U.S. ENVIRONMENTAL PROTECTION AGENCY
Annapolis Field Office
Annapolis Science Center
Annapolis, Maryland 21401
TECHNICAL REPORTS
Volume 7
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Table of Contents
Volume 7
55 Water Quality Conditions in the Chesapeake Bay
System
56 Nutrient Enrichment and Control Requirements
in the Upper Chesapeake Bay
57 The Potomac River Estuary in the Washington
Metropolitan Area - A History of Its Water
Quality Problems and Their Solution
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PUBLICATIONS
U.S. ENVIRONMENTAL PROTECTION AGENCY
REGION III
ANNAPOLIS FIELD OFFICE*
VOLUME 1
Technical Reports
5 A Technical Assessment of Current Water Quality
Conditions and Factors Affecting Water Quality in
the Upper Potomac Estuary
6 Sanitary Bacteriology of the Upper Potomac Estuary
7 The Potomac Estuary Mathematical Model
9 Nutrients in the Potomac River Basin
11 Optimal Release Sequences for Water Quality Control
in Multiple Reservoir Systems
VOLUME 2
Technical Reports
13 Mine Drainage in the North Branch Potomac River Basin
15 Nutrients in the Upper Potomac River Basin
17 Upper Potomac River Basin Water Quality Assessment
VOLUME 3
Technical Reports
19 Potomac-Piscataway Dye Release and Wastewater
Assimilation Studies
21 LNEPLT
23 XYPLOT
25 PLOT3D
* Formerly CB-SRBP, U.S. Department of Health, Education,
and Welfare; CFS-FWPCA, and CTSL-FWQA, Middle Atlantic
Region, U.S. Department of the Interior
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VOLUME 3 (continued)
Technical Reports
27 Water Quality and Wastewater Loadings - Upper Potomac
Estuary during 1969
VOLUME 4
Technical Reports
29 Step Backward Regression
31 Relative Contributions of Nutrients to the Potomac
River Basin from Various Sources
33 Mathematical Model Studies of Water Quality in the
Potomac Estuary
35 Water Resource - Water Supply Study of the Potomac
Estuary
VOLUME 5
Technical Reports
37 Nutrient Transport and Dissolved Oxygen Budget
Studies in the Potomac Estuary
39 Preliminary Analyses of the Wastewater and Assimilation
Capacities of the Anacostia Tidal River System
41 Current Water Quality Conditions and Investigations
in the Upper Potomac River Tidal System
43 Physical Data of the Potomac River Tidal System
Including Mathematical Model Segmentation
45 Nutrient Management in the Potomac Estuary
VOLUME 6
Technical Reports
47 Chesapeake Bay Nutrient Input Study
49 Heavy Metals Analyses of Bottom Sediment in the
Potomac River Estuary
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VOLUME 6 (continued)
Technical Reports
51 A System of Mathematical Models for Water Quality
Management
52 Numerical Method for Groundwater Hydraulics
53 Upper Potomac Estuary Eutrophication Control
Requirements
54 AUT0-QUAL Modelling System
Supplement AUT0-QUAL Modelling System: Modification for
to 54 Non-Point Source Loadings
VOLUME 7
Technical Reports
55 Water Quality Conditions in the Chesapeake Bay System
56 Nutrient Enrichment and Control Requirements in the
Upper Chesapeake Bay
57 The Potomac River Estuary in the Washington
Metropolitan Area - A History of its Water Quality
Problems and their Solution
VOLUME 8
Technical Reports
58 Application of AUT0-QUAL Modelling System to the
Patuxent River Basin
59 Distribution of Metals in Baltimore Harbor Sediments
60 Summary and Conclusions - Nutrient Transport and
Accountability in the Lower Susquehanna River Basin
VOLUME 9
Data Reports
Water Quality Survey, James River and Selected
Tributaries - October 1969
Water Quality Survey in the North Branch Potomac River
betv/een Cumberland and Luke, Maryland - August 1967
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VOLUME 9 (continued)
Data Reports
Investigation of Water Quality in Chesapeake Bay and
Tributaries at Aberdeen Proving Ground, Department
of the Army, Aberdeen, Maryland - October-December 1967
Biological Survey of the Upper Potomac River and
Selected Tributaries - 1966-1968
Water Quality Survey of the Eastern Shore Chesapeake
Bay, Wicomico River, Pocomoke River, Nanticoke River,
Marshall Creek, Bunting Branch, and Chincoteague Bay -
Summer 1967
Head of Bay Study - Water Quality Survey of Northeast
River, Elk River, C & D Canal, Bohemia River, Sassafras
River and Upper Chesapeake Bay - Summer 1968 - Head ot
Bay Tributaries
Water Quality Survey of the Potomac Estuary - 1967
Water Quality Survey of the Potomac Estuary - 1968
Wastewater Treatment Plant Nutrient Survey - 1966-1967
Cooperative Bacteriological Study - Upper Chesapeake Bay
Dredging Spoil Disposal - Cruise Report No. 11
VOLUME 10
Data Reports
9 Water Quality Survey of the Potomac Estuary - 1965-1966
10 Water Quality Survey of the Annapolis Metro Area - 1967
11 Nutrient Data on Sediment Samples of the Potomac Estuary
1966-1968
12 1969 Head of the Bay Tributaries
13 Water Quality Survey of the Chesapeake Bay in the
Vicinity of Sandy Point - 1968
14 Water Quality Survey of the Chesapeake Bay in the
Vicinity of Sandy Point - 1969
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VOLUME 10(continued)
Data Reports
15 Water Quality Survey of the Patuxent River - 1967
16 Water Quality Survey of the Patuxent River - 1968
17 Water Quality Survey of the Patuxent River - 1969
18 Water Quality of the Potomac Estuary Transects,
Intensive and Southeast Water Laboratory Cooperative
Study - 1969
19 Water Quality Survey of the Potomac Estuary Phosphate
Tracer Study - 1969
VOLUME 11
Data Reports
20 Water Quality of the Potomac Estuary Transport Study
1969-1970
21 Water Quality Survey of the Piscataway Creek Watershed
1968-1970
22 Water Quality Survey of the Chesapeake Bay in the
Vicinity of Sandy Point - 1970
23 Water Quality Survey of the Head of the Chesapeake Bay
Maryland Tributaries - 1970-1971
24 Water Quality Survey of the Upper Chesapeake Bay
1969-1971
25 Water Quality of the Potornac Estuary Consolidated
Survey - 1970
26 Water Quality of the Potomac Estuary Dissolved Oxygen
Budget Studies - 1970
27 Potomac Estuary Wastewater Treatment Plants Survey
1970
28 Water Quality Survey of the Potomac Estuary Embayments
and Transects - 1970
29 Water Quality of the Upper Potomac Estuary Enforcement
Survey - 1970
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30
31
32
33
34
Appendix
to 1
Appendix
to 2
3
4
VOLUME 11 (continued)
Data Reports
Water Quality of the Potomac Estuary - Gilbert Swamp
and Allen's Fresh and Gunston Cove - 1970
Survey Results of the Chesapeake Bay Input Study -
1969-1970
Upper Chesapeake Bay Water Quality Studies - Bush River,
Spesutie Narrows and Swan Creek, C & D Canal, Chester
River, Severn River, Gunpowder, Middle and Bird Rivers -
1968-1971
Special Water Quality Surveys of the Potomac River Basin
Anacostia Estuary, Wicomico .River, St. Clement and
Breton Bays, Occoquan Bay - 1970-1971
Water Quality Survey of the Patuxent River - 1970
VOLUME 12
Working Documents
Biological Survey of the Susquehanna River and its
Tributaries between Danville, Pennsylvania and
Conowingo, Maryland
Tabulation of Bottom Organisms Observed at Sampling
Stations during the Biological Survey between Danville,
Pennsylvania and Conowingo, Maryland - November 1966
Biological Survey of the Susquehanna River and its
Tributaries between Cooperstown, New York and
Northumberland, Pennsylvnaia - January 1967
Tabulation of Bottom Organisms Observed at Sampling
Stations during the Biological Survey between Cooperstown,
New York and Northumberland, Pennsylvania - November 1966
VOLUME 13
Working Documents
Water Quality and Pollution Control Study, Mine Drainage
Chesapeake Bay-Delaware River Basins - July 1967
Biological Survey of Rock Creek (from Rockville, Maryland
to the Potomac River) October 1966
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VOLUME 13 (continued)
Working Documents
5 Summary of Water Quality and Waste Outfalls, Rock Creek
in Montgomery County, Maryland and the District of
Columbia - December 1966
6 Water Pollution Survey - Back River 1965 - February 1967
7 Efficiency Study of the District of Columbia Water
Pollution Control Plant - February 1967
VOLUME 14
Working Documents
8 Water Quality and Pollution Control Study - Susquehanna
River Basin from Northumberland to West Pittson
(Including the Lackawanna River Basin) March 1967
9 Water Quality and Pollution Control Study, Juniata
River Basin - March 1967
10 Water Quality and Pollution Control Study, Rappahannock
River Basin - March 1967
11 Water Quality and Pollution Control Study, Susquehanna
River Basin from Lake Otsego, New York, to Lake Lackawanna
River Confluence, Pennsylvania - April 1967
VOLUME 15
Working Documents
12 Water Quality and Pollution Control Study, York River
Basin - April 1967
13 Water Quality and Pollution Control Study, West Branch,
Susquehanna River Basin - April 1967
14 Water Quality and Pollution Control Study, James River
Basin - June 1967 ,
15 Water Quality and Pollution Control Study, Patuxent River
Basin - May 1967
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VOLUME 16
Working Documents
16 Hater Quality and Pollution Control Study, Susquehanna
River Basin from Northumberland, Pennsylvania, to
Havre de Grace, Maryland - July 1957
17 Water Quality and Pollution Control Study, Potomac
River Basin - June 1967
18 Immediate Water Pollution Control Needs, Central Western
Shore of Chesapeake Bay Area (Magothy, Severn, South, and
West River Drainage Areas) July 1967
19 Immediate Water Pollution Control Needs, Northwest
Chesapeake Bay Area (Patapsco to Susquehanna Drainage
Basins in Maryland) August 1967
20 Immediate Water Pollution Control Needs - The Eastern
Shore of Delaware, Maryland and Virginia - September 1967
VOLUME 17
Working Documents
21 Biological Surveys of the Upper James River Basin
Covington, Clifton Forge, Big Island, Lynchburg, and
Piney River Areas - January 1968
22 Biological Survey of Antietam Creek and some of its
Tributaries from Waynesboro, Pennsylvania to Antietam,
Maryland - Potomac River Basin - February 1968
23 Biological Survey of the Monocacy River and Tributaries
from Gettysburg, Pennsylvania, to Maryland Rt. 28 Bridge
Potomac River Basin - January 1968
24 Water Quality Survey of Chesapeake Bay in the Vicinity of
Annapolis, Maryland - Summer 1967
25 Mine Drainage Pollution of the North Branch of Potomac
River - Interim Report - August 1968
26 Water Quality Survey in the Shenandoah River of the
Potomac River Basin - June 1967
27 Water Quality Survey in the James and Maury Rivers
Glasgow, Virginia - September 1967
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VOLUME 17 (continued)
Working Documents
28 Selected Biological Surveys in the James River Basin,
Gillie Creek in the Richmond Area, Appomattox River
in the Petersburg Area, Bailey Creek from Fort Lee
to Hopewell - April 1968
VOLUME 18
Working Documents
29 Biological Survey of the Upper and Middle Patuxent
River and some of its Tributaries - from Maryland
Route 97 Bridge near Roxbury Mills to the Maryland
Route 4 Bridge near Wayson's Corner, Maryland -
Chesapeake Drainage Basin - June 1968
30 Rock Creek Watershed - A Water Quality Study Report
March 1969
31 The Patuxent River - Water Quality Management -
Technical Evaluation - September 1969
VOLUME 19
Working Documents
Tabulation, Community and Source Facility Water Data
Maryland Portion, Chesapeake Drainage Area - October 1964
Waste Disposal Practices at Federal Installations
Patuxent River Basin - October 1964
Waste Disposal Practices at Federal Installations
Potomac River Basin below Washington, D.C.- November 1964
Waste Disposal Practices at Federal Installations
Chesapeake Bay Area of Maryland Excluding Potomac
and Patuxent River Basins - January 1965
The Potomac Estuary - Statistics and Projections -
February 1968
Patuxent River - Cross Sections and Mass Travel
Velocities - July 1968
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VOLUME 19 (continued)
Working Documents
Wastewater Inventory - Potomac River Basin -
December 1968
Wastewater Inventory - Upper Potomac River Basin -
October 1968
VOLUME 20
Technical Papers -
1 A Digital Technique for Calculating and Plotting
Dissolved Oxygen Deficits
2 A River-Mile Indexing System for Computer Application
in Storing and Retrieving Data (unavailable)
3 Oxygen Relationships in Streams, Methodology to be
Applied when Determining the Capacity of a Stream to
Assimilate Organic Wastes - October 1964
4 Estimating Diffusion Characteristics of Tidal Waters -
May 1965
5 Use of Rhodamine B Dye as a Tracer in Streams of the
Susquehanna River Basin - April 1965
6 An In-Situ Benthic Respirometer - December 1965
7 A Study of Tidal Dispersion in the Potomac River
February 1966
8 A Mathematical Model for the Potomac River - what it
has done and what it can do - December 1966
9 A Discussion and Tabulation of Diffusion Coefficients
for Tidal Waters Computed as a Function of Velocity
February 1967
10 Evaluation of Coliform Contribution by Pleasure Boats
July 1966
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VOLUME 21
Technical Papers
11 A Steady State Segmented Estuary Model
12 Simulation of Chloride Concentrations in the
Potomac Estuary - March 1968
13 Optimal Release Sequences for Water Quality
Control in Multiple-Reservoir Systems - 1968
VOLUME 22
Technical Papers
Summary Report - Pollution of Back River - January 1964
Summary of Water Quality - Potomac River Basin in
Maryland - October 1965
The Role of Mathematical Models in the Potomac River
Basin Water Quality Management Program - December 1967
Use of Mathematical Models as Aids to Decision Making
in Water Quality Control - February 1968
Piscataway Creek Watershed - A Water Quality Study
Report - August 1968
VOLUME .23
Ocean Dumping Surveys
Environmental Survey of an Interim Ocean Dumpsite,
Middle Atlantic Bight - September 1973
Environmental Survey of Two Interim Dumpsites,
Middle Atlantic Bight - January 1974
Environmental Survey of Two Interim Dumpsites
Middle Atlantic Bight - Supplemental Report -
October 1974
Effects of Ocean Disposal Activities on Mid-
continental Shelf Environment off Delaware
and Maryland - January 1975
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VOLUME 24
1976 Annual
Current Nutrient Assessment - Upper Potomac Estuary
Current Assessment Paper No. 1
Evaluation of Western Branch Wastewater Treatment
Plant Expansion - Phases I and II
Situaticn Report - Potomac River
Sediment Studies in Back River Estuary, Baltimore,
Maryland
Technical Distribution of Metals in Elizabeth River Sediments
Report 61
Technical A Water Quality Modelling Study of the Delaware
Report 62 Estuary
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Annapolis Field Office
Region III
Environmental Protection Agency
WATER QUALITY CONDITIONS
IN THE
CHESAPEAKE BAY SYSTEM
Technical Report 55
August 1972
Thomas H. Pheiffer*
Daniel K. Donnelly
Dorothy A. Possehl
* Currently represents the Environmental Studies Section,
Environmental Planning Branch, Air and Water Division,
Region III, EPA in the Chesapeake Bay Study.
