1972
1973
1974
1975
14 July
10 N'ovcaber
29 Mjy
3 June
16 September
20 Septenber
19 Octt.oer
February snow
13 June
12 N'oveaber
12 July
23 July
20 August
20 August
14 April
25 May
16 .lay
4 August
10 Octooer
25 N'ovenber
22 June
2 September
14 N'ove;nber
2 February
9 Oeceraoer
30 March
4 September
26 June
13 July
23 Septenber
2.40
2.00
2.94
2.94
2.43
2.30
3.86
totalling 17
1.43
2./4
1.86
11.85
2.24
5.13
1.39
1.83
2.75
2.95
2.73
2.05
3.20
1.45
1.68
1.90
1.93
2.20
2.74
1.93
2.90
2.05
1 no lies
. 5 inches
greatest one-day
precipitation
(Prince Frederick)
( Solonaon's)
(Prince Frederick)
( Soioraon's)
Tropical Storn Agues
Tropical Storni Carrie
1976
1977
16
14 October
2.87
2.31
10
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21
19
17
to
§
of 10
UJ
CL 8
ANNUAL EXTREME WGH SALINITY
I I 1 L
CD
O
5
*»—i,
O
g 16
3 14
12
10 I-
ANNUAL EXTREME LOW SALINITY
I | | I
ANNUAL MEAN SALINITY
I93O I94O 1950 I960 I97O 1980
YEAR
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Figure A—4. Annual extreme high salinity at Solomons, Md. (upper panel);
annual extreme low salinity (middle panel); and annual mean salinity (lower
panel) from 1937 to 1976.
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Some of the effects of major stornn on Chesapeake Bay are similar to
those of chronic excessive enrichment (discussed in Chapter C). The effects
of one tropical storm, "Agnes," in 1972 have been extensively documented
(Chesapeake Research Consortium, 1977). That stora, which deposited in
excess of 10 inches of rainfall in many parts of the Bay watershed (Astling,
1977), caused apparent increases in heterntrophic activity within parts (and
presumably much) of the Bay (Zubkoff and Warinner, 1977; Fleuier, Ulanowica,
and Taylor, 1977). The large flows of freshwater reduced concentrations of
phytoplankton In the upper Patuxent (Fleraer, et al., 1977) but caused
increases in phytoplankton concentration down-raver by displacement or
stimulation of growth (Zubkoff and Warrlner, 1977). Concentrations of
nitrogen were increased in the lower Bay while concentrations of phosphorus
were unaffected (Smith, Maclntyre, Lake and Windsor, 1977). In the upper
Bay, the various forms of nitrogen increased, nitrate and nitrite being from
2 to 3 times above normal, whereas, in the lower Bay, concentrations of
phosphorus were not affected (Schubel, Taylor, Grant, Cronin and Glendening,
1977). The crops of phytoplankton produced by the influx of nutrients
(Flemei, et al., 1977; Zubkoff and Warriner, 1977) appear to have been
moderated by the shading effect of tb° large aeounts of sediment brought into
the Bay by the storm.
Concentrations of dissolved oxygen were lower after the storm in the
bottom waters of some tributaries, presumably a consequence of increased
heterotrophic activity and enhanced vertical stratification of the water
column as a result of high flows (Flemer, et al., 1977; Hyer and Ruzecki,
1977). In the main stem of Chesapeake Bay, where concentrations of oxygen
are naturally low during the summer months (Newcombe and Home, 1938), the
concentrations of dissolved oxygen following "Agnes" were not demonstrably
lower (Schubel and Cronin, 1977). Fiercer et al. (1977) noted that a storm in
August of 1969 (Table A-3) carried an amount of sediment to the Patuxent
similar to that brought in by "Agnes." Tributaries to the Bay may well
suffer the effects of extreme climatic events much more frequently and
severely than the main stem of the Bay (c.f. Tables A-2 and A-3).
The full set of climatic data used in our analyses is available through
the University of Maryland computer system. A listing of the variables used
is shown in Table A-4. Documentation of programs for retrieval of the
climatic data are in Appendix A of this report.
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Table A-4. Climatic data.
A Annual Average Salinity
B Annual Average Water Temperature
C Annual Average Air Temperature
D Annual Average Precipitation
E Annual Cumulative Excesses Salinity
F Annual Cumulative Excesses Water Temperature
G Annual Cumulative Excesses Air Temperature
H Annual Cumulative Excesses Precipitation
I Annual Cumulative Deficits Salinity
J Annual Cumulative Deficits Water Temperature
K Annual Cumulative Deficits Air Temperature
L Annual Extreme Values Silinity +
M Annual Extreme Values Salinity -
N Annual Extreme Values Water Temperature +
0 Annual Extreme Values Water Temperature -
P Annual Extreme Values Air Temperature +
Q Annual Extreme Values Air Temperature -
R Annual Extreme Values Precipitation +
S Annual Episodes Salinity +
T Annual Episodes Salinity -
U Annual Episodes Water Temperature +
V Annual Episodes Water Temperature -
W Annual Episodes Air Temperature +
X Annual Episodes Air Temperature -
Y Annual Episodes Precipitation +
Z Annual Episodes Precipitation -
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CHAPTER B
NUTRIENT INPUTS
CURRENT INPUTS
There are three categories of sources of major nutrients (nitrogen and
phosphorus) Co Chesapeake Bay. These are (I) natural non-point sources from
native ecosystems—forests and marshes, (2) non-point sources from perturbed
ecosysttjns such as agricultural land and developed areas, and (3) point
sources, predominantly sewage treatment plants, but also including industrial
sources. Detailed compilations of all of these sources have never been made,
and were beyond the scope of this project. Jaworski (1980) did, however,
estimate total nutrient loadings to Chesapeake Say for the period 1969 to
1971 from a variety of sources including direct measurements of flows and
concentrations and previously established statistical relationships (e.g.,
see Guide and Villa, 1972). Loadings for earlier and later periods were
estimated for the P.ituxent, Potomac and all of Chesapeake Bay including
tributaries. A suramary of Jaworski's (1930) calculations is shown in
Table B-l, which reproduces his Table XII. Jaworski considered direct
municipal and industrial discharges, atmospheric sources, and contributions
from the upper basins of the Susquehanna River and other tributsries of the
fay. Point discharges above the fall line of the Susquehanna and tributaries
to the Bay were not distinguished trom non-point sources. The relative
contributions from direct discharges to tidewater and from upland sources ere
shown in Table B-2 [after Jaworski's (1980) Table V].
Brush (1974) summarized all of the sewage discharges in the Chesapeake
Bay basin during 1973. His summary was based on actual flows in most cases
or design flows, in unspecified instances from operating records or NPDES
permits, and included industrial discharges "where knowr.," presumably from
NPDES permits. Municipal discharges above the fall line of t.he Susquehanna
and other major tributaries were totalled and listed as a single point source
at the fall line. Treated sewage constituted about 2.7 percent of the total
freshwater flow to Chesapeake Bay, based on the data of Bru; h (1974) and the
27-year average flows calculated from streamflow data of the U.S. Geological
Survey (Table B-3). The percentage in three tributaries in which some
problems have been caused by enrichment was higher, up to 4.8 percent in the
Potomac (Table B-3).
The summary by Brush (1974) of the upland point sources allows the
calculation of maximum nutrient inputs from sewage and industry for
comparison with the total inputs calculated by Jaworski (1980). If we assu.ne
that secondary treatment is applied at all discharges, concentrations from
the literature, specifically those calculated from the data of Jaworski, et
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Table B-i. External nutrient loading for Chesapeake Bay
(1969-19/1) (from Jaworski, 1980).
Water rfody
1. PaCuxent
2. York
3. rUppauannock
4. James
5. Potomac
6. Chesapeake Bay
(Including Tribs)
(Excluding Tribs)
Ecological Surface Volume
Description Area
(10&) (106)
Eutrophic 137 660
N'on-eutrophic 210 910
N'on-eutropnic 400 1,780
Eutrophic 600 2,400
Hyper-
eutrophic 1,230 7,150
Localized
eutrophic 11,500 74,000
conditions 6,500 52,000
External Phosphorus External ;\itro
Loading
(g/yr) (g/m2/yr)
(10b)
1. 230 1.82
2. 160 0.76
3. 180 0.45
4. 1,780 2.70
5. 5,380 4.30
6. 15,100 1.30
7,350 1.10
Loading
(g/m3/yr) (g/yr) (g/m^/yr)
Ul)6>
0.38 750 5.8
0.18 1,190 5.6
0.10 1,500 3.8
0.70 10,300 15.6
0.80 25,200 20.2
0.20 109,100 9.5
0.10 70,160 10.8
15
and its estua/ies
Average Average
Depth Retention
Time
(n) (yr)
4.8 J.70
4.3 0.72
4.5 1.27
3.6 0.39
5.8 1.07
6.5 1.16
8.4 1.32
gen Atomic i\/P
Ratio of
Loading
(g/nVyr)
1.4 7
1.3 17
0.8 19
4.2 13
3.5 11
1.5 16
1.3 22
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Table B-2. Annual nutrient budget - Chesapeake Bay (1971) (froa Jaworski,
1980).
Source Phosphorus Nitrogen
(kg/day) (kg/day)
Entire Chesapeake Bay
Including Estuaries
Municipal/Industrial 28,700 87,700
Upper Basin Land Runoff 10,200 195,400
Air 2,500 14.800
Total 41,400 297,900
Chesapeake Bay Proper
Excluding Estuaries
Municipal/Industrial 16,900 45,900
Upper Basin Land Runoff 5,200 131,500
Air 1,400 8,200
Total 23,500 185,600
Table B-3. Twenty-seven year average freshwater flow from data of the
U. S. Geological Survey annual summaries of stream flow entering Chesapeake
Bay (December, 1951-1976); point sources of sewage (from Brush, 1974) and
calculated percent of annual flow that is sewage.
27-yr average Point Sources Percent of freshwater
River flow (cfs) of sewage (cfs) that is sewage
Susquehanna 38,800 557 1.4
Patuxent 1.0851 41.15 3.8
Potomac 13,900 670 4.8
James 10,100 302 3.0
Cnesapeake Bay 75,200 2,034 2.7
Patuxent flov/s were taken from the Johns Hopkins University (1966)
rather than the U.S. Geological Service data.
16
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• al . (1971) for Che Washington, D.C. area, can be used to estimate total'
loadings. From Table IV-I of Jaworski, et al. (1971) we find that a
discharge of 325.6 mgd in the Washington area resulted in loadings of 24,022
_ Ib day~l_of total phosphorus and 59,456 Ib day"1 of total nitrogen (TKN +
I N0;j 4- N02). We calculate 73.8 Ib day"1 of phosphorus and 18?..6 Ib day"1 c
« nitroaen oer 1 roed of secondary treated sewage. Using the flows tabulated
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of
nitrogen per 1 rogd of secondary treated sew.ige. Using the flows tabulated by
Brush (1974) (totals to the mouths of tributaries) and the conversion factors
abo/e calculated from the data of Jaworski, et al. (1971) we calculated the
amounts of nitrogen and phosphorus entei^ng the Bay from point sources
(Table B-4). Table B-4 shows those quantities in kg day"1 and in 10& g yr"1
Table B-4. Contributions of nitrogen and phosphorus from point source loadings
in the Chesapeake Bay basin calculated from the flows determined by Brush
(1974) using the conversion factors described in the text.
Nitrogen Phosphorus
River Kg day"1 106g yr"1 Kg day"1 106g yr"1
Susquehanna 28,841 10,527 12,061 4,402
Patuxent 2,203 804 890 325
Potomac 38,864 14,185 14,495 5,290
Rappahannock 795 290 321 117
York 323 118 131 48
James 16,151 5,895 6,528 2,383
Chesapeake Say
(including 108,916 39,754 44,020 16,067
tributaries)
for comparison with the totals of Jaworski (1980) (Table B-l). There are
some discrepancies between our calculations (Table B-4) and those of Jaworski
(Table B-l). Our estimates of loadings of both nitrogen and phosphorus were
higher than Jaworski's (1980) estimates for both the Patuxent and James
Rivers. It is possible that lossas through deposition of phosphorus and
denitrifIcation of nitrogen from point sources in the upper watershed exceed
the total non—point contribution, but that seems unlikely. For the Potomac,
Rappahannock and York Rivers, we calculated lower loadings from point sources
(Table B-4) than Jaworski found for total loadings (Table B-l). The
estimated amounts of phosphorus were nearly identical in both cases, but
there is evidence for loss of phosphorus in the riverine portions of
tributaries (Kemp and Boyntori, pers. comm.; Table B-5). For Chebapeake Bay
including tributaries we calculated that slightly less nitrogen and slightly
more phosphorus came from point sources (Table B-4) than Jaworski estimated
for total loadings (Table B-l). Our estimates of point source contributions
17
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(Table 3-4) wec
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general lower ttian our estimates for percent nitrogen from non-point upland
sources for the major tributaries (except the James) (Table 8-5) suggest that
we are in the correct range. The apparent discrepancy between our estimated
minimum non-point contributions of phosphorus from the Susquehanna and James
Rivers (Table B-5) and the Bay-wide estimates of Correll are not encouraging.
Correll (1976) also used the sewage flows reported by Brush (1974) and an
assumption of conservation of nutrients in his calculations.
If denitrification occurred in the upper basins, a possibility suggested
by recent work in the estuarine part of the Potoraac (Kaplan, et al. , 1978;
McElroy, et al., 1978; Elkins, Kofsy and McF.lroy, 1980), our calculations of
percentage nitrogen fro'a non-point sources could be in error. It appears
that direct measurement of inputs to the Bay are necessary for the accurate
assessment of the relative importance of point and non-point sources.
HISTORICAL TRENDS
Periodic compilations of total discharge or nutrient loadings to
Chesapeake Bay do not exist. There are, however, reviews for particular
watersheds thac indicate trends. Reviews of the type reported by Brush
(1974) of total discharge are possible for any tins period after
implementation of the N'PUES permit system. Records available at various
state offices should allow the compilation of discharge trends from about
1970 onwards. Such periodic reviews are strongly recommended in the future
and would be a useful part of future monitoring efforts.
Many of the changes that occurred in Chespeake Bay, and more
particularly in the tributaries, preceded the NPDSS system and loading trends
must be inferred frora more intensively studied watersneds such as the Potomac
and Patuxent and from changes in population, land use, and cultural
practices. Jawcrski, Clark and Feigner (1972) calculated loadings from point
sources of nitrogen, phosphorus and carbon to the Potomac River for 1913 to
1970. A recent modification of their Figure 3 is presented here (Figure
B-l). The phosphorus loadings used by Jaworski, et al. (1972) are nearly
identical to the total loadings given by Jaworski (1980, Table XII) for the
same time period (our Table B-l), however, the total estimates of nitrogen
input are considerably higher, 69,041 kg "jy"1 in Table B-l (the 1980
estimate of total loadings) versus approximately 23,000 kg day"* in Figure
B-l (the 1972 estimate of loadings from point sources). The overall trend
for nutrient loading is clearly upward with time, except for the recent
decrease in phosphorus loading apparent in Figure 3-1.
Two additional cultural events are documented in Figure B-l. There is a
more rapid increase in phosphorus loadings relative to those of nitrogen from
about 1955 onward, which is probably due to the use of phosphorus compounds
in detergents. The second apparent feature is the reduction in discharges
of carbon between 1960 snd 1969 that were accomplished by the implementation
of secondary treatment during that period (Anon., 1969a). .As documented by
Anon. (196°") and by Jaworski, et al. (1972), advances in treatment
capability resulting in reduced carbon (B.O.D.) loadings have, with time,
been consistently overcome by continuing growth of the contributing
population. As nitrogen concentration is only sligntly reduced by secondary
20
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versus primary treatment, there nave been no dramatic reductions in the
discharges of that nutrient (Figure K-l).
Population has been increasing throughout the Chesapeake Bay basin,
although at different rates in different localities. The lower Susquelonna
River basin experienced a population increase of about 10 percent between
1960 and 1970 while the entire State of Pennsylvania increased by 4.2 percent
(Anon., 1975). By contrast the population of the Patuxent River basin
roughly doubled during the same period, goir.g from 134,000 in 1960 to 260,000
in 1970 (Mihursky and Boynton, 1978). During approximately the same
interval, the discharges of sewage to the Patuxent River have increased aoout
ten-fold; from 2.6 mgd in 1963 (Anon., 1974) to 26.6 ngd in 1973 (Brush,
1974), with intermediate flows of about 11 ingd in 1967 (Anon., 1969b).
Sewage discharges tiius grew at a more rapid race than population during the
1960's. That largely reflects the advent of sewerage in some areas, and
subsequent increases are more likely to be snore directly proportional to
population growth.
While discharges of nutrients from point sources can be estimated for
previous periods from population size and known changes in treatment levels
(e.g., Figure 8-1), non-point contributions are not so easily calculated. We
can be fairly certain that some increase occurs in non-point contributions of
nutrients as a result of growth in population because areal yields are in
general higner for urban and suburban land than for agricultural and forested
areas (Correll, Pierce and Faust, 1975; Correll, 1976). Table B-6 shows the
percent of major land uses in tne Chesapeake Bay basin and the percentages of
total non-point contributions of nitrogen and phosphorus fron those areas.
Although residential areas comprise only 10 percent of the area, they
contribute 40 percent of the nitrogen and 53 percent of the phosphorus from
non-point sources. By contrast, the largest land-use category, forest arid
brushland, which coastuutes 52.5 of tae total area, contributes only
8.9 percent of the nitrogen and 12.6 percent of the phosphorus front non-point
Table B-6. Percentages of nitrogeu and phosphorus contributed froa various
Jand-iise types [based on annual averages of Correll's (1976) seasonal
contributions] (non-point sources only) and the percentage of each land use
in the Chesapeake Bay basin (from Correll, 1976). Open water and freshwater'
wet areas were not included.
Nitrogen Phosphorus
Percent of Percent of total Percent of total
Lafd use basin area non-point sources non-point sources
Forest and bru-,hland 52.5
Cultivated cropland 24.0
Pastureland 13.0
Residential areas 10.0
8.9
38.0
17.4
40.4
12.6
19.3
13.4
53.0
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sources. Pastureland and cultivated cropland are intermediate; contributing
phosphorus in approximate proportion to their area and contributing nitrogen
at a higher proportion than their area. Urbanization at the expense of
forest, pasture or cropland wou.'.d lead to increases in non-point
contributions of both nitrogen and phosphorus.
Urban and "other" land uses appear to be increasing in the Susquehanna
River basin at the expense of cropland and pastureland (Table B-7). The
greatest increase predicted by the U.S. Department of Agriculture (Anon.,
1969") was in the "ocher" category: an unfortunate grojping of highways
undeveloped urban fringes (brushland and woodland?), recreational areas
(parks?), and "public institutions" (prisons to military reservations?).
During the same period, urban land was projected to increase only from 4.2 to
3.5 percent of the total land area (Table B-7).
Table B-7. Land use in the Susquehanna River basin in 1964 and projected for
19d5 by the U.S. Department of Agriculture (Anon., 1969c).
Percent of total land
Land Use
Cropland
Pastureland
Forest land
Urban
Qtner
Another indication of trends in the Susquehanna basin can be obtained
froa Figure B-2, adapted in part from tne cover of the 1973 Crop and
Livestock Annual Summary for Pennsylvania (Anon., 1973), and froa Mihursky
and rfoynton (1978). Figure B-2 shows that in both the State of Pennsylvania,
of which the Susquehanna basin occupies about one-half, and the nuch smaller
Patuxent basin, the amounts of agricultural lands are decreasing. In the
Patuxent, urban areas are growing rapidly in contrast to the Susquehanni
basin (Table B-6).
The decrease in agricultural lands does not necessarily mean that
non-point contributions of nutrients from agriculture are decreasing. The
diminished agricultural ireas are apparently receiving larger amounts of
che-nical fertilizers than were applied to larger areas in the past, and
suburban lawns are often fertilised in excess. Figure B-3 shows the amounts
of chemical fertilizer sold at selected tines in Pennsylvania and Maryland
(adapted from Hargett and Berry, 1978). All data are expressed as tons
(English) of ea^a major nutrient. Data for Virginia -ire similar to those for
23
1964
23.9
9.5
55.6
4.2
f>.8
1985
12.5
6.7
57.4
5.5
18.0
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PLANT NUTRIENT CONSUMPTION
Q
z
<
(/)
o
225
150
75
-TOTAL NUTRIENTS
-P205
-K2O
PENNSYLVANIA
1955
I960
1965
1970
1075
1978
—TOTAL NUTRIENTS
— P205
— K2O
O
O
Z
§
200
120
40
1955
I960
1965
1970
1975
1978
Figure B-3. Sales of fertilizer in Pennsylvania and Maryland during selected
years ( f ro
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Pennsylvania, even to scale, and are therefore not shown. The increases in
use of some particular forms of fertilizers have been even more dramatic,
particularly nitrogen solutions in Maryland (Fig. I}-':) and Virginia (patterns
similar to Maryland, except for scale) and of nitrogen solutions and urea in
Pennsylvania (Fig. a-4). The dita in Fig. B-4 are unfortunately expressed as
total tons of Material sold (i.e., not norn.-ilized to total nitrogen as in
Fig. 8-3).
Increased application of fertilizer (Kigs. 3-3 and B-4) to diminished
land areas (Fig. B-2) does not necessarily mean increased contribution of
nutrients in runoff. Phosphorus yields from agricultural lands are closely
related to erosion, so the increased use of minimum-tillage procedures should
reduce non-point contributions of phosphorus. It has been reported outside
t'ne literature that approximately 80 percent of the nitrogen applied to test
plots of corn in Maryland over a three-year period was recovered in the crops
and soil under either no-till or conventional tillage procedures (Bandel,
pers. cona.). Uith plowint;, the nitrogen wis distributed deeper in the soil
profile, reflecting the physical disturbance. Correil, Wu, Friebale and
Miklis (1977) reported 39 percent of added nitrogen as agricultural output
froia pastu-e and hay land and 61 percent as agricultural output from
cropland. They also indicated either net gains in nitrogei or losses to the
atnospnere in their study area. in an experimental sewage disposal system at
Cape Cod, Massachusetts, aoproximately <*0 percent of tne nitrogen applied as
sewage was recovered in forage crops (Deese', Vaccaro, Ketchum, Eowker and
Dennett, 1977). Crop yield was directly proportional to application rates of
up to 7.5 cm per week, suggasLing a high affinity for nitrogen by plants in
nitrogen-linited terrestial
Taere is one encouraging aspect to the relatively high yields of
nutrients irou non-point sources in residential and urban areas (T.ible B-5).
Collection aac! treatment of runoff fron those areas is considerably nore
feasible than froa natural or agricultural areas. Hie high recovery rates of
nitrogen froa agricultural crops and soils is also encouraging, indicating
that wicn appropriate fanning practices, nutrient losses can be .Tiinimized.
These benefits must be balanced agiinst the potential hazards of herbicides
to aquatic ecosystems.
PESTICIDES
The reductions in nutrients losses and consunption of energy that are
accompiisned by minimum tillage agriculture have been accompanied by
increases in the application jf herbicides, an unknown fraction of which
reacn Chesapeake Bay. The use of selected heraldries in Maryland and
Virginia counties bordering on the Bay and lowsr reaches of tributaries has
been samnarized by Stevenson and Confer (197d). Their Tables 75 and 76 are
reproduced here as Table B-8. The uses of none compounds such as Paraquat
and Alachlor have increased considerably between 1971 and 1^75, while there
have been modest increases in others, or even decreases in some cases. The
potential effects of herbicides on the primary producers and other organisms
in the Bay is not known, but effects nave been implied on aquatic vegetation.
It is conceivable that herbicides could suppress the usual increases in
pnytoplankton that accompany enrichment with nutrients.
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CONSUMPTION OF
SELECTED MATERIALS
54
36
HOUSAND TONS
. Z &
60
40
20
Concentrated Superphosphates
Ammoniated Phosphates
Ammonium K! if rate
Nitrogen Solutions
- Ureo
PENNSYLVANIA
* /
l\;
\ J
55 60 65 70 75 7f
MARYLAND
"
J
/'
/
/
/
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^-~-<^^***^^<
, - j^-er -^ j — i [
19S5 60 65 70 75 78
Figure 8-4. Sales of selected materials in Pennsylvania and Maryland fcr
selected periods (from Harp.ett and Berry, 1978). Data from X'irginia were
similar in pattern to the trends in Maryland, but amounts used (vertical
scale on the Virginia figures) were similar to Pennsylvania.
27
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CHAPTER C
HISTORICAL CHANGES IN WATER QUALTIY
INTRODUCTION
As documented by McErlean and Reed (1979), the amounts of data that are
available to document changes in Chesapeake Bay diminish rapidly as one goes
back, in time from the present to 1968. By 1963, adverse effects of
enrichment had already been noted in some heavily loaded tributaries such as
the Potomac (Anon., 1969a), and shortly thereafter concern was being
expressed that problems were imminent in other areas such as the Patuxent
(Cory and Nauman, 1979; Cory, 1974; Flemer, Hamilton, Keefe and Mihursky,
1970). Thus, by the time an extensive data base for Chesapeake Bay began to
develop, about 1968 to 1970 (McErlean and Reed, 1979), many changes had
already occurred. Thus we decided that the acquisition of water-quality data
pre-dating 1970 was our first priority. Our second priority then became the
acquisition of more recent data from areas with a good historical base (i.e.,
date, taken prior to 1968).
In selecting data for development of historical trends we found, at
tirses, that more than one set of data was available for a given area and
period of time. This was particularly true after 1970 when the number of
studies on Chesapeake Bay increased (McErlean and Reed, 1979). In those
cases we generally chose to use the data from studies with the greatest
seasonal coverage or that included measurements of parameters of greatest
interest.
In addition we planned to obtain as many as possible oi the existing
data banks on Chesapeake Bay. Automated data systems contaiiing Bay data are
maintained by the U.S. Environmental Protection Agency (STORl'T), the State of
Maryland, the U.S. Geological Survey (water quality data mainly from the
Potomac estuary), the Smithsonian Institution, The Johns Hopkins University,
Chesapeake Bay Institute (C.B.I.), the Virginia Institute of Marine Sciences
(V.I.M.S), Baltimore Gas and Electric Company and the Philadelphia Academy of
Natural Sciences (P.A.N.S.). Of these eight data systems, only C.B.I, and
P.A.N.S. data :>anks contain data that pre-date system creatior. The C.B.I.
and V.I.M.S. data bases were given highest priority of the automated systems
because of their historical length; 1949 onwards for the C.B.I, system, and
about 1954 onwards for V.I.M.S. The E.P.A. STORET system was given high
priority early in our project and one tape of aata from the Potomac River was
acquired. We later deferred work on that tape when it becana apparent that
thei.e would be considerable difficulties in obtaining and translating all of
the available data bases within the time of our contract. Since our sponsor
of our project had already access to STORET we deferred working oa that
system. At the time of this writing, none of the other automated data
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systems have been translated to our format. Instead, arrangements have been
made with E.P.A. staff to perform part of the necessary format changes on the
Bay Program computer.
During many of the earlier studies on Chesapeake Bay, temperature and
salinity were the only parameters of water quality that were measured. We
felt that to be a useful indicator of water quality, at least one other
parameter from a selected list ("PCODE," pp. 4-5, App. B) should be present.
The parameters to be used as indicators of water quality (trophic state) were
r.hosen by consensus among the principal investigators on this project and
those choices were later reinforced by discussions at the Workshop in March
of 1979 and at the Symposium in May of 1979 (Neilson and Cronin, 1980). Of
the data sets we reviewed (Appendix B) we selected for inclusion only data
that contained at least one parameter from our "PCODE" list, usually, but not
always, in addition to temperature and salinity. The same criterion was
applied to our translations of the C.B.I, and V.I.M.S. data bases. Those
data bases could be made available in their entireties, in their original
formats.
In sorae cases, data were made available to us for our review from
continuing studies. In most of those instances, mainly involving recently
(post-1970) taken data, the data were not included in our data be=.9 (Appendix
B) but will be cited by source where used. Most of thosp data are evertually
destined to be in one of the automated data systems mentioned above. In some
instances original data of great historical value coy Id not be obtained- In
those cases, for example the early work of Patten, Mulford aid Warriner
(1963) on the lower Bay, we extracted approximate values from published
figures. These are appropriately qualified in the texr; ana the source.1:
cited. Where original data included in our data base (Appendix B) were more
complete (i.e., tables rather than figures) or equivalent to published
values, we have cited both the original source and our acquisition number (in
Appendix B).
Several areas of the Bay for which the best (nost complete or longest in
time) historical data are available are described separately in the following
sections. Some areas are reviewed in greater detail in the following
sections, particularly the Patuxent River. This generally reflects the
availability of data taken over a lon^ time, i.e., the best possibilities of
detecting trends. Because many of the methods used to measure water quality
were developed or evolved considerably during the period reviewed, we have
provided a brief section on comparability of methods, reliability of data and
limits of detection. The current trophic state of Chesapeake Bay is
addressed in the last section.
METHODS, COMPARABILITY, AND LIMITS OF DETECTION7
Quality assurance and ^t_he_ historical data record. In developing the
proposal that led to this project, the principal investigators wrestled with
the problem of verification of the accuracy of data to be acquired for
historical anilysis. We finally concluded that no fully satisfactory answer
existed. To nave attempted to verify every single data entry into oar
historical data base would have required a gargantuan effort of unfundjble
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proportions. Original data records would have to be acquired, each data
value cross-checked, and a decision made about the competence of the analyst
and about the appropriateness of the procedures used for sample collection,
storage, and analysis. Such an endeavor appeared to be extraordinarily
difficult, and perhaps futile. Clearly, quality assurance is not a practical
matter after the fact. We thus chose to employ the following guidelines:
1. We would accept all data into our data system except for those
values which were clearly erroneous or very suspect.
2. We would provide the best possible documentation of the analytical
techniques employed to produce the data.
3. We would identify to the best of our ability data sources and
scientists who supervised analyses.
4. We would provide general guidelines in this report about the
validity of techniques used in analytical determination.
5. We would include a caveat that discretion must be used in
interpreting trends, particularly for analytical values which were
obtained using the least reliable techniques.
As we stated earlier in the report, our first priority was to acquire
the oldest data possible as it was quite obvious that data frequency has
increased markedly with time and it would make little sense to expend all our
resources acquiring recent data only. Although we realize that analytical
pitfalls nay be deepest with those old data, we have been impressed with the
care with which analytical determinations were made and with the wisdom of
interpretation reflected in some of the early reports (e.g., Newcombe, 1940;
Newconbe and Brust, 1940; .Mash, 1947).
We are cautious about concluding definitely that water quality has
changed from historical trends based on the old data alone; however, we feel
the trends evidenced justify present concerns about water quality and should
not be discounted arbitrarily.
In the following section of this report ue will not exhaustively review
the history of quantitative analysis for nutrients or other water quality
parameters: a number of excellent reviews ha\e been written (e.g.,
Wattenberg, 1937; Barnes, 1959; Riley, 1975), but we will attempt to provide
some overview and evaluation about the reliability and comparability of older
techniques to present ones.
Analytical f-fethods. The most reliable parameters in the historical data
base are transparency measured by Secchi disc, nitrite and dissolved oxygen.
The Secchi disc gives good reproducibility from operator to operator.
It adequately permits estimation of the depth of the ona percent of ambient
light level as three times the Secchi depth.
The earliest method for nitrite determination was based on diazotization
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of sulfanilic acid by the nitrite followed by coupling to o-naphthylamine to
give a rose colored dye (Ilosvay, 1889). The modern technique described by
Bendschneider and Robinson (1952) is an a adaptation of Shinn's (1941) method
in which sulfanilamide is the diazotizing agent and H-(1-naphthyl) ethyleue-
diamine dihydrochloride is the coupling agent. The sensitivity and
sinplicity of this method have made it the method of choice for saline waters
for nearly 30 years.
Modern oxygeri methodology is based on the Winkler (1888) titriaetric
method. Ths essence of the Winkler procedure is a set of chemical reactions
which cenvert dissolved oxygen in the sanple to an equivalent quantity of
iodine, followed by measurement of tha iodine produced. The chemistry is
complex but the method is straightforward in application (Garritt and
Carpenter, 1566; Carpenter, 1965). The various modifications of the method
yield varying results, but these are probably not too significant in the
^stuary. Thus, the oxygen data for Chesapeake B?y is probably accurate to
-0.5 rnl/1 for any of the Winkler modifications.
Methods for phosphate and nitrate are generally reliaole if the analyst
has taken care.