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PREFACE
The Annapolis Field Office, Region III, Environmental Protection
Agency, makes data and other technical information available to all
interested individuals. The data reported for the States of Maryland
and Virginia and the District of Columbia were obtained through a
cooperative effort with the Baltimore District, U. S. Army Corps of
Engineers. The information contained in Technical Report No. 55 will
also be published in the Corps of Engineers' report to the Congress
covering the existing conditions of the Chesapeake Bay with regard to
navigation, fisheries, flood control, control of noxious weeds, water
pollution, water quality control, beach erosion, and recreation.
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TABLE OF CONTENTS
LIST OF TABLES
LIST OF FIGURES
Chapter
I INTRODUCTION I - 1
II SUMMARY OF FINDINGS II- 1
III WATER QUALITY STANDARDS Ill - 1
A. Maryland Water Quality Criteria Ill- 1
B. Virginia Water Quality Criteria Ill - 4
C. District of Columbia Water Quality Criteria Ill - 7
D. Assigned Water Uses Ill - 11
IV CHESAPEAKE BAY STUDIES IV- 1
A. Lower Susquehanna River Area IV - 1
B. Upper Bay and Upper Eastern Shore Area
(Northeast, Elk, Bohemia, and Sassafras Rivers) IV - 6
C. Upper Western Shore Area
(Bush, Gunpowder, and Middle Rivers) IV - 13
D. Baltimore Harbor Area IV - 18
E. Middle Western Shore Area
(Magothy, Severn, South, and West Rivers) IV - 36
F. Middle Chesapeake Bay
In the Vicinity of Sandy Point IV - 47
G. Middle Eastern Shore Area IV - 56
1. Chester River IV - 56
2. Eastern Bay.. IV - 63
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TABLE OF CONTENTS (Continued)
Chapter Page
3. Choptank River IV- 71
4. Little Choptank River IV- 90
5. Nanticoke River IV- 92
6. Wicomico River - Monie Bay IV - 100
7. Manokin River IV - 108
8. Annemessex Rivers IV - 110
H. Lower Eastern Shore Area IV - 116
I. Patuxent Ri ver Area IV - 128
J. Potomac Ri ver Study Area IV - 142
K. Rappahannock River Area IV - 187
L. York River Area IV - 199
M. James River Area IV - 208
1. James River IV - 208
2. Elizabeth River IV - 249
N. Lower Chesapeake Bay IV - 268
V DATA EVALUATION AND INVENTORIES V - 1
A. Data Evaluation V - 1
B. Data Inventories V - 6
ACKNOWLEDGEMENTS
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List of Tables
Number Title Page
IV- 1 Nutrient Input to Bay from the Susquehanna River IV - 2
IV- 2 Upper Bay and Upper Eastern Shore Sampling Station IV - 8
Locations
IV- 3 Baltimore Harbor Nutrient Data IV - 30
IV- 4 South River Sampling Station Locations - MDWR iy _ 37
IV- 5 Severn River Sampling Station Locations - MDWR iy _ 39
IV- 6 South River Nutrient Concentrations iv _ 44
IV- 7 Sandy Point (Middle Bay) Sampling Station iy - 53
Locations - AFO
IV- 8 Sandy Point Nutrient and Chlorophyll a^ IV - 54
Concentrations - April 1971
IV- 9 Sandy Point Nutrient and Chlorophyll a_ IV - 55
Concentrations - June 1971
IV-10 Chester River Sampling Station Locations - MDWR iy _ 5-]
IV-11 Chester River Sampling Station Locations - AFO jy _ 52
IV-12 Coliform Densities in Oak Creek and St. Michael's iy _ 55
Harbor
IV-13 Shellfish Closures - Eastern Bay Area iv - 65
IV-14 Miles River - Oak Creek Sampling Station iv _ 59
Locations - MDWR
IV-15 Shellfish Closures in Choptank River Basin iy _ 74
IV-16 Total Coliform Densities in Choptank River jy _ 75
Shellfish Harvesting Waters
IV-17 Dissolved Oxygen Values in the Choptank River jy _ 73
IV-18 Nutrient-Chlorophyll Relationships in the i\j _ 31
Choptank River
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List of Tables
Number Ti tle Page
IV-19 Choptank River Metal Concentrations IV - 84
August 2, 1971
IV-20 Choptank River Metal Concentrations IV - 85
August 17, 1971
IV-21 Choptank River Sampling Station Locations - AFO IV - 86
IV-22 Choptank River Sampling Station Locations - NMFS, IV - 87
NOAA
IV-23 Choptank River Sampling Station Locations - MDWR IV - 88
IV-24 Nanticoke River Sampling Station Locations - AFO IV - 98
IV-25 Nanticoke River Sampling Station Locations - MDWR IV - 99
IV-26 Wicomico River Sampling Station Locations - AFO IV - 105
IV-27 Wicomico River Basin Sampling Station Locations - IV - 106
MDWR
IV-28 Crisfield Harbor-Little Annemessex River Sampling IV - 113
Station Locations - MDWR
IV-29 Pocomoke River Watershed Sampling Station IV - 122
Locations - MDWR
IV-30 Pocomoke River Sampling Station Locations - AFO IV - 127
IV-31 Patuxent River Bacteriological Data IV - 130
IV-32 Patuxent River Dissolved Oxygen Concentrations - IV - 133
1968-1971
IV-33 Patuxent River Dissolved Oxygen Concentrations - 1970 IV - 134
IV-34 Patuxent River Nutrient Concentrations IV - 135
IV-35 Patuxent River Nitrate-Nitrogen Concentrations IV - 136
IV-36 Patuxent River Total Phosphorus Concentrations IV - 137
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List of Tables
Number Title Page
IV-37 Dissolved Oxygen Concentrations in the-Middle IV - ^50
and Lower Potomac Estuary
IV-38 Wastewater Loadings to the Upper Potomac Estuary IV - 153
and Tributaries - Great Falls to Indian Head - 1970
IV-39 Wastewater Loading Trends - Washington Metropolitan IV - ^54
Area
IV-40 Ranges of pH, Alkalinity, and Free Dissolved C0? IV - 163
in the Upper and Middle Potomac Estuary
IV-41 Pesticides Analyzed and Minimum Detectable Limits IV - 176
Potomac Estuary
IV-42 Rappahannock River Nutrient Data - 1970-1971 IV - 195
IV-43 York River Dissolved Oxygen Concentrations - 1971 IV - 201
IV-44 Pamunkey and Mattaponi River Nutrient Data - IV - 203
1969-1970 - AFO
IV-45 Mattaponi, Pamunkey, and York River Nutrient Data - IV - 204
1970-1971 - VWCB
IV-46 Mattaponi, Pamunkey, and York River Heavy Metal IV - 205
Concentrations - 1970
IV-47 James River DO and Temperature Values - 1971 IV - 216
IV-48 James River Organic Loading Sources IV - 225
IV-49 James River and Chickahominy River Average Nutrient IV - 239
Concentrations - 1969-1970
IV-50 James River Nutrient Concentraions - May 1971 IV - 240
IV-51 Elizabeth River Total Coliform and Fecal Coliform IV - 252
Levels
IV-52 Total Coliform and Fecal Coliform Levels, Eastern IV - 254
Branch and Southern Branch, Elizabeth River
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List of Tables
Number Title Page
IV-53 Hampton Roads Sanitation District Treatment Plants iv - 258
IV-54 Elizabeth River Survey - AFO - November 1971 iv - 260
IV-55 Elizabeth River Nutrient Data - VWCB - 1968-1971 iv - 263
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List of Figures
Number Title Page
IV- 1 Upper Chesapeake Bay Station Locations iv - 7
IV- 2 Baltimore Harbor Control Stations iv - 34
IV- 3 Baltimore Harbor Industrial Discharge Survey iv - 35
IV- 4 South River Station Locations iv - 38
IV- 5 Severn River Station Locations iv - 40
IV- 6 Crisfield Harbor - Little Annemessex River iv - 115
Survey Station Locations
IV- 7 Patuxent River Basin IV _ 141
IV- 8 Potomac Estuary Sampling Stations iv - 143
IV- 9 Total Coliform Organisms, Upper Potomac iv - 147
Estuary
IV-10 Fecal Coliform Densities, Roosevelt Island iv - 148
IV-11 Dissolved Oxygen Concentrations, Potomac iv - 155
Estuary, Sept. 10-15, 1965; Sept. 7-13, 1966;
Sept. 20-21, 1967
IV-12 Dissolved Oxygen Concentrations, Potomac iv - 156
Estuary, Aug. 19-22, 1968; Oct. 16, 1969;
Sept. 28-30, 1970
IV-13 Inorganic Phosphate Concentration as PO,, IV ~ 159
Potomac Estuary, 1969-1970
IV-14 Nitrate and Nitrite Nitrogen as N, Potomac iv - 160
Estuary, 1969-1970
IV-15 Ammonia Nitrogen as N, Potomac Estuary, 1969-1970 iv - 161
IV-16 Calcium and Barium Concentrations, Potomac Estuary-iv - 166
August and December 1970
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List of Figures
Number Title Page
IV-17 Copper and Silver Concentrations, Potomac Estuary, IV - 167
August and December 1970, April 1971
IV-18 Iron and Lead Concentrations, Potomac Estuary, IV - 168
August and December 1970, April 1971
IV-19 Strontium and Lithium Concentrations, Potomac IV - 169
Estuary, August and December 1970
IV-20 Cobalt and Magnesium Concentrations, Potomac IV - 170
Estuary, August and December 1970
IV-21 Manganese and Aluminum Concentrations, Potomac IV - 171
Estuary, August and December 1970
IV-22 Potassium and Zinc Concentrations, Potomac IV - 172
Estuary, August and December 1970, April 1971
IV-23 Vanadium and Cadmium Concentrations, Potomac IV - 173
Estuary, August and December 1970, April 1971
IV-24 Chromium and Nickel Concentrations, Potomac IV - 174
Estuary, August and December 1970, April 1971
IV-25 Wastewater Nutrient Enrichment Trends and IV - 180
Ecological Effects, Upper Potomac Tidal River
System
IV-26 Chlorophyll a_, Potomac Estuary, Upper Reach, IV - 182
1965-1966, 1969-1970
IV-27 Chlorophyll a_, Potomac Estuary, Middle and Lower IV - 183
Reach, 1965-1966, 1969-1970
IV-28 Dissolved Oxygen Profile, Rappahannock River, IV - 191
June 4, 1970
IV-29 Dissolved Oxygen Profile, Rappahannock River, IV - 192
June 8, 1970
IV-30 Dissolved Oxygen Profile, Rappahannock River, IV - 193
July 29, 1970
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List of Figures
Number Title £acj£
IV-31 James River Study Sampling Locations, iv - 211
October 14-30, 1969
IV-32 James River Fecal Coliform Densities, iv - 212
October 14-30, 1969
IV-33 Tidal James River, VWCB Sampling Stations iv - 213
IV-34 James River DO Profile, Low Water Slack, iv - 221
June 11, 1971
IV-35 James River DO Profile, Low Water Slack. iv - 222
August 10, 1971
IV-36 James River DO Profile, Low Water Slack, iv - 223
September 8, 1971
IV-37 James River DO Profile, High Water Slack, iv - 229
September 1, 1971
IV-38 James River DO Profile, High Water Slack, IV - 230
October 15, 1971
IV-39 James River DO Profile, High Water Slack, iv - 231
October 28, 1971
IV-40 James River BOD Profile, River Bottom iv - 232
IV-41 James River BOD Profile, Surface IV - 233
IV-42 James River TKN Concentrations, Bottom iv - 237
Sediment
IV-43 James River Total Phosphorus Concentrations, iv - 238
Bottom Sediment
IV-44 James River Lead Concentrations, Bottom iv - 246
Sediment
IV-45 James River Mercury Concentrations, Bottom iv - 247
Sediment
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List of Figures
Number Title Page
IV-46 James River Zinc Concentrations, Bottom Sediment IV - 248
IV-47 Total Phosphorus and TKN, Elizabeth River, IV - 265
Bottom Sediment
IV-48 Lead, Mercury, Zinc, and Copper Concentrations IV - 267
in Elizabeth River, Bottom Sediment
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1-1
CHAPTER I
INTRODUCTION
This report delineates existing water quality conditions in
the Chesapeake Bay and its tidal tributaries and evaluates current
water quality data and mo.n'toring programs in the context of a Bay
management program. Data sources for this report were the Annapolis
Field Office, National Marine Fisheries Service, U. S. Geological
Survey, Maryland Department of Water Resources, Maryland Department
of Health, Maryland Environmental Service, University of Maryland,
The Johns Hopkins University, Virginia Water Control Board, Virginia
Institute of Marine Science, and the District of Columbia Department
of Environmental Services.