Modern phosphate techniques are based on the raolybdate method of Deniges
(1920). Wattenberg (1937) discusses an acceptable early procedure and Harvey
(1948) applied a method with photoelectric detection. These procedures
suffered from color fading, salt errors, long development times and color
instabilities. Murpliy and Kiley (1953; 19^2) first suggested ascorbic acid
as reductant which gave 60 h color stability and later added antinomy which
reduced color develops..nt to 10 minutes. Jones and Spencer (1963) evaluated
five methods. All methods are subject to interference by arsenate and
organic phosphates hydrolysed during analysis by sulfuric acid in the
reagent. Arsenate interference is minimized with the Murphy and Riley (1962)
method by reading the optical densities within 30 minutes of reagent addition
to the sample.
In the best early phosphate surveys in Chesapeake Bay, Newconbe and Lang
(1939) used a manual technique apparently similar to that described by
Wattenberg (1937). Care was taken to control color development and salt
error making this data set highly reliable for dissolved inorganic phosphate.
Analytical methods for nitrate in saline waters first utilized reduced
strychnine with 8 to 24 hour development. Then diphenylbenzidine was
employed as the nitrate reagent because it gave improved color stability.
Transition to the current methods involved reduction of nitrate to nitrite by
copper-hydrazine (Mullin and Riley, 1955), amalgamated cadmium (Morris and
Riley, 1963) and copper-cadmium (Wood et al., 1967). The nitrite is then
quantiuated by the method of Bendschneider and Robinson (1952).
Historical data for ammonium ton and silicate have poor general
reliability.
Krogh (1934) suggested a distillation method for ammonium in water r.nd
air. It was tediojs and difficult to accomplish in the field without loss or
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contamination by degradation of organic compounds. Rixey (1953) suggested a
distillatlon-colorimetric method utilizing indophenol. The most widely
accepted current method was described by Solorzano (1969). It is a direct
colormetric technique which requires three reagent additions and development
time of 20 minutes at 50°C (McCarthy et al., 1977).
Silicate determination is based on formation of a heteropoly acid with
molybdate and sulfuric acid. Obviously, samples cannot be stored in glass
prior to analysis and should not be filtered using glass scintered supports
and filters. Phosphate and iron aay interfere, which is probably not
significant for open ocean but may be important in Chesapeake Bay during
seasons of low silicate and high phosphate and iron. Although the earliest
procedures were simple, and salt errors existed, the color could be difficult
to compare visually if faint. Robinson and Thoraj>son (1948) attempted to
standardize silicate procedures. Armstrong (1951) suggested an improved
approach based on Strickland's careful investigation of the properties of
silicomolybdic acid (see Strickland, 1952). ,'Iullin and Riley (1955)
investigated the activity of five reductants and recommended raetolsulphite
solution as reductant. Salt error in full seawater was found to be -9.8
percent of standard. This method obeys iieer's law up to 3 ag'l •
Table C-l summarizes methods for phosphate, silicate, amaonium, and
nitrate. These have undergone considerable modification in the last 50 years
to improve precision, reliability and ease of handling. Limits of detection,
however, have not improved greatly. In fact, laboratory notes of Newcombe
clai-B detectability of 0.01 ug atom P-l"1 with manual optic comparisons as
opposed to 0.03 ug ato^ P-l~l for current spectrophotometric nethodology.
While skepticism has been expressed about the low liraits of detection claimed
by N'ewcombe, we note that concentrations that we observed in central
Chesapeake Bay compare favorably with later observations taken by the
Chesapeake Bay Institute in the same areas. Questions about lower limits of
detection thus do not seriously affect our conclusions about historical
changes in concentrations that we reach later in this chapter.
Historical data for chlorophyll have poor reliability before the early
1950's. Furthermore, chlorophyll determination lias become routine only in
the last 20 years; thus few early data exist for comparative use.
Harvey (1934) was among the first to measure pigments as a relative
assessment of size of phytoplankton standing stock. Samples were extracted
in acetone and compared to an arbitrary standard containing potassium
chromate and iodine sulphate. Reliable chlorophyll techniques were first
developed in the eaily 1950's (Richards with Thompson, 1952), although it was
really much later that it was appreciated that chlorophyll degradation
products, such as phaeophytin may be present and give a false indication of
the presence of active chlorophyll (e.g. Yentsch and Menzel, 1963). Thus,
earlier (1950 to mid-1960) chlorophyll values would rend to be erroneously
high because corrections for phaeophytin were not reliably applied.
Furthermore, according to Vollendweider (1969, p. 21), "chlorophyll a_ values
calculated on the basis of the earlier Richards with Thompson equations are
probably affected by an error of about +25%," due to adjustments in their
original equations. Accordingly, it is clear that witii time, analytical
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Tab'e C-I. Summary of modification in analytical methods for nutrients.in
sea water.
Limit of
Ion Method Detection* Preci&ion Remarks
- Harvey
1948
Wooster &
Rakestraw 1951
Murphy & Riley
1958
0.03 ug
at/1
- 0.02
at/1
- 0.5%
Murphy & Riley
1962
Si03= Robison &
Thompson 1948
Armstrong
1951
Mull in & Hi ley
1955
NH^ Krogh
1934
Riley
1953
Solorzano
1969
N03 Mull in & Riley
1955
0.03 ug
at/1
0.07 ug
at/1
0.1 ug
at/1
0.1 ug
at/1
0.18 ug
at/1
0.10 ug
-it /I
0.10 ug
at/1
0.02 ug
at/1
- 0.5X
- 5/,
- 3/0
± 0.5^
- 0.14
at/1
- 0.07
at/1
- 0.05
at/1
- 2/,
ug
ug
"S
Fades-Silt error 10-204 be-
tween distilled & sea waters
Color unstable with
temperature
Ascorbic acid reductant-
color/stable 60h, U/i .-salt
error, 2ih color development.
Antimony gives 10 Min coin*
development Salt error JT G.7/
FCU- & Fe interference
Salt error minimum. P04S
& As04 = interference
P, Ge, V may interefere.
Salt error up to 10,i
Distillation & titr.ution
- 0.07 ug Distillation £ colorr.ietric
determination of Indophenol
Direct coloroaetric deter-
mination of Indophenol
Cu catalyst with hydrazine
reduction of TOJ to .NOJ.
Marked salt effect.
Morris & Riley
1963
Wood et al.
1967
Armstrong
1963
±2*
0.05 ug
at/1
Amalgamated Cd column
efficiency 91 + 1%.
No salt error.
Cu-Cd column efficiency
99 ± U.
<0.25 ug - 0.4 (bT>) UV spectrophoto;Tietry.
at/1
*In the hands of a competent analyst using the best available
colorisetric detection devices available at the tine.
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determination of chlorophyll has resulted in lower values. This means that
increases observed In chlorophyll in the historical rscord during this study
are probably real.
Chronology o£ eolorir.etr ic detect ion device u_s£. The determination of
nost non-conservative substances in seawater usually involves "coloriraetric"
techniques. Nutrient (N'OJ, N05, etc.) concentrations in seawater have always
been determined principally In such a manner. Colorimetric technology has
Improved substantially since nutrients were first measured in sea and
estuarine waters. This improvement would improve detection liraits for
procedures when nost other factors (e.g., reaction chemistry) have remained
the sane, since tlir: overall sensitivity of any method depends on both
chemical and detection factors.
There are some excellent published reviews on the subject of apparatus
and analytical aethods of oceanography (Barnes, 1959; Riley, 1975), so it
makes little sense to repeat such information exhaustively here. However, we
have produced a Table (G-2) which gives a brief generic description of the
instruments employed in color detection and a Table (C-3) which gives an
approximate chronology of use of these instruments.
Table C-3. Approximate chronology of extensive use of "colorimetrtc"
detectors lor nutrient analysis in sea and estuarine waters.
Color
Visual
Filter
Year
pre 1930
1930-1940
1940-1950
1950-1960
1960-1970
1970-1980
Comparator Photometer
X X
Photoelectric
Filter
Photometer
Spectro-
photometor
x*
X*
*Priraarily as field kits (e.g. Hach or Helige Instruments)
Primarily as components of automated analysis systems
UPPER CHESAPEAKE BAY
The earliest measurement of water quality in the upper Bay that we
encountered [excluding the early observations of Cumaing (1916) and Olson,
Brust and Tressler (1941) in Baltimore Harbor] were made on three dates
during August and September, 1938 (our data base code number '•1022005).
38
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Temperature, salinity, and concentrations of dissolved oxygen and phosphorus
were measured at 3 to 8-ra depth intervals at &tat torts from near the mouth of
thf> Paluxent River (discussed in a later part of this chapter) to near
Annapolis or Sandy Point. Froui August 1949 through May 1951 the Chesapeake
Bay Institute (C.B.I.) conducted a series of cruises the length of the Bay
and measured phosphorus, chlorophyll and turbidity, in addition to physical
parameters. Hires, Stroup and Seitz (1963) and Stroup and Wood (1966)
prepared graphical summaries of the data collected on those cruises, which
have also been published in C.B.I, data reports 1-10 and are in the C.B.I.
data base. From 1950 through 1952, Mr. Janes Van Engle measured
concentrations of phosphorus over four oyster bars in the Fishing Bay area.
Those unpublished data were made available to us through the Annapolis Field
Office of the U.S. li.P.A. and have been entered into our data base (M022017).
Between February 1964 and April 1966, C.B.I, collected data on nutrients in
the upper Bay including the three for™s of inorganic nitrogen. Chlorophyll
and attenuation of light were also measured in addition to physical
parameters. Tabular presentations of the 1964-1966 C.B.I, data are available
(Whaley, Carpenter and Baker, 1966; Carpenter, Pritchard and Whaley, 1969)
and the data are in the C.B.I, data base. From April 1965 through January
1977 the Chesapeake Biological Laboratory (CBL) conducted a study of the
upper Bay during which chlorophyll and turbidity were measured in addition to
the physical parameters. These results are summarized by Flemer (1970), with
emphasis on the distribution of chlorophyll £ and Secchi disc depth. Also
included were estimates of primary production and the lateral variation of
chlorophyll a_. These data have been incorporated into our data base
(M000295). During 1967 and 1968 the Federal Water Pollution Control
Administration (now E.P.A.) conducted a number of water quality surveys in
the upper Bay and tributaries. These have appeared -is several data reports;
data report Mo. 4 (Anrn., 1968), data report Mo. 12 (Marks and Villa, 1969)
and data report No. 23 (Anon., 1971b) (M022009 in our data base). During the
same period the State of "-'aryland studied the Elk Fliver and the C & D Canal
(Brunoric, 1968) (M022011 in our data base). Slightly later, 1969 through
1971, E.P.A. again assessed the water quality of the upper Bay (Anon., 1971a)
(U022006 in our data base). The E.P.A. studies generally included all the
major nutrients, chlorophyll, D.O. and physical parameters. Major trends
during 1968 through 1971 were summarized by Clark, Donnelly and Villa (1973)
(M022007). During 1969 to 1971 C.B.I, again conducted a series of Bay-wide
cruises. Nutrients and chlorophyll (Taylor and Grant, 1977) and physical
parameters (Taylor and Cronin, 1974) were reported separately in tabular
form. The data are also in the C.B.I, data base and are reported on in part
elsewhere in this chapter (Middle Bay and Lower Bay).
There have also been a number of studies dealing with phytoplankton in
the upper Bay and phytoplankton-nutrient relationships for which a data base
exists that we did not acquire because it duplicates more readily available
data (e.g., Loftus, Subba, R,io and Seli.s/er, 1972; Tyler and Seliger, 1978).
Clarke, Donnelly and Villa (1973) reported trends of increasing chlorophyll
and nutrient concentrations in the upper Bay based on the data in Anon.
(I971a,b,c) (M022006). Clarke et al. (1973) commented on excessive algal
blooms, including changes in species composition (a shift toward blue-green
algae in sorae tributaries). They also noted historical increases in
concentrations of phosphorus end the possibility that nitrogen was becoming
3S
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the limiting nutrient (based on very low concentrations during periods of
maximum algal blooms). Salas and Thornann (1976) showed historical changes in
concentrations of chlorophyll and nitrogen to be relatively greater than
those of phosphorus. Their figures and analyses were based on vertically
averaged concentrations over the J^ngJ^h ££ t_he _B_ay_, a serious flaw as
processes of nutrient uptake and reniineralization are quite different in the
turbulent upper Bay and the two-layered lower Bay (V.'ebb, 1980).
We have reviewed the same data base used by Salas and Thoraann (1976)
except for the period after tropical storm "Agnes." In addition we used the
data reported by Taylor and Grant (1977) for the period 1969-1971 and the
data for 1966 and 1967 reported by CBL (M000295). Our analysis included
stations from C.B.I, station 85BJ and upstream (aproximately from Annapolis
up).
V.'hen only upper Bay data are included, the increased concentrations of
phosphorus during May through August in later years are apparent (Fig. C-IJ.
In the studies by C.B.I, in 1949-1951 and 1964-1966, concentrations of PC>4 -P
were generally about 0.2 ug-at !"*• or lower during May through August. In
later years, 1969-1971, higher maximum concentrations were observed, 0.5 to
over 1.0 ug-at 1~^ during the same months (Fig. C-l). During the rest of the
year, phosphorus concentrations, while variable from year to year, show no
trends of increase (Fig. C-l).
The upper Bay has changed from a pattern of maximum phosphorus
concentrations in the spring and fall, with a sunnier minimum, to relatively
uniform concentrations all year.
In contrast, the concentrations of nitrate plus nitrite-N, the only
forms consistently measured over time, have not changed in the upper Bay,
except possibly during November (Fig. C-2). Minimum concentrations of
nitrogen occurred in September (< 8 ug-at 1~^, Fig. C-2). The seasonal
pattern ior N.">j »• Nli - N is fairly typical for the entire Bay, although
minimum concentrations may occur earlier down-Bay (see later parts of this
chapter).
The evidence for increased concentrations of chlorophyll a_ is not nearly
as clear (Fig. C-3). Although concentrations never exceeded 10 ug 1~1 during
the 1949-1931 studies by C.B.I. (Stroup and Wood, 1966), no measurements of
chlorophyll a_ were made during August and September of that study. By 1965,
maximum concentrations of 55 to 80 ug 1~1 were observed in the upper Bay
during July and September. The concentrations reported during May through
August for 1969-1971 by C.B.I. (Taylor and Grant, 1977) were slightly higher
than previously observed for these months. The concentrations reported by
E.P.A. (Anon., 1971a,b,c) were considerably higher during the same period.
We were unable to resolve the discrepancy between these two sets of data. It
should be noted that although the sampling was less regular in the E.P.A.
study, the spatial coverage was greater and more samples were taken on most
dates than during the C.B.I, studies. The maximum chlorophyll _a
concentrations during the summers of 1966 and 1967 reported in the studies by
CBL (M000295) (Fig. C-4) were somewhat higher than those reported by C.B.I.
during 195't-1966 (Fig. C-3). Minimum concentrations were similar in the two
40
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For the purpose of examining trends, data for parameters which have the
longest records were selected.
Secchi depth (Fig. C-5) was generally in the range 1.5 to 4 m in the
mid-1930's and the early 1960's. The maximum value of 4.G m was recorded in
the 1970's.
Dissolved phosphate was conparable at all depths from 1936-1951, with
values from undetectable to 1.3 ug atom-I"1 (Fig. C-6 to C-8). By 1964-1966
maximum values increased to 2 ug atora-1""^- and by the mid-1970's values of 2.5
ug atotn'l""'- were observed.
Chlorophyll a_ data show some increases in the mid-Bay between 1951 and
1964-1966. Peak values in the euphotic zone (upper 10 m) are less chan 25
ug-l~l (Fig. C-9). The highest values were observed in the deep water.
usually in winter or spring. Peak values were 28 to 45 ug-l~l.
Occasionally, the data for surface waters show increased chlorophyll a_ near
the Potomac River mouch. Since this is not a regular feature, we cannot
conclude that the Potomac is a major source of phytoplankton for the mid-Bay.
Most chlorophyll a_ results from phytoplankton growth in the Bay itself.
If J_n situ phytoplankton growth were increasing in the mid-Bay region
during 1936-1978, maximum pH values for surface waters might also increase
with removal of greater amounts of C02 in daylight hours. The pH data in
Figure C-10 do not show increases in maximum values. Most pH values range
7.8 to 8.5. In contrast the pH of water 20 to 30 m deep is usually 7.4 to
7.9 probably due to respiratory C02 production (Fig. C-ll). Thus although
photosynthetic and respiration affect the vertical pH gradient there is no
clear indication of increasing pH in surface waters over time due to enhanced
photosynthesis. However, note that the buffering capacity of sea water makes
pH a poor indicator of changes in trophic state unless very high values
coincide with high rates of primary production.
Phosphorus probably limits biomass in spring when inorganic nitrogen is
abundant (Taft et al., 1975; Taft and Taylor, 1976a,b). However, there are
too few data to establish clearly a limiting nutrient in other seasons,
Fleraer and Biggs (1971) have noted that "the suspended particulate organic
material in the lower study area is suffering a relative loss of nitrogen
with respect to carbon." A graph of the Secchi depth and phosphorus data
(Fig. C-12) reveals an inverse relationship. But since most phytoplankton
species can store phosphorus beyond immediate requirements, phosphorus
limitation of the phytoplankton biomass cannot be established solely from _
this graph. Additional information about the physiological condition of the
organisms such as alkaline phosphatase activity would have to be used (Taft
et al., 1977). Such information is not available in the historical data
base.
The range of dissolved oxygen values for surface waters is comparable in
the earliest and latest data sets available (Fig. C-13). Oxygen
concentrations in the deep water, however, seem to be depressed for longer
periods in summer and over wider regions of the mid-Bay. Newcombe and Home
(1938) and Taft et al. (1980) discuss oxygen depletion. The oxygen demand
46
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studies. If the stations from the CBL study that we did not include in
Figure C-4 (Appendix B) were included, the range of chlorophyll a
concentrations would be further increased. Based on the C.B.jl. <
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results from accumulation of algal organic material in the deep water and on
surface sediments. When the watc-r column is sufficiently stratified, oxygen
Is removed from the lower layer faster than it is replenished from the
surface. Thus, in wet years oxygen depletion should be more exaggerated than
in dry years. Unfortunately, the data base is not complete enough to test
this hypothesis.
The data for nitrogen are least complete. The annual trend is for
nitrate to be the dominant inorganic form in winter and spring, ammonium in
.summer and nitrite in fall. Long term trends cannot be defined at present.
This is in part because sources are different for the various forms of
dissolved combined nitrogen. The spring freshet contributes nitrate from
ijroundwater and snow melt in the Susquehanna drainage basin (Carpenter et
al., 1969). Little of t.his nitrogen appears to be utilized in the upper Bay
because ammonium from plaaktonic and benthlc regeneration is abundant.
McCarthy et al. (1975, 1977) have shown that at ammonium concentrations
greater than 1.0-1.5 uM, nitrate uptake by phytop lank ton is minimal. The
nitrite maximum often observed in fall (McCarthy et al., 1977) seems to
result from oxidation of ammonium accumulated below the pycocline during
summer stratification. However, rates and sites of oxidation are poorly
understood at present.
Silicate showed comparable ranges in 1937-1938 and the early 1970's
(Fig. C-1A). Annual variations are 0 to 60 ug atom-l"! b^c no long term
trend is discernable.
In the middle Bay, as elsewhere, long-term residents report greater
frequencies of brown water blooms. In the summer of 1979, offensive odors,
similar to dead fish but with no fish evidenced, were reported on several
occasions and noticed by one of us (DRH).
In summary, the middle Bay appears slightly richer in phytoplankton and
phosphorus now than in the mid-1930's. The greatest change was from
1951-1965. The magnitude and duration of deep water anoxia may have
increased since 1965, but since 1964-1966 were relatively dry years, they
might be expected to have had more favorable conditions for deep water
reoxygenation. Thus 1964-1966 is not an average period, making it a poor
base line reference.
LOWER CHESAPEAKE BAY
Data for the lower Bay (Smith Point and south) are available from the
C.B.I, cruises in 1949-1951 on phosphate and chlorophyll, and in 1967 on
chlorophyll and in 1969-1971 on inorganic nitrogen, phosphorus and
chlorophyll. Some data on nutrients and chlorophyll for June of 1972 are
available from Smith, et al. (1976). Chlorophyll &_ measurements are also
available graphically from Patten, Mulford and Warriner (1963) for the early
1960's and from Fleischer, et al. (1976) for the mid-1970's. Sufficient data
exist to establish trends for chlorophyll a_ and orthophosphate-P.
Orthophosphate concentrations were generally below 0.2 ug-at 1 during
January through April in the early 1950's rising to maxima of 0.8 to
56
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1.0 ug-at 1 in mid-to late summar (Fig. C-15). In 1969-1971 concentrations
of orthophosphate were somewhat higher, 0.3 to 0.7 during the same period
(Fig. C-15). Maximum concentrations in the summer and fall are occasionally,
but not regularly, higher.
Nitrogen (NOJ + N02 + NliJ - N) has not been measured long enough to
establish trends in the open lower Bay. The two-year data from the C.B.I.
cruises establishes a clear pattern for NO^ + NOj - N maxima of 12 to
25 ug-at 1~1 in March and April falling to low summer values of generally
less than 1.0 ug-at 1~^ by June. Occasionally higher values are observed
during August and September when concentrations begin to increase again.
McCarthy, Taylor and Taft (1977) provide a description of the seasonal
patterns of nitrogen concentration and use by phytoplankton.
Because ".itrog-'n is most often the limiting major nutrient in higher
salinity areas of Chesapeake Bay (Webb, 1980), one would not expect the
observed increases in phosphorus to lead to increased algal stocks.
Concentrations of chlorophyll a_ have not increased greatly, if at all, over
the period of record (Fig. C-16). There is a definite spring maximum in some
years of up to 22 ug 1~~1 of chlorophyll a. During the rest of the year,
concentrations are generally below 13 ug 1~ •
The early C.B.I, data often show a chlorophyll maximum in the vicinity
of Smith Point to below the mouth of the Rappahannock River which may occur
at any tirae of the year. The chlorophyll maximum is sometimes associated
with a variation (either an increase or decrease) in phosphorus. The depth
profiles show a shoaling of the channel in that area which often markb the
down-Bay limit of anoxic bottom waters. Low concentrations of dissolved
oxygen do not normally occur in the Bay very far below Smith Point (the mouth
of the Potomac River on the Virginia side), so that parameter has not been
routinely measured except in the studies by C.B.I. The chlorophyll maximum
might thus be caused by natural features of the Bay. An excellent baseline
exists in the 1949-1951 data of C.B.I, for comparison with future data on
chlorophyll.
The lower Bay has experienced increases in concentrations of phosphorus
in recent years wit!1 an apparent effect on algal standing stocks. Recent
measurements of primary production (or often productivity) are sufficiently
different in method from those of Patten (1962) (Patten, et al. 1963) that
direct comparisons cannot be made. We conclude, however, that the lower Bay
remains relatively unperturbed.
CHOPTANTC, CHESTER AND MILES RIVERS
The lower Choptank and Chester Rivers as well as Eastern and Fishing
Bays were sampled for temperature, salinity, turbidity, dissolved oxygen,
chlorophyll a_ and orthophosphate-P by C.B.I, in 1949-1951 (Hires, et al.,
1963; Stroup and Wood, 1966). In 1964-1966 C.B.I, sampled the Chester and
Miles Rivers for the same parameters plus the three major forms of inorganic
nitrogen (Whaley, et al., 1966). A survey of the Chester River was conducted
by E.P.A. during 1970 (Anon., 1971b) (M022035). One can thus examine trends
for the Chester River between 1950 and 1964-1966 and 1970, and for the Miles
53
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River and Eastern Bay between 1950 and 1964-1966. These are distant from
large metropolitan areas, surrounded by rural areas and smaller communities.
The somewhat limited sampling in 1950 showed concentrations of
chlorophyll a of 6 ug 1~1 or less in the Chester, Choptank and Miles Rivers.
Concentrations of PO^-P never exceeded 0-6 ug-at I"*-, with maximum
concentrations observed in the late sumaer and fall. By 1964-1966,
concentrations of chlorophyll _a were only slightly higher in the Chester and
Miles Rivers on the average, but occasional blooms of up to 45 ug !"*• were
observed in the Chester. Concentrations of P0j3_p were commonly in excess of
0.5 ug-at I""*-, and sorie times over 1.5 to 2.0 ug-at 1~^, with maxima still
occurring in the fall and very low values in the spring. In 1970,
concentrations of chlorophyll a_ of up to 29 ug 1~1 were measured in the
Chester River. Concentrations of PO^-P were commonly in excess of 2.0
ug-at 1~1 during the summer months, but still apparently low in the spring.
During 1964-1966 concentrations of NOJ + N'OJ - N were typically 20 to 43
ug-at l~l during the spring and generally below 10 ug-at 1~^ during the
summer in the Chester and Miles Rivers. Concentrations of nitrogen were
generally highest near the confluence with Chesapeake Bay in summer months,
often being less than 1.0 ug-at 1~^ at upstream stations. The samples taken
by E.P.A. in 1970 show no increase in nitrogen over the 1964-1966 valuss.
The middle eastern shore tributaries have experienced increases in
concentrations of chlorophyll a_ and PO^-P, but not nitrogen. Chlorophyll a
concentrations are generally 1.5 to 2.0 times higher than indicated by the
earliest data, with occasional blooms of much greater concentrations. The
mainstem of the Bay "nay be a major source of nitrogen for the middle eastern
shore tributaries during the summe..' months.
MAGOTHY, SEVERN AND SOUTH RIVFRS
The tributaries of the Bay in the -'icinity of Annapolis were surveyed by
C.B.I, in 1964-1966 (Whaley, et al., 1966) and by E.P.A. in 1967 (Marks and
Villa, 1967) (M022036 in our data base), and again by E.P.A. in 1970 (Anon.,
1971b) (M022035).
During the earliest studies, concentrations of chlorophyll jj were often
high, 30 to 52 ug I"1 near the ncuths of the Severn and Magothy Rivers in
1964 and over 100 ug 1~1 in the lower Severn in 1967. Concentrations of 40
to 50 ug 1~~1 were common in both the Severn and Magothy during 1967. During
1970, concentrations of chlorophyll a_ in the Severn River were similar to
those observed in 1964-1966.
Concentrations of phosphorus were generally below 1.0 ug-at 1~1 except
during the la'-e summer when concentrations ranged as high as 1.5 to 2.1 ug-at
1~1. Concentrations of PO^-p were somewhat higher during 1967 than during
1964-1965. By 1970 even higher concentrations of phosphorus were observed in
the Severn River, up to ^.6 ug-at 1"^-•
Nitrogen concentrations showed a pattern identical to that for the upper
Bay (Fig. C-2) with no apparent increase with time. Concentrations of XOJ +
61
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HO2 ~ K were frequently higher near the Bay than farther up the Severn and
Magothy Rivers during the suTinier months in 1964-1966. Concentrations at
upriver stations were similar to those downstream during 1970.
The patterns in the South River have paralleled those in the Severn and
Magothy Rivers except that concentrations of both major nutrients and of
chlorophyll a were somewhat lower than in the other two Rivers through 1967.
The South River was not included in the 1970-1971 studies by E.P.A.
The Bay tributaries in the vicinity of Annapolis showed effects of
enrichment in their lower reaches at th ; tine of the first studies in
1964-1966. In more recent years, chlorophyll o_ concentrations have increased
upstream, and maximum summer concentrations of P07+ P have increased
throughout. The South River appears to have changed less than the Severn and
Magorhy Rivers. Like the eastern shore tributaries, the western shore
tributaries may have received inputs of nitrogen from che Bay which were
supplemented by landward sources by 1970.
PATUXENf RIVER
The data base for tha Patuxent River estuary, which is the most
historically comprehensive we have, begins in the period 1936 to 1940 with
the studies reported by Newcorabe and Home (1938), Newcorabe, Home and
Shepherd (1939), Newcombe and Lang (1939), Newconbe (1940), Newcozibe and
Brust (1940) and Nash (1947). The origiral data (M022004 and M022005 in
Appendix B), which were not all found, are nore extensive than reported in
the literature. Even though the methods for some parameters were in early
stages of development, others have changed little (Table C-l), and some, such
as Secchi depth, while subjective, are unchangeable. Mihursky and Boynton
(1978) recently reviewed the data base for the Pntuxent estuary. Table C-4
reproduces their summary (their Table D-l). Mihursky and Boynton (1978)
cited Stross and Stottlemeyer (1965) in their text but not in their summary
table. An M.S. thesis by Stottlemeyer (1964) was not noted. After
termination of the data acquisition portion of this project, we located the
original data of Stross and Stottlemeyer (1965) for the period 1963-1964 and
unpublished data of Stross for 1960-1961. These data should be added to the
data base. Other omissions can be found in Table C-4, particularly the
unpublished data of Allison (1964).
Mihursky and Boynton (1978) noted several historical changes in water
quality in the Patuxent estuary. They observed that over the period of
record there have been increases in annual maximum concentrations of the
major nutrients, increases in concentrations of plant pigments and rates of
primary production, decreases in the transparency of the water and decreases
in the concentrations of dissolved oxygen in bottom waters in some parts of
the estuary. On the following pages we will attempt to document the observed
Flemer and Heinle (1974) noted increased maximum concentrations of
nitrate in the spring and phosphorus in the suramor at Lower Marlboro and
Trueman Point based on the work of Herman et al. (1968) (M022001) and that
Flemer, et al. (1970) (M022003). Mihursky and Boynton (1978) added
62
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Table C-4. Water quality studies of the Patuxent River.
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comparisons with the earlier data (H022005) and a few observations made in
1972 and 1976. Figures C-17 and C-18 show time related changes in nitrate
and phosphate (two of the more reliable parameters from the historical data
set) for a group of stations within the sediment trap portion of the estuary
and a group oC stations from the middle and lower estuary where two-layered
circulation typically occurs (Owens, 1969). Data taken by CBL in 1978, 1979,
and 1980 as well as some data taken by the State (not included in our data
base, Appendix 3), have been added.
It appears that annual maxima of nitrate concentrations have increased
historically (Figs. C-17). Winter maxima of nitrate concentrations on the
average are highest and may be good indicators of nitrogen loading. Maximum
winter-spring concentrations are now considerably higher than during the
studies of Newcombe, Nash and co-workers in the late 1930's (M022005) or
those of Herman, et al. (1968) (M022001). The annual cycle of nitrogen
concentrations in the lower estuary remains qualitatively unchanged, however,
with very low values typically occurring from mid-June until October or
November (Fig. C-17) (Mihursky and Bovnton, 1978; P.A.N.S., unpublished
data). The synoptic study of Ulanowicz and Fleraer (1978) (M020001) indicated
a very close coupling between primary production and rates of disappearance
of nitrogen from solution during October.
Maximum concentrations of phosphorus have clearly increased upstream of
Benedict Bridge (Fig. C-18). Downstream of the bridge, where phosphorus
concentrations are considerably lower, presumably as a result of dilution of
phosphate-rich freshwater by relatively phosphate-poor salt water, there
appears to ha/e been a modest increase in concentration maxima also (Fig.
C-18). On the average, summer phosphate concentrations, below Benedict
Bridge, have increased rather dramatically. Presumably, increased phosphate
loadings from upriver and increased rates of phosphate release by the
estuarine benthos both contribute to this effect, but further resolution of
this will await further research and study. Clearly, phosphorus flux
information is needed.
On the basis of the 1963 to present data set, it appears unlikely that
phosphorus limitation is a factor upstream or downstream of the bridge
through most of the spring and summer. Such limitation may have been present
prior to that period, however, when phosphorus loadings were smaller.
Conclusions about the possibility of nitrogen limitation occurring are
difficult to reach on the basis of the nitrate concentration data alone, for
other forms of inorganic nitrogen such as ammonia (historical data for which
are scarce and have poor reliability), need also be considered. However,
nitrogen limitation below Benedict Bridge seems quite possible considering
tie data presented in Figures 17 and 18. In addition, light, limitation
snould be considered a strong possibility upstream.
An interesting phenomenon noted by Uebb (unpublished) during our study
was that a late sunnier-early fall and, to a lesser extent, an early spring
N'OJ-N concentration maximum occurs in many localities in the Bay. Webb and
D'Elia (1930) have reported high concentrations of NOJ-N in the water column
exceeding 5 uM (0.07 mg/1) for the lower York River. Figure C-19 shows a
striking example of this seasonality in unpublished data we acquired from
G7
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P.A.N.S. for the Patuxent River near Benedict, Maryland. Such observations
militate against the commonly accepted notion that NOf-N is never abundant
enough to be worthy of measurement. Morever, Webb (1980) has suggested that
in addition to its importance as a seasonal factor in the Bay, NOJ-N may be
an important indicator of historical enrichment trends in the Bay. An
ongoing research program in 1930 has again verified a late summer-late fall
NOJ maximum throughout the Bay, with NC>2 concentrations reported which exceed
10 uM.