The Bay is discussed in terms of study areas based on hydro-
logical significance or geographical expediency, The study areas
are as follows: Lower Susquehanna River, Upper Bay and Upper Eastern
Shore, Upper Western Shore, Baltimore Harbor, Middle Western Shore,
Middle Chesapeake Bay, Middle Eastern Shore, Lower Eastern Shore,
Patuxent River, Potomac River, Rappahannock River, York River, James
River, and Lower Chesapeake Bay Waters.
Chapter III sets forth the beneficial water uses for the study
areas together with the water quality standards established for the
support of these uses. Chapter IV contains a brief description of
the study area followed by the identification of the data sources
and the extent of current data available. The available water quality
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1-2
information is assessed for each study area, to the extent possible,
with specific reference to the following parameters: bacterial
densities, dissolved oxygen, nutrients, heavy metals, and pesticides.
Where sufficient data exists, as in the case of the Potomac Estuary,
water quality trends are identified and their significance discussed.
A discussion of inventories of industrial and municipal waste-
water discharges is included in Chapter V as well as an evaluation
of the available data base for the Bay. All of the existing data on
each study area are not presented but will be generally available from
the Environmental Protection Agency or the appropriate collection
agency.
Chapter II presents a summary of the findings based on the
information contained in Chapter IV, the body of the report. It
is recognized that the report will be critized for not addressing
the adopted water qualtiy standards only for the numbered parameters
of dissolved oxygen, bacteria, pH, and temperature. The authors
feel that the insidious parameters—nutrients, heavy metals, pesticides,
and toxic chemicals--must be placed in proper perspective before
such parameters manifest their presence in serious violations of
existing water quality standards.
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II - 1
CHAPTER II
SUMMARY OF FINDINGS
1. Based on nutrient input studies of the major tributary water-
sheds of the Chesapeake Bay, the Annapolis Field Office finds
the Susquehanna River to be the largest contributor of nutrients
to the Bay. This is due to the fact that the Susquehanna River
is the largest source of freshwater to the Bay, providing
approximately 50 percent of its freshwater inflow. Its nutrient
input to the Bay exceeds the combined input of the Potomac
River and the James River, the second and third largest contri-
butors of nutrients to the Bay, for all the various nutrient
fractions measured.
2. Blooms of blue-green algae were first reported in upper
Chesapeake Bay tributaries in late August 1968. The blooms
occurred in the Sassafras River near Georgetown, Maryland, and the
Elk River downstream from Elkton, Maryland. Since 1968,
these blooms have gradually increased in si/e, density, and duration,
In 1971, blooms became evident early in the summer. In June,
the upper Sassafras River showed chlorophyll ^values of 121.5
yg/1; the Northeast River, values of 224.0 yg/1. In July, the
Bohemia River had chlorophyll a^ values of 110.0 yg/1. The major
problem areas appear at the headwaters of each of the upper
Bay tributaries.
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3. Prior to 1966, 21 public bathing beaches in Baltimore County,
located on the shores of Middle, Gunpowder, Back, and Bird
Rivers, Chesapeake Bay, and Bear Creek, were open. The number of
bathing beaches approved for operation by the Baltimore County
Health Department has steadily declined since then, mainly due to
bacterial pollution problems. Only six permits were issued to
operate public bathing beaches for the 1971 summer season.
4. Major souces of pollution in Baltimore Harbor include
wastes from the Baltimore City Patapsco Wastewater Treatment
Plant, which discharges primary treated effluent directly into
the Harbor, direct industrial discharges, sewage overflows
and leaks into Harbor tributaries, urban runoff, and the occurrence
of spills of hazardous substances from vessels and dockside
facilities.
5. A December 1971 field investigation by the Annapolis Field
Office of industrial discharges into Baltimore Harbor identified
significant discharges of ethion, cyanide, phenol, nutrients,
and various heavy metals into the Harbor.
6. A comparison of bottom sediment data from Baltimore Harbor
with recent sediment data obtained in the vicinity of Tangier
Island showed excessive amounts of volatile solids, chemical
oxygen demand, and oil and greases in the bottom sediment
from the Harbor. Tangier Island, located in the lower Chesa-
peake Bay off Pocomoke Sound, is considered a clean area with
regard to pollutants in the bottom sediment surrounding the
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island.
7. The dissolved oxygen standard of 5.0 mg/1 is generally
being maintained at the surface in the middle Western Shore
tributaries (the Magothy, Severn, South, Rhode, and West Rivers).
However, the DO level is occasionally depressed, below a depth
of 5 feet, during late summer in the upper Severn and South Rivers.
Fecal coliform concentrations are generally satisfactory in the Mag-
othy and South River?, although 127 acres in the South River are
closed to shellfish harvesting to safeguard against possible failure
of a wastewater treatment plant in the upper portion of the river.
Excessive fecal coliform densities in the Severn, Rhode, and West
Rivers are attributed to wastewater treatment plants and defective
septic systems discharging into these rivers. As a result, 1481 acres
in the Severn River and 63 acres in the Rhode and West River system
are now closed to shellfish harvesting. High nutrient concen-
trations have been recorded during the summer months of 1971
in the Severn and South Rivers, contributing to the algal "blooms"
which have occurred in these areas as recently as December 1971.
Occasional algal "blooms", with corresponding high total PO. values,
have also been observed in the Magothy, Rhode, and West Rivers.
8. While dissolved oxygen and coliform concentrations in the
Sandy Point area of Chesapeake Bay are generally quite satis-
factory, nutrient concentrations have shown a trend to increase
in the last three years. The concentration of total phosphate
has nearly doubled since 1968, contributing to the alarming
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rise in the chlorophyll .a density during this time. A fourfold
increase in the chlorophyll ^density (from an average density
of 36 pg/1 in June 1968 to 153 yg/1 in June 1971) indicates a
serious threat to water quality conditions in this area. High
nitrate-nitrogen concentrations noted in late winter and early
spring, as compared to summer values, are attributed to increased
loadings from the Susquehanna River durinc, the winter and spring
periods of high flow rates. In addition, operation of the Sandy
Point wastewater treatment plant, with a planned ultimate capa-
city of 19.0 MGD, will tend to further increase the concentrations
of nutrients in the Bay, possibly leading to hypereutrophic con-
ditions in this area.
9. Very little has been done in the way of intensive bacterio-
logical studies in the Chester River Basin, with the exception of
the Radcliffe Creek area, where excessive coliform densities were
found by Maryland Department of Water Resources surveys. Shell-
fish bed closings in the remainder of the basin are not widespread,
and are confined to narrow portions of the Chester and Corsica
Rivers and one small creek. The only samples indicating depressed
dissolved oxygen conditions in the basin were taken in Radcliffe Creek
on July 14, 1970. Samples taken under similar temperature conditions
on August 24, 1971, did not show the low DO levels. Nutrient data
are very limited in the Chester basin but some algal bloom condi-
tions were noted in the upper section of the river in September of
1970. In December 1971, the reddish brown discoloration in this
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area was tentatively identified as a dinoflagellate (Massartia
rotundata). ,
10. Many small areas in the Eastern Bay region have been closed
to shellfish harvesting due to bacterial pollution. Most of these
areas are in narrow sections of creeks and rivers or along shore-
lines. The pollution can be attributed primarily to septic tank
leaching. Dissolved oxygen in the basin generally meets standards
with the exception of the St. Michaels Harbor area where DO read-
ings below 4.0 mg/1 have been reported. These oxygen depressions
are probably due to poor flushing in the harbor. Conditions were
favorable to algal growth in the late summer of both 1970 and 1971
with less growth in 1971 than in 1970. Total phosphate concentrations
were high during some of the bloom conditions but there are insuf-
ficient nutrient data to establish any definite nutrient-phyto-
plankton relationships. A small section of trie Miles River was the
only area in the Eastern Bay region in which sampling was done. More
intensive studies covering a broader area must be undertaken be- -
fore an adequate evaluation of the water quality in the basin can
be made.
11. Bacteriological conditions in the Choptank Basin are poor,
with many violations of standards in both Group A and Group C waters.
As a result of the bacterial pollution, the Choptank represents a
great loss in natural resource potential. More than 5400 acres
of shellfish beds have been closed to harvesting. Dissolved oxy-
gen levels in the Choptank currently meet standards with concentra-
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tions rarely dropping below 5 mg/1 even during the summer months.
Some high nutrient levels have been documented, particularly in
the upper sections of the stream where excessive algal blooms have
occurred. These blooms seemed to be associated with total Kjeldahl
nitrogen (as N) concentrations greater than 0.9 mg/1 and total
phosphorus (as PO.) concentrations greater than 0.3 mg/1. The
most prolific blooms were recorded in the Denton area and were
probably due to over-enrichment from sewage and industrial wastes.
Metals analyses indicates that some concentrations were significant-
ly above fish toxicity levels but that generally the water in the
basin is relatively free from contamination by heavy metals.
12. The opening of 375 acres of shellfish beds in the Little
Choptank River, which had previously been closed, indicates that
bacteriological conditions have recently improved. The 875 acres
now closed to shellfish harvesting are probably affected by leaching
from septic tanks near the shoreline. The only known industry in
the basin is the Madison Canning Company in Madison, which uses
land disposal techniques; thus, there is no discharge to the Little
Choptank River from this source. Intensive investigations in this
river would be desirable to ascertain existing water quality con-
ditions and to identify any trends.
13. Bacteriological conditions in the Nanticoke River have serious-
ly degraded between 1967 and 1971. While only occasional violations
of the 240 MPN/100 ml fecal coliform maximum were noted in 1967,
violations of the fecal coliform standard were noted at most of the
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stations sampled in July and August of 1971. Dissolved oxygen
concentrations were generally good in 1971, ranging from 6 to
8 mg/1. However, an exception was noted in the Nanticoke Harbor
area in August 1971, when depressed DO values were noted. At
the same time, an algal bloom in the area was believed responsible
for a fish kill involving large numbers of menhadden. Nutrient
concentrations, in particular total phosphate and ammonia nitrogen,
are low throughout most of the Nanticoke estuary. In 1971, the
concentrations of zinc, mercury, copper, and cadmium were accep-
table, but lead and chromium concentrations exceeded the maximum
limits allowable for drinking water.
14. Poor bacteriological conditions in the Wicomico River and
Sharps Creek have resulted in the closing of 22 acres in the lower
Wicomico to shellfish harvesting. Coliform densities in Sharps
Creek averaged 18,500 MPN/100 ml in 1971, while coliform densities
near Salisbury ranged from 2,400 to 54,000 MPN/100 ml. Seepage
from the Green Giant Company in Fruit!and, septic tank Teachings,
and the discharge of inadequately treated waste from the over-
loaded Salisbury treatment plant are responsible for the high
bacterial counts. Dissolved oxygen concentrations are generally
adequate upstream from Salisbury, but an oxygen sag begins near
Harbor Point and does not recover until White Haven. Nutrient con-
centrations, relatively low throughout most of the Wicomico River,
increase near Harbor Point to 3 mg/1 and 2.2 mg/1 for TKN and TP,
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respectively. Inefficient treatment of wastes by the Salisbury
plant is responsible for both the oxygen sag and the high nutrient
concentrations noted above.
15. Although very little information concerning water quality in
the Manokin River is available, a few interpretations of the
abstract information that is available can be made. In general,
water quality conditions appear to be satisfactory. A 1967 Federal
Water Pollution Control Administration (now EPA) report on
immediate pollution control needs for the Eastern Shore made no
mention of needs in the Manokin River. A further indication of
satisfactory bacteriological conditions is the fact that no
shellfish areas in the Manokin River have been closed. However,
intensive sampling of this area is necessary to determine more
exactly current water quality conditions and trends.
16. Bacteriological conditions in the Little and Big Annemessex
Rivers are satisfactory in the designated shellfish areas. However,
exceptions are noted in the Little Annemessex River near the two
major discharges located in this area. Coliform counts of 240,000
MPN/100 ml and 46,000 MPN/100 ml were found in September 1968 near
waste discharges from the town of Crisfield and from Mrs. Paul's
Kitchens seafood packing plant, respectively. However, both
waste sources are scheduled to receive secondary treatment in the
future. Dissolved oxygen concentrations were found to be adequate
in September 1970, although some depression of oxygen levels may
occur in low-flow periods. Although total phosphate values are
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low in the Annemessex Basin (ranging from .05 to .28 mg/1), TKN
values were much higher, ranging from .80 to 1.20 mg/1 in
September 1970.
17. Bacteriological conditions in the Pocomoke River are generally
poor, with many samples in 1971 having fecal coliform counts greatly
in excess of the 240 MPN/100 ml standard set for this river. While
bacterial quality in a major portion of the Pocomoke River remained
unchanged between 1967 and 1971, a distinct improvement occurred
downstream from Pocomoke City after a secondary treatment plant,
treating both domestic and industrial waste, began operation. Vio-
lations of the coliform standard of 70 MPN/100 ml in Pocomoke Sound
has resulted in the closing of shellfish beds in this area, including
1485 acres in Virginia waters. Nutrient concentrations are generally
high in the Pocomoke River, with exceptionally high values found
near Snow Hill, where Maryland Chicken Processors discharges inade-
quately treated poultry processing waste into the river. Also, in
the summer of 1971, dissolved oxygen values in the Pocomoke River
were low, with an oxygen sag occurring at Snow Hill. However,
nutrient and DO concentrations are generally satisfactory in
Pocomoke Sound.
18. In the Patuxent River, coliform densities are generally satis-
factory; however, high coliform concentrations (21,000-24,000
MPN/100 ml) were noted in the vicinity of the large wastewater
treatment plants located between Laurel and Bowie, Maryland.
Dissolved oxygen concentrations appear to have degraded between
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II - 10
1968 and 1971 to a level approaching the average daily standard
of 5.0 mg/1, particularly during the late summer and fall periods
of low flow rates. The data also indicates that nutrient con-
centrations (NO, as N and total PO^) have increased between 1967
and 1970, a probable cause of the several algal blooms which have
recently occurred in the lower Patuxent River.
19. Since the first, sanitary surveys in 1913, the water quality
of the upper Potomac Estuary has deteriorated. This is attributed
to the increased pollution originating in the Washington Metro-
politan Area.
20. Since the summer of 1969, the high fecal coliform densities
previously found near the waste discharge points in-the tipper
Potomac Estuary have been reduced by continuous wastewater
effluent chlorination. At present, the largest sources of bacterial
pollution in the upper estuary are from sanitary and combined
sewer overflows, where, at times, about 10 to 20 MGD of untreated
sewage enters the estuary because of inadequate sewer and treatment
plant capacities. In the vicinity of Roosevelt Island, high bac-
terial densities occur as a result of sewerage overflows along the
Georgetown waterfront. Activation of the Potomac Pumping Station
in May 1972 and the closure of the so-called "Georgetown Gap"
in September 1972 will shift these overflows downstream. By
1973, expansion of the sewage treatment facilities at Blue Plains
should abate the overflows.
21. Effluents from the 18 major wastewater treatment facilities
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ii - n
and cohDir.ed sewer overflows, with a total flow of 325 MGD,
contribute 450,000; 24,000; and 60,000 Ibs/day of ultimate oxygen
demand, phosphorus, and nitrogen, respectively, to the waters of
the upper Potomac Estuary.
22. Historical data records show that dissolved oxygen levels
in the upper Potomac Estuary have decreased. A slight upward
trend occurred in the early 1960's due to a higher degree of
wastewater treatment. However, with the increasing population,
the amount of organic matter discharged increased to a record
high in 1971, resulting in a critical dissolved oxygen stress in
the receiving water. In recent years, dissolved oxygen concentra-
tions of less than 1.0 mg/1 have occurred during low-flow, high
temperature periods.
23. The recent detection of heavy metals in bottom sediments of
the Potomac Estuary has raised sufficient concern to include the
accumulation of metals as a water quality problem requiring
additional study and analysis. Significant concentrations of
lead, cobalt, chromium, copper, nickel, barium, aluminum, iron,
and lithium in the bottom sediment were measured in the vicinities
of Woodrow Wilson Bridge, Possum Point, and Route 301 Bridge.
24. In recent years, large populations of blue-green algae, often
forming thick mats, have been observed in the Potomac Estuary
from the Potomac River Bridge (Route 301) upstream to the Woodrow
Wilson Bridge during the months of June through October. In
September of 1970, after a period of low stream flow and high
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temperatures, the algal mats extended upstream beyond Mains Point
and included a nuisance growth within the Tidal Basin. The
District of Columbia Department of Environmental Services reported
algae nuisance conditions in the Tidal Basin as early as 1966.
25. The effects of the massive blue-green blooms in the middle and
upper portions of the Potomac Estuary are: (1) an increase of
over 490,000 Ibs/day in total oxygen demand, (2) an overall
decrease in dissolved oxygen due to algal respiration in waters
12 feet and greater in depth, (3) creation of nuisance and
aesthetically objectionable conditions, and (4) reduction in the
feasibility of using the upper estuary as a potable water supply
source because of potential toxin, taste, and odor problems.
26. In the saline portion of the Potomac Estuary, the algal
populations are not as dense as in the freshwater portion.
Nevertheless, at times large populations of marine phytoplankton,
primarily the algae Gymnodinium sp., Massartia sp., and Amphidinium
sp., occur, producing massive growths known as "red tides." On
February 28 and 29, and March 1, 1972 extremely widespread "red
tides" were observed in the lower Potomac Estuary.
27. Approximately 15,550 acres of oyster bars are closed to shell-
fish harvesting for direct market consumption in the lower Potomac
Estuary because of bacterial pollution. Of the closures, approx-
imately 15,162 and 398 acres are located in Virginia and Maryland
estuaries, respectively.
28. Water quality conditions in the Rappahannock River, with a
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few exceptions, are generally satisfactory. During 1971, fecal
coliform counts in the Rappahannock River were less than 100/100 ml,
except in a 5-mile reach directly downstream from the City of
Fredericksburg. During low-flow periods, degraded bacteriological
conditions occur downstream from Fredericksburg as a result of
waste discharged by the city and by the FMC Corporation. Less than
3 percent of the available oyster bars in the Rappahannock River,
2363 acres, are now closed, out of a total of 69,008 shellfish
acres. In the summer of 1971, dissolved oxygen concentrations
ranged from 7.3 to 8.9 mg/1. However, in 1970, oxygen sags were
noted at River Miles 100 and 80 during periods of low flow. Both
nutrient concentrations (total phosphorus and nitrate-nitrogen)
and pesticide concentrations (chlorinated hydrocarbon and phos-
phorus) remained low during 1970 and 1971. In addition, concentrations
of heavy metals (mercury, lead, and arsenic) were usually less than
the detectable limits for those metals.
29. Bacteriological standards in the York River are exceeded in
the vicinity of West Point, at the confluence of the Mattaponi
and Pamunkey Rivers, and near Yorktown. Elsewhere in the York
River (from 4.5 miles below West Point to near Yorktown) bacterio-
logical standards are being maintained. Industrial discharges,
in particular that from the Chesapeake Corporation at West Point,
and inadequately treated residential sewage have resulted in the
closing of 5092 acres to shellfish harvesting in the York River.
Although this represents 27 percent of the available oyster bars,
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this is an improvement over 1967, when 39 percent of the available
bars were closed. The dissolved oxygen standard of 5.0 mg/1 was
upheld during the summer of 1971 at all stations sampled. However,
in July and August of 1970, DO values of 3.6 mg/1 and 0.8 mg/1 were
noted immediately below the Chesapeake Corporation discharge output
at West Point. Nutrient concentrations in the York River were low
during 1970 (total phosphate: .10 mg/1 or less, and nitrate-
nitrogen: .19 mg/1 or less). The following metals were found in
the York River system, in most cases at levels near the minimum
detectable level: chromium, zinc, copper, mercury, manganese, lead,
and arsenic.
30. Contravention of bacterial standards for shellfish harvesting
(70 MPN/100 ml) in the James River has resulted in the closing of
approximately 50 percent of the total available shellfish beds.
Approximately 46,727 acres of the 93,062 shellfish acres available
have been closed due to degraded bacteriological conditions in
the James River. The largest closure, 36,275 acres in the Hampton
Roads area, is due to the numerous industrial and domestic waste dis-
charges in this area.
31. In the fall of 1971 an intensive sampling survey by the An-
napolis Field Office in the James River detected average fecal
coliform counts of 24,300 MPN/100 ml and 65,900 MPN/100 ml, well
above the fecal coliform standard for primary contact recreation
(240 MPN/100 ml), at stations below Goode Creek and below the Richmond
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Deepwater Terminal, respectively. The discharge of raw wastes from
the City of Richmond to Goode Creek was the cause of the extremely
high bacterial levels downstream from Richmond. Although this
raw waste discharge has now been eliminated, periods of high
storm runoff will result in the bypass of raw wastes from com-
bined sewers to the estuary.
32. Dissolved oxygen concentrations in the James River, measured
by the Virginia Water Control Board during the spring and summer
of 1971, were generally greater than the 5.0 mg/1 standard, with
some exceptions noted during the July - August low flow period.
Between June and December 1971, the Virginia Institute of Marine
Science collected DO and BOD data during low water slack conditions.
Three oxygen sags were noted: 1) downstream from the City of
Richmond wastewater treatment plant discharge to the vicinity of
Turkey Island (10 miles); 2) downstream from Hopewell to the mouth
of the Chickahominy River (20 miles); and 3) downstream from James-
town Island. The first sag, with DO values depressed to 3.0 mg/1,
is the result of the high organic loading exerted by the Richmond
STP: a 5-day BOD loading of approximately 38,364 Ibs/day. A com-
bination of poorly treated domestic wastes and a heavy organic in-
dustrial effluent from the Hopewell area contribute to the second
DO sag. The Continental Can Company and the Hercules Powder Company,
both discharging into Bailey Bay, contribute 5-day BOD loadings of
approximately 39,840 Ibs/day and 39,400 Ibs/day, respectively. Dur-
ing 1971, DO concentrations of 0.0 mg/1 were recorded on several
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occasions at the Route 10 sampling station in Bailey Creek. BOD
data for the James River, while not conclusive, did manifest maxima
in the area of the oxygen sags downstream from Richmond, Hopewell,
and Jamestown Island.
33. Nutrient concentrations in the James River have not appreciably
changed between levels found in 1966 and in 1971. Highest con-
centrations were foind in the late spring: in May 1971, ammonia-
nitrogen varied from .030 to 3.900 mg/1, nitrate-nitrogen varied
from .190 to .950 mg/1, and inorganic phosphorus (as P) varied from
, .010 to .140 mg/1. While phosphorus concentrations do not vary
greatly throughout the James Estuary, nitrogen concentrations are
greatest downstream from Richmond and Hopewell. The former increase
is due to primary treated domestic waste from the City of Richmond,
while the latter increase is due to organic industrial wastes
discharged into Bailey Creek. Nutrient concentrations were excess-
ively high in Bailey Creek in 1971: ammonia-nitrogen varied from
2.0 to 11.0 mg/1 and TKN varied from 7.0 to 14.0 mg/1 at the Route
10 Bridge, one-half mile from the confluence of Bailey Creek with
the James River. While nutrient levels in the Estuary are
sufficient to support excessive algal growths, no chlorophyll a^ data
has been taken during periods of high nutrient concentrations.
34. Traces of both chlorinated hydrocarbon and thio-phosphate
pesticides were detected in surface waters of the James Estuary
during the late spring and early summer months of 1971 (May - July).
In general, pesticides in the James Estuary were found at levels far
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below the point at which they would constitute a hazard to health.
The United States Public Health Service standards for public and
municipal water supplies at the raw water intake were, at no time,
contravened by any of the pesticides analyzed. Although the tidal
James Estuary is not now used as a public or municipal water supply,
studies are currently underway to determine the feasibility of such
a water use for the upper Estuary.
35. Heavy metal concentrations—arsenic, cadmium, chromium,
copper, iron, lead, manganese, mercury, and zinc-- in surface
waters of the main stem of the James Estuary are not critical.
The highest concentrations of metals were found between River
Miles 77.44 and 98.34. High heavy metal concentrations of
iron, manganese, and zinc were found at River Mile 0.65 in Bailey
Creek, one-half mile from its confluence with the James Estuary
at River Mile 77. A number of industries discharge significant
quantities of wastes into Bailey Bay, including Continental Can
Company, and Firestone Company.
36. The Elizabeth River, a tributary estuary of the James River,
is an excessively utilized waterway with regard to waste assimilation,
Five sewage treatment plants—Western Branch STP, Washington STP,
Lamberts Point STP, Great Gridge STP, and Pinner Point STP-- op-
erated by the Hampton Roads Sanitation District Commission, provide
primary treatment only. Frequent overflows of untreated sewage to
the Elizabeth River are the result of poor plant operation and/or
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hydraulic overloads. In addition to domestic waste discharged by
sewage treatment plants and toxic wastes discharged by a variety of
industrial concerns, the area is plagued by frequent spills and
waste discharges from the extensive shopyard and docking facilities
in the area.
37. Current routine monitoring programs of the regulatory
agencies are adequate to show contraventions in the adopted
numerical water quality standards. More frequent routine mon-
itoring for standards violations would be desirable.
38. A knowledge of water quality of the entire Chesapeake Bay is
essential. Water quality sampling over an extended period of time
and as frequently as possible is needed. Sampling in the tidal
tributaries should occur at slack water tide with freshwater inflows
recorded. Concurrent slack water boat runs up the entire main channel
of the Bay would be a vital element of this program. The resulting
data from the tidal tributaries would then be integrated with the
slack water runs' data to give an overall picture of the water quality
conditions of the Bay for the sample period.