Methods used to measure primary production in the Patuxent estuary vary,
but those of Stross and Stotcletaeyer (1965) and of Flemer, et al. (1970) were
nearly identical. Rates of primary production appear to have increased
between 1963-1964 and 1969-1970 in approximate proportion to the increases in
concentrations of chlorophyll, described below. There were large
year-to-year differences in rates of primary production during both studies.
Maximum concentrations of chlorophyll _a have increased considerably in
the lower Patuxent estuary (downstream from Benedict) since the first
measurements were made by Stross and Stottleiaeyer (1965) and by Herman, et
al. (1968) (M022001) in 1963-1964. In 1963-1964 maximum concentrations of
chlorophyll j3 were up to 18 ug 1~1 at Benedict and downstream and up to 40 ug
I"1 at Lower~Marlboro during May, June and July (Fig. C-20). By 1968
concentrations of chlorophyll 11 of up to 60 ug 1"! were observed at Benedict
and Lower Marlboro. During 1970 and 1973, concentrations of chlorophyll a up
to 80 to 100 ug 1~1 were observed, and few observations were as low as the
1963-1964 data. During 1977 and 1978 many of the observations in the lower
estuary were within the range reported for 1963-1964, but many were higher.
Extreme values of over 100 ug !"*• were observed in 1973.
Similar trends occurred during the months of August, September and
October except that concentrations at Lower Marlboro were somewhat higher
during those months than during May-July in 1963-1964, and did not increase
in later years (Fig. C-21). The increases in chlorophyll a_ from 1968 and
later at stations in the lower estuary were not as dramatic as during the
months of May-July, for maxim,! greater than 60 ug 1~^ were not observed.
Chlorophyll a_ concentrations measured in the Patuxent during the winter
months after 1970 (by P.A.N.S.) have not been made available to us, but the
data of Flemer, et al. (1970 (M022003) indicate an increase over the
concentrations found in 1963-196^ (Fig. C-22).
Inasmuch as methods for measuring chlorophyll were not well developed
until the 1950's, we cannot determine with certainty if standing stocks of
phytoplankton increased in the Patuxent estuary between the studies in the
1930's and those of Herman, et al. (1968) (M022001). It seems likely,
however, that increased algal stocks would result in increased turbidity,
particularly in the portion of the estuary downstream from the sediment trap
region (the sediment trap region varies in salinity, but is generally
upstream from Benedict). Turbidity, measured as Secchi depth, was recorded
in the earliest studies. The same technique continues in use today, although
other measures of turbidity, convertible to Secchi depth, are also used.
Examination of Secchi depth, as a function of salinity and month, revealed
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that the most notable decreases occurred in the months of July, August and
September (Fig. C-23), from 1969 onward, a feature shared by the central Bay
(Fig. C-4). Surface salinity was chosen as the abcissa (x-axis) in Figure
C-23 rather than location in the estuary because of the effect that varying
flows have on the position of the sediaent trap. High concentrations of
inorganic sediment occur in parts of the Patuxent characterized by salinities
less than 8 °/oo in July and less than 10 to 12 °/oo in August and September
(Fig. C-23). Secchi depths in excess of 1.5 m were common in the early
studies at higher salinities. Transparencies of the water in the lower
estuary during 1963 were similar to those observed during 1936-1940. The
1963 values were calculated from optical densities (O.D.) in original data of
Stross and Stottlemeyer (1965) (located too late for inclusion in our data
base). Stross and Stottlemeyer found O.D. from log Iz-log Iz+l (Sverdrup,
Johnson and Flemming, 1942). We calculated extinction coefficients (K) as
2.3 O.D. (Sverdrup, et al., 1942) and then used the relationship Secchi depth
equals 1.43K established for Chesapeake Bay by Keefe and Flecier (1976).
Stross and Stottleni?yer observed even greater Secchi depths during July of
1964 than during 1963 in the lower estuary; five observations in excess of 3m
and two over 5m, but unfortunately did not measure salinity on that date.
We feel that the decreased Secchi depths in the lower estuary during
July-September in later years reflect increased algal stocks. There is less
certainty concerning the much smaller decreases in Secchi depth in the
sedinent-trap part of the estuary (salinities < S °/oo) shown in Figure C-23
and reported also by Mihursky and Boynton (1978) in their Figure 1V-3
reproduced here as Figure C~24, as turbidity in that part of the estuary is
greatly affected by wind (Cory and Najman, 1970). The seasonal patterns of
salinity and temperature in the Patuxent during the early studies (M022005)
were similar to those observed by Fiercer, et al. (1970) (M022003)
(Fig. C-24), so Secchi was probably not greatly decreased by higher flows
during the later studies. In addition, we often noted comments on the
original field notes such as "Bay too rough, went to river instead,"
suggesting that many of the early trips on the Patuxent, especially during
1936 were made on windy days. One might, therefore, expect higher turbidity
than was characteristic of the period. The increase in turbidity between
1936-1940 and 1969-1970 in the sediment trap area thus probably represents a
real change in the character of the estuary. We do not know if this
represents increased algal stocks or increased amounts of detritus and
sediment, or both.
One of the most comnon effects of excessive enrichment is increased
community metabolism indicated by higher concentrations of dissolved oxygen
(D.O.) during daytime and lower concentrations of D.O. at night. Cory (1974)
noted evidence for such changes in the Patuxent at Benedict during the period
1963 thorugh 1969. He observed both greater extremes in concentration of
D.O. and a reduced ratio of production to respiration, from 0.84 in 1964 to
0.60 in 1969, suggesting increased heterotrophy at the study location. Cory
installed his automatic sampling apparatus again in 1977. Although the
results have not been published, they have been made available for our use
through the U.S. Geological Survey (U.S.G.S.). Figure C-25 shows weekly
maximum and minimum concentrations of D.O. during May through August at 1-m
depth at Benedict Bridge. Maximum concentrations have clearly increased and
75
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JFMAMJJASOND
MONTHS
Figure C-24. Ranges of temperature, salinity, and Secchi depth in the
"turbidity maximum" area of the Patuxent estuary (from Mihurjky and rtoyntrn,
unpbulished).
77
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minimum concentrations have clearly decreased at that location. A similar
change, but of lesser magnitude has occurred in the weekly mean of daily
aaxiaum and rr.iniiiuni concentrations. Concentrations ranged between 33 and 147
percent of saturation in 1977, nearly identical to tha range observed in 1969
by Cory (J.974).
In a stratified body of water, such as an estuary, increased
productivity in surface waters can cause decreased concentrations of oxygen
in deeper waters (e.g., Curl, et al., 1978; Glendening and Curl, 1978; Webb
and O'Elia, 1980). A phenomenon like this is known to occur naturally in the
central part of Chesapeake Bay (Newcorabe and Home, 1938). Measurements of
surface and bottom concentrations of D.O. in the Patuxent estuary during
1936-1939 (M022005) provide a basis for comparison of ^ore recent data. Nash
(1947), in discussing the annual cycle of dissolved oxygen at a station near
the -oouth of the River, stated that concentrations in bottom waters at
upriver stations were sometiT.es 40 percent of saturation. A survey of the
d.Jta base (M022Q05) revealed that concentrations of D.O. were only
occasionally lower in botton waters than in surface waters during July and
August at locations upstream fro.-"- St. Leonard's Creek during 1936-1939. Low
concentrations of dissolved oxygen were conrnonly observed downstream from the
:nouth of St. Leonard's Creek in the early data. Figure C-26 shows all
neasurements from the nouth of the Patuxent (Drum Point) upward to Lower
Marlboro taken during July of 1936-1939. Measurements made during 1977-1979
by the State of Maryland, W.R.A., and by the University of Maryland, CBL,
nainly during studies funded by the State of Maryland, Power Plant Siting
Program (PPSP), are shown for comparison. It can be seen in Figure C-26 that
the recent .ueasucements tend to be somewhat lower in portions of the estuary
where the ranges of the two periods overlap. In the segment of the estuary
froa Benedict Bridge to Jack Bay (Stations 17 to 13 of Nash, 1947) the
concentrations observed during July of 1977-1979 were ail lower than in the
early period.
Nash (1947) observed that the differences between surface and bottom
concentrations of D.O. were sometimes greater when vertical stratification
was stronger. Some of the high (near saturation at 5-6 ppm) concentrations
in bottom waters in the early data (Fig. C-26) were observed during periods
of apparent vertical mixing as salinity differences were near zero. The very
high concentrations in the lower estuary appear, from examination of the
original laboratory notes, to be valid observations of super-saturation in
deep waters, and were often higher than surface concentrations at the same
locations. Stress and Stottlemeyer (1965) calculated that the depth of the
eup.iotic zone was often deeper than 5 m in the lower estuary; about the depth
of the halocline, which from vertical profiles of salinity from both periods
usually lies at about 5 to 6 a in the lower Patuxent above Point Patience and
somewhat deeper below Point Patience. Their observations of Secchi depths of
3 to 5 m in July suggest that the euphotic zone could be 9 to 15 ra deep at
times. It, thus, appears likely that photosynthesis occurred below the
halocline during periods of greater clarity of the water, i.e., prior to 1966
(Figs. C-24 and C-25), perhaps causing the observed super-saturation below
the halodine.
During the months of September through May, concentrations of D.O. in
79
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bottom waters in the Patuxent estuary were not markedly different fro-
surface concentrations, and showed no trends with time. Low concentrations
of D.O. (less than I ppm) wore observed in bottom waters from Benedict to
Brooraes Island in June of 1978 (no data for 1977 or 1979) and August of 1977
and 1978 (Fig. C-27). The only observation of a concentration less than 1
pprn in the early data is a single value of 0.78 ppra in August, 1939 at
Sheridan Point (Fig. C-27). Allison (1967) observed one value of 1.6 ppra at
the bottom at Benedict Bridge in August of 1961. Surface concentrations of
D.O. in point samples from the Patuxent do not clearly show the trend
apparent in the data of Cory (Fig. C-25).
The reduced concentrations of D.O. in bottom waters between Benedict and
Broomes Island appear to be caused by respiration and decomposition of
organic matter produced within the Patuxent estuary rather than by intrusion
of Bay waters naturally low In D.O. Although low concentrations of D.O. are
often observed below Brooaes Inland, on occasions when concentrations are low
above Brcomes Island, they are frequently higher downstream near the raouth of
St. Leonard's Creek. This cart be seen in the data fton 1977-1979 in Figure
C-26. Detailed observations of the vertical distribution of D.O., salinity
and in vivo fluoresceuce in the lower estuary during the summer of 1979 by
Mr. Stephen Doraotor of the Chesapeake Biological Laboratory clearly show
diminishing concentrations of D.O. as one proceeds upstream from the
confluence with Chesapeake Bay during periods of vertical stratification.
As nutrient loading to the Patuxent increased through the 1960's
(Chapter B), maximum concentrations of nutrients in the estuary also
increased (Figs. C-17 and C-18). Concentrations of nitrogen still decrease
to near the liaits of detection during the summer and fall and thus may limit
phytoplankton growth, but concentrations of phosphorus now remain somewhat
higher all year. Webb and D'Elia (1980) have shown how diminished
concentrations of D.O. in botto waters is correlated with increased
phosphorus concentration, presumably from accelerated rates of release of
phosphorus from the sediments, a phenomenon that probibly now occurs in the
lower Patuxent estuary. Increased nutrients have led to increased
concentrations of chlorophyll a_ (Figs. C-20, C-21, C-22), primary production
;:nd increased community metabolism (Fig. C-25), perhaps with a decrease in
production to respiration ratio (Cory, 1974). Increased surface production
coupled with a diminished euphotic zone in the lower estuary which is often
vertically stratifit.l have led to greatly reduced concentrations of D.O. in
that portion of the Patuxent. Low concentrations of D.O. have caused
mortalities of oysters at depths greater than 5 m between Benedict and
Broomes Island (Krantz, pers. coma.). From about 1976 onward, eel fishermen
have observed mortalities in their traps in the lower Patuxent estuary.
While concentrations of D.O. of less than 2 ppm were sometimes observed in
the early data, protracted periods of that condition, such as observed in
1977 and 1978 apparently did not occur. Finally, the minimum concentrations
observed in recent years at the surface (approaching 2 ppm; Fig. C-25) are
reaching levels that can be expected to cause mortalities of fish.
POTOMAC RIVER
The Potomac River estuary has been studied with varying intensity since
81
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1913. Wolman (1971) reviewed the history of the effects ot a growing
population on continuing efforts toward Improvement of water quality In the
Potomac. Early efforts were devoted to the reduction of B.O.D. by providing
first primary treatment in 1938 (Wolman, 1971) and later adding secondary
treatment in the late 1960's (see Fig. B-l).
As the most apparent problems in the Potomac were in the upper reaches
near Washington, D.C., most of the scientific and monitoring efforts have
been concentrated on the upper watershed and the tidal-fresh portion of the
estuary. Gumming, Purdy and Ritter (1916) apparently sampled nutrients and
dissolved oxygen over the oyster bars in the lower estuary during 1913, but
our efforts to locate their unreported data were unsuccessful. The first
studies of water quality th.it encompassed the length of the estuary were
those of C.B.I, during 1965-1966, reported by Carpenter, Pritchard and Whaley
(1969). By the time of those studies, chlorophyll a_ concentrations of 80 to
100 ug 1~1 were common in the portion of the estuary up to 20 miles or more
downstream from Washington, 9.C. As reported by Wolman (1971) problems with
reduced concentrations of ox/gen were common, and other workers had noted the
additional demand for oxygen caused by excessive algal blooms including
blue-green algae (Jaworski, Lnar and Villa, 1971; 1972; Jaworski, Clark and
Feigner, 1971). Comparison of the 1965-1966 data with the results of
intensive surveys during 1969-1971 (U.S.E.P.A., 1970a,b,c) (M022038, M022042,
M022043) by Jaworski, et al. (1972) showed no trends for that period,
concentrations of chlorophyll a_ exhibiting the same seasonal patterns in both
surveys, and concentrations of both major nutrients being relatively high.
Reviews of data frora more recent water quality surveys by E.P.A. (Pheiffer,
1975; Villa, Clark, Roesch and Smith, 1977; Clark and Roesch, 1978) which
were conducted after the implementation of phosphorus removal at the Blue
Plains sewage treatment plant show reduced concentrations of phosphorus in
the upper Poto:aac. Concentrations of nitrogen were similar to those found in
previous surveys and concentrations of chlorophyll a_ were as high or higher
than previously observed.
The floating mats of blue-green algae that were prominent during the
1960's were not observed in the most receiit studies, but blue-green algae
still dominated the blooms. Ar a, cyst is cyan.ps, the blue-green algae dominant
during t.he 1960's was not abundant in the work reported by Pheiffer (1975),
Villa, et al. (1977), and Clark and Roesch (197?), and while concentrations
of chlorophyll a_ were not reduced, slightly higher concentrations of
dissolved oxygen were noted in :he most recent studies. It should be noted
that in addition to the reduction J.n phosphorus loadings (Pheiffer, 1975) the
1970's have been relatively wetter than average years (Table A-l) reflected
in reduced salinities at mid-Bay (Fig. A-4). It is not yet clear what the
effects of flow versus loadings from Blue Plains are on conditions in the
upper Potomac. In spite of the offort expended on the upper Potomac estuary
to date, there is as yet no clear consensus that improvements will result
from the removal of one or the other of the major nutrients. As indicated by
Villa, et al. (1977) and Clark and Roesch (1978) the general conclusions
reached by JawDrski, Clark and Feigner (1971) are still valid. Control of
one or both nutrients will be required to effect improvement in the upper
Potomac. If nitrogen removal is necessary, the cost may be high. As
continuing efforts are barely maintaining status-quo with regard to B.O.D.
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(Anon., 1969a) It may be necessary to look to other tributaries such as the
York or Rappahannock, or the upper Bay Itself, for clues concerning necessary
improvements in water quality.
The lower Potomac (up to about, river mile 43, on soma occasions) was
included in the nutrient, turbidity, D.O., temperature, salinity, and
chlorophyll sampling conducted by C.B.I, in 1949-1951 (Hires, Stroup and
Seitz, 1963; Stroup and Wood, 1966). Table C-5 shows the concentrations of
P04J-P at the surface and chlorophyll a_ at the surface and bottom observed
during 1949-1951. The sampling dates are arranged out of chronological
sequence to provide an indication of an annual cycle. Table C-6 shows
comparable data from the same stations during the 1965-1966 sampling (Whaley,
Carpeneter and Baker^-1966) that was reported by Carpenter, et al. (1969).
Concentrations of P04 -P were higher during January to May in the later
studies. They were about the same in July and August of both studies and
lower at some stations and higher at others during October to November in the
later data.
The concentrations of chlorophyll a_ in the lower Potomac were generally
higher in 1965-1966 than during 1949-1951 during all months that ware sampled
except March-April (Tables C-5 and C-6). In May of 1950 the concentrations
of chlorophyll a_ were higher in bottom waters than at the surface (Table
C-5), an intriguing observation in light of the deep-water migrations of
dlnoflagellates observed in the Bay more recently (Tyler and Seliger, 1978).
The same phenomenon occurred on one cruise during May, 1965-1966 but was
obscured by the grouping of the data we user' (Table C-6). Liinoflagellate
"blooms" via the transport phenomenon described by Tyler and Seliger (1978)
may thus have occurred in earlier year^, although this evidence is weak. The
most notable increases in concentrations of chlorophvll ji occurred during
July. In 1949-1951 concentrations were 3 to 5 ug 1~* in surface waters
compared to 9 to 13.3 ug I"1 during July of 1965.
The slightly higher concentrations of phosphorus and considerably higher
concentrations of chlorophyll a_ during the summer in the lower Potomac
estuary suggest early effects of enrichment. The changes in the lower
estuary could become more pronounced as greater areas in the upper estuary
become light-limited through self shading of dense algal blooms. Under those
conditions in other tributaries such as the Patuxent, nutrients appear to
pass through the sediment trap (turbid) portion of the estuary and are
increasingly being expressed as higher algal standing stocks in the lower
estuary. The Potomac is a larger system with greater dilution in the lower
reaches by Bay waters, but also stronger vertical stratificaiton. Organic
production in the Potomac is thus likely to be retained within the estuary.
While the prognosis for improvement of the upper Potomac estuary through
conventional or even advanced waste treatment is poor, removal of nutrients
might prevent or delay degradation of the lower estuary.
JAMES RIVER
Aside from the observations of Gumming (1916) in the Hampton
Roads-Norfolk area on organic loading and sanitary conditions, and a later
84
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Table C-6. Ranges of concentrations at the surface of orthophosphate-P
(ug-at I""1) and at surface and bottom of chlorophyll a_ in the lower Potomac
during 1965-1966. Only stations within the areas samples in 1949-1951 were
used.
_3 Chlorophyll &_
PO-P Surface Bottom
Jan. 0.25-0.38 3.2-4.6 3.1-SG
Mar.- Apr. 0.07-2.60 1.1-20.0 1.1-9.5
May 0.04-0.60 5.8-13.2 4.3-9.8
July 0.17-0.32 9. 0-13. S 1.0-1.8
Aug.- Sept. 0.37-1.03 9.0-26.4 2.9-9.6
Oct.- Nov. 0.08-1.20 9.3-24.0 3.6-11.0
similar report, the first useful data on the James River begin in 1950 with
the early C.B.I, studies. Until the work of Brehmer and Haltiwanger (1966)
(M022018) in 1965-1966, no measurements of water quality were found for the
James River upstream from river mile 25 (25 nautical miles above the
confluence with the Bay). Unfortunataly, river flows were unusually low
during the summer months of Brehmer's and Halciwanger's study (their Appendix
E).
By the time Brehmer and Haltiwanger began their study, the upper James
appears to have already been greatly affected by enrichment. Chlorophyll a_
concentrations of 50 to 80 ug 1~1 were common at their upper three stations
in the tidal-fresh portion of the estuary, and 20 to 50 ug 1~~ were often
observed at their middle stations. Those observations can be contrasted with
earlier data from the upper Bay or the Patuxent where chlorophyll jj
concentrations in the low-salinity areas were rarely above 30 to 40 ug 1~^
and often lower in the summer months.
Concentrations of nitrogen in the upper James often show clear gradients
with much higher concentrations upstream during October through January,
higher concentrations downstream during March a.id May, and variable patterns
the other months, usually with highest concentrations at about river mile 47,
the middle- of the tidal fresh portion of the River.
Concentrations of orthophosphate-P show no seasonal or longitudinal
patterns in the data of Brehmer and Haltiwanger (1966), being generally less
than 1.9 ug-at I"-1- all year. The pronounced suciner minimum observed in the
earlier data from the upper Bay (Fig. C--1) was completely absent from the
data from the upper James in 1965-1966, suggesting again that changes had
already occurred.
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In the lower Jatnes River (river mile 0 to river mile 25), where
salinities are higher, the earliest data (Stroup and Wood, 1966; Brehmer and
Haltiwanger, 1966) show a minimum concentration of phosphorus in the spring,
generally less than 0.5 ug-at I"1-, and slightly higher concentrations in the
fall, similar to the pattern described by Newcombe (1940) for the middle Bay.
Data collected in the 1970's (Adams, Walsh, Grosch and Kuo, 1975) show
markedly higher concentrations of orthophosphate during December through May.
Concentrations were similar during June, July and November in all the
studies, and slightly higher during August through October in the 1970's
(Fig. C-28).
There have been dramatic increases in NOJ + N02 - nitrogen in the lower
James estuary (Fig. C-29). At the time cf the studies by Brehmer and
Haltiwanger (1966) (M022018) the seasonal pattern of nitrogen concentrations
in the lower James was similar to that in the lower Bay, except that spring
maxima were up to 50 ug-at 1~^ in the James (Fig. C-29) compared to about 25
ug-at 1~1 in the lower Bay (as recently as 1972; McCarthy, et al., 1977). We
plotted ranges of data from the mid-channel "reference stations" of Adams, et
al. (1975) for the section of the James estuary. Concentrations in the
spring months were similar in the two studies, bat concentrations during July
through December were much higher in the more recent samples of Adams, ct al.
(1975). At times, but not always, the highest concentrations of nitrogen in
the outfall studies of Adams, et al. (1975) were at their station 10 (on
their map) designated station 18 in their computer printout. Those high
concentrations undoubtedly were the direct result of the Williamsburg sewage
outfall a short distance downstream, but nevertheless represent current
anbient conditions in the lower James. Deletion of data from that station
tfould not significantly alter the pattern of concentrations shown in Figure
C-29. Recall that low flo is during the summer months sampled by Brehmer and
iialtiwanger (1966) might have resulted in greatly reduced non-point loading
of nitrogen during that period.
In spite of the high ambient levels of both phosphorus and nitrogen in
the lower James (Figs. C-28 and C-29), concentrations of chlorophyll a^ have
not apparently increased (Fig. C-30). In fact the pronounced spring bloom
which sometimes occurs in the lower Bay (Fig. C-16) appears to be absent in
the James in the more recent data (Fig. C-30). Brehmer and Haltiwanger
(1966) occasionally observed concentrations in excess of 20 ug 1 of
chlorophyll ji during March and April which were not seen by Adams, et al.
(1975). Brehmer and Haltiwanger (1966) also recorded a significant bloom, up
to 17 to 19 'ug 1~* of chlorophyll a_t in November and December, similar to the
early observations of spring and fall "blooms" by Nash (1947) in the lower
Patuxent River during the late 1930's. Adams, et al. (1975) found
concentrations generally below 7 ug 1~1 during the same period.
In the lower James estuary, the apparently unchanged concentrations of
chlorophyll
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dramatic increases in catches of menhaden in recent yrars (Chapter D).
The lower James is relatively turbid, compared to portions of Chesapeake
Bay with comparible salinities, bur no more so than the lower reaches of
other tributaries where increased nutrients have resulted in higher
concentrations of chlorophyll. Turbidity however has been suggested by a
number of people (in the fora of personal communication) as a possible reason
for the relatively low concentrations of chlorophyll in the lower James.
The most dramatic effects of enrichment in he Jaiaes River are apparent
in the upper reaches. Unfortunately we have no good record of historical
trends as changes apparently occurred prior to the fvrst studies of the
River.
OTHER TRIBUTARIES TO THE LOITER BAY
The York and Rappanannock Rivers were sampled occasionally 2or
phosphorus, turbidity and chlorophyll a^ during the C.B-I. studies in
1949-1951 (Stroup and Wood, 1966). Table C-7 shows the ranges of
orthophosphate-P and chlorophyll £ observed in 1949-1951. The seasonal
pattern of phosphorus concentrations was different from rhe lower J=jies River
during the same period in that during July through October in the York and
during July in the Rappahannock there were, relatively high concentrations of
phosphorus in surface waters, but rarely in excess 01 1.0 ug-at 1~1. D~ta
presented in Appendix B of the Existing Co..ditions Report (U.S.A. Corps of
Eng., 1973, Table B-XI-49) indicate concentrations of 1.6 to 16 ug-at I"1
during February, April, May aud September in the Rappahanncck during 1970.
Table C-7. Ranges of concentrations of or^hophosphate-P (ug-at 1~J) and
chlorophyll a_ (ug 1~"1) from the lower York and Rappahannock Rivers during the
1949-1951 studies b. C.B.I.
Dates _j York _g Rappahannock
PO/j-P Chi a_ P04-P Chi a
1 July-3 Aug., 1949 1.0-3.0 — 0.8-2.0
18 Aug.-6 Sept. 0.8-3.0 — 0.2-0.4
10-25 Oc:. 0.7-0.8 — 0.3-
25 Mar.-25 Apr., 1950 0.1-0.2 4 0.1-0.2 6-8
20-25 May 0.0-0 +1 4 0.0-0.1 3-8
14-19 July 0.2-0.2+ 5-V 0.1-0.3 4-',+
14 Oct.-2 Nov. 0.7-0.9+ 1-1+ 0.3-0.4 l-6+
0-1
10-23 Jan., 1951 0.1-0.2 — 0.0-0.1 1-7
21-31 May 0.44 — 0.16
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In the York. River, concentrations ranged froa 1.6 to 3.2 ug-at 1 during the
sane period (U.S.A. Corps of Eng., 1973, Table &-XI-52) (data taken from
Pheiffer, Donnelly and Possehl, 1972). The njaber of observations listed in
the Existing Conditions Report were somewhat fewer than in tiie C.B.I, data
(Table C-7) but increased concentrations of phosphorus are indicated. The
Virginia Water Quality Control Board (1976) shows that during 1968-1971 5.5
percent of stations sampled in the Rappahanr.ock River had concentrations of
orthophosphate-P in excess of reference standards. In 1972 to 1975 3.4
percent of the samples exceeded the standards. The reference level for
orthophosphate-P is 3.2 ug-at I"*, a concentration considerably higher than
those observed in the Rappahannock in 1949-1951 (Stroup and Wood, 196&). In
the York River, the Virginia State Water Quality Control Board (1976)
observed no phosphorus concpntrations in excess of the relatively high
reference levels.
Chlorophyll £ concentrations in the lower York River estuary are
considerably higher in recent years (Haas, Hastings and Webb, 1980) than were
observed in 1949-1951 (Table C-7). Neither the Corps Report (U.S. Corps of
Eng., 1973) or the Virginia 305b report (Va. State Water Quality Control
Board, 1976) provide data on concentrations of chlorophyll for comparison
with the earlier data.
In recent years visible bloonis of dinoflagellates ("red water") have
occurred in the lower York River and other tributaries. There were large
year-to-year variations in the frequency and duration of these bloods
(Zubkoff and Warriuner, 19/5) but they were not frequently noted in earlier
years. N'eilson (1978) commented rhat diurnal fluctuations in concentration
of oxygen, an indication of increas'.-d community metabolism, have been noted
in recent years. The periodic low concentrations of dissolved oxygen
observed recently in the lower York River (Haas, 1977; Webb and D'EUa, 1980;
O'Elia, et al., 1980) were not observed often in the earliest data available;
the C-3.I. data for 1949-1961 (Hires, Stroup and Seitz, 1963).
Concentrations of dissolved oxygen were less than 2 ppta in bottom waters of
the York River on only one of nine occasions when measurements were made
during the months of July, August, and Septenber. In recent years there are
protracted periods when bottom waters are low in dissolved oxygen.
There are insufficient data to establish trends for concentrations of
nitrogen in the York and Rappahannock Rivers. But it appears that phosphorus
and chlorophyll _a have increased in the lower estuaries. It has been shown,
however, that considerable short-term variations in concentration occur for
both N' and P (Webb and D'Elia, 1980). These variations are due to
hydrographic processes.
A number of the smaller tributaries to the Bay in the Hampton
Roads-Norfolk area have been surveyed in recent years (N'eilson, 1978). Many
show severe effects of enrichment, but receive huge amounts of effluent and
non-point runoff relative to their volumes. There are dense algal blooms and
periods of low oxygen concentrations in several of the smaller tributaries
including the Elizabeth, Back and Poquoson Rivers.
The data base for the smaller tributaries of the lower Bay in part
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reflects the first preception of problems. Discharges that are high in
B.O.D. in the freshwater portions of the larger tributaries have been the
first order of concern. More attention needs to be given in future studi_s
to se.ison.il, monthly and weekly variations in nutrients and distribution of
chlorophyll ji, and the vertical distribution of dissolved oxygen in the
stratified portions of the estuaries.
SUMMARY OF WATER QUALITY TREVDS
The changes that have been observed in concentrations of nutrients and
chlorophyll a_ in various parts of the Bay can be explained in a way that
conforms to the conceptual model presented by Webb (1980). Figure C-31 shows
the box model from Figure 2 of Webb (1980). The most important feature of
the conceptual model is that increased inputs of nutrients or organic carbon
result in increased f 1ows of material and energy through the Bay ecosystem.
There may, or may not, be increases in the sizes of the comp.irtr.ents, i.e.,
the standing stocks of the components such as nitrogen, phosphorus, algae,
fish, etc. Changes in rates of flow through an ecosystem would be undetected
by most routine studies of water qualtiy, which sample only standing stocks.
Few < f the studies we reviewed included measurements of rates of
transfer through trophic levels of the Bay ecosystem. Those that did usually
only measured rates of primary productivity. The following conparisons of
effects of enrich-nent on various parts of the Bay, therefore, begin with the
assumption that increased inputs of nutrients or carbon to a portion of the
Bay cause increased rates of flow of nutrients and energy through the biota.
Increases in standing s:ock are taken to mean either that the size of a
compartment has increased to accommodate higher flows, or that flow out has
decreased, causing accumulation within a particular component.
There are clearly different results from the additions of nutrients to
various parts of the -Jlay and its tributaries. Table C~8 shows a summary of
the changes observed in three major components of the Bay ecosystem,
phosphorus, nitrogen, and algae, represented by chlorophyll _a.
In the upper Bay, concentrations of phosphorus have increased,
concentrations of nitrogen have remained unchanged and chlorophyll has
increased. The loading trends developed by E.P.A. suggest that inputs of
both nitrogen and phosphorus to the upper Say are increasing (Guide and
Villa, 1972). It appears that virtually all of the additional nitrogen is
either presently passing through the nutrient pool into other component: of
the ecosystem, or is being lost through processes such as denitrification
(Kaplan, et al., 1978; Elkins, 1978; McElroy, et al., 1978; Elkins, Wofsy and
McElroy, 1980). The seasonal pattern previously shown by concentrations of
phosphorus in the upper Bay no longer occurs. Concentrations of phosphorus
are now variable but, in aggregate, uniform all year in the upper Bay.
Jaworski (19bO) has concluded that based on ratios of nutrients in inputs to
the upper Bay, phosphorus should be limiting. However, in our opinion the
historical trends suggest that nitrogen is the more likely limiting nutrient
at present. The upper Bay is relatively turbid and it is quite likely that
low light intensity often limits algal production. There is evidence that
some species of algae grow at lower light intensities in the presence of
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higher ..onct-ntrations of nutrients, however, and the relationships between
light, nutrients and algal production in the upper Bay are likely to be
complicated and variable with time. Our perception of nutrient limitation in
the upper Bay has recently besn Hide more complicated by the discovery by
Loftus, Place and Seliner (197'j) that dinoflagellnle blooms initiated by
nutrient pulses from land runoff may become carbon-lira!ted in the upper Say.
The role of inorganic carbon in these cases is to prolong the duration of the
blooms, and presumably, increase the total production of a bloom. The
occurrence of blue-green algne in areas of low or no salinity, and the
possibilities of nitrogen fixation and secondary effects on consumers further
complicate the interpretation of events in the upper Bay.
The effects of enrichment in the middle Bay are modest (Table C-3).
Early signs of change are present In the fora of slightly higher
concentrations of phosphorus and increased concentrations of chlorophyll. No
one has yet determined whether the decreased transparency of waters in the
middle Bay, apparently caused by incre,.»oed phyloplankton, has partly offset
the presumed increases in primary production indicated by the higher standing
stocks of algae.
There .-.re some indications that increased algal production and the now
common occurrenre of dinoflagellate blooms in the middle Bay are having an
effect on the intensity of the deep water 0.0. minimum. There are major
effects of altered 0.0. regimes on rcmineralizatiors from the sediments (Webb
and D'Elia, 19^0), a prooes.7 which nay in turn be driven by rates of
deposition or particulate organic natter to the sediments (Boynton, Kemp and
Osborne, 1980).
The lover Bay appears to be relatively unaffected by nutrient inputs.
Only phosphorus has increased slightly. The reasons for the slight impact of
added nutrients on the lower Bay nay be two-fold. first, the exchanges of
water across the Bay mouth are large and dilution, therefore, great. More
importantly, nutrients added to the upper Bay and tributaries, particularly
nitrogen, release phytoplankton from nutrient limitation. The nutrients are
then incorporated into particulate forms and trapped within the region of
utilization by the two-layered circulation of the Bay. Evidence from the
tributaries suggests that as algal stocks increase, light becomes more
important as a limiting factor and nutrients pass further downstream before
being incorporated into oiomass. Increased (over conditions in 1949-1951)
algal production probably now extends below the Potomac River in the mainstem
of Chesapeake Bay.
There are increased concentrations of both major nutrients and of
chlorophyll a^ in all parts of the Patuxent R.iver estuary. There appears to
have been a downstream progression with time of areas with increased
concentrations of chlorophyll a.
Because of the extent of the data base in the Patuxent River estuary
(Appendix B), some of which we did not obtain, that system provides the most
well documented example of the effects of enrichment in a Bay tributary. As
nutrient concentrations increased in the upper, turbid portion of the
Patuxeat, chlorophyll j3 increased somewhat. Ambient concentrations of
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nutrients are now relatively high all year in the upper Patuxent, suggesting
light linitation of primary production. Episodes, of low concentrations of
D.O. In the upper Patuxent appear to be related to high concentrations of
partlculate carbon, bat not chlorophyll. Increased nutrient concentrations
in the lower, two-layered part of the Patuxent have been paralleled by large
increases in maximum concentrations of chlorophyll and decreases in
transparency of the water during the summer -joaths. Increased variations in
concentrations of D.O. in surface waters and extended periods of near anoxia
in hot ton waters which now occur were not observed in earlier studies. There
have been reports of mortalities of benthic animals and effects on commercial
fisheries that are caused by reduced concentrations of oxygen. Ratios of
nitrogjn to phosphorus are low in the inputs to the Patuxent (Jaworskl,
1980), in the nutrients remlneralized by the benthos (Boynton, Kemp and
Osborne, 1980) and in the water colimn during the summer months. Data taken
during the late 1930's suggest that natural dissolved phosphorus
concentrations in surface waters were high enough to support the algal
standing stocks presently being observed. The fact that phosphorus
regeneration from the tediraents is enhanced by increased organic production
(Nixon, 1980; Boynton, Kemp and Osborne, 1980) and further enhanced by
reduced concentrations of D.O. (We'ob and O'Elia, 1980) suggests that algal
production in the lower Patuxent could not be reduced by controlling
phosphorus in the watershed. Some nitrogen appears to be lost from the
Patuxent through denitrification at present (the nutrient budget cannot be
balanced) (Mihursky and Boynton, 1978; Boynton, Kemp and Osborne, 1980).
During early studies, concentrations of nitrate and nitrite were very low
during the suisaer months, and still become quite low at times, suggesting
that nitrogen control would reduce algal production.
The apparent high dependence of phytoplankton on recycled nitrogen
during the sunvner months in the Patuxent (Boynton, Kerap and Osborne, 1980)
suggests that total annual in_p_ut_ rather than seasonal inputs are controlling
the magnitude of primary production. This hypothesis has been proposed
previously for coastal waters in general (Snayda, 1976). Thus, seasonal
removal of nitrogen would be less effective than year-round control, unless
it were specifically known that seasonal pulses of nutrients passed through
the system unassiaiiiated.
The changes that have occurred in the Patuxent are likely to progress
further as loading increases with population growth in the basin. Similar
changes could be expected with urbanization of other medium-sized tribjtaries
of the Bay.
The extensive studies of the Potomac estuary show that the earliest
problems were with high B.O.D in untreated and treated sewage. Recognition
of changes brought about by nutrient additions did not occur until after the
advent of dense algal blooms. Nutient and chlorophyll concentrations were
not measured early enough in the upper Potomac to document changes.
Increased production of algae in the Potomac is now occurring in the
lower reaches, but the concentrations of chlorophyll ^_ are still generally
lower than the earliest observations from the Patuxent. The area in the
Potomac where the next major changes might occur is between river miles 30 to
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50, the usual upper limits of salt iricrusion. During one year of the
19S9-1971 E.E.A. studies concentrations of chlorophyll well in excess of 60
ug !"*• were reported for that area (Jaworski. et al., 1972), but
concentrations were generally below 35 ug I"'-.
The uncertainty over nutrient limitation in the Potomac was mentioned
previously. Work presently underway on the Potomac by E.P.A., the State of
Maryland, and the U.S. Geological Survey may help resolve the issue. An
empirical example which nay be applied to the upper Potomac, or the
low-salinity turbid areas of any Bay tributary is available in the Paralico
River estuary in N'orth Carolina. The Pamlico is heavily loaded with
phosphorus from cotnrnerical mining operations but has relatively little
external input of nitrogen, only about 5 percent of the annual phytoplankton
needs (fCuenzler, Stanley and Koenings, 1979). Phytoplankton production an^
standing crops, which are modest (and similar to the pre--perturbation
conditions in the Patuxent) are sustained by nitrogen recycled within the
system. We suspect that tributaries to Chesapeake Bay, including the
Potomac, mi^ht be functionally similar to the Pamlico estuary, given an
excess of phosphorus without large amounts of ndded nitrogen. However, the
role of nitrogen fixers (blue-green algae) and the conditions that promote
their development in some tributaries (e.g., the Potomac, James and some
areas in the upper Bay) but not in others (e.g., the Patuxent, York and
Rappahannock) needs to be better understood before nutrient limitations can
be understood with certainty.
The Rappahannock and York Rivers ">-'ve both experienced increases in
concentrations of phosphorus and chic.ophyll ji (Table C-8). Our data were
not sufficient to establish trends for nitrogen. The changes in the lower
reaches of both Rivers appear to be similar to those occurring in the
Patuxent. Minimum concentrations of dissolved oxygen in bottom waters of the
lower York River have decreased, but secondary effects are not well known
(but see Neilson and Cronin, 1980).
The processes involved in the periodic anoxia in the lower York Estuary
are complicated (Haas, 1976; Webb and D'Elia, 1980; O'Elia, Webb, Wetzel,
1980) and result in cyclic changes in rates of remineralization of nutriments
from the sediments. The variability in rates of remineralization
demonstrated by the studies on the lower York River is extremely important as
it illustrates the tenuity of steady-state models currently used to predict
estuarine water quality by management organizations (e.g., see Salas and
Thomann, 1976 or more recent examples in O'Connor, 1980). Where cyclic
changes have important effects on ecosystem function a good fit by a
steady-state model should probably be considered merely fortuitous, and of
little predictive value.
Changes in the upper James estuary have essentially paralleled those in
the Potomac, but have been less well documented. Industrial effluents and
their B.O.D. are more important in the James, but the systems are otherwise
similar.
The changes that have occurred in lower James (Table C-8) are perhaps
the most interesting that we have encountered. There have been increases in
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both major nutrients without concurrent increases in chlorophyll _a. It has
been suggested that dilution is a major factor in the maintenance of the
lower James in a relatively unaltered state (Ueilson, 1978). It is difficult
to see, however, how dilution can account for the relatively low
concentrations of chlorophyll _a in the presence of increased nutrients. We
proposed earlier in the chapter that the conditions in the lower James could
fit the conceptual model proposed by Webb (19SO) (Fig. C-31), if increased
flows through the primary producers were accumulating in other compartments
(trophic levels). If that were the case, one might expect effects of
increased production to be manifested in the concentrations of dissolved
oxygen in the bottom waters of the lower James, a two-layered estuary. Low
concentrations of 9.0. In bottom waters have been detected in recent years
during studies conducted by the V.I.M.S. (published in: Corps, of Eng.,
1973). Unfortunate?y, the early data base does not allow the establishment
of trends with certainty, but there were no instances *hen 0.0.
concentrations were less than about 3 ppm in the early studies by C.B.I.
(Hires, Stroup and Seitz, 1963). Periodic monitoring of dissolved oxygen
should be continued in the lower James. It would also be extremely useful to
have some recent measurements of rates of primary production and respiration
from the lower James or the lower Bay that are directly comparable to the
early Wi>rk done by Patten, et al. (1963).
r
INORGANIC
NUTRIENTS
PHYTOPLANKTON
OTHER
AUTOTROPHS
V,
s
DEAD
ORGANIC MATTER
DISSOLVED AND
PARTICIPATE
s,
J>
HETEROTROPHIC
BACTERIA
HERBIVORES
BACTERIVORES
CARNIVORES
AND
OMNIVORES
Figure C-31. Box diagram of conceptual -nodal proposed by Webb (1980),
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CHAPTER D
COMMERCIAL FISHERY PRODUCTION
At the beginning of our efforts to document the effects of excessive
enrichment on commercial fishery yields we were aware that variations in at
least two important fisheries, oysters (Uianowicz, Caplins and Dunnington,
1980) and striped bass (Merriman, 1941; Heinle, et al., 1976; Boynton,
Setzler, Wood, Zion, Homer and Mihursky, 1977; Van Winlcol, Kirk and Reist,
1979) were closely correlated with variations in climate. In the Gulf of
Mains (Sutcliffe, Drinkwater and Mtiir, 1977), and in other coastal areas,
Sutcliffe (1972) proposed mechanisms by which climatic variations affect
commerical fisheries through variations in nutrient inputs and subsequent
primary production. Jeffries and Johnson (1974) proposed an effect of
temperature on larval flounder in Narragansett Bay which explained much of
the subsequent variation in coramericsl catch.
For the foragoing reasons, we felt that an analysis of the effects of
climatic variation on commercial landings was imperative before the effects
of excessive enrichment could be evaluated. The funding provided for this
task was largely consumed by the compilation of the data base. The format of
the National Marine Fisheries Service (M.M.F.S.) data base (catches broken.
down by county or water area) was not appropriate for distinguishing Bay-wide
trends. We modified the N.M.F.S. data base to permit comparison of trends in
landings with time for Maryland and Virginia, or for both states combined,
excluding coastal catches. Following this effort, funding was not jivailable
for extensive analyses, however some our colleagues were able to use the data
base in Appendix C to analyze the effects of climatic factors on commercial
landings in Maryland. A paper has been prepared for publication (Uianowicz
et al., ras. submitted) and appears as Appendix D. Maryland catch statistics
were used in the analysis because of the specific interest of the authors.
The separate catch statistics for the Virginia portion of the Bay are
available in our data base (Appendix C) and are used in tha remainder of this
Chapter, which introduces some qualifications concerning the masking of
possiMe effects of enrichment by variations in climate which have
periodicities in excess of the time scale of changes we perceive to be caused
by enrichment of Chesapeake Bay.
LONG TERM TRENDS OF FUNCTIONAL GROUPS OF FISH
The paper by Uianowicz et al. (ms. submitted) describes a number of
remarkably good correlations between climatic variables and co;nnercial
fishery landings. A simple correlative approach to the analysis of fishery
data introduces a serious hazard of discovering good correlations which
cannot be explained biologically. We attempted to determine the best time
lag to use for a simple correlation between commercial landings of five
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anadromous species and deviation from January and February mean air
temperature. The catch of one of the species tested, striped bass, is known
to be inversely related to deviations from winter temperatures (Merriman,
1941; Heinle, et al. , 1976). We- postulated that other anadromous fishes-
might be affected by the same variation in food resources thought to affect
striped bass. In addition, we hoped that variations in the simple
correlation coefficient as a function of titne lag would indicate the age at
which a given species had the greatest impact on the commercial landings.
Table D-l shows that the catch of striped bass ana white perch were strongly
and inversely correlated with deviations fro:n long-term average winter
temperatures, regardless of time lag of 1-8 yrs, indicating a relationship to
cold winters. The catch of alewives was positively correlated at all time
lags. The catches of gizzard shad and American shad were riot correlated to
winter temperatures at time lags of 1-4 yrs but were at lags of 5-8 yrs. As
American shad mature at an average age of 4-5 yrs (Jones, Martin, and Hardy,
1978), the time lag for the correlation seems logical. Gizzard shad,
however, mature in 2-3 yrs (Jones, et al., 1978) making the highly
significant correlations at 6 and 7 yrs difficult to explain. The
correlation coefficients for striped bass were highest at 2 and 3 yrs lag,
concurrent with the age of entry into the commercial catch. The continuing
high correlations for that species may reflect the continued effects of
dominant year-classes ^n the fishery.
Table D-l. Correlation coefficients between commercial landings of five
species of anadromous fish and deviations from average winter temperatures
with tirna lags of 1-8 years.
Time Lags (yr)/Correlation Coefficients
12345678
Species K'=49 N=48 N=47 N=45 N=45 M=44 N=43 N=42
Alewife .476 .388 .326 .347 .388 .499 .513 .471
American Shad .093 .015 .026 .166 .242 .236 .282 .328
Striped Bass -.464 -.590 -.565 -.445 -.325 -.301 -.328 -.274
White Perch -.409 -.375 -.441 -.462 -.389 -.309 -.382 .273
Gizzard Shad .133 .020 .019 .072 .263 .444 .341 .124
Another quite plausable explanation for the small effect of time lag on
the correlation coefficients for alewives, striped bass and white perch may
lie in the autocorrelacion of climatic variables. Heinle, et al. (1977)
noted that poor and good years for the striped bass fishery were clustered,
i.e., periods of several poor years alternating with periods of several good
years as shown by Figure 4 of the paper by Ulanowicz, et al. (ms. submitted,
see Appendix D). Thise may in fact be related to long-term (20-22 yr)
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climatic cycles (Van Winkle, et al., 1979) which are thi.iiselves correlated
with solar cycles (Mock and Hibler, 1976; Hibler and Johnson, 1979). The
period of the cycle shown for soft-shelled claims in Figure 3 and for striped
bass in Figure 4 of the. paper by Ulanowicz, et al. (ms. submitted) is
approximately 20 yr, noted also by Van Winkel, Kirk and Reist (1979) and in
Figure A-l.
If effects of cultural activities, such as excessive enrichment, on
commercial landings have occurred only relatively recently (since about
1965-1970 for effects of trophic changes in most of the Bay; Chapter C), and
the direction of the changes they cause matches the long-term cycles, those
cultural effects would be dificult to detect. Landings of striped bass and
American shad in Chesapeake Bay are now at all-time lows. We cannot yet tell
whether thir, is within the range of natural variation, or is an effect of
man. Note chat during the same period, freshwater flows to the Bay have been
higher than average, and salinities lower (Chapter A).
We suspected that factors afferning the success of one spring spawning
anadromous species might similarly it.-luence other anadromous species which
spawn in the spring. As can be seen in Chapter C, the greatest effect3 of
enrichment of the Bay occur in the low salinity areas. Total catches in
Chesapeake Bav of four anadromous fish, alewife, American shad, striped bass
and white perch, were compared with total landings of seven species which
spawn in marine waters, bluefish, croaker, flounder, scup (porgy), seabass,
seatrout (weakfish) and soot from 1952-1975 and are plotted in Figure D-l.
Prior to the decade of the 1970's, the lowest total landings of the
anadroinous group were 530 million pounds, occurring in 1960. The highest
landings were about 45-50 million pounds in 1965, 1967 and 1968. Since 1969
the landings of the anadromous group have declined to a series of new lows in
1971-1975 of about 20 million pounds. Landings of the marine group were
highest in the late 1950's, and lowest in 1969. The trend for the marine
group has been generally upward since 1969, but not to previous high levels.
There is a rough inverse relationship between the catches of the marine group
and the anadromous group up to 1970 (Fig. D-2). After 1970 the decreased
landings of the anadromous group are not offset by proportional increases in
landings of the marine group.
The total landings for Chesapeake Bay are completely dominated by
menhaden (Fig. D-3). Note that menhaden catches in recent years have been
300-500 million pounds versus about 30 million pounds for all other fish.
Menhaden catches fluctuated between 100 and 200 million pounds annually
between 1930 and 1952. They then rose to between 200 and 350 million pounds
annually through 1969 and then rose again to present high levels, fluctuating
around 400 million pounds annually (Fig. D-3).
Menhaden occupy a relatively low trophic level, feeding primarily on
zooplankton and on phytoplankton larger than 20 urn in diameter (June and
Carlson, 1971; Durbin and Durbin, 1975). Increasing planktonic production
and standing crops (Chapter C) might thus favor menhaden. The increased
catches of menhaden from 1970 onwards coincide in time with some of the
observr-d changes in the Bay that suggest increased production of plankton.
It is not clear from our historical review of water quality that the dramatic
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increase in catches during ths early 1950's was accompanied by any change in
planktonic production.
Given the increases in catches of menhaden, we examined the trends for
conraerical landings grouped by trophic level. Fish were assigned to three
groups: plankt5vores, top carnivores, and invertebrate carnivores
(Table 0-2), based on general knowledge of the fisheries staff at the
Chesapeake Biological Laboratory, our knowledge of the literature, and an
ongoing project on food habits of fishes in Chesapeake Bay (Homer and Jones,
pcrs. conna.). In the Maryland portion of Chesapeake Bay, catches of
planktivores have remained relatively constant since the early 1950's
(Fig. 0-4). Declines in catches oT anadronous planktivores such as American
shad and alewives (see Ulanowicz, et al., ris. submitted, Appendix 0) since
1969 have been offset by increases in catches of merhaden in the upper
Chesapeake Bay. Landings of top carnivores and invertebrate carnivores have
l/een declining slowly (Fig. 0-4). In the lower Bay menhaden completely
dominate the planktivorous category. Catches of rcenhaden have increased as
discussed previously. Catches of top carnivores and invertebrate carnivores
have declined (Fig. D-5) in a pattern similar to that seen in the upper Bay
(Fig. D-4).
Table D-Z. Trophic groupings of Chesapeake Bay fishes. Generic and specific
names indicate dorsinants in the catches but are not all-inclusive. Common
names are as reported in the National Marine Fisheries Service data base.
Planktivores
Alewife
Alosa pseudoharengus
American Shad
Alosa sapidissima
Atlantic Menhaden
Brevoortia tyrannus
Butterftsh
Peprilus triacant'nus
P. alepidotus
Gizzard Shad
Oorosoma cepedianum
Top Carnivores
Bluefish
Pomatomus saitatrix
Flounders
Pseudopleuronectes americanus
Seabass
Centropristes spp.
Striped Bass
Morone saxattlis
Weakfish
Cynoscion regalis
Invertebrate
Predators
Blackdrum
Pogonias cromis
Catfish and Bullheads
Ictalurus spp.
Croaker
Micropogon undulatus
Eels
Anguilla rostrata
Scup
Stenotonus rhrysops
Swellfish
Sphaeroides maculatus
Spot ~~~~~
Leiostomus xanthunis
White Perch
Morone americanus
SUMMARY
There has thus been a Bay-wide decrease in anadromous spawners from
about 1969 onwards, including planktivorous species (Fig. D-l) when menhaden
are not included- Catches of menhaden have increased from 1969 onwards.
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Increases in cat..-.!; (and presumably abundance) of one top carnivore, bluefish,
have been more than offset by decreases in an anadromous top carnivore,
striped bass. In a general way, the fish population in Chesapeake Bay is
becoming more dominated by pianktivores, with diminished nuubers of
invertebrate predators and top carnivores (Figs. D-4 and D-5). However, it
cannot be safely concluded that this represents the sort of shift in
community structure that is known, to occur in other ecosysteos as a result of
excessive enrichment (Webb, 1930). As mentioned previously, the period
during which the Bay tv:-, experienced apparent changes in trophic state, from
the mid-19601s onward, aay coincide with the half cycle for natural
variations in abundance. If species whose abundance might be sxpected to
increase naturally (e.g., striped bass, alevives and soft-shelled clams; c.f.
Ulanowicz, et al., cis. submitted) do not do so in the next few years, we may
more strongly believe that permanent changes have occurred.
The full historical record of cotrrnercial landings for Chesapeake Bay,
and the ocean side of Maryland and Virginia is available through the
University of Maryland, Computer Science Center. Documentation for the use
of the fisheries data base is in Appendix C.
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CiiAPTER E
TiiE CURRENT STATUS OF Cii
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this project (McErlean and Reed, 1979) has yet to be tested. It or one like
it may prove to be a useful tool for indicating future and past changes in
trophic state of Chesapeake Bay. We believe that such indices will be most
useful in identifying problem areas and conditions for more intensive study,
but are of limited usefulness in providing managers with specific courses of
action to correct the problems.
Although there are no simple, universal indicators of trophic state or
of the status of the Bay as a whole, increased primary production is an
important factor and is usually indicated by some increase in algal biomass,
not necessarily proportional to the increases in production. Increases in
algal biomass are of obvious concern for the potential effects of algal
decomposition on oxygen concentration. Accordingly, we chose a commonly
measured indicator of algal biomass, the concentration of chlorophyll a_, as
one usable indicator cf trophic state. It is only an indicator, however, not
an accurate measurement. This approach is consistent with that taken in most
studies of the effects of nutrient enrichment in freshwaters.
An estuary contains longitudinal gradients in chemical composition that
result in gradients in natural trophic state; consequently we have selected
different "standards" for chlorophyll for different parts of the Bay to
reflect these gradients. We wish to emphasize that although these standards
are somewhat arbitrary, they were chosen on the basis of (1) our best
scientific judgment and experience, (2) standards adopted for other areas,
and (3) deflection of levels from his'oric, natural periods of stability. As
emphasized in Chapter C, early (prior r.o 1960's) attempts at estimating
chlorophyll ji probably erred on the hijjh side, so the increases that have
been observed since the late 1950's are probably analytically real and
properly comparable. The reader is reminded here in considering our
standards that a chlorophyll a concentration of about 100 ug 1~1 would
represent enough organic plant material alone to deplete about 12 ing 1~1 of
dissolved oxygen during decomposition (an amount of oxygen that would clearly
exceed summer saturation values in the Chesapeake estuary or its
tributaries).
In low-salinity areas (less than 8-12 ppt) concentrations of chlorophyll
&_ between 30 and 60 ug !"*• during the summer months were taken to indicate
moderate enrichment. Concentrations over 60 ug 1~^ were taken to indicate
high enrichment so that injury to the desired quality of the system is
present or potential. In areas of higher salinity, historical data indicate
that concentrations of chlorophyll a_ rarely exceeded 20 ug I"*- during the
summer in unenriched portions of Chesapeake Bay. Therefore the observation
of concentrations of 20 to 40 ug i~^ during the summer was taken to indicate
moderate enrichment. Concentrations over 40 ug 1~1 were taken to indicate
considerable and probably undesirable enrichment. Figure E-l shows the
present (1970-1979) trophic state of Chesapeake Bay based on the summer
distribution of chlorophyll £ (from all of the data sources used in this
report) .
Changes in trophic state are not necessarily detrimental.
Aquaculturists have been fertilizing ponds for centuries to increase
production. When ehinges in trophic state detract from human uses, they are
110
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- „.. ,.,. - ,,,, ~-r-v. „
_ Chesapeake Bay - \ -V »-f<
\ Region ( 'W^-J^ ^
i i'^^l^1 "S^ ^
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,? 1 -' \X A - i - •" '^ '
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i ^\,Vpi>'r,t:3
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|s ijs4 . •vf.^->-Y ii^M-^
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perceived as detrinental (see Meilson, 1980). However, one of the greatest
difficulties managers face in dealing with changes in the "trophic status" of
the Bay is that different users have different perceptions as to what
constitutes a detrimental effect. Relative abundances of various commercial
fisheries species may be altered by enrichment to the simultaneous delight
and disgust of fishermen who specialize on the differently affected species.
As stated .ibove, one clear effect of enrichment that virtually everyone
preceives as detrimental is oxygen depletion in the v/ater column. We derived
a Bather stronf. consensus from the participants at our workshop in March 1979
that alteratio is of natural patterns of concentrations of dissolved oxygen
can provide a neaningful indication to managers of an important consequence
of enrichment. We stress "alterations" because although low D.O.
concentrationj are certainly of ecological importance, some portions of
Chesapeake Bay have naturally low concentrations of D.O. in bottom waters
(Newcomhe anc Home, 1938; Hires, Stroup, and Seitz, 1963) and probably are
unalterable by management of anthropogenic enrichment. In contrast, Figure
E-2 shows portions of Chesapeake Bay where our data review suggerts that
alterations of natural oxygen regimes have occurred. Detrimental effects
have been noted in parts of the sub-estuaries of the mid-bay, e.g., the loss
of oysters from leased grounds in the Patuxeni, and obnoxious dense algal
populations in the upper Potomac River. However, the picture is not yet
clear Jor the bay proper. Deep water oxygen concentrations result from very
complex infractions of respiratory and chemical processes with physical
mixing processes. Oxygen measurement after a long quiescent period may
reveal anoxia whereas observations following enhanced vertical mixing may
show oxygen ;;o present. The onset of seasonal oxygen decline in the spring
is linked to the effect of freshwater inflow on stratification and
re-oxygenatioii in the fall is related to che effects of surface water cooling
and local wind velocity on destratification. Because these complex
relationships are not completely understood and because the historical data
are not accompanied by derailed local meteorological records, we must still
view the apparent trends in the mid-bay cautiously.
Many of the detrimental effects of excessive enrichment are related to
changes in the quality of organisms (i.e., species composition) rather than,
or in addition to, changes in the quantity present. This is still another
determinant of "trophic state" and "water quality." For example, blue-green
algae become dominant under some circumstances, leading to other changes in
the trophic structure and quality of an ecosystem. It has been suggested
that "management" of trophic structure by the manipulation of nutrient
balance might be possible in some cases (Ryther and Officer, 1980).
Management would allow increased rates of production to be channeled into
desirable products.
An increased supply of harvestable species is a worthy goal. However,.
our present knowledge of trophic structure and transfer rates is inadequate
to permit intelligent tuning of production in estuaries. Webb (1980) has
pointed out that many commonly accepted concepts about trophic relationships
are really little more than dogma. Chesapeake Bay is too valuable a resource
to risk further damage by allowing changes of the sort that have occurred in
the upper Bay, and some tributaries, so that conservative management
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••
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Chesapeake Bay -
Region
Q>
• .-*« >«
> \ \v* ,v ^5
^v?%
r t -:^3^
s
1
,m.
^fl
' >S
• ^' 4
, > rj --/ sTl
•, ^V^s >^H
-- >a-*i xV.»
'
Figure E-2. Portions of the Chesapeake Bay where natural regimes of
dissolved oxygen appear to have changed (=;ee text).
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practices are strongly recommended.
Because not enough is presently known to "manage" properly our inputs to
the Bay, sensible efforts to reduce then should continue. The indications
that nitrosjen, rather than phosphorus, is limiting in the lower and middle
Bay suggest that affordable advanced technologies for N removal or new H
input strategies should be sought. Workable management programs for the
future may involve practices, such as land application, that are
unconventional and have been anathema to many practicing sanitary
engineers—but our minds must remain open to possible solutions to the
problems, be they institutional, legal, social, or technological.
We strongly recommend continued reasoned and scientific approaches to
the assessment of nutrient enrichment of estuaries. There is presently too
great a desire for quick fixes to the problems and a need for better
communication among managers, scientists, modelers, and the public. For
their part, managers must have patience with the limitations of present
scientific knowledge, be aware f the role of "basic research," and
understand that indices and models do not exist that can give as output
instant managerial solutions. For their part, scientists must be willing to
seek practical applications of their basic research findings and to
communicate and interpret scientific findings to the managers, the modelers
and the public. For their part, modelers should be candid about the
limitations of their models and impress upon the other parties the usefulness
of models in finding gaps in knowledge and in designing future research
programs to address the environmental problems. And finally, for its part
the public must patiently realize that solution to enrichment problems may be
costly, difficult and slow to implement, and unpopular for other reasons—but
essential for future uses of the Chesapeake system.
There is no doubt in the authors' minds that Chesapeake Bay has been
affected by nutrient enrichment from man's activities. Although present
trends are disturbing, enrichment problems are not yet of critical
proportions throughout most of the estuary, and the Bay remains for the most
part an attractive and useful ecosystem. But demographic projections for the
Chesapeake's watershed and our present evidence of extending alteration are
portents of serious ecological losses in the future—unless preventive action
is taken in the present.
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Appendix A
Accessing Environnental Data Base
Directory Climatic Data
J. S. Wilson
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Appendix A
Computer System
Access to the University of Maryland computer facilities used to store
the data and programs described herein require both an account number and
password. Interested persons may request the creation of a computer account
through the Office cf User Services, Computer Science Center, University of
Maryland, College Park, :Q, 20742 (301) 454-4255. Applicants need request
access to the UHIVAC 1108 oi.ly since no project data is immediately
accessable via the companion computer system (UNIVAC 1100/41).
Since instruction in the operating system command language is beyond the
scope of this report, no detailed explanations of the computer commands
recommended for use in accessing project data will be given. An assumption
of working familiaricy with the UNIVA.C command language is made.
Documentation of the operating system command syntax and usage is found in a
Computer Science Center computer note CN-13.3 l_. Computer notes are
available for reference or sale at the program library, Computer Science
Center, (301) 454-4261.
Accessing Climatic Data
The 26 annual series of environmental data referenced in Chapter D of
this report are stored as individual elements (named A-Z) of a program file
on a reel of magnetic tape (reel number P10934) at the Computer Science
Center of the University of Maryland. The program file is the first file on
tape P10934 and was copied using l^COPY with the "G" option at a density of
6250 frames per inch.
The individual annual series are described below with their
co-responding element naires.
A Annual Average Salinity
B Annual Average Water Temperature
C Annual Average Air Temperature
D Annual Average Precipitation
E Annual Cumulative Excesses Salinity
F Annual Cumulative Excesses Water Temperature
G Annual Cumulative Excesses Air TemperatuL^
H Annual Cumulative Excesses Precipitation
I Annual Cumulative Deficits Salinitv
1 University o_f_ Maryland UN'IVAC U00_ Series Re_ Publication CN-13.3 Prochazka,
J.C. and E.U. Putnam, Computer Science Center, University of Maryland,
January 1976
130
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J Annual Cumulative Deficits Water Temperature
K. Annual Cumulative Deficits Air Temperature
L Annual Extreme Values Salinity +
M Annual Extrene Values Salinity -
N Annual Extreme Values Water Tenperature +
0 Annual Extreme Values Wator Temperature -
P Annual Extreme Values Air Terapetature +
Q Annual Extreme Values Air Teraperatu, 2 -
R Annual Extreme Values Precipitation +
S Annual Episodes Salinity +
T Annual Episodes Salinity -
U Annual Episodes Water Temperature +
V Annual Episodes Water Temperature -
W Annual Episodes Air Temperature +
X Annual Episodes Air Temperature -
Y Annual Episodes Precipitation +
Z Animal Episodes Precipitation -
The following operating system commands will create a mass scorage file
and copy the climate data into that file.
@CAT,P CLIMATE.
@ASG,T TAPE.,U9S,P10934
@COPY,G TAPE..CLIMATE.
If no other data fron the tape is required, it m?y be released by the
following commands.
9REWIND TAPE.
@FRES TAPE.
The Univeristy of Maryland Text Editor processor <@ED> may then be used
to examine and extract individual elements of the mass storage file CLIMATE.
which now contain the climatic daca. The Text Editor is documented in
Univeristy of Maryland Computer Note CN-7.9 1_ (or latest version). This
manual is also available from the Computer Science Center's program library.