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CHAPTER III
WATER QUALITY STANDARDS
The following is a condensation of the pertinent sections of the
Maryland, Virginia, and District of Columbia Water Quality Standards.
MARYLAND
Water Use Categories:
I - Shellfish Harvesting, II - Public or Municipal Water Supply,
III - Water Contact Recreation, IV - Propagation of Fish, Other
Aquatic Life and Wildlife, V - Agricultural Water Supply, and
VI - Industrial Water Supply.
Bacteriological Standards:
For Group "A" Water Uses - Coliform organisms to be less than
70 per 100 ml (MPN) of sample (Shellfish Waters).
For Group "B" Water Uses - Monthly average values (either MPN
or MF count) of coliform organisms not to exceed 5,000 per 100
ml of sample; nor to exceed this number in more than 20 percent
of the samples examined during any month; nor to exceed 20,000
per 100 ml in more than 20 percent of the samples examined
during any month; nor to exceed 20,000 per 100 ml in more than
5 percent of such samples (Public or Municipal Water Supply Uses)
Water Contact Recreation Uses - fecal coliform organism density
not to exceed 240 per 100 ml (MPN).
For Group "C" Water Uses - Fecal coliform density not to exceed
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240 per 100 ml (MPN).
Dissolved Oxygen Standards:
For all water use categories other than IV, DO concentrations
must not be less than 4.0 mg per liter at any time, except
where—and to the extent that—lower values occur naturally.
For Group "A, 13 and C" Hater Uses - For the propagation of fish
and other aquatic life (Water Use Category IV) in all other
waters, the DO concentration must not be less than 4.0 mg per
liter at any time, with a minimum monthly average of not less
than 5.0 mg per liter, except where—and to the extent that-
lower values occur naturally.
pH Standards:
For all water use categories other than IV, pH values must not
be less than 5.0 nor greater than 9.0, except where—and to the
extent that--pH values outside this range occur naturally.
For Group "A, 6 and C" Water Uses - Normal pH values for the
waters of the zone must not be less than 6.0 nor greater than
8.5, except where—and to the extent that—pH values outside
this range occur naturally.
Temperature Standards:
For all water use categories other than IV, there must be no
temperature change that adversely affects fish, other aquatic
life, or spawning success. There must be no thermal barriers
to the passage of fish or other aquatic life. Maximum
temperature must not exceed 100°F beyond 50 feet from any
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point of discharge.
For Group "A, B and C" Water Uses - For tidal waters used for
the propagation of fish and other aquatic life (Water Use
Category IV), temperature must not exceed 90°F beyond such
distance from any point of discharge as specified by the
Maryland Department of Water Resources as necessary for the
protection of the water use. In addition, for all tidal waters,
maximum temperature elevation is to be limited as follows:
For natural water temperatures of 50°F or less, the
temperature elevation must not exceed 20°F above the
natural water temperature with a maximum temperature
of 60°F.
For natural water temperature greater than 50°F, the
temperature elevation must not exceed 10°F above the
natural water temperature with a maximum temperature
of 90°F.
Any deviation, other than natural, from the above requirements
is to be evaluated for risk to the propagation of fish and
other aquatic life by the Potomac River Fisheries Commission
in those waters of the Potomac River and its tributaries
under the jurisdiction of the Fisheries Commission and by the
Department of Chesapeake Bay Affairs with respect to all
other tidal waters, and will be permitted or denied by the
Department of Water Resources after consultation with such
agency (also applies to pH and DO standards).
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VIRGINIA
Water Uses Assigned:
A. Waters generally satisfactory for secondary contact
recreation, propagation of fish, shellfish, and aquatic
life, and other beneficial uses,
B. Waters generally satisfactory for primary contact recreation
(prolonged intimate contact and considerable risk of
ingestion), propagation of fish, shellfish, and other aquatic
life, and other beneficial uses.
Bacteriological Standards:
For Class IIA and IIB Hater Uses:
Shellfish Waters - The median MPN coliform organism density
shall not exceed 7C per 100 ml, and not more than 10 percent
of the samples ordinarily shall exceed an MPN of 230 per 100
ml for a 5-tube decimal dilution test (or 330 per 100 ml, where
a 3-tube decimal dilution test is used) in those portions of
the area most probably exposed to fecal contamination during
the most unfavorable conditions.
Primary Contact Recreation Uses - Fecal coliform (multiple-
tube fermentation of MF count) within a 30-day period not to
exceed a long mean of 200 per 100 ml, and not more than 10
percent of samples within a 30-day period will exceed 400
per 100 ml.
Dissolved Oxygen Standards:
For Class II Water Uses - Minimum DO concentration of 4.0
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Ill - 5
mg per liter and a daily average of 5.0 mg per liter.
pH Standards:
For Class II Uater Uses - Not less than 6.0 or greater than 8.5.
Temperature Standards:
For Class II Water Uses - 4.0°F rise above natural (September-
May). 1.5°F rise above natural (June-August).
Additional Virginia Standards:
1. Free from substances attributable to sewage, industrial
waste, or other waste that will settle to form sludge
deposits that are unsightly, putrescent, or odorous, to
such degree as to create a nuisance or to interfere
directly or indirectly with specified uses of such waters;
2. Free from floating debris, oil, grease, scum, or other
floating materials attributable to sewage, industrial
waste, or other wastes that are unsightly to such degree
as to create a nuisance or to interfere directly or in-
directly with specified uses of such waters;
3. Free from materials attributable to sewage, industrial
waste, or other waste which produce odor, or appreciably
change the existing color or other conditions to such
degree as to create a nuisance or interfere directly or
indirectly with specified uses of such waters;
4. Free from high-temperature, toxic or other deleterious
substances attributable to sewage, industrial waste, or
other waste in concentrations or combinations which
-------
Ill - 6
interfere directly or indirectly with specified uses of
such waters; and
5. There shall be no sudden temperature changes that may
affect aquatic life. There shall be no thermal barriers to
the passage of fish. Essential spawning areas shall not
be affected.
The Maryland standards contain general or aesthetic criteria similar
to the criteria set vorth above.
-------
Ill - 7
DISTRICT OF COLUMBIA
The waters of the District of Columbia shall at all times be free
from:
Substances attributable to sewage, industrial wastes, or
other waste that will settle to form sludge deposits that are
unsightly, putrescent or odorous to such degree as to create
a nuisance, or that interfere directly or indirectly with
water uses;
Floating debris, oil, grease, scum, and other floating
materials attributable to sewage, industrial waste, or other
waste in amounts sufficient to be unsightly to such a degree
as to create a nuisance, or that interfere directly or in-
directly with water uses;
Materials attributable to sewage, industrial waste, or
other waste which produce taste, odor, or appreciably change
the existing color or other physical and chemical conditions
in the receiving stream to such degree as to create a nuisance,
or that interfere directly or indirectly with water uses; and
High-temperature, toxic, corrosive or other deleterious
substances attributable to sewage, industrial waste, or other
waste in concentrations or combinations which interfere
directly or indirectly with water uses, or which are harmful
to human, animal, plant, or aquatic life.
Criteria shall apply to an entire stretch of the stream. However,
reasonable allowance shall be made for the mixing and dispersion
-------
Ill - 8
of approved discharges. Sampling frequency shall provide a sound
basis for computations. Within the limits of field conditions,
sampling point locations will be selected to permit the collection
of representative samples. The following criteria shall apply to
all stream flows equal to or exceeding the 7-day, 10-year minimum
flow except where, and to the extent that, natural conditions
prevent their attainment.
I. Potomac River: D.C. - Montgomery County line to vicinity
of Key Bridge (including tributaries).
Uses to be protected
Recreational boating
Fish and wildlife propagation
Industrial water supply
Water contact recreation (Anticipated future use
predicated on the delivery of water of a quality suitable
for water contact recreation at the Maryland - District
of Columbia boundary line. The District of Columbia
will protect swimming as a use in suitable areas in the
upper reaches of this portion of the Potomac River within
the District of Columbia. The objective date for this
use is 1975).
Water Qualtiy Criteria
Fecal Coliform - not to exceed 240 per 100 ml in
90 percent of the samples collected each month.*
Dissolved Oxygen - not less than 4 mg/1; daily
average not less than 5 mg/1.
pH - 6.0 to 8.5.
Temperature - not to exceed 90°F. There shall be
no sudden or localized temperature changes that may
-------
Ill - 9
adversely affect aquatic life. No increase in natural
water temperature caused by artificial heat inputs shall
exceed 5°F after reasonable allowance for mixing.
II. Potomac River: Vicinity of Key Bridge to D.C. - Prince
George's County line (including tributaries).
Uses to be protected
Maintenance of fish life
Recreational boating
Industrial water supply
Water Quality Criteria
Fecal Coliform - not to exceed a geometric mean of
1000 per 100 ml nor equal or exceed 2000 per 100 ml in
more than 10 percent of the samples.*
Dissolved Oxygen - not less than 4 mg/1 (daily
average not less than 5 mg/1) from Key Bridge to
Rochambeau Memorial Bridge. Not less than 3 mg/1
(daily average not less than 4 mg/1) from Rochambeau
Memorial Bridge to D.C. - Prince George's County line.
pH - 6.0 to 8.5.
Temperature - same as I.
Policy Statement
There are no waters within the District of Columbia whose
existing quality is better than the quality indicated by the
established standards. Accordingly, it is the policy of the
District of Columbia to improve the quality of all its waters as
-------
Ill - 10
reflected in the standards. All industrial, public, and private
sources of pollution will be required to provide the degree of
waste treatment necessary to meet the water quality standards. In
implementing this policy, the Secretary of the Interior will be
kept advised and will be provided with such information as he will
need to discharge his responsibilities under the Federal Water
Pollution Control Act, as amended.
*Not applicable during or immediately following periods of rainfall
-------
Ill - 11
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IV - 1
CHAPTER IV
CHESAPEAKE BAY STUDY AREAS
A. LOWER SUSQUEHANNA RIVER AREA
The tidal reach of the Susquehanna River extends from Havre De
Grace, Maryland, to the foot of Conowingo Dam, approximately 10 miles
upstream. This stretch of the river is protected by Group B water
quality standards. Beneficial uses include public or municipal water
supply, water contact recreation, agricultural water supply, industrial
water supply, and propagation of fish, other aquatic life, and wildlife.
According to the Maryland Department of Water Resources (MDWR),
discharges of treated and untreated sewage from the communities of
Octoraro and Port Deposit, along the lower main stem, have resulted
in bacterial counts exceeding water quality standards. The great
assimilative capacity of the River in this area prevents severe bac-
terial degradation. Also, during periods of severe drought, the in-
trusion of saline water from the Bay may render the lower few miles
of the river temporarily unsuitable as a source of public water supply.
The dissolved oxygen (DO) standard of 5.0 mg/1 has been contra-
vened immediately below the Conowingo Dam during the critical summers
following deep-water releases from the reservoir. Recent fish kills
below the Conowingto Dam have been attributed to oxygen deficiencies
in these waters. Dissolved oxygen concentrations of 3.0 mg/1 were
-------
IV - 2
measured at mid-pool below the dam during the summer months of 1971.
However, the DO level of the river recovers quickly downstream from
the Conowingo Dam with no violations of standards.
The "Chesapeake Bay Nutrient Input Study," Technical Report Number
47, by the Annapolis Field Office, analyzed nutrient contributions to
the Bay during the period June 1969 to August 1970. Major tributary
watersheds of the Bay include the Susquehanna, Patuxent, Potomac, Rap-
pahannock, Pamunkey, Mattaponi, James, and Chickahominy Rivers. The
nutrient input to the Bay from the Susquehanna River is as follows:
Table IV-1
Parameter
Average
Monthly
Concentrations
Average
Monthly
Contribution
Percent Input
to Bay
(mg/1 )
0.18
0.12
0.67
0.91
0.23
3.64
(Ibs/day)
33,000
20,000
93,000
153,000
29 ,000
513,000
(Ibs/day)
49%
54%
60%
66%
T\%
51%
T. P04 as P04
P (Inorganic)
TKN as N
N02 + N03 as N
NH3 as N
TOC
These nutrient contributions were based on average monthly flows
for the 15-month study period, measured at Conowingo, Maryland. The
above data, when comoared with data from the other rivers in the study,
show the Susquehanna River to be the largest contributor of nutrients
to the Bay. This is due to the fact that the Susquehanna is the
largest contributor of freshwater to the Bay (approximately 50 percent)
-------
IV - 3
For an average month during the 15-month study period the flows for
the three major nutrient contributors were: the Susquehanna River,
32,133 cfs, the Potomac River 9,634 cfs, and the James River 5,740 cfs.
Detailed nutrient-flow relationships are contained in Technical Report
Number 47.
As a result of accelerated eutrophication in the upper Chesapeake
Bay tributaries and the significance of the Susquehanna River as a
nutrient input to the Bay, a nutrient survey of the lower Susque-
hanna River Basin was initiated by AFO in June 1971 with the cooper-
ation of the Commonwealth of Pennsylvania. This continuing survey is
intended to accomplish the following: quantitatively delineate the
contributory nutrient loadings (nitrogen and phosphorus) from critical
sub-basins and specific major metropolitan area discharges; determine
the relative contribution of nutrients from non-point sources, such as
agricultural and other types of land runoff; permit a mass balance of
the nutrient load over an annual cycle including the fate of such
nutrients in the impoundments and establish the necessary treatment
requirements to achieve allowable nutrient limits. In addition to
water sampling, effluent samples from 26 wastewater treatment plants
are being provided to the AFO on a monthly basis for analysis.
The AFO tested for heavy metals in the summer of 1971 in the
pool below Conowingo Dam. In the water samples, mercury, lead, and
zinc were detected at .0001, .001, and .057 ppm, respectively. The
mercury and lead readings represent the minimum detectable limit for
the laboratory procedure employed and, thus, the actual concentrations
-------
IV - 4
of the two metals might have been lower. The zinc concentrations are
normally high and oftentimes measured at an order of magnitude similar
to the various nutrient fractions.
The AFO ran heavy metal analysis on water samples obtained from the
pool below Conowingo Dam again in February 1972 to determine the
concentrations of various metals in water discharged from the impound-
ment. The results were as follows: iron .72 ppm, manganese .32 ppm,
zinc < .02 ppm, copper < .03 ppm, chromium < .03 ppm, lead < .03 ppm,
cadmium < .01 ppm, and nickel < .05 ppm.
The above metals reported as "less than" represent the lower levels
of sensitivity of the instruments employed in the metals measurement.
The source of iron and manganese could be upstream mine drainage. Pyrite
would be a source of iron.
J. H. Carpenter of the Johns Hopkins University's Chesapeake Bay
Institute (currently Director of Oceanography Section, National Science
Foundation) analyzed water samples for the presence of iron, manganese,
zinc, nickel, copper, cobalt, chromium, and cadmium in both the dissolved
and suspended states. The water samples were collected at weekly inter-
vals from April 1965 through August 1966 at Lapidium, Maryland, about
1 mile below the Conowingo Dam. Average concentrations of heavy metals
associated with suspended sediment, for which data was available,
were as follows:
Copper - 2 ppb, September 1965 through January 1966, and June 1966
through August 1966; 3 ppb, February 1966 through May 1966.
Nickel - 4 ppb, September 1965 through January 1966, and June 1966
-------
IV - 5
through August 1966; 9 ppb, February 1966 through May 1966.
Zinc - 8 ppb, September 1965 through January 1966, and January 1966
through August 1966; 27 ppb, February 1966 through May 1966.
Manganese - 75 ppb, September 1965 through January 1966, and June
1966 through August 1966; 225 ppb, February 1966 through May 1966.
Iron - 400 ppb, September 1965 through January 1966, and June 1966
through August 1966; 1,500 ppb, February 1966 through May 1966.
The periods of high metal concentration were usually associated
with high river flows and high concentrations of suspended sediment.
Carpenter's data will provide some of the needed background infor-
mation to assess heavy metal contributions to the Bay from Susquehanna
River Basin drainage.
-------
IV - 6
B. UPPER BAY AND UPPER EASTERN SHORE AREA
This area includes the Northeast, Elk, Bohemia, and Sassafras
Rivers and the open Bay waters from Sparrows Point northward to the
mouth of the Susquehanna River. Beneficial uses include municipal,
industrial, and agricultural water supply; water contact recreation;
propagation of fish, other aquatic life, and wildlife; and shellfish
harvesting. Recent studies indicate that this is a critical spawning
and nursery area for several species of fish. Specific uses for these
estuaries and the criteria to support the uses are set forth in the
water quality standards section of this chapter.
Sampling stations were established in the upper Bay in 1968 by
the Annapolis Field Office and maintained during the subsequent summer
sampling seasons. A map showing the station locations and brief
descriptions of these stations can be found on the following pages.
The Maryland Department of Water Resources also monitored the stations
during the summer months of 1970 and 1971. The following measurements
were taken by the Maryland Department of Water Resources in 1971:
water temperature, pH, Secchi disc, conductivity, salinity, DO, total
coliforms, fecal coliforms, NO2 + NO3 as N, total P04, organic P04,
chlorophyll a_, NH~ as N, and TKN. The following discussions are
based on the data obtained from this cooperative program.
BACTERIOLOGICAL CONDITIONS
The bacteriological quality of the estuaries is generally good
except in areas where wastewater treatment facilities are inadequate.
-------
IV - 7
UPPER CHESAPEAKE BAY
STATION LOCATIONS
Figure IV-1
-------
IV - 8
Table IV - 2
Station Locations
1. Sassafras River, at Georgetown Bridge
2. Sassafras River, Nun Buoy "6"
3. Sassafras River, Can "3", Ordinary Point
k. Sassafras River, mouth, off Betterton
5. Chesapeake Bay, off Grove Point Buoy "1"
6. Elk River at Turkey Point, Buoy N "6"
7. Elk River at confluence with Bohemia River, Buoy N "10"
8. Bohemia River at Long Point, Buoy N "2"
9- Bohemia River at Georges Point
10. Elk River at confluence with C & D Canal, Buoy "19"
11. Chesapeake and Delaware Canal, Buoy W "26"
12. Elk River at Paddy Piddles Cove, Buoy N "6"
13. Elk River off Locust Point, Buoy N "IV
Ik. Northeast River channel off Rocky Point, Buoy R "2"
1|?. Northeast River off Roach Point, Buoy N "10"
16. Northeast River off Charlestown, Buoy N "8"
17- Northeast River at mouth of Northeast Creek
Tl. Sassafras River, mouth, off Betterton (same as Station k)
T2. Chesapeake Bay, off Sassafras River, north of channel between
N "26" and N "2"
T3. Chesapeake Bay, Buoy N "2" at Spesutie Island channel
T^. Chesapeake Bay, Buoy N "22" off Still Pond Creek
T5. Chesapeake Bay, Buoy C "1" off Romney Creek
T6. Chesapeake Bay, Buoy "12" off Fairlee Creek
TT. Chesapeake Bay, Buoy C "3", lower tip Pooles Island
T8. Chesapeake Bay, Buoy S41B, off Gunpowder River
T9- Chesapeake Bay, Buoy R ''6" above Swan Point
T10. Chesapeake Bay, between Buoy C "5" and S "l8B"
Til. Chesapeake Bay, off Craighill channel light
-------
IV - 9
The communities of Charlestown, North Chesapeake City, South Chesa-
peake City, Meadowview, and Northeast have been directed by the MDWR
to construct or improve treatment facilities.
Sampling data of the MDWR obtained during June, July, and August
of 1971 showed fecal coliform densities at all stations considerably
less than the primary contact recreation standard of 240 MPN/100 ml.
On October 18 and 19, 1971 the following densities were recorded.
Sampling
Station Date Time Fecal Coliform
MPN/100 ml
1 10-19-71 1546 930
9 10-19-71 1232 230
12 10-19-71 1328 220
13 10-19-71 1333 430
17 10-18-71 1638 430
The pattern depicted above, showing high bacterial occurrences at
various locations, cou'id indicate extreme weather conditions and
probable storm water impact.
DISSOLVED OXYGEN CONDITIONS
Data obtained by the MDWR and the AFO during the 1971 water quality
surveys were reviewed for contraventions of the DO standard. No signi-
ficant contraventions of the 5.0 mg/1 daily average DO standard were
recorded at the sampling stations. On June 6, 1971, surface-water DO
measurements of 5.4, 5.0, and 5.1 were recorded at Stations 2, 3, and 4,
respectively, in the Sassafras River. While on October 18, 1971, at
-------
IV - 10
Stations 16 and 17 in the Northeast River surface-water DO concentra-
tions were 5.8 and 5.4 respectively. It is expected that DO concentra-
tions dip below the standard during the decay and respiratory phases of
excessive algal blooms in the upper reaches of the tributaries in this
study area.
NUTRIENTS
Background data on nutrient fractions are available for the sum-
mer seasons of 1968 through 1971. The MDWR analyzed approximately
185 samples for the various nutrient fractions in this study area
during 1971. The AFO performed about 190 nutrient analyses in 1971.
WATER QUALITY TRENDS
Blooms of blue-green algae in the upper Bay tributaries have
been associated with increased nutrient concentrations. In late
August of 1968, excessive blooms of blue-green algae were first
reported in the Sassafras River near Georgetown and in the Elk River
downstream from Elkton. On August 27, 1968, when blooms were observed,
chlorophyll a_ was measured at 257 micrograms per liter in the Sassafras
River near Georgetown. In the Elk River, 140 micrograms per liter of
chlorophyll a^ was measured on August 28, 1968. Total inorganic phosphorus
concentrations were higher in the areas of the blooms when compared to
concentrations measured below these areas.
In sussequent years, since 1968, these blooms have gradually
increased in size, density and duration.
-------
IV - 11
By 1969, all of the headwaters of the upper Bay tributaries were
affected with the uppermost stations of the Sassafras, Elk, Bohemia,
and Northeast showing September chlorophyll a_ values of 97.5, 120.75,
387.0, and 117.75 yg/1, respectively.
During the early summer of 1970 there was a great deal of rain
and therefore, extensive blooms didn't occur until late in the season.
August values in the upper two stations in the Elk were 213.8 and
151.5. All four stations in the Northeast were badly hit with chloro-
phyll a_ values of 165.0, 163.5, 287.3, and 315.0, respectively, from
mouth to headwaters of the river. The Bohemia also had a large standing
crop in August with chlorophyll a^ values of 141.0 and 180.0.
In 1971 blooms became evident early in the summer. In June the
upper Sassafras was showing chlorophyll a_ values of 121.5; the Northeast
values of 224.0; and in July, the Bohemia values of 110.0.
The major offending organisms found to be present in these blooms
are Anabaena. Oscillatoria (two forms of filamentous blue-greens) and
a coccoid blue-green Anacystis (the problem organism of the Potomac
River). All three of the nuisance blue-greens were found in great
abundance.
These blue-greens seem to be unsuitable as food for grazing zoo-
plankton populations, and therefore, are not consumed until they reach
huge standing crop proportions that are readily visible as floating
masses in the water.
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rv - 12
The major problem areas appear at the headwaters of each of the
upper Bay tributaries. With each year, however, the area encompassed
by the large algal standing crop increases, especially during the hot,
low-flow months. Because of this large standing crop, there is a
potential water quality problem.
In addition to this abundance of blue-green algae, there also
seems to be a diverse but relatively small quantity of healthy green
phytoplankton.
Although there is an imbalance in the phytoplankton community, the
other trophic levels seem to be healthy. The bacteriological quality
of these tributaries is basically good. The zooplankton and bottom
communities seem to be diverse and healthy. Every spring this area is
used by huge numbers of anadromous fish, such as striped bass, alewives,
and several species of clupeids.
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IV - 13
C. UPPER WESTERN SHORE AREA
The study area includes the Bush, Gunpowder, and Middle rivers.
Back River is discussed in the section on Baltimore Harbor.
Romney Creek and Swan Creek are included in this discussion as they
are recipients of effluent from wastewater treatment plants in the
northern portion of study area.
The tidal waters of Bush, Gunpowder, and Middle Rivers are classi-
fied in the Maryland water quality standards for water contact recreation,
industrial water supply, and propagation of fish, other aquatic life
and wildlife. No specific standards are assigned to Romney and Swan
Creeks.
No current (1970-71) water quality surveys are available for this
study area except for a Romney Creek study carried out by the
Annapolis Field Office on June 11, 1970. Bathing beach reports of the
Baltimore County Hea'ith Department concerning bacterial analyses were
received for the period 1966 through 1971. Other water quality sur-
veys reviewed for this report were a study encompassing the Bush
River, Romney Creek, and Swan Creek conducted by the Annapolis Field
Office during the period of October to December 1967, and a 1965
summer survey by Mr. John R. Longwell, Maryland Department of Water
Resources, results of which are contained in a report entitled
"Physical, Chemical and Bacteriological Water Quality in Gunpowder Falls
and Little Gunpowder Falls.1'
Personnel of the Department of Water Resources report that little
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IV - U
development has taken place in the study area since 1965 and that
water quality remains generally good in the Bush, Gunpowder, and
Middle Rivers. It was noted, however, that during December 1971 the
presence of algae (Massartia) was reported for the first time in the
Middle 'River. The following is a brief discussion of the available
data mentioned above.
WATER QUALITY CONDITIONS
During the August 1965 water quality survey, the Maryland
Department of Water Resources (MDWR) found that the median DO values
in the Gunpowder River below the confluence of Gunpowder Falls and
Little Gunpowder Falls ranged from 6.9 ppm to 9.0 ppm. The overall
maximum DO value was 9.4 ppm and the minimum 5.8 ppm. The 1965
determinations for fecal coliforms (£. coli) showed minimum and maximum
values of less than 3/100 ml and 230/100 ml (MPN)..
The Department of Water Resources has not conducted recent water
quality surveys in the Middle river. In December 1961, the MDWR received
reports for the first time of algae in the Middle River. It was
believed to be, at the time of observance, the phytoplankter
Massartia.
Dissolved oxygen concentrations during the October to December
1967 survey ranged between 9.0 ppm and 11.0 ppm. With the exception
of two sampling stations, fecal coliform densities were usually below
100/100 ml. At Stations 18 and 19, located near the Edgewood Arsenal,
fecal coliform densities exceeded the contact recreation standard on
two occasions.
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IV - 15
The Edgewood Arsenal has taken steps to provide treatment to
its waste. Wastewater treatment facilities are under construction
and should be completed this year.
On June 11, 1970, the Annapolis Field Office conducted a 1-day
water quality survey of Romney Creek. This limited survey indicated
a high phytoplankton count. An algal bloom was found just downstream
from the Sod Run wastewater treatment plant. High phosphorus and
variable nitrogen readings were recorded during the survey. At the
two stations located below the point of discharge, chlorophyll a^was
measured at 192.0 and 210.0 micrograms per liter, indicative of the
bloom conditions. Additional sampling data will be needed to identify
the Sod Run plant as the primary cause of the algal blooms.