1 Text Editor User's Guide, Computer Note CN-7.9, ,P.E. Hagerty and K..E.
Sibbald, Computer Science Center, Univeristy of Maryland, August 1976
131
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*
Appendix B
Environmental Data Base Directory
M. Cole-Jones
A. B. Caplins
J. S. Wilson
D. R. Heinle
132
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Table of Contents
Preface 133
Listing of data files by number 134
Key to file descriptors 135
Parameter code. 137
Abbreviated description of data files ^-"
Data Base description 142
Instructions for use of Data Base
133
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Preface
The beginning point for the following data base was the compilation from
the NODC system by Lynch and McErlean (EPA Contract #68-01-3994 to the
Chesapeake Research Consortium, Inc.)- It was apparent that the Bay Data
Directory produced by that contract did not include reference to a number of
older studies and some fairly large recent sets of data. The following data
base directory is meant, in part, to supplement the work that preceded it.
It is designed to include all of the information necessary for direct
incorporation into the EDBD data directory. Lines beginning with "1" on page
2 identify that information. Since we hive also acquired actual data, in
contrast to EDBD or the compilation by 1-ynch and McErlean who only identified
data bases, fields describing the actual data content were necessary. Lines
beginning with "5" on pages 2 and 3 identify the major categories of
information in the data base.
There are a number of automated data bases which have not been acquired
by this project because of insufficient time, funds, or legal restraints.
Those that we know of are: State of Maryland; U.S. Geological Survey;
Smithsonian Institution; and the Phildalphia Academy of Natural Sciences.
Some of these dat-i should be available upon the completion of litigation
concerning power plant operations (Section 315, PL 92-500).
134
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GhCbPIO LAiAtlLES
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5 59 ttUIt. (KI-.CDn) (COL t-11), EM. dM-ELYi) (CCL 15-16),
5 5S S/i!.rLli.C rt0 ACbur'UtLt (COL ?5) , bl.ACCr tlAhLK (COL 2t)
IF lhi-T hEJLClICh, REASON
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5 L'4 LAlA Shth.l.S (CCL 7), REP (CCL 6), PhtlOGRAFi £ (COL 9)f
5 6i* ANALOG tCR;-S (CoL 10)
5 Ci* !-.ACr.l!.t RLALALLL iiCLhCt CARLS (CCL 12), 1APE (COL 15),
5 6*, lr 01- lAI-t, V;i-Al K1J-&D Ci- ROS1 S1STLK (COL 15-tO)
137
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****** PQQ[)£ ******
00005 SAMPLING STATION LOCATION, VERTICAL, PERCENT OF TOTAL DEPTH (FEET)
OOOlO TEMPERATURE, WATER (DEGREES CENTIGRADE)
00020 TEMPERATURE, AIR (DEGREES CENTIGRADE)
00031 LIGHT, INCIDENT, % REMAINING AT CERTAIN DEPTH
00060 FLOW, STREAM, MEAN DAILY (CU3IC FEET PER SEC.)
00061 FLOil, STREAM, INSTANTANEOUS (CUBIC FEET PER SEC.)
00070 TURBIDITY, ( JACKSON CANDLE UNITS )
00074 TURBIDITY, TRANSMISS10METER, % TRANSMISSION
00075 TURBIDITY, HELLIGE (PPM AS SILICON DIOXIDE)
00076 TURBIDITY, HACH TURBIDIMETER ( FORMAZIN TURB UNIT )
00077 TRANSPARENCY, SECCHI DISC (INCHES)
00073 TRANSPARENCY, SECCHI DISC (METERS)
00095 CONDUCTIVITY AT 25 DEGREES C (MIRCOMHOS)
00096 SALINITY AT 25 DEGREES C (MG/ML)
00295 OXYGEN, DISSOLVED (ML/L)
00299 OXYGEN, DISSOLVED, ( ELECTRODE ) ( MG/L )
00300 OXYGEN, DISSOLVED (MG/L)
00301 OXYGEN, DISSOLVED (PERCENT OF SATURATION)
00310 BIOCHEMICAL OXYGEN DEMAND (MG/L, 5 DAY - 20 DEG C)
00400 PH (STANDARD UNITS)
00410 ALKALINITY, TOTAL (MG/L AS CAC03)
00415 ALKALINITY, PHENOLPHTALEIN (MG/L AS CAC03)
00425 ALKALINITY, BICARBONATE (MG/L AS CAC03)
00430 ALKALINITY, CARBONATE (MG/L AS CAC03)
00440 BICARBONATE ION (MG/L AS HC03)
00445 CARBONATE ION (MG/L AS COS)
00480 SALINITY - PARTS PER THOUSAND
00500 RESIDUE (SOLIDS) TOTAL (MG/L)
00505 RESIDUE, TOTAL, VOLATILE (MG/L)
00510 RESIDUE, TOTAL FIXED (MG/L)
00530 RESIDUE, TOTAL, NON FILTERABLE (MG/L)
00600 NITROGEN, TOTAL (MG/L AS N)
00602 NITROGEN, DISSOLVED (MG/L AS N)
00607 NITROGEN, ORGANIC, DISSOLVED (MG/L AS N)
00608 NITROGEN, AMMONIA, DISSOLVED (MG/L AS N)
00610 NITROGEN, AMMONIA, TOTAL (MG/L AS N)
00613 NITRITE NITROGEN, DISSOLVED (MG/L AS N)
00615 NITRITE NITROGEN, TOTAL (MG/L AS N)
00618 NITRATE NITROGEN, DISSOLVED (MG/L AS N)
00620 NITRATE NITROGEN, TOTAL (MG/L AS N)
00623 NITROGEN, KJELDAHL, DISSOLVED (MG/L AS N)
00625 NITROGEN, KJELDAHL, TOTAL (MG/L AS N)
00629 NITROGEN, ORGANIC, KJELDAHL, TOTAL, (MG/L AS N)
00630 NITRITE PLUS NITRATE, TOTAL 1 DET. (MG/L AS N)
00631 NITRITE PLUS NITRATE, DISS. 1 DET. (MG/L AS N)
00550 PHOSPHATE, TOTAL (MG/L AS P04)
00653 PHOSPHATE, TOTAL SOLUBLE (MG/L)
00660 PHOSPHATE, ORTHO (MG/L AS P04)
00665 PHOSPHORUS, TOTAL (MG/L AS P)
00666 PHOSPHORUS, DISSOLVED (MG/L AS P)
00669 PHOSPHORUS, TOTAL HYDROLYZA8LE (MG/L AS P)
00671 Pr;iPHORUS, DISSOLVED ORTHOPHOSPHATE (MG/L AS P)
00572 PHOSPHORUS, DISSOLVED HYOROLYZABLE (MG/L AS P)
138
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00573 PHOSPHORUS, DISSOLVED ORGANIC (MG/L AS P)
CARBON, TOTAL, ORGANIC (MG/L AS C)
CARBON, DISSOLVED ORGANIC (MG/L AS C)
CARBON, TOTAL (MG/L AS C)
CHLORIDE (MG/L AS CL)
00530
00631
00590
00940
00945
00955
OU956
31501
31505
31506
31614
31615
31616
31677
31751
32209
32210
32211
32212
32214
32216
32221
32230
32235
50060
70205
70505
70507
71100
71845
71351
71836
71883
74010
98753
93754
93755
98756
93757
98753
93759
93760
9S761
93762
93763
93764
93765
SULFATE, DISSOLVED ( MG/L AS S04)
SILICA, DISSOLVED (MG/L AS SI02)
SILICA, TOTAL (MG/L AS SI02)
COLIFORM, TOTAL, MEMBRANE FILTER IMMED. M-ENDO HEO 35C (#/100ML)
COLIFCRH, TOTAL, MPN, CONFIRMED TEST, 35 C (TUBE 31506)
COLIFORM,TOTALVMPN,CONFIRMED TEST,TUBE CONFIG. (MPH/100ML)
FECAL COLIFORM, MPN, TUt3E CONFIGURATION
FECAL COLIFORM, MPN, EC MED, 44.5C, (TUBE31614)(MPN/100ML)
FECAL COLIFORM, flEM3. FILTER, M-FC BROTH 44.5 C («/100ML)
FECAL STREPTOCOCCI, MPN, AD-EA, 35 C (MPN/100ML)
PLATE COUNT, TOTAL, TPC AGAR 35 C/24HR (#/l ML)
CHLOROPHYLL A UG/L FLUOR3METRIC CORRECTED
CHLOROPHYLL-A, TRICHROMATIC UNCORRECKD ( UG/L )
JG/L) SPECTROPHOTOMETRIC METHOD
TRICHROMATIC, UNCORRECTED ( UG/L)
TRICHROMATIC, UNCORRECTED ( JG/L)
TOTAL, TRICHROMATIC UNCORRECTEO ( UG/L)
(PHEOPHYTON-A + CHLOROPHYLL-A).SPEC-ACID
A
B,
C,
CHLOROPHYLL
CHLOROPHYLL
CHLOROPHYLL
CHLOROPHYLL
CHLOROPHYLL-A, % OF
CHLORPHYL A (MG/L)
CHLOROPHYLL, TOTAL (SARGENT METHOD-667MU) UG/L
CHLORINE, TOTAL RESIDUAL (MG/L)
TIDE, RANGE (FEET) BETWEEN ADJACENT HIGH - LOW TIDES
PHOSPHATE, TOTAL, COLOR I METRIC METHOD (M3/L AS P)
PHOSPHORUS, IN TOTAL ORTHOPHOSPHATE (MG/L AS P)
SEDIMENT, SUSPENDED PARTICIPATE (MG/L)
NITROGEN, AMMONIA, TOTAL (MG/L AS NH4)
NITRATE NITROGEN, DISSOLVED (MG/L AS N03)
TOTAL, AS P04 -
TOTAL, SOLUABLE
( MG/L AS FE)
METHYL PJRPLE (
PHOSPHORUS,
PHOSPHORUS,
IRON, TOTAL
ALKALINITY,
TURBIDITY,
PHOSPHORUS
PHOSPH3RUS
MG/L
AS PC
MG/L AS CAC03)
PHOTOMETRIC 420 MU (MG/L)
PARTICULATE UNREACTIVE (UG AT/L)
PARTICULAR REACTIVE (UG AT/L)
LOSS ON IGNITION (OF SUSPENDED SEDIMENT) (MG/L)
NITROGEN, PARTICULATE, ORGANIC (UG AT /L )
PLATE COUNT, TOTAL, BACTERIA, TPC AGAR, 20 DEG C, 36 HRS
COLIFORM, TOTAL, MPN, TJ3E CONFIGURATION
CHEMICAL OXYGEN DEMAND, DISSOLVED, KMN04, (
CONDUCTIVITY AT AMBIENT TEMP (MICROMHOS)
CARBOHYDRATE, PARTICULATE ( MG/L AS SUCROSE)
NITROGEN, PARTICULATE (MG-AT/L AS N)
CARSON, PARTICULATE ORGANIC (?)
02 CONSUMED / L )
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1 10 ESIUARY LLR1KG IhE PfcEICD JULY 19&3 - ttEPUARY 1965
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1 10 19t7 IP.Kt 1970 VAlLh CLAI.11Y SLRVEi Of PATUXLM KIVEK
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1 10 rnCLLClIVIlY Or li:t PAlL'XEL'i RIVER ^6fc - 1971
1 ' "i tARLY Ct-hi, LICL LAt PILR LA1A 193^-^3
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1 7 tARLY Cht^ LICL LaL CbuiSL DAI A 1936 - 1939
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1 7 LAI A Pf.fCnl ir 2i) .
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1 7 CPtSAPx-.Ar:E LAY MiTFJEM It.'FLI STULY
1 7 tFA itCH.ICiiL i-hpOM .^7 i>EPT 1972
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1 7 LCGrtJir-llVr, L/.Citi-lOLCGlCP.L S'ltLY UPPcR CKt5A?f,AKE EAY DRLDGIivG
1 7 tPGIL LiitGiAL CKuIiit RcPCR.l (.- 1 1^67
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1 10 V.AUEh ibALl'IY Sul.VtY Gt "HE rLAL Ot Tht CK-ti EAY
1 10 KAhiLAJ.L IRILL'TAPJES DATA r.EPCPl #12 (1969)
1 10 A.isi; LA'iA P.LPChT * 23 (1970-71)
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1 7 PCLLLUG: SURVEY Gr 'II.E PAIAPSCG RIVEP, PALIILGFE EAREGR
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1 7 EL?C fclVLh - C&L- CAi'.AL; PHYSICAL, CEtMGAL, At.L EACTERIGLGGICAL
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1 7 PG'lGi-AC r.iVEP 1967
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1 7 rl£h KILL IKVEfeTICAllGi S S'i KIChAELS LAt-.tGR, CAR GREEK, KILES' FIVER
1 7 PHYSICAL, utEf-JCAL AKL5 EAG'iERlCLGClGAL LATER CLAL1TY ,
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1 7 MIA hEPGHT ;/i)
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1 7 PCICi-AC hl\Lh (t.GP.GAKTOkiO KIXhR £\}1tA£) PLtl.Ic tLALTL
1 7 -i-LUIIl, I- 7^ L'ARCn 1916 LLGL S. GUl'i-.li.Gi;
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1 10 PLlCi-AC hlVLh (KLf
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K022C31
1 7 197t,197? (2 MiPChlS) £ ILLOGICAL illUDILS d. ThF PCTO! PC rlVhh
1 7 l.tAi, Irk. i GP.Ghi.lGU. O-K t-Ch ft f CO (^u£L 197t-,79')
1 1C PG'iXi.AG MVth (I CnGAllGl.I' ) rA it.LIi.f, SlllA
1-.022-G22
1 7 PG1G:-AC HVrP. 1977 ZGCPLAMClGf yi'HVLY
1 10 t-LvEii pLM.'i irliJ.'G Pt'OGP/'.f- (Pr^p)
KG22033
1 7 197t PATLXtl 1 r.IUr ilLVbY
1 1C rC'*£i- t-LAl.'i ^1'io.! C r
1 7 Ultr. Cl/iLIll Lr IKE PO'id'/C f.i'TUARi UlLFhh'J t^,A^F /Sib ALLEJ
1 7 i'ht.Sr. AM- GuLSlCI. CCVL L'/-!^ PtfORT i?30 1570
1 7 LhrLf-, Ci.tf-APc/.Kt i/'i I.A1LK CUALI7Y i'iULIfS : fcUt'K hIVI-h, 1-tl-f.iiY CI.Lfcf,
1 7 iPti-l'i'ii: I.Ai.nChi, i-V,Al, ChLtK 19ob-?1; CdL CAi.AL, CI:i£'irh MVLh 1970;
1 7 itVthi. hlVtii 197C-71; Cui.fC^LLn, KlCLLt, tli.L hlVH-i: 1971
1 7 LAI A hLpOh'J. fr 3 2:
1-0^2056
1 7 V.Ait,r. CLALITi il-PVLY Lr 11. t AM A-PC'Llii I LiKLPCLllAi
1 7 LATf hf.PGh'i tIC 1967
1 7 Lt-LL-lAL t./lLP, Cl^.Lm f-LKVtit, Gi- IhL POlOi-.-'-L iJVtP. t;?ll.
1 7 Al,(-.GGillA LolLAKl 197C; ^.iGU.lCC i.lVth AM- Si. CLLrCL'l
1 7 AI,L I-htlGl tAiK 1971; C'LCGuliA,, rAi 1971 L/-1/ KfPOI-,1 {-'33
1 7 lA'.l-h t.U/-Li'il i-Ui;Vi_Y Or TI:t UpiaF PClCi'/iC triGARi
1 7 tll-OhCH tM CCtfti.Li-CL AhtA U1A JicPOhT J-29 1970
1 7 >',!. VL1 f-ti-LLIS Lr Li-liApfcAf.l. i/Y IKFb'i MLLY 19C-9-7&
1 7 L/.'u r.crGi.l t'31
1 7 rCICi-./C L.i-lbAhi 1,/it'UV.AihS IhL/TiiM PL/-fi
1 7 ioriVLi LAI A i-r.PC'h'1 i27 1S'7C
1 7 Mlr.lLM LA'iA Gi. if.Lli'hl-,1 i/lt'LrS Or 1ft PA1ULK1 LSTL
1 7 19c6-6t I;/;! A- htfuhi *• 1 1
1 7 CGI.^GLlLAltL VvAltF CUPIIIY tL-h\£.Y Or IhL PCTCt'/C LSIU/F.Y
1 7 LA'iA htPGh'l ),25 1970
1 7 V. A. left ClAL17i ibhVhl GF lit PG1C/AC tSTUAF.Y LfFAYrHlb At-C 1RA1 SKC1?
1 7 LAI A r.Ll'OJiT !/2:'fc 1970
1 7 ll.Vh£llGA13Gi.S Gr ll't PGLLLIiGI. n.L ^AM'J/i.Y CGM'IllGKi; CF Tf h
1 7 PG'iG.VAC KAlchittli vlTK ipLtlAL J-U- hht f.LL 1'G i,r,Lr rlJUKlGA i 1GL /I'D
1 7 U.IJ'iAFY CCi.LI'ilGi.L Gr J-.Kf LLir Ii)h II 1I.K LfiLP rC'IQAC fIVtr.
1 7 LlOhMC LAi_GhA1GhY uU'1) r t £ f-,L AJ'.l 1916 KIGK i . CLt-.i If.Gi
i- 000295
1 7 tlLLGClG/L AIL- G..CLOGIC/-L U^K/PCh GI, 'Iht trPtCTi- Gr
1 7 irtt.LGli.G ^-t-uIL LlcfG^AL li, ILt uPfth LlltApL/Kh t/Y
1 10 irGIL LU,l-(j'^l,L I., 112, LPPPPi Gi E£APt/-.KC l/'Y
142
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* KOOG295 *»«»»*•
1 2 (-.000195
V 4 C tIC LAb
1 7 fclOLCGlGAL AI.L CLGLCG1CAL fchSf.APCK LI. Trt EJ-rLCTi Cr
1 7 AKD iPGIL DISPOSAL IN IPPth CbESAf h>-.KL EA1
1 10 MOIL DISPOSAL II, IPPLK Chl.SAPLAKt EAi
1 If f.Ch'ih At-.thlCA, U.S., Mfl'LAl'D, CCASTAL . ChLSAFLAKfc. EA1
1 17 hAlEr. kUALHY LA'IA GKLY thCCELC tf-C't' tt'LLClLL ALL MD-ChAI-f-FL
1 17 MA11LIS. hf.PCHT ALtG INCLULLS DAI A tRGi- 5 tAY IFANSLCli. V.lTh
1 17 SlAUCi-.S f-ACh; IUS LATA t-0'i LLCCLEX
1 16 LlthAhlAU
1 20 GhtSAPtAKE EIOLLGICAL Ltb
1 21 iGX ;C
1 22 SuLCi»uf.£
1 23 l-.ALYLAt.D
1 25 206iifc
5 35 1 GhL A
b ^2 1 tt-hllC GHG
5 ^3 1 SLSTGIv
5 45 1
5 46 1
5 53 1 SLCO.l
5 57 SUS
5 5c 73079530243363 5S32?676043?
5 57 1C
5 57 7307i.62G615139 392653760119
5 57 1IC
5 57 73C7&6203t'4l13 392341760613
5 57 SAS
5 57 7307902i;2135o1 39223I70C151
5 57 Ilio
5 5c 7307S621005251 592055761G21
5 57 IVC
5 5^ 73079611645330 3916537u1430
5 57 VC
5 5o 75079611465254 3i>l4f57M624
5 57 VI
5 5c 73079602915126 39C9527o211t
5 57 t-LAI.iaGN SlnTlUN 1
5 5fc 73C7t62iOOGCOO 312000762000
5 57 PLAf-KlLi. STAlltA 2
5 5t 7307tb322t30CO 363230762400
5 57 PLAf.KlCN S'iA'IKt. 3
5 5fc 73C7t642550000 3&4500762500
5 57 PL/-U1U, il/illGf, 4
5 56 7307t-65274COCO 3657007624CO
5 57 PL/.l^TCr, S1A11GI. 5
5 Lfc 730796024GOOGO 3SC40076200C
5 57 PLPhL'iGf-. SI AllOt, 6
5 5f- 7?C7961 1740000 391700761400
5 57 PLAKK'iCIi blATlGI, 7
5 5t> 73C?io212COGOO 3922CG761000
5 57 FLA^^,'lo^ timCK fc
5 56 73C79620540000 392500760400
143
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5 bl J-UKf.lU. SI /TICK 9
5 5e 75079^0725000 39
b 57 X CCVh f Gil i
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5 59 0^2666 XXX^.Ot 002 ^ 019
5 fcO LOi. tf 7I.L£:
5 o2 L^Vt (.ChCK A
144
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1
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K020001
G L1G L/-F
1972 FA1UEET R
A Sl'i'.CP'iiG ViEh
i.GR'ih AKRR1GA,
A!-, EAlRthtLl LE
IVi.li SlrOPTJC rl.lSlC/L/Chff 1C
Gf A CGA£"i;.L FL/II1. tS'ILAPl
U.S., GGA.'.TAL, I.AhlL/.l.L, FA1U
f-SE LA1A SL1 . SGlM- FARm.ltR
tOR 24 RGIRS, GTR'tR PPhAi'tTEfr KR 3 i^AYS U
L«TA GGLLEG'ilGl-.
Ei'tGRT It'CLbL't-S Si VtPAL PAR#
."L LAI/5 SE'l
>tfT RIViR
S ARE hEPCKltE F.Gl/'hLY
GIPLY). TRE ORIGJ1.7L
^.E^Ei:1S, E.G. TILE,
CUUtr/i VtLCGITY, Al>: 'iEKP V.F-ICh ; RE f 01 RErGFl£D IK IMS LAI A ShT
10
300
4bO
60C
625
630
lUPLhATUht,- V.A'iEH (LEGntES
OXYGEN, LISi'-OLVtL' (t-G/L)
SALIl.l'ii - FAhTE PER IIGIL.M:
MlhCGEN, AM-GMA, LISSCLvEL
MlRGCtli, KJELLALL, 1G1AL (1-,
I.17RI1E PELS MlhAlE, 1GTAL
CEMIGhADE)
D
(i-G/L AS i\)
G/L AS h)
1 LET. (KG/L AS N)
b69 PhGSt-hC^US, TOTAL MLEGLlZAfcLt (f-.G/L AS P)
671
6t-1
322C9
3223T
71 100
96764
9c765
PhGSFhGRlS, LJSSGLVcL CRTKGFPGSPRA1E (J',G/L AS F)
CAhEGI. , L1SSGLVEI CRGAMC (!•
n/L AS G)
GELGRGPHYEL A LC/L 1-LUCRG,- E'if'JG CORRECTED
ChLChOFMbL, TOTAL (SARCEj-1
KETKCC-667I-U) UG/L
SELlMihl , SLS^cNDEt PAhTlCULAlE tfC/L)
MlhOGth, PARilGULAlE (IC-f-.l
CAhEO:\, PAHIGLLATt CfGAi.lG
/L AS N)
(':) <1,SG>
KGfcti'I fc. LLAKGV.IGZ
301 325-42C1
GhtSAFtAKE L1GLOGIGAL LAlCRAlC/i - GR L
P. 0. I-.GX 3o
SOLOi-.Cf-S
^.3
2 Cbb 6
.145 GARL IhAGtS lh E-2 tGhfAT
1
1
1
1
1
1
1
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730766 12654137
P-01-02
73C7£b12fa55157
F-02-C1
7307fcb22095303
P-C2-02
73C7b622190COd
t— 03-01
GOOGO
GCf'OO
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OOGOO
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00000
3b1b^3 762517
3'Hc55 762517
362050 762933
3c'21GO 762^ Ob
D "o i ^'-/1 c^jjc; "o1^*: T 3624^2 7635C7
5 57 P-04-01
5 5t 7307bt2;9935fc5 3t'293b 763955
5 57 P-04-02
5 5b 7307cc3'203302 3t3230 764C32
5 57 P-C5-01
5 5b 73070^3^404464 3fc'344fc 764C44
145
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5 57 F-05-02
5 f>b 7307^63^912033
5 57 P-06-G1
5 57 P-07-01
5 56 73C7t'0'*'462it503 5t
5 57 Lii-'i^hLi: &1A 1
5 57 UIvAt.LL- S1A 2
5 5l> 7307fc63'i'40i4i
-------
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K322001 ******
1 2 K022001
1 4 C E10 LAi;
1 7 nlEb^SKY, KCERLEAN, 1 EFf.AI^ 1967 NF-I RRF' 67-59
1 10 COOPERATIVE, ZGOPLANtaON li.Vr.STIGATlCKS II- IhL PA'IUXtKl RIVER
1 10 ESTUARY CIK1KC TEE PtRICD OILY 1963 - FEERUARY 1965
1 14 KORlh AKER1CA, US, hARYLAND, COASTAL, PA1UXEM RIVEP
1 17 J.tTbCDS: i\Ei\ZEL, AUo 19c2. INSTRUCTION i-ANLAL FOR RCbllN'E hEASURFNFNTS
1 17 F'CR U.^. PhOGhAI-' IK tIGLOGY. fcLh^DA PICL. STA1IG1*
1 17 TOTAL ZOGPL.ALKlGh (Thl.S DATA (MOT EbCCEbb): hi-CMSIS Al-^hlCALA, ACAR1IA
1 17 CLA l)SIl, LUKllEt-CRA AtFIMS, ACARTIA lGt:£A, CILi.'GPPORE &
1 17 COLLLiMTERAlEii. LREAKEGV.K BY STATIONS OF GlhtKS
1 17 26 ChUlStS, ti (K.lADSlATlCb.S SAMPLED FCB TE.LP, SAL1UM1, TUKEItm
1 17 4 SIATlOfvS SAMPLED +- Of:CL/i-CMh FOR iiAI-,fc. FLLS MTFATfc , Pr.CSPhAlE,
1 17 SILICATE Ai'.D GHLGhG'f I.1LL . LXTRACltD ERG't' CRUISE KC1ES AKD LAEGFATORY
1 17 AhALlSLS htCCKL^. SURFACt Af:D EOlTCi-. SAKPLES tCR J'-OST PARAKEItftS.
1 17 10 TEi-iPERA'IORE, V.A1ER (DhG'niES CLiNTICKALE )
1 17 75 TUMtlBm, EhLLlGE (PPi. AS SILICON LICX1LE)
1 17 **iO SALIKI1Y - PARIt PER IHOUiiAl.D
1 17 955 SILICA, DISSGLVfX (f.G/L AS SI02)
1 17 6lb KiiRAlE Kl'inGbEK, DISSOLVED (tG/L AS !•)
1 17 666 PhGSPhGhUS, ulSoCLVEL IhC/L AS P)
1 17 661 GARhGis , L-1SSGLVED CEG/nQC dvu/L AS C)
1 17 32209 CHLOROPHYLL A IG/L FLUGnCKETRIC GGKHEC1EL
1 16 tGK hEIl^LE
1 19 301 326-^261
1 20 CHESAPEAKE EIGLGG-ICAL ILL - Cl L
1 21 P. C. EGX 3h
1 22 oGLCi\CLS
1 23 fX
1 25 2C&fco
1 27 flLL SIZE IS 67k CARD INAGLL' If; t-2 tORK/.T
1 27 7 PARAMETERS l^t/.SURbD AT ^ S1A11GKS TUCr PEP KCMI. FCR 16 I-:CS
1 27 1 ALDIIlGl'AL SlAllUl-S SAKPLcE v.l'ih LESS FRECCE1-GY. SUFFAGF AKD
1 27 EGTTOK SAKPLES FOR f-GST PARAS-^TERS
5 35 1 102
5 37 1 356
5 39 1 112
5 40 1 112
5 41 1 111
5 ^5 1 554
5 46 1 534
5 5o 18M
5 57 LG*Li. KARLECRO 1-63
5 56 7307c634S03505 363930764055
5 57 rUhh LIKE 2-63
5 5fc 7307co347C0250 36'370576402C
5 57 ThUa-.M. PG1M 3-63
5 5fc 7507o6344G2550 363
5 57 CHALK POINT 4-65
5 5o 7307fc654202350 3o3
5 57 i-ENLLlCl hr.lLCE, 5-63
5 56 7307^634005200 3c3050764020
5 57 SKERILAi', POINT 0-6?
147
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5 57 uuttf, lht,L 7-63
,5 5e 73076o235643CO 3^540763630
5 57 bhOOKtS ISL^KD fc-63
5 5t 7307fc623535300 362350763330
5 59 071C63 02C965 002 3
5 bO kAhlht CCLL-JCKES
5 62 {-..Ahlht CGLt-JCK£i> A
148
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****»" i C220C2 **»*»*
1 2 KC220C2
1 4 bo EPA I-EG 3
1 7 FATbJitM MlVrh 1967 ILF.b 1970 V-ATi-h CbfiL - LPA.
1 1C k/ilth CUAL11Y tUnVLY Ch Tht F/lb'Ui'i IIVKh EAiA
1 10 *15 (1967),£16 (196b), *1V (1969),£?4 (1970)
1 14 !-.Chlh AKEF.ICA, bt. i.AKYLAi.L, CCAt-lAL, PAlu/hN'i hIVKh
1 17 ALL LAVA (1966-70) '«/£ rr.EYlCUtLY hi.GGLti- t i LPA ; It: tl
1 17 bhLhh A.GLNCY CCLE : 1113'iXk«l
1 17 10 ItKfEhMbhL, UTt/i (ItGhEti; CtMIG;-,ll- 1965, ALL / L'nPf 1 I ill*: '\::'.'f
1 17 (3) ll.Cr.GAf 1C PKGSPrOnliS AblC' Ah/'LY?:J; - 1UFPK1 AfL PJLEY 1962
1 17 (4) Ul. tlAiLA.RL I.ElLCLt ell tXAMJ.A'ilGt Gr V.ATEh AKL V./ilElA'lhh 1965
1 17 (5) U2 i. 1.C3 ^fii,iCt,LAl-L Aft PA.RtCIt 196fc
1 17 (6) Kf-5 PhLLGL-hli-GCLCl.Ilt, tV.tGA f-Lll,GLf VA1LP, A!;£ UA.^TL V,AThh 1969.
1 17 (7) x-UL S1AI L-APtD 1-E1KCLS, 1965
1 17 (t>) ICC tV.PCA 1969
1 17 (9) CfL A SihlCKLA/L J-ID PAI-.tCNS 196£
1 17 (10) tb tlkLb i-1 t-tlttr t'iAI.LARD b,' lit
1 17 (11) tALH.m itCh.'Af-, tALIi.CiLlth PPT
1 17 (12) CUI.LbCilVllY ttCKI.AJ. tALi; Ci-L'iEi, KlCr.C.'I.Ct
1 H' JAr-tt i,. f-AF.Ki.VC. VILLA, Jh.
1 19 301-224-2740
1 20 Ai.i.AhOLIt flLLL CM-ICE - tt-A
1 22 Ai,;.At
143
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1 23 M;
1 25 21401
1 27 M fi/HCI.i, htU'. LLL, Kill:!,: GMU.r. i.A?rL_i) tCn 'iti.P, 1C1AL P,
1 27 l.'.U.C P, IK.',, I.C2+I.C3, i-K?, Ci.L, (,'GCAi.SKi ALLY fGL-, 'i
1 27 ^ iri'h LOhAlGr.
5 35 1 Ct.L A 3C7
5 57 1 142
5 3c 1 -23
'3 3V 1 1C1IL 5-t 7307t65'
5 57 lf,/.iLt.h GCbr.'I
5 ^t, 7307004^930000 3ti*SC07ti*3GO
5 59 032CGV 112370 13 1fc
5 60 f.Ah'ift GGLh-JGI.Lt A
150
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ii ;\022CO~
1 2 i-.C22003
1 1 G cIG LAt
1 7 fc.A. tLLI-th El AL, M.I RFF 71-6, ?1-ci-
1 10 trrcGT5 Ot ThLhKAL LGALlhG A'-D V.ATFP CWL1I1 Gfv E'S:IbA/iiOLVt.l: (i.G/L)
1 17 ^cO SALli-.lTY - t-AHt PLf< If.CbSAM
1 17 cOO r.ilhuGLl:, 1C1AL (i-.G/L A:? i< )
1 17 602 M'IhGGfcl. , bJL^CLVl-.L (i-u/L AS ;.)