Operating records from the Sod Run plant showed a 6005 removal of
approximately 68 percent for the month of January 1972.
Swan Creek receives effluent discharges from the Aberdeen Proving
Ground and from the Glenn Heights and Town of Aberdeen wastewater
treatment plants, which discharge into Swan Creek above the Aberdeen
Proving Ground's discharge. In the 1967 survey frequent high fecal
coliform counts were found at a sampling station located downstream
from the three discharges. It should be noted that the effect of.
tidal excursion makes the identification of bacterial sources dif-
ficult. In addition, high chlorophyll values were reported in the
tidal headwaters of Swan Creek below these discharges. The high
chlorophyll values coincided with the higher nutrient figures for
phosphates and Kjeldahl nitrogen recorded during the 1967 survey.
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IV - 16
Currently, the Aberdeen Proving Ground discharges untreated
effluent from sedimentation tanks and backwash from filters at the
water filtration plant into the headwaters of Swan Creek. Action
has begun to alleviate the current situation by providing treatment of
sludge and filter backwash at the main potable water treatment plant
serving the Aberdeen Proving Ground area.
WATER QUALITY TRENDS
The insufficient data base precludes evaluations in terms of
nutrient enrichment in the Bush, Gunpowder, and Middle Rivers.
Romney and Swan Creeks receive nutrients from wastewater treatment
plants in the area. These creeks appear to act as nutrient traps or
settling basins for the nutrients. Localized algal blooms have
occurred in these creeks.
The Baltimore County Department of Health conducts sanitary
surveys and performs bacterial analyses of beach water as its bas*fs
for issuing permits to operate public bathing beaches. Prior to
the 1966 summer surveys, 21 public beaches were located on the shores Of
Middle, Gunpowder, Back and Bird Rivers, Chesapeake Bay, and Bear Creek.
The results of the 1966 summer surveys justified the closing of
four beaches in Middle River, two in Bird River, two in Back River,
and four in Bear Creek. The Health Department's 1967, 1968, and 1969
surveys showed no significant changes in water quality in the beach
waters. Seven applications for permits to operate public bathing beach-
es for the 1970 season were received and approved by the Department
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IV - 17
of Health. They were: four beaches in Chesapeake Bay, two beaches in
Middle River, and one beach in Gunpowder River. In 1971, seven applica-
tions were received and six permits issued.
Beaches are closed in Baltimore county when the 240/100 ml
fecal coliform standard is frequently exceeded. In several instances
the closures of beaches have been traced to failing individual sewage
disposal systems surrounding the beaches. The Health Department sur-
veys have also pointed out unsanitary conditions associated with the
actual beach area, which included picnic grounds, dressing rooms,
showers, and toilets.
In order to identify trends other than bacteriological, mon-
itoring data should be sought for nutrients, pesficides, and heavy
metals.
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IV - 18
D. BALTIMORE HARBOR AREA
In February 1969, the Maryland Department of Water Resources,
with Federal financial assistance under Section 3(c) of the Federal
Water Pollution Control Act, initiated a 3-year study of Baltimore
Harbor for the purpose of developing a comprehensive water quality
management plan. Since that time the Maryland Environmental Service
(MES) has taken over the responsibility for completing the project.
The field work was completed in February 1972. The recommended
management plan is expected later this year. The plan will include a
detailed description of existing water quality conditions in Baltimore
Harbor. Therefore, the following discussion is a brief review of water
quality conditions in the Harbor, based on contacts with Mr. William
Sloan, Baltimore Harbor Project Leader, MES, and current data from
the files of the Annapolis Field Office.
Major sources of pollution in Baltimore Harbor include wastes
from the Baltimore City Patapsco Wastewater Treatment Plant, which
discharges primary treated effluent directly into the Harbor, direct
industrial discharges, sewerage overflows and leaks into Harbor
tributaries, urban runoff, and the occurrence of spills of hazardous
substances from vessels and dockside facilities.
MUNICIPAL AND INDUSTRIAL DISCHARGES
The Patapsco Wastewater Treatment Plant currently discharges
approximately 13 mgd of primary treated wastes into the Harbor in the
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rv - 19
vicinity of Wagners Point above the mouth of Curtis Bay. Expansion
plans for the Patapsco Plant include secondary treatment facilities.
In addition, the MES study may include a recommendation for nutrient
removal at the Patapsco Plant. The Back River Plant, Baltimore City's
major wastewater treatment plant, provides secondary treatment to
approximately 158 mgd of wastewater, of which 38 mgd is discharged into
the upper portion Back River. Highly eutrophic conditions, as in-
dicated by a heavy algal standing crop, exist due to the discharge of
treated wastewater containing large amounts of nutrients from the
Back River Plant.
Bethlehem Steel (Sparrows Point Plant) purchases the remaining
120 mgd of secondary treatment effluent for use as process water. The
process water, in turn, is discharged near the mouth of Bear Creek
which has experienced extensive algal blooms during the summer months.
The MES study included a point of discharge evaluation for the Bethle-
hem Steel wastewater outfall to determine if better dispersion would
result from a discharge point in the main Harbor.
While some of the industries in the Baltimore area have been
authorized to connect to the city's wastewater treatment system most
major water-using industries discharge directly into the Harbor. Those
industries that do not discharge into the city's system must obtain an
industrial waste discharge permit under the 1899 Refuse Act.
In December 1971, the AFO conducted a field investigation of sever-
al of the major water-using industries known to be discharging sig-
nificant quantities of wastes into Baltimore Harbor (see attached map).
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IV - 20
Effluent samples were obtained as well as receiving water samples
opposite the discharges. Quantities of wastes (Ibs/day) were cal-
culated from flows provided in applications submitted by the industries
under the 1899 Refuse Act and based upon a single sample representa-
tive of the daily discharge. The following information is provided as
an indication of industrial waste problems in Baltimore Harbor. It should
be emphasized that the information presented does not include all of
the parameters measured in the discharges.
The FMC Corporation discharges its waste into Stonehouse cove,
a tributary of Curtis Bay. Ethion, an insecticide, was found in the
discharges of two outfalls at concentrations of .028 mg/1 and .661 mg/1,
respectively. A water sample taken opposite the outfalls contained
1.118 mg/1 ethion. Although no specific water quality criteria for
ethion has been established for particular water use classification,
ethion is known to be an acutely toxic insecticide.
Two discharges from Allied Chemical Corporation were found to
contain 8.8 mg/1 and 4.5 mg/1 of chromium, respectively. This chromium
input was calculated to be 37 Ibs/day. The receiving water sample
taken adjacent to the discharges contained .30 mg/1 chromium. The
U. S. Public Health Service (PHS) drinking water standard is .05 mg/1
and the fish toxicity level for chromium is 2.0 mg/1. Phenol was also
detected in the actual effluent at .180 mg/1 (3 Ibs/day). A water
sample collected opposite this outfall contained the same concentration,
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IV - 21
.180 mg/1 of phenol, an amount greater than that specified in the
PHS drinking water standards (0.001 mg/1).
The water quality criteria for fish and aquatic life cited in
these discussions were obtained primarily from the publication
Mater Quality Criteria, Second Edition, by J. E. McKee and H. W. Wolf,
The Resources Agency of California, State Water Resources Control Board,
revised 1963. The Public Health Service drinking water criteria, as
well as the fish and aquatic life criteria, are presented for comparison
purposes only. For the most part, the constituents in the industrial
wastes are not covered by numerical criteria in adopted water quality
standards.
One outfall from the Amstar corpqration was found to be discharging
36,962 Ibs/day of total carbon, concentrated at 214.38 mg/1 in the
actual effluent. It is known that organic particulates (carbon) reduce
dissolved oxygen in the water and form harmful sludge deposits. Signi-
ficant discharges of phenol and sulfate were also detected at Amstar
Corporation.
Effluent from the Glidden-Durkee Division of SCM Corporation
contained 19,723 mg/1 of sulfate (47,335 Ibs/day). The receiving
water sample near the outfall had 4,990 mg/1 sulfate. Concentrations
of 353 mg/1 and 18.7 mg/1 of total Kheldahl nitrogen and total phosphate,
respectively, were present in one outfall discharge. This same dis-
charge was found to be contributing 648 Ibs/day of ammonia nitrogen
(270 mg/1). For the purpose of comparison, this ammonia concentra-
tion, 270 mg/1, is approximately twentyfold greater than that contained
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IV - 22
in untreated domestic sewage.
American Smelting and Refining Company's discharge contained
6.5 mg/1 of arsenic (108.5 Ibs/day). The concentration of arsenic
in the immediate receiving waters was close to the fish toxicity
level of 1.0 mg/1. Copper was also present in the effluent at a
concentration of 76 mg/1 (1,200 Ibs/day). Copper was detected in the
receiving water sample at 12 mg/1. Fish toxicity levels and drinking
water standards for copper are 0.15 mg/1 and 1.0 mg/1, respectively.
The actual effluent had a pH of 2.5 while the immediate receiving waters
had a 3.5 pH. Fish tolerance levels range from 4.5 to 9.5 and the
water quality standards assigned to the Baltimore Harbor by the State
of Maryland are 5.0 to 9.0.
The December 1971 survey disclosed that the Bethlehem Steel Cor-
poration at Sparrows Point was discharging cyanide into Baltimore Har-
bor. The cyanide concentration and loading from this critical discharge
were found to be 16.1 mg/1 and 193 Ibs/day, respectively. Recommended
maximum drinking water criteria and fish toxicity levels are 0.01
mg/1, and 0.1 mg/1, respectively. The receiving water sample taken
opposite the discharge contained 14.0 mg/1 of cyanide. Phenol was
also detected in several of Bethlehem Steel's discharges. In the
effluent of one particular discharge, phenol was concentrated at 23.5
mg/1 (282 Ibs/day). The receiving water sample had 21.0 mg/1 of
phenol. Drinking water standards for phenol are 0.001 mg/1, while the
levels considered to be toxic or lethal to fish are 0.4 to 0.6 mg/1.
A low pH of 2.1 was measured in the receiving waters opposite two of
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IV - 23
Bethlehem Steel's discharges.
Critical concentrations of heavy metals in the actual effluents
from Bethlehem Steel were found for the following: iron, zinc, lead,
and copper. Iron was found being discharged at 888,000 plus Ibs/day.
Iron concentrations in water samples collected near several outfalls
ranged from 1.2 to 70.0 mg/1. All concentrations are in excess of
the PHS drinking water standards (0.3 mg/1) and fish toxicity levels
(1.0 mg/1).
Over 50,000 Ibs/day of zinc was being discharged by Bethlehem
Steel during the December 1971 survey. The highest amount detected
in a receiving water sample was 10 mg/1, which exceeds the PHS drinking
water standard (5.0 mg/1), the fish toxicity level (0.15 mg/1), and
the concentration (5.0 mg/1) at which zinc becomes aesthetically
undesirable (causes a greasy and milky appearance in the water).
Lead and copper were discharged at rates of 6,335 and 127,000
Ibs/day, respectively. Receiving water samples had concentrations of
2.0 and 27.0 mg/1 for lead and copper, respectively. Small traces of
lead are highly toxic to aquatic life, as lead is an accumulative poison.
The fish toxicity level for copper is 0.15 mg/1. The drinking water
standards for lead and copper are 0.05 mg/1. The drinking water stand-
ards for lead and copper are 0.05 and 1.0 mg/1, respectively.
Solids were discharged at the following rates: 32,600,000 Ibs/day
of total solids and 1.700,000 Ibs/day of suspended solids. Both the
drinking water standard of 500 mg/1 and the 4,000 mg/1 limit which
renders water unfit for human consumption were exceeded by all of the
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IV - 24
receiving water samples.
The cumulative sulfate contribution from the major outfalls was
150,027,919 Ibs/day. One particular discharge had a concentration of
118,196 mg/1 and a loading of 135,132,243 Ibs/day. The water sample
taken opposite this critical outfall also contained 118,196 mg/1 of
sulfate. The recommended drinking water standard for sulfate is
250 mg/1.
The combined loadings from the major discharges for total car-
bon, phosphate, and ammonia were 182,492 Ibs/day,+ 23,000 Ibs/day,
and 17,860 Ibs/day, respectively. Receiving water samples contained
concentrations of phosphate ranging from 0.8 mg/1 to 5.9 mg/1. For
purposes of comparison, it should be noted that this discharge of
phosphate, in excess of 23,000 Ibs/day, is equivalent to approximately
one-third of the phosphate load in the entire upper Potomac Estuary from
the Washington Metropolitan Area. Its role as a nutrient in
accelerating the eutrophication process is well documented.
The Maryland Environmental Service's comprehensive study of the
Baltimore Harbor provided for a 1-year's study of the higher trophic
levels of the fauna in the harbor. The study was carried out by the
Chesapeake Biological Laboratory, Natural Resources Institute, Uni-
versity of Maryland. The study concludes that species showing reduction
in numbers from the mouth of the Patapsco River to Fort McHenry are
those which live in or on the bottom or are dependent on benthic species,
Also, the fauna present in Bear Creek, Colgate Creek, Northwest Branch,
Middle Branch, and Curtis Creek are species either adapted to a highly
polluted environment or, if present, exhibit a detrimental physical
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IV - 25
condition as a result of the environment. The report contains several
recommendations, one of which recommends that the biological potential
of Baltimore Harbor could be improved if the addition of untreated
industrial and domestic effluents into the tributaries and main Har-
bor were prevented by curtailment or treatment of present discharges
of foreign material into these areas.