1 17 C07 f.UKCGLl , ChC-AMG, DlfS&LVfcL (h.G/t, AS fO
1 17 cOo 1.1'IhGGf.r, Pi-hGMA, LISSGLV^D (fG/L AS t)
1 17 615 Mlhlit 1.11FGGL1-. , ElSSGLVfcl. (t-C/L AS |v )
1 17 61t Mil /.'in HllhCCtiV, Lli^CLVFL (i G7L A 5 lO
1 17 6fc1 GAht-Gl., Li:-£GLVt,L ChGA.MG (.-G/L At G)
1 17 b65 PhG^H.Gul';-, 1G1AL (i-G/L AS P)
1 17 Gtb fhGSPr.LtiUS, DISSOLVfcD (i C/L t L; V
1 17 671 Pr:CSPt.GrL.S, LiSSGLVti; uhlrrPK:>Pi/,1L (1-C/L AS P)
1 17 522C9 U.LGP.CrhlLL / L'^/L bLbGhGf.h'IPIG CfPhEGli-L
1 17 711GO StLlfthl, i-bbrli'DtL PAFlICLL/.7:i (! U/L)
1 17 9t7tr GAI-LG'iAbl-A'in, PAF'llCTLA'h (i G/L /.i SUCPGSt)
1 17 ^7rI: MIi,GGLi\, t-AhllGu'L/'if. (i C/L ^S !)
1 17 Hi-AL htPGP.i Gi, 1PL LffKGTS. CF Ihtri'AL LGAbll.f: A, C UAlfch C.L'A-Llll
1 17 GK LSlLAP.ll,t PKIn/.t.^ fRGblG'ilGi 1S6i.--19b9-1970-197 1
1 17 S,'iA'ilGiS 1 - 9 SbhfrACc. Gl'L^;
1 17 61A"1G1\£ 1G-1*i t-bKtACt AM FCllGr.
1 1b LGIAL1 htli.LL/D.A. fLLI-.Lh
1 19 501 526-^1
1 2C Ct.tG^PtAKh L1GLGGICAL LAtOBAIGM - «tL
1 21 P. G. tG>. 56
1 22 i,CLG..Gt,i>
1 25 i'.^'
1 '^ 20bCfc
1 27 29 1c rLGGFiLS
1 27 1o PAh/,f.t'itPS F-t:AfcURtL APPRO. 2 llt'HS Pr). iuK'Ii- FCf, 27 M-l-Tf S
1 27 «1 14 ilAllGf-6. ALL S.A.-PLFE SbftAGL, if S'iA'llGfS ALSO SAi-FLLT tCTlGl'.
5 55 1 GhL A ^30
5 57 1 it-CCFl i;30
5 3c 1 550
5 59 1 LJP 1LP IP 9Gi(
b 'tO 1 lG5,:-G2,i,h3,LGF,LM690
b *<2 1 LISS; 147
5 ^3 1 StSlGK
151
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5 46 1
5 53 1 i-Ah'i CAhrGN
5 54 1 rAK'l CAhbChlDf- 436
5 55 1 PARl MlhGGMv 552
5 57 HILLS thlLGL 1 - 66
5 5b 73076644S20000 364^00764200
5 57 i'Alt-, kAlbn ChttK 2-Gc
5 5b 7307tt>4473300 3fc
5 57 htSltHK LhAlsCi- 3-fcfc
5 5t 730700^4720^05 5^
5 57 JUG LAY 4-6b
5 bi 7307&644610300 3^4600764150
5 57 ttiM\C MhSh 5-bo
5 5t 7307t644510200 3t4500764l20
5 57 I.C1TINGIAK 6-be
5 5c 7307164^223005 3^4230764205
5 57 LGVvLh KAhLtCKG 7-cb
5 5b 750?t634903505 5t3930764G55
5 57 CCUTGU- Chtt.K b-68
5 5c 7507b63470455C 563745764050
5 57 i5ttf LAKL11-G 9-66
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1 17 SlhfACL , t'JD DLP1K AKD ICTlCv SAi-FLLD. £.C.".E CLOSE Ih'ILRVALS,
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5 57 tltt: St-AKS 1-26 (103-39)
154
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5 56 73076622321005 362310762205
5 57 lAiLOhS I 205-36 (63-37)
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5 59 070736 061659 002 5
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157
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******* KC22CC5 ******
1 2 .\022GC6
1 1 t,S tPA htG 3
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1 17 c) ^u^Pr.Y A.'.D EILLY :§62
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5 56 73079621004120 392042761010
5 57 Tt-AhStCl 3 SlATIOf. 3
5 5C 72079621100366 392106761036
5 57 lr«N£L.Cl 3 STA'IION 4
5 56 73079621100544 3921047610511
5 57 IhAf.bLC'i k STA11CN 1
5 56 73079621001161 3920U7610T*
5 57 Ir.At.SLCl 4 S1ATICK 2
5 5c 73078621003330 392033761030
5 57 iKJ-.l.bEC'l 1 £1 Allot.1 5
5 5c 73G79621C05511 392051761051
5 57 Ir.AI.SLCT 4 S'iAllON »4
5 56 7307962111C192 392109761112
5 57 lh#K3td 5 iJTAllOt: 1
5 5t 73079621000264 392006761024
5 57 'u>AKSrt'l 5 £1A TICK 2
5 56 730796210013t6 3S2016761036
5 57 lr.Af.SLC'1 5 S1A110K 3
5 56 730796210140^6 392044761106
5 57 T/.Af.oiCl 5 SlAlIC-h 4
5 56 7307962111020^ 39210076112^
5 59 112167 112167 001 0 022
5 60 LCr. i tlNLc. A
5 62 h.E. Kl!,Li-AtS /
162
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K022CC9 ******
1 2 f,022009
1 4 US 'EPA REG 3
1 7 i.AlLH ClATLITY SURVEY CF i-GUr.EA.S'l RIVER, ELK RIVER, C&D CA.I.AL,
1 7 IrChEMA RIVER, SASSAH-AS RIVER ARE L'PPLt. CEtSAPEAKE BAY, SlKKEIi 1968.
1 7 WATER CUALITY SURVEY CF Iht HEAD CF The. CFRSAPt/KE BAY
1 7 KARYLAlvD TRIEUTARIRS DA1A REPORT 412 (1^69), i-23 (1970-71)
1 14 fcOrtth AhEnlCA, U.S., tM.YLAf.B, COASTAL, CEtSAFEAKE' FAY AM, TRIES
1 17 1969 PhiTCPLAKKTGE DATA 1.01 ENCODED
1 17 DATA APPEARS 10 LE IK STCRFT UKDER AGEi.CY CCEE: 11123CVC
i 17 STATION LOCATJCI-.S CF *'S 2,5 , t> ,7,6,9,1C , 12,13 V.'tRL CHANGED
1 17 1M 1&71 REPORT.STCRET LCE£1-"T PECCCMZF IhESE ChAl.GES, INL'ICATIhG
1 17 THAT 1968-09-70 SAhPLES l-.ERE A1 KEY. (1971) LGCAT1CLS, V.hlCb IS Uf'TPliE
1 17 10 TthFERATUhE, V.ATtR (DECREES CEMIGPACE)
1 17 70 T'JREIblTY (JACKSGC CAtDLL LMTii)
1 17 77 TRAI.SPARtKCY, i-ECChl LISC (IfChtS)
1 17 95 CONDUCTIVITY AT 25 TtGKttS C (MRCQhCS)
1 17 299 OXYCLfj, DISSOLVED, ( ELLCTRCDc ) ( i-G/L )
1 17 300 OXYCtK, DISSOLVED (^C/L)
1 17 310 EICCEtKlCAL Oil'GW DEr/.r.D (i-.G/L, 5 DAY - 20 TEG C)
1 17 ^00 PE (S'lAivDARD LLITS)
1 17 nfcO SALINITY - PAFTS PEH TPCU^^C
1 17 b10 M1ROGEK, AM-:CM«, TOTAL (J-G/L AS i;)
1 17 625 KITF.OGEN, KJELLAEL, 'iO'i'AL (i-.O/L AS N)
1 >7 629 MTP-CGLN, OEGAMC, KjLLE/hL, TO'iAL, (i.G/L AS N)
1 17 630 M1R1TE PLUS KlTRAlj , TOTAL 1 CET. O.G/L AS t.)
1 17 66C PhOSPLATE:, GRTP-0 (i-.G/b fiS PC^)
1 17 6f'0 CAREOf,, TOTAL GhCAHC (^G/L)
1 17 31506 COLlt01-,h, TC1AL, I-'Ft., CCi.rli r-LD TiiJ , TUEL COf-FIG. ([• PfVIOOKL)
1 17 21615 ttCAL CCLIrOI.N, 1-f !•<, tC f-.tD, W .5 C (iHi-L 51614) (f-PK/IOOiVL)
1 17 32211 CELOhOPhlLL A (LG/L) St't CTROtf'CTGf t IF.1C ^ tTPCC
1 17 32221 OE'LCROPhYLL-A, % Cr (PtTftMTCl-A + Cf.LCRCPi.YLL-A),SPEC-ACID
1 17 71cbb PhCSPEORlS, TOTAL AS ?C4 (i-G/L)
1 17 '.\ATER TEKP 196b YS1 IKthFISTGE Of DC E'RCEE
1 17 HfaS tPOKf-Af; SALllOi-'ETER 1970-71 rERCur.l ThEhi-' A.;. D SALll'Ch ETEh
1 17 PR PECKKAr, N-l I-E1ER ; 1965 - rIELD PI^ t-ETL'R
1 17 DO hlKKLER (STAhD i-Elh) /Ni) YSI D.O. KL1FP (If SITL'rYSI 00299 PRCEE)
1 M fcOD SlAKDARi. hElPCLS
1 17 lURLlL-lTl JTU EACK PhOTGLLtCTRIC ^.EPEELC^ETER
1 17 SALINITY 19&C i.YDRCi-.ETEPS; 19o&-70 fLOK!-,AE SALirCJ-:£lER
1 17 LlOE'i RX'iir.G'llOK SECC! 1 DISK
1 17 TOTAL PEOSPhCRUS i-.ENZtLi OORU !!• (19&5 ); t URPPY AFILt Y( 1962 )
1 17 l'.C2 '& 1,03 1966 - V,COL(1967); 1969-70-71 - STRIOKLAivD AKD PARS01-S
1 17 TOTAL kJELDAEL MTRGGEi. (TKiv) STAKLA.ED hfTi-CES
1 17 CELORAFhYLL A STR10KLALD Af.D PARSOKS
1 17 COiaiCTIVITY 1969 t b.CKf-./t. SALIt.Oi rTER
1 17 PEAtOPIGl-EMS Cfi ChL A) SIAI-DAKD 1 ETt CDS
1 17 1NGRGAI 1C EECSPEORLiS M'hPhY & RILEY(19'62)
1 17 AH-CMA 19C9-70-71 tV.i-CA
1 17 'iCTAL Gf-.GAMC CAREOt 1970-71 1-ir.PCA 1971
1 17 CuLltORi-S i-ULTIPLE TURE ttF:' 1970-71 STA.l TARD MiTKCtS
1 17 fECAL CCLItCRKS L.C. 1970-71 STAl.DfED KPIKI'S
1 1ti OhTtRlO V1LL/-, JR.
1 19 301 224-27^0
1 20 AI.iAPGL.iS tltLD OtEICt - EPA
163
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1
1
1
1
1
1
1
5
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5
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5
21
22
23
25
27
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35
37
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59
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44
45
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53
54
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21401
17
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S'lATICKS SAhPLED 3 10 7 TIKES A 1EAR (! IF Ftp 21 Sl/TIGLS)
FOR APPRO X 14
1969 - 1 1INE
ChL A
TP, IP
FAPAhtTLRS
PER kEhK FCH 3 SEPmil- WH-.KS
261
76
440
600
!
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5 5o 730796202344L2 39224176031)2
5 57 1- 2 tAl, i.ChTH OF GhAf.t;EL, tETKLLK I>.2 AM i;4
5 56 73C79620351366 392316760536
5 57 T- 3 fc^-Y K2, LMBAKGE SPESbTIl f:AhhCv£ CHM'LL
5 56 73C7962C551422 392512760542
5 57 1- 4 LAY BUOY 22, OFf STILL PGlNO
5 5b 73C7962100J4lfcfc 39204676101&
5 57 T- 5 LAY LDOY C1 OFF RCKKLY CF.EfK
5 5fa 73079621104326 392142761C3C
b 57 'I- 6 BAY fcl/GY 12 otf FAIhLLE CREEK
5 5& 73079611544162 351546761412
b 57 1- 7 LAY EOCY 03 LCV.EH IIP FCOLES ISLAtD
5 Si 73073091166010 391612761600
5 57 1- c i-AY hbOY S41L, ttlhEE,1- FCOLES ISLAND All KCUTh Ot GUI-PONDER
5 56 73079611663204 391630761L24
5 57 'I- 9 £AY bUOY R6
5 5b 75C79'b019b5142 390954761&12
5 57 1-10 fcAi LfcTV.tEJ; C5 AKD S let
5 56 73C79612003564 391036762054
5 57 T-11 tAY OFF OfiAIGhILL ChAhhrL LIGHT
5 5fa 730796121314C2 39111^762342
5 57 2-71 SASSAFRAS Hfc
5 56 73079525251437 392213755547
5 57 5-71 rCl.D CftEhK R4
5 5b 73079620511252 392515760122
5 57 6-71 Ahi.CLL P011.T life
5 5t 73079525765079 392757755609
5 57 7-71 LOt.G P01M R2 tOFc!:IA
5 5b 73079525633^36 392tt3375534b
5 57 6-71 tOhtl'.lA AtOVL EhlLGL
5 5fa 73079525722072 592727V55202
5 57 9-71 rluY 13 OLLlOV.K *KAnF LL^
5 5b 73079535052102 393020755512
5 57 10-71 i.tLCh POUT tLCY 19 BLK
5 56 73079535121503 393110755253
5 57 12-71 tLOY 07 ELK
5 5fc 73C7955521540C 393250755146
5 57 13-71 tLOY M6 ELK
5 56 73079535410063 593406755103
5 59 062766 Oc2471 003 1 0261
5 62 ;-,AP1hi:, COLE-JOLES A
165
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»»«*•* jvG'22010 *»»•'**
1 2 KG22010
1 4 C L1G LAt
1 7 POLLUTION SURVEY Or TEL PATAPSCG RIVtr,, EAL'ilt.Cht fiARtCP
1 7 1936-1939 RGB-till A. LmLtFORD
1 llJ f.GKTE' A.StftlGA, U.S., fARYLAU., CC/'STAL, GhhSAPEAKE fcM .PAIAFSCG RIVFR
1 17 Ph - ERCKKAi. Ph KETER OH L/'i-CTTL IKCICATCRS
1 17 D.O. - Mi.KLLh IsGLlFlEL
1 17 PC4 - NhkCGKiJL 1939
1 17 TOTAL IKON - THOMPSON,T.G. 4 ft.V. ihE.Ki.tF 1935 "Thf Li TtM^J./ilIO?'
1 17 Ct IRON Ifv SLA hAlth" J.LU. CCKSLIL. 10:33-3o
1 17 ALSO S1ANDARD NtlhOLS CF i-AlLn AK/tLlfES Cf IKt, A.K'ERIC/-h. PLELIC
1 17 hhALTh ASSGC. 1936
1 17 Itt.fLhAlL'Kc. - W1A IS SKLTCKY. OCCASIONAL ICIt.S Of "TI.i:i.M'-I.Trfi
1 17 OUT OF OHLtti1' AI-.D UMilALLl HIGh VALUti RL.C,IL1 IK COLL
1 17 kODItlCATIGN 'V"
1 17 10 IfchPthAlbF-h., WAIhf. (LtGRLLS CEN'llGKALL)
1 17 77 •IRAt.iPAKEl.Ci, StOCLl LISC (INCrES)
1 17 300 GX1GLJ-, LISiOLVLD (i'G/L)
1 17 ^00 PR (STANLAf.D LiillS)
1 17 ^bO SALlliITl - PAhlS fti: ThCUSAl.L
1 17 669 PhC^PKCniS/iGlAL hlCRGLYZAbLi: (fG/L AS h)
1 17 7^010 IhGf., 1C1AL ( KG/L AS rh.)
1 1b DGKALD h. LtlKLL
1 19 301 3£6-1261
1 20 ChESAfLAKE E1CLCG10AL LAEChrilGRi
1 21 P.O. bO>' 3d
1 22 SGLGhaS
1 23 i-.AiiYLAM
1 25 206i..8
1 27 9 STATIONS SAl-i-LLD CfCt GE IVICf- A .-.Gi.'ih tLh 20 i.GMrS FOR
1 27 TU-PLW.IUht, I-h, LlSSCLXtC fXYGf.l , ANL Si1 LI! 3TY
1 27 SCi-L ALL1T101-AL STATIONS Lib PAhAMThnS JANPLLL' UITF LESS FRECbfhCY
1 537
1 9^
5 ^5 1 ^c2
5 16 1 'iM
5 4t 1 509
5 53 1 TOTAL IfiGiv I'll
5 5^ 1 SLGGhl 37
E> 57 l-3t> FORT CAP.KGLL
5 5o 73079613310^00 3913007631^0
5 57 1/.-36 LLALli.G PT
5 5t 730796l5320J4t5 39130c76?,2'45
5 57 ll-3b SLF1/LS PT
5 £b 730796133';0005 391300763^05
5 57 111-56 F1KEIOAT 1XGK
5 5ti 730796133-403cO 39130c763^30
5 51 lV-3o 5IO.L1.GUS1 CGVt
5 5ci 730796133^3505 391330763^55
5 57 V-5t GtF CAhll; if-Al-Gh
5 5e 730796132^^^50 3612^5763^^0
5 57 Vl-3fc GP.UK t/At.Gh
5 5o 73079613255050 391£5S7o3500
5 57 Vll-3t KIi.Lin' tMLGF
166
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5 5fa 750796132^2552 39U"257i3i<52
5 57 VIlI-3£ RAILi.CAL thltGE
5 50 730796151^5555 391155763^35
5 57 X-36 rUUACt/hAhLEY Crui-K
5 5o 730796131^03 391 1 10763^3
5 57 XA-3fc KAhLLY CfiLLK
5 57 1XA-36 fbhhACL Chtfr.K
5 5b 73079615150155 3911057
5 57 >i-3b 1KSILE iiLLMS i-1
5 5b 750796132^4265 391
5 57 X1I-36 Off LUPOM SiV.LF.
5 5b 730796133^1^60 39131^763^^0
5 57 XlII-3fc SOLLLf-S FT
5 5o 73079613313570 391337763150
5 57 X1V-56 ttAfi ChttK
5 5b 7307961239^565 5913itt!762955
5 57 SAKLY i-C'lM
5 50 7307960203300C 590030762300
5 57 StVtl. r'l hl.CLL
5 5b 7307960292<1i»51 390915762^^1
5 57 CLLGA1L ChEEK
5 5o 73079'613520DJ5 39 150676 5?: 15
5 57 V. t STERN rL hf,
5 5b 73079613575530 59155376373C
5 59 0^030 Ofc0239 002 3 010
5 60 DO!. hElt.Lt A
5 t2 /.^hTI.E COLh-uGi-LL A
167
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****** K022G11 ***«.**
1 £ NC22011
1 1 t-D LEPT NAT EE'i.
1 7 ELK RIVER - C&D CANAL; PhYSlCAL, CPEi-lGAL, AKB tAC'll-MCLGGICAL
1 7 U1ER CbALITY REPORT NO 1 CCT 19>7 - JbLY 196t
1 11 l.CRlh AhERICA, U.S., t>ARYLAND, COASTAL, LLK RIVER ANO Cl EFAPEAKL
1 11 DELAWARE CANAL
1 17 D.O. '*AS KEASCREC U'lT'h A YS1 F.CDEL SY tP OXYGEN KE1EK
1 17 l.'ATER TEKP, CONDUCTIVITY, AND SALINITY VLRE > EASL'RFL HTh
1 17 Ai\ INDUSTRIAL INSTRUMENT KS5 SALINC1ETER.
1 17 Ph V.AS- r-EASbnEB V>lTh A SAIiGEivl Ph HE1EP, KCLEL PE
1 17 AIR lEt-'P V>AS DETERIilNED IN 1 i F, ShACE v.Ilh A tISCPER ^CI
1 17 SUEEACE bACIEP.IOLOGIGAL SAKPLES V.ERE TA.NLN IN STERIL1ZEL 125 KL SOREV.-OAP
1 17 hCl'iLES. E-G1TOK SAKPLES WEhL 1AKEN l^l> C SltKILE EVACLA1EL 10QrL Ai.PLLj „
1 17 IN A EY'iECti S'lLMil VA'iM LI rLLl. it'-.t-L'tL i.hRl AlA.LYZi-L rOh OtLlh'/; ,-
1 17 LACithJA Ai>t': tCh L.LOL1 f.l 'ith ELkiC: [.AICP-AICRY Ot 'IKE L1ATE
1 17 DtPT OF htfLlE. COLMS /-RE CIVti- t.L I- CS'i-P^Cl^t Lh-l-L'l- Ehh PLh 100f.L
1 17 V.t/il>Lh AND TILL DAI A Aht GIVi.l. IN Ir.t PiPCR'l, PUT LAiP ! Cl hi CGLEL
1 17 1U Itl'fERAlbhE, hATLh (TEGhEEF Ghi.llGPALt)
1 17 20 'IE!-PiRATUPE, Alh (Es.Ghi.'LS CLlTlGhADi.)
1 17 IOC H. (ilANLARL Uil'iS)
1 17 IcO SALINITY - PAFTS PER T! OL'SAl £
1 17 299 OXYGEN, J.1SSOLVEL', ( LLrCUGLL ) ( NG/L )
1 17 31fcH ttCAL CCLlfOhh, i-.Pt., 1UEE CCf r ICLHAiIGK
1 17 9&760 CCLIEChK, T01AL, i.Ph, 1UP1 CL! EIC'oRATlGi.
1 17 9C762 COt.LLCllVllY AT Ar.JtlEil Ihi'P (i.ICf-Ct-'hOS)
1 27 ElGl.'l SlAlIOlS SAhfLED ON 'H PEE SLP^EAIL DATLL E OP Stv'EN P/.hAI-.ETLRS:
1 27 D.O., PE, E.CCLI, CCL1 frChl-S, lErP, .lALIt.HY, AND CCi Db'C'I^VllY
5 3t 1 31
5 11 1 10
5 15 1 57
5 1t 1 56
5 1b 1 31
5 53 1 iL'CAL CCLlEGFi'.S 1C
5 51 1 AIR lEf.P 21
5 55 1 CONDUCTI\m 56
5 57 El
5 5b 73079525t931tb 392636755916
5 57 E2
5 57 E3
5 5c 730795259oOis6b 39290675561C
5 57 E4
5 5t 730795350^3010 39303175^100
5 57 E5
5 5b 73079535211535 393213755155
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5 5t 73079535^0333^ 593133755C3C
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5 5c 73079535122310 ;
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5 59 10316? 0709ot 001 3 OOb
5 60 IU. tEll-.Lh A
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1 17 6lfa MlhA.ih ll'i^OOth, LJSLOLVIC (tC/L />£ !)
1 17 625 M'lliGGU , KJrLLAi.L, 1G1AL (i-G/L /.i !")
1 17 650 fLGSPhAlt , TG1AL C G/L AS Pl4)
1 17 t71 PrGSPP'C.MjS, KiSSGLVH' ChT! GPrGSrt fil. (! G/L A.S P)
1 17 V40 GhLGnILK (i u/L AS GL)
1 1? SU SLLfATF, LItSOLVEi) (i G/L /S SC4)
1 17 955 SlLIGA.LISSCLVtL (fG/L AS S1C2')
1 17 315C1 CCLIKP.V, TOTAL, t-hl-Hiyi-h ML1LP IMtD. 1,-f-J.DG i'l-T 5:C (i?/1CCI'L)
1 17 51751 PLATL GGU'i, '1GTAL, 'ifG AGAii 35 C/?*-'HF (*/11.L)
1 17 7C507 i-hGSi'HGiiLS, JI, TOTAL GfTi.CPrCSfhATk (.H7L AS P)
1 17 9c754 TbhPlflTl, PhGTGKiThIC 420 ,-.U (^C/L)
1 It LK i.UTh PAhllCK
1 19 215-299-1114
1 20 AGAL-LKl Gt hATlhAL SGIEKChS' Oi- PMLADLLP1- 1A/C£PT Or Llhi-
1 'L^ 19Ih A»NL- I he PAhKV-A^
1 22 PKILALi-LrFIA
1 23 r-ti.r.JblLVAMA
1 25 19103
1 27 (SUh'vLlS) 3 STATIOJ-S SOP.FAGL/irCT'jGI- 1 X/t-'G 11-12 KCS/5 IPS
1 27 (V-C ) 3-4 irtAllGIvS SPi-.PLfcL AT 4-5 P.I & I.G TILtS AT LA.FLi
1 27 AIL LATii SUrJ.hh StASGi i-OF 4 YtAPS
5 37 1
5 3t 1
5 39 1
5 40 1
5 41 1
180
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4
I
I
I
5 M 1
5 *n 1
5 ^t 1
5 *i9 1
5 53 1 SiCCLI
5 54 1 SPLClflC GGt-D
5 55 1 fclCAKL-GI.ATh. 1C1' 210
5 55 1 CAhtGKAlt 1Gb 15C
5 55. 1 tfcCAL CCLlKiiK 32
5 55 1 IC'TAL SGL1LS 131
5 55 1 VGLIlALa SGLILS 130
5 55 1 HXbL SOLUS 130
5 55 1 TOTAL FLAIL COUM' 311*
5 57 1-66 FCfLS CF-tLK
5 5t 7307tbc53S25?c 31-2327765956
5 57 2-66 301 LhlDGL
5 5t 7307t625191»205 3c2lU0765925
5 57 3-66 i-.ORGAMUlVChLAK Kll.T
5 5t 73C7c6^50t2155 3&2G25765b15
5 57 1-09 POftS Chtti;
5 5t 73G7b720^CG35C 3^2^05770030
5 57 2-fcS* i-LAKT SI'ik
5 5t- 7307^625192^11 3B212c7659"it
5 57 3-69 KOhGAl.TG^:,
5 56 73e7o615995C09 3t19507o5909
5 57 KAlhlAS i-GIi-'T ^4
5 56 7307t7cOU2^HO 3o
5 57 1-ThANSLGT FGPtC
5 56 730766253945^5 3e23
5 57 2-ThAi.£tCT PUrLl CnEtk
5 t,c 7307072030412^ 3123^277001^
5 57 3-iP./.^fcCT i-Gl-bi GrittK
5 5c 7307c72G303323 3t2332770033
5 57 ^-ThAf.SLC'i r'CPLt ChLtK
5 56 73076720302530 3t2323770050
5 57 5-lRAi-.Sr,Cl K.FiiS G^LhK
5 5o 73G7072C311161 362316770111
5 57 LL01 i-i
5 5o 7307072040133^ 3c2i, 13770034
5 57 tlGi S
5 56 73076625295169 562256765919
5 57 kCt-1 FOttS ChLtK
5 56 73076625392576 3t2327765S5c
5 57 LGi^-2 l-.ChGAhlL*-?.
5 5c 73C7c625Cfc5505 362050765b55
5 57 LG ST^.TlOl' 1-A
5 5b 7SG7t62535352C 3c233?7o5950
5 57 LG S1AT1GI. 1-r
5 5c 73076720302106 3b232C77001o
5 57 LG S'JA'i'lGl, 1-C
5 56 7307'1720300il95 362309770Qi)5
5 57 LG STA'ilGr, 2-A
5 56 7307C625193253 3c?139765923
5 57 LG S1AT1G! 2-1-
5 56 730766251935^6 36213^7^5956
181
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5 57 LC STAlIOf. 2-G
5 5t 73076720103200 36213C77G02o
5 57 LO S1A11O. 3-A
5 5t 73076625062427 562022765t47
5 57 DO STA110K 5-t
5 55 72076625091256 312015765926
5 57 DO S1A1IOK 3-C
5 56 73076720001 10C 3^2010770010
5 57 LO IRAttLO'l 1-1
5 56 73076625394565 3^23^^765955
5 57 LO IrAlSECl 1-2
5 b£ 7507672030^124 3^23^2770014
5 57 LiC Ih At- SLOT 1-3
5 5b 7307^720303323 362322770033
5 57 CO ThAKSLCT 1-4
5 5b 73076720202530 362323770050
5 57 DO IhAlSfCl 1-5
5 5b 73076720311161 362316770111
5 57 1C lhAl>SLCT 2-1
5 56 7307tt-25194115 362141765915
5 57 FG IhAi.SECT 2-2
5 5« 75076625193265 36212t765925
b 57 LO IhAKSECT 2-3
5 56 7307^525193555 362135765955
5 57 i-G Tl'Ai.StCl 2-U
5 5o 73070720103135 362132770015
5 57 LO Tnff-tLCT 2-5
5 5t 75076720103305 562150770035
5 57 to TPANSLC1 3-1
5 57 LC lj,n££C'I 3-2
5 5o 750766250910^2 2
5 57 CO IrALSi'Cl 3-3
5 56 73076625091350 3t2C157c5930
5 57 LiO IKAl.StC'I 3-4
5 5o I207662509152fc 362012765956
5 57 CO lh/,i>SLCl 3-5
5 58 75076720000275 362007770025
5 59 0^2466 121274 001 3 000
5 60 DAVt, iSORCK A
5 62 i-AFlht COLE-JOKLS A
182
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******* K022G21 ****»»•
1 2 N622021
1 1 FA ACAD N3 PHL
1 7 A ChEKICAL, LACTEKICLCGICAL AND FKYSIC/L STl'Dl' CJ.1 ThE CbESA.FEAKE
1 7 eAY IN ThE VICINITY OF CALVEET CLIFFS 196t ,69,70,71,72,73,75
1 7 FOR EALT1KCRE GAS AND ELECTRIC CGI-PANY (tG&E)
1 10 CALVEhT CLIFFS P.ASEL1NE STUDY l-CR PGif
1 11 NORTH AI-.thlCA, U.i>., KALYLAND, COASTAL, CfLSAFEAKE £AY
1 17 10 TEhPERAlbPE, kATLR (DEGREES CENTIGRADE)
1 17 70 TURBIDITY, ( JACKSON CANDLE UMTS )
1 17 300 OXYGEN, DISSOLVED (i.G/L)
1 17 510 fclOCREKICAL OXYGEN DthAfcD (KG/L, 5 DAY - 20 DEC C)
1 17 100 Ph (STANDARD UNITS)
1 17 110 ALKALINITY, TOTAL 0-G/L AS CACC?)
1 17 M5 ALKAL1.M1Y, PhLLCLPKIALLli. (hG/L A£ CACOi)
1 17 140 LICAhfcChAIii 101; (t G/L PS HCC3)
1 17 115 CARtCl.'ATc, 10K (t-G/L AS CC3)
1 17 ItO SALINITY - PARTS PEh TPOUSAM
1 17 60b MlhOGEK, AK1,OMA, DISSOLVED (f:G/L ;S ! )
1 17 610 MTRCGEi-, AU.GMA, 1CTAL (1 C/L AS i\)
1 17 t>13 Wlf'Ilfc M'IKOGEK, DISSOLVED (KG/L AS K)
1 17 615 KlThllE MTfCGEi , TOTAL (I-C/L AS N)
1 17 616 MThAlE MTRCCEK, DISSOLVED (i-G/L AS J.)
1 1? 625 MIRGGE'C, KJLLDAhL, TOTAL (i-G/L AS i.)
1 17 650 PhOtfhATE, TOTAL (J.G/L AS PCI)
1 17 665 PhOSPhOftbS, TOTAL (i'G/L AS P)
1 17 671 PLCSfLGhliS, DISSOLVED OhIK.PP.CSPhME (KG/L AS P)
1 17 910 OhLOI.lDE (tC/L fl£ CL)
1 17 916 SULtATt, DISSOLVED ( LO/L AS ^01)
1 17 955 SILICA, DISSOLVED (tG/L AS 5102)
1 17 956 SILICA, 1C/1AL d-C/L f.S SI02)
1 17 31501 CGLIfChK, TOTAL, I'hhtFAt'f FlL'Ith IKi.ED. t'-LMC t tt1 350 (r'/100F'L)
1 17 31610 rLCAL OOLlrOnt, i-.r.Kr. flLii-r, 1-,-F C br.Vlb 11.5 C (*/10C!-.L)
1 17 31751 PLATb COUNT, TCTAL, TPO AGAE 35 C/£1tK (1, n KL)
1 17 70507 Pi.CSrhGKIS, II TOTAL OrTFOPhC.SPliATf (KG/L AS P)
1 17 9o753 ALKALINITY, KLIhY'L PO/.PLE ( i-G/L AS C/.CC3)
1 17 Sb751 TuhLlDlTY, PhOTOftTRlO 120 .\U (f-G/L)
1 17 STAI.bAhD i\EThODS 12Th ED FCR 196fc,b9,70
1 17 STAUARD KETEOCS 1ST P. ED ^G^ 1971,72,73
1 17 l-.LhFhY & RILEY (1962) FOK TP
1 17 SLRtA.OE: 196c (JUNE,AL'G.SLPT,DEO) (H STATIONS)
1 17 Sti'.fAOL: 1969 (JA1 , JULY , AUG.StPl ,CCT ,1.0V, DEC) (5 STATIONS)
1 17 SbhtACL AND bOTTOi-: 1970 (ill I-OS Eittt'T JAi )
1 17 SbhFAOE AfL EGTTvJh: 1971 (12 KGS, 5 STATIC! S)
1 17 SlihtACt: AND tOTTO;- 1972 ( 12 KOS, 5 STATIONS)
1 17 SbWAU AND POTION 1S73 (12 N OS, 5 STATIONS)
1 17 Sbi.fAOE AND tOTlOf-1 1975 (6 (CS, 1 STATIOI'S)
1 17 1975 ! tASbl Ei-tl.TS wthh DCNE IN KEP[L1CAT",
1 17 ADDITIONAL PARAfLTfrhS t-FASbKED OR CALCULATE.!: PUT NOT fciCClLi If CLLLI-:
1 17 PONON, IhON, t-ANGAt'ESE, GOPHER, tlGKEL, ?,1IC, ChEOMLK,
1 17 POTASSlUi-:, I AGi.bSIl:!,, TOTAL HARDNESS, CALC1L1 HARDNESS,
1 17 fAhiNESS, CALCILK ill CARLCN DIOXIDE
1 16 DR. CLYLc. (.GbLDj,!'
1 20 Til, ACADEKY Ot7 i-ATUrAL SCIENCES OF FULADfc LPnIA/I EPT LI.'
1 21 191 P. Ai.D TPE P/l KVAY
183
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1
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1 22 PhlLALfcLPhlA
1 23 PtH.iALVAi IA
1 25 19103
1 27 5 S'lniGi.^ (4 li; 1966) 1ANPLSX AfPhCX 1 X / KG FGii APRGX 12 l.C/Yh FGh 7 Yh;
5 37 1 576
5 3fc 1 645
5 39 1 1470
5 40 1 2151
5 41 1 fcC5
5 44 1 364
5 45 1 645
5 46 1 645
5 47 1 1622
5 4fc 1 642
5 49 1 1186
5 53 1 fclCAhECNAlt IOK 179
5 54 1 CAhfcUlvA'ik, ION 262
5 55 TC1AL PLATE COUM 272
5 57 KEf,V-GY
5 5fc 73C7t62265K"43 362614762533
5 57 hGCKY PtlKT
5 5o 73076622434533 3&2443762S53
5 57 LIT'iLE COVE PC1KT
5 5b 75076622124100 3621"076221C
5 59 060t>6c ObC275 001 3 005
5 60 KAllGi^ hGSS A
5 62 MifcTKfc CCLb-JGi.tS A
184
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****** f'.C22022 ****!<*
1 2 (.022022
1 4 FA ACK l.S Fr.IL
l' V CF.ESAPEAKe iAi SbKVEiS (CALVEhl CLltl-S) SURVEY REPORT FGP•
1 7 EALTINOltE GAS & ELECTRIC (EOftt) 1963 TRRU 1975
1 1C CALVbRl CLIFFS £ASF LINE STUDY
1 14 KCR71: AKEK1CA, U.S., COASTAL, kAF-'YLAKD, Cl'e.i: BAY
1 17 SUFVEY ALSO IliCLCLLb : FCClfcX ACUAIIC ALGAE, PROTOZOA,
1 17 HACKClNVERTEtRAILS, FIEhE'S
1 17 kEThGCS:
1 17 196fc ThrU 1972: 5 HI & Lf TIDE DATA, SFMKG 6 FALL SEAS01 , 4 STATICtS
1 17 1973 ChEKlCAL & PHYSICAL DATA br-DLR SEPARATE COVER
1 17 1974 3 hi & LO TILE LATA, tALL SEASON, »» S'miCl.S
1 17 197^ LA1A - iAKPLES AT 2 FT., l.CT AT SUfiFACE
1 17 1975 6 FLOOD & LbE, 2 SEA5GKS
1 17 IFv/.t.SPAhLNCl KEA&UKEhEMS I!- 1972 ALL 197^ wLRE hLCOfttL AS FEL1,
1 17 (StCChl CISC) LIT THE OBSERVED FkASLKLt'.L! T5 APPFAHS TO EE IK MtlET.S.
1 17 LA'iA f.USl HAVE EiitU H1SLAEELLED.
1 17 10 TEKPEhATURL, V.ATEfi (DhGhLLS CEl.TlGl.AtE)
1 17 76 TlhilLlTl, F.ACF TUhtlDl!'FlEi\ ( FOFKAZlh TLT.t Of!lT )
1 17 77 TRANSPARENCY, SECCrl DISC (IfChFS)
1 17 95 CONDUCTIVITY AT 25 DEGREES C (MRCCf-hCF)
1 17 300 CXYGL1-', D1SSCLVF.L (t.G/L)
1 17 310 L10CEEMCAL OXYGEiO Lt-KAt-.i) (iO/L, 5 DAY - 20 DEC C)
1 17 4CO Ph (£I/.M,ARD UMTS)
1 17 tlO ALKAL1UITY, TOTAL (KLi/L AS CAC03)
1 17 115 ALkALIIvITY, PhEi.CLfhTALi'.IlM (>G/L AS CACO;)
117 HO falCAhtCKATK 101. OG/L A.'J hC03)
1 17 145 CAKtCi.ATE IGf< (i G/L A>1 CG3)
1 17 IfcO SALlKllY - PAKTS Ptji TrOoSAKD
1 17 SCO KtSlDUL (SOLIDS) TOT^L U.C/L)
1 17 505 RESIDUE, TOTAL, \OLATlLf (4\0/L)
1 17 510 htSlLLE, TCTAL HXtD IMVL)
1 17 610 MThOGEi. , Ai-.i-.OMA, TO'i/.L (KG/LAiH)
1 17 615 lilTRITt WTROGtr , TC'iAL (MJ/L /S D
1 17 b20 MTRAIE l.lThOGLJ., TOTAL (fG/L AS >,)
1 17 625 UTfiCGEk, KJELUhL, TOT/L (^G/L AS JO
1 17 630 MTRITE FLOS MTRA'ih, TC'iAL 1 DtT. (fG/L AS F)
1 17 650 PhOSPrATL, TCTAL (i-C/L AS POD
1 17 bt5 PhOSFLGhUS, TOTAL (hG/L AS P)
1 17 671 FhGSFhORUS, DISSOLVED GhThOFhCSFh/dh (KG/L AS P)
1 17 940 ChLGKILt: (KG/L AS CL)
1 17 94b SULFATE, DISSCLVL'D ( fC/L hS S04)
1 17 956 SILICA, TOTAL (KG/L A3 S1G2)
1 17 31501 CCLIFORi-,, TOTAL, f-.tMRAI.E- F1L1KF I;!FL. l-.-i'fCO KFD 350 (ir/100f-L)
1 17 3ioi6 tLCAL ccLitcw., ^:h^.L^ ULTEH, K-BC C.^GTH 44.5 c (i-/iootx)
1 17 31751 PLATE CObfcT, TOTAL, TPC AGAh 35 C/24rF (t/1 i.L)
1 17 70505 t'iiOSPKATE, TOTAL, CCLCHi-tlhlC f-LltOD (^G/L AS P)
1 17 9^754 TURBIDITY, PhOTOi-tThlC 120 KU (I-C/L)
1 17 9t764 taTRCGti;, FAH'ilCULATh (hC-A'l/L hi, I)
1 1fc Dh. CLYDE GOLLLEN
1 20 ACALEM' OF NATURAL SClEt-CfcS OF FFlL/.Dt LPF.IA/Ct P'l LIKf,
1 21 19'lh f.i\D TfcE PAF,Kk,AY
1 22 PhJLADtLfF.IA
1 25 fLl-f.SYLVANlA
185
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1 25 19102
\ 21 2 "& £ hIGi t-.l.l LGV, TILES SAf-t-LtC 2\l \\\ FOR 6 IPS AT 4 3T/iTICKS
5 37 1 + hAGh( rOhr.A2.lt-.} 472
5 36 1 . 461
5 29 1 1465
5 ^0 1 1610
5 *»1 1 ^69
5 i*^ 1 -»-tLCAL CCLlFChM 526
5 **5 1 ^62
5 ^t> 1 72
5 ^7 1
5 ^c 1
5 ^9 1
5 53 1 2ECCKI 79
5 54 1 CGf.LUC'IIVm' 470
5 b5 1 tlC^hECI.AIfc. ION 470
5 55 1 CAKL-ChAlE 101. 433
5 55 1 TOTAL SGL1LS 462
5 55 1 ICiAL HXLL cCLIDD 465
5 55 1 VOLATILE SCLID.S 46S
5 57 1 SCl-lh K£I'.V,COD tfACh
5 5t 7307to22990554 362905762934
5 57 i iCLlh LOKG fctACh
5 5t 7307ct227701bc
5 57 3 CAHf Uit.CY
5 5e 7307fc622660017
5 57 4 iGtTh hGCKl
5 5o 73C7c6224401£
5 59 OcCofac Ot2b75 000 0 CG4
5 CO i AhlAK hUSS A
5 62 J-Ai.Ti.c CGLL-JCi.LS A
186
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*fctfcft*
J-,'02202'3.
1 2 H022023
1 4 US EPA REG 3
1 7 V.AlEft CUAL1TY SURVEY OF Thb CHESAPEAKE EA1 IN IKE VICINITY OF
1 17 SAKDY POINT DATA REPORTS i13 (1966), #14 (1969), £22 (1970)
1 14 NORTH AMERICA, US, MARYLAND, COASTAL, CHESAPEAKE EAY
1 17 196b DATA ON DGI'.INANT PhYTOPLANKTOt'i LOT ENCODED
1 17 ALL STATIONS AND ALL DATA CODED RY L'PA AND IN STOEET UKDtfi
1 17 AGENCY CODE : 11121R',,v
1 1? 00010 WATER IEKP bECKMAN SALIKETLh (CENTIGRADE) '
1 17 00070 TURRIDITY (JACKSON CANDLE UNITS)
1 17 00077 LIGHT EXTINCTION SECChl DISK INCR'ES
1 17 00095 CONDUCTIVITY AT 25 DEGREES C (FICFOChKS)
1 17 00300 DISSOLVED OXYGEN STANDARD hlTrCDS VdUKLEh J-G/L
1 17 00400 PH FIELD Ph KEItR ?
1 17 00460 SALIMTY bECKN7.N SALINOhETER m
1 17 00310 EOD STANDARD tJETKGDS 5 DAY, 20 DtGHES CEKT NG/L
1 17 00660 1NORGAMC PhOSFhCRUS f-iL'RPHY & RILLY (196D KG/L /S P04
1 17 00125 TKh STANDARD KE.ThGDC i-'G/L AS t'.
1 17 00630 i-v02 & NO 3 STRlCt.LAt.D AND PAFSO'-S !'G/L AS N
1 17 00610 I.K3 PhEKCL-hYPCCLGRITL hC/L AS I
1 17 OOcfeO TCC DCW-LECKKA1. CArfcOKACECUS AlALYZER KC/L
1 17 OC690 TOTAL CARtC'I. DGV,-EECi;hA\ CARBOI. Al.'ALYZER r'G/L
1 17 31506 CCLIKORM STAl-'L f"ETF TUtE LACTGSL tILE 35 DEGREES CEM HPK/100KL
1 17 32209 ChL P STRlCKLAKi Afsb PAhSCKS i-.G/L
1 17 31615 FECAL CCLItChi-, STAND f.LIit TILE E.G. 45 DEGREES CLHT KPr
1 17 71fcfc6 TOTAL fi.GSPhCKliS t-G/L AS PC4 fENZEL & COR\;IK(1S65) ;
1 17 hLRPKY & RILEY (1962)
1 17 1968 16 STATIONS (3 AT 5 TRAt.ShCTS PLUS CRAIGFir. LT)
1 17 1569 23 STATIONS (3 AT 5 lhAKSECIS PLuS c TRISECTS HTK 2 STATI
1 17 RLIS OKE TRANSECT V.ITh 3 STATICi-'S AND CR/JGhILL LIGHT)
1 17 1970 23 STATIONS
1 17 10 TthPERATUhl, UTEK (DEGREES GLM1GPADE)
1 17 70 TLREID1TY, ( JACKSCr- CANDLE UNITS )
1 17 77 IRAKSPARE1CY, SECCM DISC (INCHES)
1 17 95 CONDUCTIVITY AT 25 DEGREES G (KURCOi-.J U )
1 17 300 GXYGhtv, DISSOLVE! (i-.G/L)
1 17 310 bICCh?! ICAL OXYGEN DEKAND (KG/L, 5 DAY - 20 DEG C)
1 17 400 Ph (STANDARD UMTS)
1 17 4fcO SALINITY - PARTS Pth THOUSAND
1 17 610 MTROGLN, AM'.GNIA, TOTAL (tG/L AC h)
1 17 625 NITROGEN, KJELDAHL, TOTAL (KG/L AS N )
1 17 630 NITRITE PLUS NITRATE, TC1AL 1 DST. ^.G/L AS N)
1 17 660 PHGSPhATh, ORThO (N.G/L AS PG4 )
1 17 6bO CAEitCii, TOTAL, ORGANIC (NG/L AS C)
1 17 690 CAhfcClx, TCTAL (KG/L AS'C)
1 17 31506 GGLlrORK, TCTAL, hH; ,tCI\r IRKtD Tt.3T.TLtE GGf-flG. (NPN/100KL)
1 17 31615 FECAL CCLlFGRh, I- Ph , EC FED, 4'l .50, (TUE-r 31614 ) (hPL /1COKL)
1 17 32211 ChLGFCH.YLL A (UG/L) SftCThGrLGTCMTRIC KEThGD
1 17 71tbo PhGSPJ-.GRUS, TOTAL, AS P04 - l.G/L
1 "ib * .V,. i-.Ahkij & D.k . LLAi-
1 20 ^i,i,^rbLlL riiLi t.UiCL L i~ [,S KPA KtGlGi. 3
1 21 Ll.i.tKLli. oGJL NGt GENTth
1 22 1-i.l /,-GLlL
187
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1 iT 'd '.-Al.'ilLi-^ (1C li 1.:. I ;
5 it I C.-.L /, «r<
5 i? 1 tY
5 ir 1 1C1Z-
S I-t 1 In £ ii.u.u UH
t '•C, 1 ia i+;.L.; IK!, i f ; .-?; 1
t A2 1 'ICC 1C iC
5. At 1 irtCAL CCLlrCf; i. i?0
i- A; 1 ;.<.?
1
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5t V2'CYt.'-.Ct'tt''ioV :",Ci,tt7or-:i7
f-7 A/'-i ill: r tr'-t
5«. 7if.-7bc-i?r'.-«cic ?^i'-i,r,'\.:iCc
''-1 vfr 'KM-r/rii i.- JLL irl
72C7SoCi::A3t05 I'^o^v'/t :-'.f«.
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7i^7Sf'Ci5;i;-<7c, ":.,.C5?7Vt^-33.
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7;C7UGc5C^t?7 :^-'.^: i\ 1 C;>7
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Access* IT; the riutronhicdtion )ata base
At the ti"no of this report the Uutrophication Jati base consists of the
data sets described in detail in this i-wndix- One shO'iM note tint there
.issesslon number/data set references in the directory for which no actual data
exists in the oroject data base. 'Jnl • the data sets described by the
individual, iet.iiled descriptions be-;tnnin; on na^e 9 of Appendix U exist as
machine readable entities In the dat.i base.
At the present tirae, and until the transfer to STORiT and/or the
Chesaoeake (Jay Proc;rvn Database, the data base is available through the
facilities of the Univeristy of .laryland Co-inater Science Center, specifically
on the UN IV VC ll:>-5. Access to this comutor systOT may be arranged as
indicated for access to the cliuitic data. Prior to transfer to the pentanent
repository, the data base oay exist in -vus storage and on na^actic tane hrit a
copy of each data set will exist on a reel of Ti.;neLic tane (reel ninhcr
Pl'JJJii) at the Corputer Science Ceater. The first file on tape P1093'* contains
the climate data as documented in Apendix A. The third file on this taae
contains the synbolic listing of, and the machine execut ible (absolute) code of
a pro«ra'n which may £>e used to copy selected data sets fro:n the tape to mass
storage files. The vnass storage? files lav ,ie printed on a hi^h-speed orinter,
punched onto cards, used .as data files fov analysis p'n"rass or co'iiec! to
aa.;netic taoe for transportation t-> Dthrr computer facilities.
Since we anticipate tnat additional 'J.ata sets will bf added to the
database .vhile it is resident on t-ie Univeritty of 'larvJand systei, the d^t-a
extrjctio'i pro ',ra i will produce, uoon request, a listing of the data sets
currently on taoe ."'IJ'JJ^. Alternatively it will accept as innjt, t'ie na^e of
data set an<: resopnd by creating a 'iiss s^on^c fiJe, novf.tr; fie t;r-e t'» the
orooer location i;id copvirv; the data sot fron tan3 to the nass st'-ra^e file.
'Joeration of the Jata >et Kxtraction Proo.r^'i
The foliovin* seiuence of conputc-r O")e>" '. ti'.i'x systen co'.nan-ls ~iay be used
to access individual data sets in the data bisc.
-'•:\r,P XVfA.'JLL.
JASG ,T r-\pi: .
J FW.-: T..I
ftie pro^ra-n will query the user as to what action is requested. The two
Dossihle actions are:
1 ,')utr>'Jt a li?t of data sets in the data base;
2 -opy a data set fro;n the data base to ;nass storage.
The program will nrint
)? fO'J Ji:,l \ LIST OK )\IA ~^T5 .lO'JPTs) (Yr:S/:iD)
A rCS will cause a list of the currently available data sets to be
213
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displayed at the user's terminal Trie! a slnilar list to be written to i tmoray
file n.TicJ 14. This file <14.> .lay So ex.anined with the Text Editor aa.1 will
serve -as reference during the life of the computer run. The oro-;rai will then
query the user as if a .'.' ) had been entered.
r
A ft) -fill cause the nfo »ra'n to print
:u v\-^i OF r:t-: >:si:U ,'G ^E'JF)
The user should respond bv typing in at the keyboard of the tenirial the 7
character assession nu'ihcr of the desired data set- ii-tch enti'y -Tist be on a
separate line but nultipl? reiu^sts mav '>c entrreJ via the keyboard or by
typing the:-s into i teioorarv dnt.i filo and MJJ'ln'» the file. In either case,
the proper rer -iin.it ion sir»n-il to the oro.;ran is the i-w;a M^')F.
Oat.i sets extracted by th« nro:',r;n will nov exist in ^iss storage as
(cataloged) , public .•;)!•' or data files. .-i'sch files will be n.iintii no !
in T.TSS storage for 20 davs unless accessed bv any aser. The file.s will b3
afforded neither read nor write protection and thus :r coninnds ( CiiA^.:.^ , )F.L:'.rz) and by so-ie mer.it in-
conra.inds, (JOSLiir-! , '.')Ar.\,I , ,P (entered ^t_hiv^t
the brackets) is the assession nu'nber of the dataset. C'.'-13 (l=irest version)
discussers other ooeratint; sv^teni coTnand-s whir.fi ~nv be used to examine or
the data set-3.
D.it'i frcn A'itO'i;i tod )it^.
Jata >ots acquired fron iutoTitel data systems are usual lv still in t'f'«ir
or ;inal fonit when aade available to this project. Since these data <=-";t.i. are
•nachine ( co.nmiLer) readable- the nast effecicut way to convert theTi to the
eutrop'iication oroject standard fornat (L>2) ; s throa",h a cmr>uter translation
pro ;ran. A unique translation -iro^ran ir> reiuireri for each iif fer."':t "f"rci.;n"
or input data set but the lesion concept is the sa'ie for all. \11 computer
activities -tssociated with a data set are keved to the assession number of the
data set. The assession nu Tiber is the root of any related filenaie.
Parameter Identification
iiach iiniiue parameter in tne "forei",q" or iao'it data s«t nust be
identified an i in exact determination nade of the -ethods used to calculate
that parameter. A look-uo or translation table containing cole pairs (old-new)
for each nara-neter in the data set is created. The oiri-&*>!e ib~"tne )at data set and the new co ie is the corresoo'.iin';
SIO.iCT code to be .ised ir. t!',e eutronhicatii-vn ^r = -;•_». •.- -\,IL i set. The zolu
translat io'i file n.-i.'ie consists of the issession na-ie root and tliP j>rifix. '"f.
,\ny new oara-iters which, occur in the input data set are ad:! el to the file
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J'it a froi 'Jon- v ito'i ift-J S
i'nlii ie-it ton.'i <:•> j other ior-i !<-nMf ion eonc'-'rnin^ a ot not avif 1 »'">1"
froi in lutos.ituJ j»t.» syst«-T ire .»st* i t> identify thr *;••'•! -,)•; MSO I in the
col l«'Ctian of the obaerv.it. i.^ns/T;">-;>irfi<; it s. in the c r. • -;' toii;, emec in 1 1 /
>l'li?r, .i it.:i stits tho tecnni'7'ieu -isor, •>;/ ^ircne Gole-Jo.iv- co -iro.-ifrly tck'itifv
tneae ncchods see i b-vrihy of .5 no r 1 oc '<. r.Kr:r oameter cole fro~5 the
jf-K'ir cole 'wok or a locilSv generate-! i>u*'J^e••J '.it . X eoit-'i-xx cont.iinln', instruction's f>r
c^calliir- the »»n rire^ire-!. fhf tii,- foriit. (;>^) Is n1?'' ! ror
Jit. i Hi;r-i fro-a non-.iato i itit 1 in i t'ro-i •* ito Tttci 1 tea -jy«tt?"ii. fh<> f-nc.') Id ! ita
s'ltf'ti .ire useJ in tMitfirlti^, t'te ! it.i Hrcctly into i c'jriv>arcr (i-ita file b/
i bists for croitlT'. mncH c-iriis on i
kt'vpsincfr. i^jocf. carri i--c<3 ar«4 5»<». ;.'ew .jar i jotc-rs fic-jj.-iti.Te i in t'ie i.'lt.i r<'it ire a Mcd to
Vorif Icat. io i
> it.t «hic;i edits in -» c'npjtcr ''iti t>-i';'> iv-Jti1 • ir*"1 isal-iti?.i froi tiie
'> olic.il 1 <•"•;, ffticLs or -.it'-itr tnf '-".".V 5 C ; •-;: -,f L.ie viHHtv if ttif» orl",inii
:nea ;ur-; ".;-:'t f^ch-.i jjc-:. ^.i.llttv ns-trnc-T 5u:' ^''is iSn'.'Ct of Llie -iitl
CO I l»T,r.i >n ictlvlt'fi is :';:: r.« in in«; i ;-.j it.- -ir •><,•••.• ti'ihnrs of t'u; Troioct
•i.in.i ',« a->t tc;ri. J'.)Tin-iri'-o=\.'; of •: > v. :t-,-i :--.•« :iolo ! it t -;ij.h their so.irc^'5 i i;
ilso .-'ifficuit sincf the ;»*{•; ;', •_••_• :s - •• T>: trcomiv t.1-'1 !.n » files.
-'a.iiit--' a.i«5-!r.-:r.ct" l". t ii -: ii'.'i i-- .'Ifirlv i -irii.irv fincti-jn -ml r-.'sooiniMl i tw
ai tnc- !.jt i Dise Tint '•(••'.
Verification o'~ tr i;i ;l.':!.ioii<5 for- i-:t'i -•itc i 1 ita svMens
\n exnior-itory amlvsis of the "foreign" -iiti fomt i= caniuctO'l to
Jeter i us t'sc fi;r i of e jf '.'Tl'i.'s. A cin-ii Jate tr.Tisi.it i on
!>i o,;r.-: •: Is .ipvf-1 ooc'i. iis-nliy in a nro.;r.i *iin: I'.n^ia^c 'Jesi™n.'l for character
amir's lit ion. \ test .i.Tt-* set co'it.; inin?, in e/ !T>1 nocossjrv. I.nf or-iit ion (nunber of
locitions, -iit.^-?, records, etc.) on trie trsml-j :! on i •; ^pnoratrl by the
tr,in> i-it i 3n pro^r-ii aai this infov'.it i^n i := con:>arol to hotli the ontnat and the
ino-ji J.iti. Tne tr.iTislation oro^.r.i'i ml t'"f ".-'- fomitt^d JTta get generated
by it iro not ,icce->tei -lfiti I thfse Jpscr i Tt ion-; .!r" i r. -.",re.j ;enc. \fter thi0;
Ly:>c Ji" tf"5C ii s n-c::?sfu) 1 v c y>n>ieLe-i , the tr.in^ i n t ion outn it l«j not verified
^n ,T c'ioncter !>/ cnarict.^r basis.
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Verification of manually entered data sets
The original encoding sheets .ire conoared to the hardcopy output ou a
100X, character by character, line by line basts. All noted discrepancies are
corrected before the data set is accepted by the data base uumn^er.
"Coded" Parameter Codes
Many computer pro';rans in the project calculate .1 "hashed" address when a
5 di^it STOIIfclT parameter code is encountered. This is necessary to reduce the
parameter code related storage requirements from a minimum of 99-J99 (5 dibits)
to a few hundred locations. A special code number is used in the hashing
routine to generate a uniTue storage address for each STOSiRT parameter code.
.Jhen new parameter codes are added to the file PCJTE., a check mast be made to
confirm the validity of the existing special code or to calculate a new one.
The program CJJi'IAS.:l does the checking.
Oata base design
Oata storage and retrieval systems, regardless of the medium, 'nust
accurately retain and reproduce the original information. In -in automated data
stora^e/retreval/manipulation or data base system, oositive stens nust be taken
to ensure that all information stored in the data base system is, in actuality,
an exact representation of the information sjmlied Cor entry. In such a data
base system, an essential design criterion requires that authorized revisions
of the data base are retained as !inabif»uous alterations Lo one 'master1 set of
records which may then be cooied for added security. Additionally, the data
base storage mechanisms should be conservative of the storage resource.
liutrophication Pro ject ')ata Codebook
Overview
.•teanin>;ful water quality data collection efforts precisely define each
parameter of interest aruj locate the measurement of each parameter at a fixed
point in soace and time. The ei-trophicat ion pro-ject data format (K-2) is
designed to record, in a unified format, the data collection efforts of nany
different researchers who used a variety of specailized dati recording schemes.
Format ii-2 comprises three record tvneo which, in combination, serve to relate
the measurement of each parameter with the identification code of that
parameter, to further identify the location, date, time and depth at which the
measurement was made as well as to link the information to the ncrson, ^ro-.n or
agency responsible for the orij'iml collection. The thro."1 record types are
(1) header recor-is, (2) date/location record? and (3) data records, deader
records (card type 1 ) are used to name the station or collection location.
The intended use is to provide visual identification for station locations
during the verification and editing of data. Jate/loc-Jtion records (card t^'pe
2) are formatted to record the data collection date, the location, U, the
nearest second of latitude and longitude, and the maximum water depth at the
station. Jata records (card type i) .-re used to rocor.t up to four data
measure lants. iiach measurement consists of t':e parameter identifier or code,
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the sarnie depth and the value of the =:ieasurement. A ti~.i2 field is used to
record the time of collection (when known) of the data '>roups recorded on the
sane record(card).
1. General Introduction
The EutropHication project, data foriat (C-2) consitd of three different
card types. 5;tch card type has the card tyjV designation (1, 1 or J) in colunn
30. The identification nu-nher of the data set (the assession number) is
encoded in the first seven card col;r-ms of each card of all three ca*~d tyy>es.
The assession number is coded in the seven (7) colunn block in the uoner left
of the S-2 codin;', sheet. The assession nanher does not change within a data
set.
2. Card Type 1
2.1. .\S3iiaSLO;: UiTliJE1!. (Col 1-7)
As noted in the introduction, the assession nun her occupies the firr,
seven positions of all cards, regardless of type. The assassion nu.ibor i;
encoded by placing it in the ssiall uraper left hand block, on each K-2 colin^,
sheet. The data entry person will pancu that block as the first seven
positions of all cards, th.'is position 'umbering for all cards starts v/ira
col 8.
2.2. JI'jGiUPTIO.J (Col ;? - 7'3)
The body ot card type 1 is free field and is intendel to he used to record
the narne (and optional number designation) for each station ^nd its nssoclatad
data. Ihe lnfor:aation "lay be coded in card columns 3 through 7d inclusive.
This card nay also he u.-^cd to record ano-nalies in tne data, fither in tvvi
orivxincil data or in data translation to £.-2 fot'iat. '-.'hen a conneit ab.rat th.i
•data should be nrinted aloni; witn any analysis of the data, enter a "*"
(without the quotes) in col 8 and then enter the comment in the reMainder of
the field (un to col 78). The text in col. 3 - 7H of card tvne 1 is not
controlled since there is no intention cor usinf> the contents of this field an
a search algorithm.
2.3. TSST C\U (Col 79)
Golu-nu T) is the :
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i ;S w
'"•>.r,: Col s - u)
:l i f'J ii ; i t s of the ve-ir of sn:>lJtv.', ii.ite iii colnn.i'5 4 .nvl '•>.
',(.»!,.• t'li* ;;•;•• ' ,: ; >. v.il-ic oi t'ic rsvii'i of th--> smli-T", >' itc (Jiiiuarv i, July 7,
;i-c<- iV.T ','• ; • -1 , 1) .1,1] II. ThtJ Cu-_> J[".!t nv of t;>e ")ont :i Is coJe-J in
C.ll. 12 ,i.<
r.u- •-, , "• '• r'ttli (col U - 27) i«i •!•;.,•{ to encoK? t'i» hrvi.in l/Vir;;ini,i
;rij loaat?- - ^.l^oastr-ict of tHe licit-lie 11 J I >n-.l tu ie of the -it.Ttion
j«".?.,r.; 'Jonstrictl JH .)!' t'u- !!/V'i -;ri ! l.-^
f'it" ;!«' •: ."i'-rm of i;i^ L use r ic t i n-\<: for c'j'is t r-ic r. i-i -, a ;rid locitor .ire
C Tnt.'i Lr.c i ?,; ' :.- i i.).XV - .lavii'Tnent i 1 >ili 'li-;e )i rue t .-iry ,l.irv!->o-Vt for
[ntc-rvl.!w'! 1 rt!-,ie f ro i tlu: ).I:..T In ',-.'••/. -'.rincri, '.',1 1 ioivil )re tn^ -ranhic 'Jati
Ci'-itur, 2.1J; f.-.-m.;!^ Avoni:^ •;.;., .,' ishin^.t 0:1, ).C, .!>215, (/•»?) 634-7.^)8. -\
;riij loc it>";f ,,'»l.fr can Sj con:? t rue to t ov t ' tr-r Is.-ivin"; the: co'i->irible nLice
ii,;i'.') or i, •4i-"<* ail lo.-i ;i f.i le . I'u- ftrst ii;ir ('-ol 1 '» ) of t!'<> -;rld locitor
is t i? -j;its.,,, ' - r. i will ilv-iy; ->e 1 7 for -iiti for L:5«- C'lcs.i.TL'aV.e !>.iy
-. -;it« ire:
. - ': } teas -Si >it uf JoTeos l.fit'ile;
;^,> hunir'!'.* .iir-.U of •Is'-rivs loT-:lta--1'»;
(-,-- •'* t-?T; ii'^i!: o* 'c.^ri-f-s .'on •' LU !f>;
(•:c- •/-> unit-; !i;lt of ^--',rt-::s l-it.iti.'f;
(.,--',-. V 'itiits -Ji'-'.ffs if '•' tri'fs Ion ',i tu-if;
(,. "t t' t<>ns -!i-,iL of se -_•)•:•)•; litit'i-ie;
ic"' 'i'.'t f t^ri"? li :tc of ;cr:>'r!;; lu:l '.! L i Jc;
' ,i'ci units lii-.ic of s«'CTi.ls litltjle;
' J?) unir.1; ii'iil of <;i.»c>vi is L">n :I t>i 1e;
' JK>t~ . 'S;;^th it fin station loc it io-i, it knojii, is co le-i in ~ieters in-
.'iCfi --, * -'("'licit; .ieci • \\. :>oiat.. If t'it"? 'i^-.iL'i i^ km^n in reftt, not
the .--.*'£« in feet is co-it-.1 -rii T <1> is colt.-:! in the neM fieM ()3PT!
f'ie )£•,»£- .«Je Mo-iif icit i ^n fio! ! i'i -is PI' Li iiviicitoi f'ir> .inits 'isod to
rf."i->r-l both v"••• "t-Jtto'.i ij >t i nJ t'ic- iaii.-J i'lal si-T>lp .loot'-is. fhus t.Lio -inits
of -icasare r-.r >'*!: He con-;i'it int t'lru^i ;'i'>.it fie ilita for in In-livi-lual
stali vi. :; , . rv l^ ro-j-jirt;t for dt"-.t'is --',ich .irr recoried in neters. Code
.1 1 for iejK . n feet.
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3.6. LYn.rJ)': (Col 34 - 39)
i'tie station latitude is recorded, to the nearest second, in this field.
Left justify tlie field when the full precesion is not knovn.
3.7. Lo:j:;rra)!' (col 40 - 46)
The station longitude is coied in this field. Left justify the field when
the full precision is not known.
3.:s. J.USS[G;;SO ?OSITIOMS since a single card type 2
is permitted.
4. CAK-) ifPii 3
4.1. TI 11 ( Col 3 - 11 )
Tne ti;ne of the collection of the sample is coded in hours (col 6 and 9)
and ninutes (col 10 and 11) bdsed on a 24 hr clock and Kastern Standard TiTie.
4.2. )V£A 0.10'Jl'
Fo-ir datn (;ro.ips nay be coded on on card type 3 if all of the
observations were made at the tine coded on the card. Additional data groups
for th? saiue sar.nlc ti ~in. are coded on .succeeding cards with the tine field
co:ledfor each cari. -"Cach nev sample ti:ne withi i a single sample -lay requires
a new card type 3.
4.2,1. PA'l\ IZru;1-; CO^E (Col 12-1G, 2:5-32, 44-48, 6-1-64)
The oroject e:nr>loys STO-iiiT parameter codes and descriptions to identify
saiipli-i^ activities. Codes not fo'ind in the STOR"T docineritation are locallv
generated. Periodically, STOii^T is supplied ,s.
G! 1 SrO^uT code units .ii-^/l recorded data units uf-at/l
C! 2 ,-5TO'l"T code units •!,',/! recorded Jata units -n",-«t/l
C I 3 JTOH'JT code units uinlios recorded Jat.'i units nhos
C! f> ST-l'MT code units HP, /I recorded data units meql/1
2,y _. ____ - —
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C'i 7 SUX'-CT cole units u Titos recorded data units TTVIOS
C'l 4 STJ.J'T code units T-,/1 recorded dita units 'jncorrectel u".-H/l
GI ') SM-i:-;" code .i-iits n-;/l recorded dnfi units '.ncorrocted -nr»,-ac/l
4.2.3. 3VIPL.-: ')'A'T-l (Col 15-21, i4-37, 5J-5J, f)&-.jJ)
S.iTil<> .icpths (if known) are r'),ie-! in iec<>rs -n; 1 tenths excoot .is -lotcH in
the Joca. ie:itatio:i for the hottoi.i .lupth tiela. Observations «ivea ns surface
are coJeJ as 'J.5 :i. Ml 'tenth entries siioolsl '«» co.ie.' wit'i explicit rltici'ial
no i n 13.
'4.2.4. 0'53.:.'V-\rio:J or u:->i3J.l.M-::.T (Col 22-27,'H-43,34-3^,70-7^)
Tiie observation or nc-isare ncnt for the i>,ira ictor colod in the .H jaccnt
!->ar.i.itL«r field is eaterc;'! witli .in e.licit ;lecirnil r)oint. V;ilue:; .iot rc-i'iirin-;
special treitnent (a code To.iifier) r.-jT^e fro-i V'lljl) to ').')'))')!.
4.3. r,;Kr c>\iO (Col ?•))
Code a <3> if 'tore earn tyr>e 3 recordr; follow the present card or co-!c a
to indicate that the next card is thit of ,i auw station. Cole i ir,
this field on the last card in the data set.
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Appendix C
Fisheries Catch Data Documentation
R. E. Ulanowicz
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Appendix C
Robert E. Ulanowicz
The cumulative catch statistics and the environmental data used in the
multiple regression analysis are stored on tape P10934, file 12, element
DATALL (via the @COPY,G option) at the University of Maryland Computer
Science Center.
All of the data for a single year are stored on five consecutive records
of 76 characters length according to the format [14,12F6.2/4(4X, 12>'6.2/) ] .
The first integer variable identifies the year in which the statistics were
collected. The next 24 values give the Maryland catch in 1000 pounds of the
following oniraerical species:
1. Alewife 9. teakfish 17. Oyster meat
2. Blueflsh 10. American shad 18. Maryland Catch Total
3. Butterfish 11- 5'pot 19. Black drum
4. Croaker 12. Striped bass 20. Catfish & Bullheads
5. Flounder 13. White perch 21. Eel
6. Menhaden 14. .Yellow nerch 22. Gizzard shad
7. Scup 15. Hard crab 23. Soft clam
8. Black seabass lb. Soft crab 24. Northern puffer
The remaining 26 variables characterize the environment during that year.
Variables 25-28 are the average daily salinity, water temperature, air
temperature and precipitation, while variables 29-32 are the cumulative
excesses of the same variables taken in th'2 same order. Cumulative annual
deficits in salinity, water temperature and air temperature occur in
positions 33-35. .'..'hile the extremes (high and low) of salinity, water
temperature and air temperature alternate in positions 36-41. Extreme daily
rainfall occupies slot 42. Episodes of high and low (respectively) salinity,
water temperature, air temperature and precipitation round out the series in
the last eight values, These last 26 variables are described in Chapter D.
Missing data are denoted by a value of -1. The years 1938 through 1976
are presented, so the element consists of 195 records.
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Appendix D
Cli-natic Factors Influencing
Commercial Seafood Landings in Maryland!
Robert E. Ulanowicz
f
Mohammed Liaqnat Ali
Alice Vivian^
Donald R. Heinle4
University of Maryland
Chesapeake Biological Laboratory
Solomons, Maryland 20688
William A, Richkus
J. Kevin Summers
Martin Marietta Corporation
Environmental Center
Baltimore, Mar/land 21227
^-Contribution XXXX, Center for Environmental and Estuarine Studies o^
the University of Maryland.
2Senior Scientific Officer, Fisheries Campus Chandpur, P.O. Baburhat,
')xst Comilla, Bangladesh.
^Sperry-'Jnivac Corporation, Lexington Park, Maryland 20653.
ACfl2M Hill, 1500 114th Avenue S.E., Bellevue, Washington 9800A.
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Abstract
Multivariate correlation of Maryland commercial fish and shellfish
harvests with records of air and water temperatures, salinity, and
precipitation yields provocative results. Greater than 50% of the variation
in catch of all but one of seven commerically important species in Maryland
watfirs could be explained by appropriate annual characterizations of forty
years of daily environmental records. Many of the teras in the regressions
agreed with previous qualitative hypotheses about factors affecting the stock
sizes of these fish and shellfish, but causal links could not be
unequivocally identified. The results should help in the organization of
further research and management concerning these species and may afford
estimates of catches one or more years into the future.
Introduction
Annual population levels of commercially harvested fish and shellfish
usually fluctuate widely over the years. Such variation is often'attributed
to tha strong influence of: important environmental variables, such as
fluctuation of water temperature, upon spawning success (Slssenwine, 1978).
Environmental variables may directly affect the mortality rates of
pre-recruits or indirectly exert influence by altering the abundance of
foraga or predators. Many other aspects of the ecosystem may also alt-^r
population levels (Gushing, 1975), however, exact causative mechanisms in
most fisheries are seldom known.
*
Year to year fluctuations in the abundance of exploited species will
determine in part the magnitude of annual harvest of those speci.es. But, the
relatisnship will not be completely deterministic, since landings will also
be influenced by socio-econoraic factors (e.g., prices and costs as they
affect effort) as well as biological factors unrelated to exploitation
(flicker, 1978). Despite these many complicating factors, significant
correlations between various environmental variables and commercial landings
of various species have been found in a number of fisheries. Dow (1977), for
example, showed that temperature correlates well with the landings of 24
species of finfish, Crustacea, and mollusks off the coast of Maine.
Sutcliffe (1972) found freshwater input to St. Margaret's Bay to be a good
indicator of Tisheries production, possibly because of the stimulation of
production caused by the nutrients in the runoff water. However, in neither
case were the observed relationships demonstrated to help in predicting
harvests, nor were the specific mechanisms responsible for th<: observed
relationships rigorously delineated. In contrast, a regression model of
brown shrimp landings off North Carolina, using temperature and salinity as
independent variables, was found to be a reasonably accurate predictor of
future landings (Hunt, et al., 1979). Hunt's model has proven to be a useful
management tool for this fishery, helping fishermen to'decide; horf to gear up
for the coming season (M. Street, North Carolina Division of Marine
Fisheries, personal communication).
f
Thus, the value of correlative or regression models of fisheries is
two-fold: First, significant correlations can serv-j t.o guice research into
identifying the causes of annual variation in catch; and secondly, if
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validated, such models nay forecast harvest in cases where more detailed
deterministic models cannot be developed for lack of information.
To date the relationships between environmental variables and commercial
landings in the Maryland portion of Chesapeake Bay have not been investigated
in a systematic manner. Since most of the dominant species reproduce in
Maryland waters, the influence of environmental variation on harvest of these
species may be particularly strong. Thus, we have developed multivariate
regressions of the landings of major commercial species, using as predictors
those environmental variables considered to have biological significance for
the species being examined. Although measures of catch per unit effort
(CPUE) would have been preferable as indicators of stock size, adequate
effort data were not available. The results provide valuable insight into
factors which may contribute to determining the population dynamics of these
species and may also prove to be of value in establishing management
practices.
Species Addressed and Data Available
Seven dominant species in Maryland landings were selected fir analysis.
Oysters (Crassostrea virginica), hard crab (Callinactes sapidus), soft shell
clam (Mya arenaria), and striped bass (Morone saxatllis) were chosen because
they are the four species which yield the greatest dollar value to the
Maryland economy. Menhaden (Brevoortia tyranus) and alevife (Alosa
pseudoharengus and A. aestivalis combined) were selected because they have
been dominant in number of pounds harvested. The bluijflsh (Pomatomus
saltatrix) was included because its harvest has increased dramatically in
recent years, and there was interest in deteiarining if this increase might be
related to environmental variation.
A 33-year record of annual catch data for 24 eomnercial species was
available from records maintained by the Chesapeake Biological Laboratory and
the NOAA Fisheries Statistics Division. These records consist of total
Maryland landings (Chesapeake Bay 'and Atlantic Ocean) for each year,. -Tire"'
Chesapeake Bay portion of the harvest heavily dominates the catches of the
chosen species (857, or more of total). Because_of Lhe difficulty in
obtaining sufficient information to separate" Bay catch from the State total,
the total was assumed to be -representative of Chesapeake Bay.
Annual Characterizations of Euvironmental Data
The environmental variables for which long term records exist are water
temperature, air temperature, salinity and precipitation. All four have
potential relevance to the levels of conmercial harvest. Cross correlative
relationships among these variables would be accounted for in the step-w?se
multivariate regression procedure employed in the analysis (discussed belcw).
Daily recordings of these variables exist for a period exceeding 40 years as
taken from the Chesapeake Biological Laboratory pier at the mouth of the
Patuxent estuary in Solonons, Maryland. pec=tuse this location is central to
the Maryland portion of Chesapeake Bay, these' data were assumed to be
characteristic of conditions in the Btxy'as a
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the nearby Patuxent River Naxal A.ir Test Center in Lexington Park, Maryland.
While catch figures represented the total landings for a season,
environmental data existed with much finer temporal resolution. Our goal was
to pair each annual catch figure with a value of an environmental property
which might be representative of the effect that variable had on the stock
during the year the daily readings were accumulated. One straightforward way
of characterizing a year is to calculate the annual average of the variable
in question. The stock, however, may be more sensitive to shorter-term
deviations from this average. In an effort to quantify these deviations we
devised four different ways of treating each of the original four time series
to yield 26 annual series of environmental data.
The first of these methods, calculating the annual average, has already
bean mentioned. But the annual mean conveys little information on the
cumulative amount of stress or benefit experienced by the populations because
of the extreme high or low values of environmental variables. To portray the
cumulative effects of these deviations, we defined variables analogous to the
degree-days of agricultural science. Here the effect of a variable is
assumed to he manifested only when its value goe3 beyond a certain
"bias-level." If, for example, the organism is assumed to be cold stressed
when the water temperature falls below 4 °C, then three successive day.c; of
jl °C water temperature will contribute nine degree-days towards the index of
'cold stress.
For each of the four variables recorded, a high and a low bias level
jwjre chosen such that when conditions exceeded these bounds at Solomons, we
I guessed that there were significant regions throughout the Maryland section
jof the Bay wheie'fish and shellfish were stressed (or benefited) by the large
'excursions from the norm. These bias levels are shown in Table 1.
' Of course, the fishery might be responding to individual episodes of
js tress, rather than the yearly cumulative value. We, therefore, elected to -
'measure the lengths of the longest episodes during a year that a variable was
•beyond the bias values. These episodes were intermediate time-scale
'phenomena (on the order of one to several weeks), and we wished to avoid
contamination from high frequency events. For example, salinity nay have
remained above 16.2 ppt for all of a 28 day period, save on the 15tn day when
it dropped to 16.1 ppt. To characterize the episode as 14 days in duration
would clearly be erroneous. To avoid such contamination we chose a
"gap-interval" for each variable ranging from 3 to 5 days. If the variaole
did not go beyond the bias level for a duration not exceeding the gap
interval, the episode was not terminated, although the days on which the
lapse occurred were not tallied in the episode length. Thus, the episode of
high salinities mentioned abo^e would be counted as 26 days.
Finally, the possibiJ itv remains that the stocks might be acutely-
affected by short-term, intense stresses. ~wt~~telt tfrts eventuality would- be -
reflected in the annual extrerna of each variable. _--- ._--
These four operations, when applied to the four daily ti">e series,
yielded 26 annual time series of "interest. (Cumulative and , extreme low
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precipitations are uniformly zero by definition, and provide no information.)
These series constituted the possible "predictor vectors" from which those
yielding the best multiple regressions would be chosen. The values for the
26 variables calculated for the years 1938-1S76 are listed in Ulanowicz, ot
al. (1980).
Degression Methodology
In nost fish stocks, yearclass size is considered to be established by
the juvenile stago (Gushing, 1975). For example, oyster spat set (analogous
to juvenile stases or finfish) is a good indicator of spawning success
(Galtsoff, 1964). Thusp'fecruXraeat 'vand subsequently harvest) is often
correlated to those conditions in Lh.j past which helped determine the level
of juvenile success. In populations whore all individuals in a yearclass sre
recruited inta the fishery at-the c~3T>~ age, and annual landings coru.ist
primarily of a single yearclctbS, 3 significant correlation might be obtained
when the environmental Variable i.i question was lagged-against landings by
the number of ysarj; ci'*"* vaX^nt--'*:<> tnc age at recruitment.
For raost species harvested'"in Maryland, recruitment is not simultaneous
for all members of --». yeArclass; s:v' landings in one /ear may consist of
members of several -jr ,-any ye irclasses. Thus, environmental characteristics
important to establishing yearc^ss strength may be partially correlated with
landings recorded over several years, and vice versa. In order to account
for such extended oartiai recruitment, step-wise regressions w°re employed,
allowing the contribution \>f a given environmental variable to be assessed by
successively lagging that-'iue;ies which do not spawn in Maryland and where
en/ir',nmeni:al conditions in the Bay would not influence yearclass size (i.e.,
•nenSuJen and bluefis^)/, any significant correlations arising would either be
the 'esult of ho" Bay/ environmental conditions influence the availability of
the species tc Maryi-ind tis'serTe", or how Bay conditions might be correlate'*
with critical conditions at the remote spawning bite. Oysters and striped
bass, being the lorgcr-lived of the species or interest, were regressed
agaiast_-coruiitions,'as long ago as nine years in the past. Conditions
affecting the remaining species were Investigated over the past five years.
:-. —-T^ rcutir3.-uced in the search for key factors was th; stepwise multiple
ro?,'rfssion routine BMDP2R written by the Computer and Health Science
Department, University of California, Los Angei.es, and adapted for execution
OM the Univac 1108 at the Univsrc/ily of Maryland Computer Science Center.
Because we had to choose from a'-iong as many as 260 possible predictor
vectors, it was inpraccical to determine the best multiple regression in one
-pasc through the program. Successive multiple regressions were, therefore,
run for each year of lag. That is, the criterion vector was first run
against the 26 environmental series with no lag; then against the same set
Jagged by one year; by two years, etc. After the appropriate number of lags
had been run, the chosen sets of vectors from each year's lag were aggregated
into one run to determine the final set of predictor vectors and the multiple
regression equation. Each run was terminated '-.'hen the F-to-enter value of
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the next variable to be added to the regression dropped below V.S-j-
corresponding roughly to a p < 0.05 level of significance.
Results and Discussion
To facilitate easy recognition of the environmental variables in the
regression equations that are to follow, we adopt a two-letter, one-digit
code to designate each of the 260 possible predictor vectors.. The first
"tCitter will be either A, C, E or X according to whether the proc ssed .
variable represented an annual average, cumulative deviation, episode or
extremism, respectively. The second letter will designate air temperature,
water temperatrura, daily precipitation, or salinity by I, W, P or S,
respectively. When it is necessary to distinguish between high or low
deviations of these variables, the low values will oe designated by writing
the second letter in the lower case. Finally, the digit will designate cue
number of yeirs lag behind the harvest figures. As examples, Cs3 would
indicate cumulative low salinity three years in trie past, whereas EW2 would
denote the longest episode of high water temperatures two years ago.
Regression equations, F and R- values of those regressions for each of
the seven species are presented in Table 2. Plots of annual Iandin3s of the
species and the predicted values generated by the regression equations are
presented in Figures 1 to 7.
The number of variables entering each regression ranged from 2. in the
case of blue crab and menhaden, to 7 in the case of oyster (Jable 2).
Becatisp of the nsaimer in which these regressions were cimed out ^260
independent variables entered in a step-wise manner.), there exists a strong
possibility that spurious variables night enter the regression. In such
cases, however, the spurious variable is unlikely to contribute to explaining
a large proportion of the total variation. Thus, of the terms in the seven
regression equations in Table 2 we focused our interest first upon those
individual variables which • c-Guxributed a major share of-the raultipie RA,
since these factors would appear to have the greatest likelihood of revealing
a causal ciechanism. The equation derived for soft clam harvests included one
such variable.
In the clam regression, only three environmental variables entered with
coefficients that were significantly different from z.ers, and one (episodes
of low water temperature one year before harvest) accounted for 59% of total
variation in catch. The other two variables entering were extreme high
salinity one year before harvest, which acounted for 15% of the variation,
and extreme low..water temperature- three years before harvest, which accounted
for another 13%. Environmental data were available to assess the predictive
value of this equation for the year 1977. As can be seen in Figure 1, this
projected value has one of the largest deviations from the observed value of
any in the graph.
Interpretation of this equation in terras of causality is complicated by
the absence of effort data. For example, the effects v7hich lihe'rise in
number of licensed clarnaers (froa 3 in 1952 to 100 in 1957 to 200 in 1979
[Richkus et al., 1980]) had on catch cannot j& accounted for, aiid they may
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have been substantial. Still, the strong correlation between extreme low
water temperature lagged one year with catch suggests a causal relationship.
In Maryland,~~sort" sirexl cAains, spawn in spring and fall (Pfinzenmeyer,
1962). However, the spring set each yea'r is alr,o.«j: totally eradicated
because of predatiou by benthic feeding fish and crabs whicri'Taigr.jtf* onto
Maryland claa grounds each spring and Icsvc each fall (Holland et al., 1979).
Factors influencing- the strength of the fall set (which occurs from October
through December) a.id the ensuing survival of juveniles have not been
identified. It appears that these factors are the ones most likely ro have
the greatest effect on the magnitude of corrr.evcial claa landings. Since
Maryland is near the southern boundary of the geographical range of
soft-shell claras (Manning, 1957), cold water temperature? rcay, in some
unexplained way, enhance the survival of a previous year's set. Furthermore,
during some years (i.e., when a dry fall is followed by a cold winter),
extreme high salinity and extreme low water temperature could both occur at
the s.ize tine.
Manning and Dunnington (195b) showed that Maryland cla>is grow at a rapii
rate, achieving legal size (2 inches, 5.1 cm) at an age of 16 to 22 months.
Whence clams spawned in the fall of one year vould enter the ?croercial
fishery during the spring two years later. Er-rtretae low water temperatures
generally occur in January or 'February of each year and during so^c years
coincide with periods of high salinities. Tnus, two of the s.ost significant
variables in the regression node! c.'uld be exerting an effert on juvenile
clams from set to the age of & to 7 months, when they are approximately 0.5
cm (0.2 inches) in size. Low wate) tempera;ure may delay movement of
predators into Maryland waters, permitting "uvenile darns to grow to a less
vulnerable size. High salinities -luring th<: juvenile life stages could also
favor growth and rapid maturation :>!' clams.
The other significant variaDl<; in the regression is difficult to
interpret causally. Extreme temperatures 3 years afrer set would have little
likelihood of~influencing landings in any given year, since soft-shell clams
in Maryland live only about 3 yef.'rs (Manning, 1957). Three year old clams
probably contribute little to toial landings. Also, the regression
coefficient is negative, contradicting the positive correlation with extreme
low temperature one year ago.
The blue crab regression, although it explains only 36% of variation in
landings, suggest. = p-.^sibJe •r-ausal relationship. Both variables entering
the regression (Table 2) have 0 lag and negative coefficients, end Ui«y botn
reflect effects of low water'temperature. Such cold temperatures occur in
January or February each year and can cause mortality of crabs overwintering
in Maryland waters (e.g., Krantz, 1977). The regressions suggest that winter
kill may have a significant effect on Maryland blue crab harvests.
The remaining five regressions are composed of variables which are less
readily explained. The two terms entering the menhaden regression have 4
year lags (Table 2), yet menhaden which raake up Maryland landings are of ages
2 and 3, with almost no l> year old fish taken (J. Merriner, personal
communication). Thus, any causal nechdnisra suggested by the regression would
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have to be a second generation response, except that menhaden do not become
sexually mature until ages 3 or 4. Similarly forty-one of the total
sixty-eight percent of the variation in alf.vif-; catch is explained hy the
negative correlation with episodes of drought three ye^rs in the past.
Both species included in landings as alewives *[ A. pseudoharenqyis and
A. g.es_tivalJH) are anadroinous, tributary spavners. in Maryland (Hildebrand and
•SchTo^'ifr, .1928). Thus, poor spawning success could readily bf> related to
low freshwater runoff caused by low precipitation'."" tioV-Vir..',-' ihe age of first
spawning of these species is from 3 to 5 years, with the majority spawning at
4 or 5 (Davis et alt, 1971). The regression suggests the possibility that
recruitment in Maryland occurs at a younger at;e, but datu on the age
distribution of the catch are u.i. vall-ible to confirm or refute this
suggestion. The other variables 3rjt*-ring the alewife regression (Table 2)
all have lago of 1 or 2 yenro. Since fish lakc.i in a given yenr wo^lci have
been present in the Atlantic Jcean I anil 2 >e.irs before being harvested,
these correlations arc difficult to .nxclaiu in a causal manner.
Juvenile bl'iefish use Chcraoeakii 5,iv *i * :iur^cry area and there exists
the possibility that a distlnc? Cii.'npertke 2;.\ stock of bluefish exists
(Kendall and Ualford, 1979). 31>»-*ii-: , beirv; a r^arine species, -ire geii'.-rally
not found in low salinity water;, a'-.J their distributions can be well defined
by salinity patterns (Lippson et *;., 1930). rhui, the precipitation
variables entering tlu> regr-ssic^ (Tnl -- 2) rviv reflect diminished nursery
habitat caused by iiii;h precipitation, ('e composition of Maryland bluof'sh catch is
; nknownv and the particular lags in the pro:icpit.ition variables in the
regression are not readily explain.id.
The rMv,-u Vdi'Libljs ir. tne oyster rcr.ressio;: explain 22f- of the total
variance. Thirty-on'.- ^orcent of the variance is attributed to the episodes
of low water temperature nina years ago. Ulanowlcz et al. (1%.)) also
reported the strong influence of factors nine year1: past, prr>su~ably because
of some intrinsic environmental cycle. Probably the best qualitative
interpretation of the various terms would be that spat setting success is
abetted by low temperatures and high salinities, whereas the orowth of the
adults is fostfred by periods of warm siianer temperatures.
Eighty-two percent of the variation in catch of striped bass could be
quantified by six variables. The correlations with temperature appear highly
contradictory at first glance, but actually agree with current hypotheses.
The first two terms (52% variance explained) show a favorr.ble correlation
with cold air te;apui'aturcs nver a season. Cold seasons are conducive to
greater amounts of ice formation along river euges. T'v2 sro-.irin* from ice
floes contributes high quality detritus to the riverine system to supplement
the food source for zooplankton, in turn providing the larvae with abundant
food (rieinle et al., 1976). The delivery of this detrital material to the
tidal estuarine nur.oery area is facilitated by higher flow rates (as
reflected in the positive correlation with episodes of low salinity).
Boynton et al. (1976) have previously remarked that year class success
correlates jointly with cold winters and high runoff. The organisms
themselves, however, do not tolerate low water temperatures well (Davis,
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1973) — whence the negative correlation with cold water temperatures, as
evidenced by the last three terms (21% cumulative variance e.xplained) .
Concluding Remarks
The results of the analyses presented here are provocative but should be
viewed with caution. The fact that substantial portions of the variabiity in
landings of all the specJ.es considered can be explained by various
combinations of environmental variables suggest the important role which
eiiv'ir'onTneHCdl ~e«jitil Ltl3ft3--play Aa . d_as
supported by the Environmental Protection Agency's Chesapeake Bay Program,
Eutrophication Project, grant no. Sub R806189010. Dr. "artin WHey provided
comiaents helpful in revising the Manuscript. The Computer Science Center of
the University of Maryland donated some ot the computer time uied in this
project .
Literature Cited
Boynton, W. R., E. M. S^tz]°r, K. V. Wood, H. H. iion, M. linger and
J. A. Mihurskv
1976. Potomac River fisheries prograa ichtnyoplankton and juvenile
investigations. Ref. Ho. 77-169CBL, Cer.ter for Environmental and
Estuarine Studies, Solomons, Md.
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Cashing, 0. H.
1975. Marine Ecology and Fisheries. Cambridge University Press, New
York.
Davis, J., }. V. Iferriner, W. J. Ho.i^man, R, H. St. Pierre and W. L.
Wilh-on
1971. Aiv.'jnl Progress Ho port, Anadroaous Fish Project. Proj. No.
Va. AVC7-1. Virginia Institute of Marina Science, Gloucester
Point, V~.
Davis, M. D.
197?. The ctfect of total dissolved solids, temperature •and pH on
rhe survi'/.il oi iau^ture ;.trlped bass. Prog. Fish-Cult.
33(J):1!>7-16U.
:>nv, R. L. """"•-"-. , .
1J77, Effects of climatic cycl<_.> on.the relative abundance and
a/ailability of con.'ie rci.il marine and estuari'ne cp4. The African oyster, Cras;:osrre,i virt>inica Graelin. Fish.
Bull. f>4: 1-430. ~
Heinle, D. R., D. A. Fierier and J. F. Ustach
397^. Contributions of tidal narshlanJs to Mid-At lintic eR^l!arine
food chains. Pa^as 309-320 j.n M. U. Wiley, ed . , Estuarine
?r'>f-f»sc5cs, Vol. IT, Ac
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Lippson, A. J., M. S. Haire, A. F. Holland, F. Jacobs, J. Jensen,
R. L. Moran-Johnson, f- T. Polgar, and W. A. Richkus.
i 1980. Environmental Atlas of the Potomac Estuary. Johns Hopkins'
University Press, Baltimore, Md. ;
Manning, J. H.
1957. The Maryland soft-shell clam industry. Study Reoort 2.
Maryland Department of Research and Education, Solomons, Md .
Manning, J. H. and E. A. Dunnington. . .
1956. The Maryland Soft Shell Clam Ft-shp.rv: A preliminary
investigation report. Proc. "at. Shellfish A-scc-r:. 46:100-110.
Pfitzenmeyer, H. T.
1962. Period of spawning and setting of the soft- shsiled clam, Mya
arenaria, at Solomons. Chesapeake Sci- 3(2) : 11A-120.
Richkus, W. A., J. K. Summers, T. T. Polgar and A. F. Holland.
If/80. A review and evaluation of fisheries stock management models.
Martin Marietta Laboratories, Baltimore, ,"'d.
Sicker, W. E.
197-2, - .Computation and Interpretation of Biological Statistics of
fish PopuiVL-ia'is...^ Bulletin 191, Department of the Environment
Fisheries and Marine ~S~eivi/ ••=>-.
Sissenwine, M. P. ~" --•._„_
1978. Is MSY an adequate foundation for optimum yield? Fla-
3(6):22-42.
Sutcliffe, W. II. Jr. - - -
1972. Souie relations of land drainage, nutrients, particulate
material, and fish catch in two eastern Canadian bays. J. Fish.
Res. Board Can. 29:357-362.
Ulanowicz. R. E., W. C. Caplins and E. A. Diin-.ir,&i.uu
1980. The forecasting of oyster harvest in Central Chesapeake Bay.
F.stuarine and Coastal Marine Science (in press).
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Table 1. Parameters -fed in calculating
cumulative variables and episodes.
Variable
Salinity
Water Te;aper;iturv
Air Temperature
Precipitation
High Bias
16.2 °/oo
26.5 oc
30 <>c
3 cm/d\y*
Low Bias
10.5
4 OG
0 «C
0 cni/dav
*Tiiis value becomes 0.01 era/day in calculating rain
episodes, i.e., any day it rains is counted.
Table 2. Multlvariate regression models of landings (in metric tons)
of designated species; see text for code to predictor variables.
Species
Soft clam
(Mya arenaria)
Blue crab
(Cal linecte?
sapidus)
Bluefish
(Poraatomus
saltatrix)
Alewif e
aestivalis ana"
Menhaden
(Brevoortia
tyranrus)
Striped Bass
(Morone
saxatilis)
Oyster
(Crassostrea
virginica)
Regression
-4878 + 34.22Swl + 31'JXSl
Multiple
R2
0.86
- 346Xw3
Hc = 15320 - 44.53CwO - 1403XwO 0.36
lo«Hb = 1.927 - 0.0545EP3 0.77
- 0.0393XP9 + 0.0045ZW7
+ 0.0095Kp6
Ha = -4208 - 22.84EP3 + 0.68
114.9Xt2 + 225.1XW2 -t- 8.12Cfl
logl!m = 3.193 - 0.065CT4-- 0.56
+ O.Oi55Ep4
Hb = 3022 - 351.7AT3 + 2.055Ctl 0.82
+ 3.15:Es9 + 240.1AW9
- 232.1Xw2 - 4.50Cw2
H0 = -955.3 + 18.18Ewl
+ 28.42EW1 + 26.11EW2
- 9.45Cw2 + 332.2XS6 - 9.73Es5
0.82
234
F df
44.4 21
8.3
14.7
17.5
17.6
14.3
29
21,1 25
23
23
22
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Fig. 1. 'iaryland soft clan Landings frora 1952 to 1977 (solid line) and
landing oredicted using the regression model (Table 2). Landings for 1977
did not enter into the derivation of the model.
Fig. 2. Observed and forecasted values for hard crab catch, 1945 to 1976
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Fig. 3. Actual and predicted catches of menhaden, 1946 to 1976,
Fig. 4. Annual landings of alewife, 1944 to 1976, as computed with predicted
values.
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10
Fig. 5. Predicted and recorded weights of bluefish landings, 1947 to 1976,
Fig. 6. Comparison of recorded and predicted oyster catch for the years 1947
to 1976.
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1
75
Fig. 7. Predicted and tabulated landings of striped bass from 1944 tn 3976,
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