BOTTOM SEDIMENT
Analyses of bottom sediment in Baltimore Harbor were made during
1971 by the AFO as part, of a continuing program. The maintenance of
shipping channels in the Harbor requires periodic dredging and sub-
sequent disposal of the dredged material. The dredged spoils were
analyzed for potential pollutants in instances where the spoils
were planned for deposition in healthy envircns.
On several occasions in 1971, bottom sediments (upper 2 or 3 cm)
from the Harbor were analyzed for total Kjeldahl nitrogen, chemical
oxygen demand, volatile solids, mercury, lead, zinc, cadmium, chromium,
copper, and oil and grease. Some of the high concentrations measured
and respective sampling locations were as follows:
Volatile Solids - 143,300 ppm Northwest branch opposite
Amstar Corporation; 149,500 ppm Curtis Bay near Thomas Point;
214,000 ppm Bear Creek at Long Point; 217,700 ppm Middle
Branch at Buoy N6; 170,000 ppm Colgate Creek headwaters;
142,200 ppm right side of shipping channel off Sellers Point.
COD - 343,280 ppm Northwest Branch opposite Amstar Corporation;
666,980 ppm Bear Creek near Long Point; 552,920 ppm Middle
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IV - 26
Branch at Buoy N6; 661,000 ppm Colgate Creek headwaters.
Oil and Grease^ - 17,510 ppm Northwest Branch off Amstar
Corporation; 81,220 ppm Bear Creek at Lloyds Point;
38,150 ppm Middle Branch Buoy N6; 76,410 ppm lower portion
of Northwest Branch.
TKN - 2,703 ppm Curtis Bay at Buoy 16; 3,993 ppm Sparrows
Point Buoy N8; 6,220 ppm Bear Creek near Long Point;
5,811 ppm Middle Branch Buoy N6; 3,180 ppm right side of
shipping channel off Sellers Point.
Mercury - 0.043 ppm Northwest Branch opposite Amstar
Corporation; 0.026 ppm Curtis Bay both at Buoy 16 and at
Thomas Point; 0.045 and 0.046 at two of the Northwest
Branch sampling stations; 0.068 ppm opposite Hawkins Point
and adjacent to the main shipping channel.
Lead - 3,271 ppm upper Northwest Branch and 1,673 ppm
opposite Amstar Corporation in the Northwest Branch; 2,200 ppm
Colgate Creek near Dundalk; 936 ppm Colgate Creek headwaters;
1,502 ppm right side of Shipping channel off Sellers Point.
Zinc - 4,710 ppm Bear Creek at Long Point; 2,828 ppm Colgate
Creek near Dundalk; 3,324 ppm Colgate Creek headwaters;
2,589 ppm right side of shipping channel off Sellers Point.
Cadmium - Undetectable in many instances; 51 ppm Bear Creek
near Long Point; 251 ppm Colgate Creek near Dundalk; 315 ppm
and 192 ppm, middle of channel and right side of shipping
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IV - 27
channel, respectively, off Sellers Point.
Chromium - 9,425 ppm Bear Creek off Long Point, 2,654 ppm,
8,100 ppm, 6,763 ppm, and 5,681 ppm, respectively, for
stations in the upper portion to the lower portion of North-
west Branch; 3,035 ppm right side of shipping channel off
Sellers Point.
Copper - Not measured at several sampling locations; 502
and 518 ppm at two sampling locations in middle portion of
Colgate Creek; 320 ppm right side of shipping channel off
Sellers Point.
A comparison of Baltimore Harbor bottom sediment data with recent
data obtained in the vicinity of Tangier Island is presented herein.
Tangier Island, located in the lower Bay off Pocomoke Sound, is consid-
ered a clean area with regard to pollutants in the bottom sediment
surrounding the island.
TKN values for bottom sediment near Tangier Island ranged from
140 to 770 ppm. Most TKN values in Baltimore Harbor ranged between
1,000 and 3,000 ppm.
With the exception of two sampling stations near the bulkhead
at Dundalk Marine Terminal, COD in Baltimore Harbor was found to
range from approximately 100,000 to 700,000 ppm. COD ranged from
2,390 to 10,540 ppm at Tangier Island.
Volatile solids in Tangier Island sediment samples ranged from
5,800 to 20,800 ppm. Baltimore Harbor sediment values of volatile
solids ranged from 12,500 to 217,700 ppm; most samples were in excess
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IV - 28
of 100,000 ppm.
Oil and grease concentrations ranged from 140 to 460 ppm in
bottom sediment adjacent to Tangier Island. The lowest value in Balti-
more Harbor was 420 ppm, while the highest value was 81,220 ppm.
Eight samples fell within a concentration range of 10,000-40,000 ppm.
Of the 39 bottom sediment analyses of Baltimore Harbor reviewed for
this section of the report, all but one exceeded the highest value
(460 ppm) for oil and grease measured at Tangier Island.
Lead was detected in only two of six samples at Tangier Island
at low concentrations (0.4 and 0.7 ppm). Eight of the Harbor samples
contained lead in excess of 1,000 ppm.
Cadmium was also low in Tangier Island samples, averaging 0.23 ppm.
Although undetectable in most Harbor samples, cadmium was measured in
five samples at concentrations as follows: 35.6, 51.0, 192.3, 251.2,
and 315.4 ppm
Concentrations of zinc in Tangier Island sediment were low: 8, 13,
12, 27, 12, and 11 ppm. The range for zinc in Baltimore Harbor was
27 to 4,710 ppm. At least half of the samples were in excess of 1,000
ppm.
BACTERIOLOGICAL PROBLEMS
The bacteriological conditions of tributaries to Baltimore Harbor
are poor. Gwynn Falls and Jones Falls, tributaries to the Harbor area
of the Patapsco River, are severely degraded by very high bacterial
densities, due mainly to storm sewer drainage and sewerage system
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IV - 29
overflows and leaks, all of which enter these streams from the Baltimore
Metropolitan Area.
The Baltimore County Department of Health, in a recent water
quality study of Bear Creek, noted that the only public beaches
available to the Dundalk community are located in Bear Creek and that
these have been closed to swimming since 1966. The degradation of
bacteriological conditions in Bear Creek is attributed to discharges
of sewage and industrial wastes in the area, storm water drainage,
and tidal action causing pollutants to flow into Bear Creek from
Baltimore Harbor. As noted earlier, Bethlehem Steel has a major
discharge located near the mouth of Bear Creek.
Likewise, bathing beaches in Back River have been closed since
1966 because of excessive bacterial counts. The major contributors
of bacteria to Back River are its polluted tributaries. In 1965,
the AFO conducted an extensive water pollution survey of Back River.
In this study it was found that Herring Run was the source of almost 90
percent of both coliform and fecal coliform bacteria contributed by
the five tributary streams and the Back River Wastewater Treatment
Plant. Moores Run and Stemmers Run, together, provided about 10
percent of the total, while the contributions of the Back River Waste-
water Treatment Plant effluent, Bread and Cheese Creek, and Redhouse
Creek contributed about 1 percent or less.
NUTRIENTS
During the 1969, 1970, and 1971 summer months the Maryland
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IV - 30
Environmental Service (MES) monitored the various nutrient fractions
and measured chlorophyll a^ values in Baltimore Harbor in an attempt
to assess the problem of algae in the Harbor. The table below
presents nutrient data collected by MES at Harbor sampling stations
on August 25, 1971, during an algal bloom (see attached location map).
The samples were taken during daylight hours between 10:00 a.m. and
2:00 p.m. EST.
Table IV-3
August 25, 1971
Sta. Temp.°C DO NH-, as N NOo+Nthas N Tot. POa Chloro. a TKN
1
1A
2
3
4
4A
4B
5
5A
6A
7A
25.3
26.4
26.1
27.2
26.0
25.8
25.5
25.8
27.2
26.4
25.4
mg/1
8.2
9.7
9.1
13.7
7.4
8.4
5.8
7.6
14.1
2.4
5.4
" mg/1
.11
.40
.53
.90
.43
.70
.53
.37
.57
.55
.60
"mg/1
.03
.11
.11
.16
.09
.09
.09
.09
.11
.05
.12
mg/1
.41
.21
.30
.93
.26
.30
.30
.30
.45
.28
.26
yg/l
m
108
144
258
144
144
51
72
456
102
54
mg/1
1.25
1.35
.93
2.61
1.49
2.01
1.17
1.21
3.27
1.12
1.21
The above table shows chlorophyll a_ values measured during bloom
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IV - 31
stages of algae in late August 1971. At Stations 3 and 5A, where the
highest chlorophyll a_ values were recorded, surface water oxygen satu-
ration conditions also occurred, probably due to the high photosynthe-
sis accompanying the algal processes. Stations 3 and 5A are located
at the mouths of Colgate Creek and Bear Creek, respectively. High total
phosphate values were recorded during the blooms. Ammonia and
nitrite-nitrate nitrogen decreased with algal activity, while increases of
total Kheldahl nitrogen indicated higher concentrations of organic
matter in the water due to the by-products of algal production.
An examination of sampling data collected on July 8 and August 2,
1971, gives reason to believe that blooms of algae could have occurred
during these periods. They did not, however, even though warm water
temperatures were recorded together with nutrient, concentrations in
the water considered more than sufficient for the occurrence of algal
blooms. Possibly the presence of toxic material inhibited algal growth.
The question of possible algal poisoning will be addressed in the MES
study report on Baltimore Harbor.
The earlier discussion of municipal and industrial discharges
identified these discharges as significant contributors of nutrients
in Baltimore Harbor.
DISSOLVED OXYGEN
Dissolved oxygen concentrations shall not be less than 4.0 mg/1
in Baltimore Harbor according to water quality standards established
by the State of Maryland. This standard was seldom contravened in
surface waters during the 1971 surveys. More often, saturation
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IV - 32
conditions were observed during the daylight hours when algal
photosynthesis occurs. Mr. William Sloan, MES, carried out diurnal
studies (24 hours) of algal processes during 1970 and 1971 in an
attempt to determine the effects of algal respiration on DO during
hours of darkness. Mr. Sloan reports that his tentative findings
are inconclusive. While DO showed no appreciable fluctuation in
Bear Creek and Stony Creek, the studies showed significant fluc-
tuations in DO in the Northwest Harbor and off Wagners Point. In the
upper reach of Northwest Harbor, DO was observed to vary from high
values of 9.0 and 12.0 ppm to low values of 0.6 and 4.0 ppm, respec-
tively, on separate occasions during the early morning hours (darkness)
The MES report is expected to expand the algal respiration studies.
Although surface waters generally meet the DO standard, sub-
surface waters at the 15-foot level are frequently depressed below
the standard. During the summer of 1971, the lowest subsurface DO
concentrations were observed in the Inner Harbor at sampling stations
6A and 7A. At depths greater than 15 feet, concentrations of DO are
often quite low.
The Maryland Environmental Service's report will examine the DO
problem as it relates to benthic demand, wastewater demand, algal
demand, and reaeration.
GENERAL
The consulting firm of Arthur D. Little, Incorporated, was
retained by the Maryland Environmental Service to investigate oil and
chemical spill hazards; preventive measures in industrial plants in
-------
IV - 33
the Baltimore Metropolitan Area were recommended. Findings and
recommendations of the Arthur D. Little report, "The Prevention of
Spills of Oil and Chemicals into Baltimore Harbor and Environs,"
will be incorporated into the forthcoming water quality management
plan of MES for Baltimore Harbor.
-------
IV - 34
Figure IV-2
-------
IV - 35
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-------
IV - 36
E. MIDDLE WESTERN SHORE AREA
The area covered in this section of the report is located just
south of the Baltimore Metropolitan Area and includes the Annapolis
Metropolitan Area. The Magothy, Severn, South, and West Rivers are
the major drainage areas. The drainage area includes 270 square
miles of land and over 190 miles of waterfront.
All the rivers mentioned above are protected by water quality
standards to permit water contact recreation and propagation of
fish, other aquatic life and wildlife. In addition, the Magothy,
Severn, South, and West Rivers are designated as shellfish harvesting
waters in the standards of the State of Maryland.
The Maryland Department of Water Resources conducted field
surveys on the Severn and South Rivers during 1970 and 1971. No
similar surveys by the Department were conducted for the Magothy
or West Rivers. The 1970 and 1971 surveys included measurements of
the following parameters: water temperature, pH, secchi disc,
conductivity, salinity, DO, total coliforms, NOo + NQ^ as N, total
P04, organic P04, chlorophyll a_, NH3 as N, and TKN.
The AFO, Environmental Protection Agency, conducted a water
quality survey of the Annapolis Metropolitan Area during 1967.
The data report from this survey covered the West, Rhode, Magothy,
South, and Severn Rivers. In 1970 a survey was conducted on the Severn
River on a 1-day basis in March and June by the AFO.
The Smithsonian Institute's Chesapeake Bay Center for En-
-------
IV - 37
Table TV - k
State of Maryland
Station Location List
Station Number Location
SRO Turkey Point - mid-channel
SROW Turkey Point - west side of channel, 10-foot
depth contour
SROE Turkey Point - east side of channel, 10-foot
depth contour
SRI Mouth of Selby Bay
SR2 Cedar Point - mid-channel
SR2W Cedar Point - west side, 10-foot depth contour
SR2E Cedar Point - east side, 10-foot depth contour
SR3 Ferry Point - mid-channel
SR3W North Point Almshouse Creek, 10-foot depth
contour
SR3E East side of channel, 10-foot depth contour,
Ferry Point
PPT Mid-channel - Poplar Point
SEh Mid-channel - Boyds Point
SR5 Mouth of Broad Creek
SR6 Head of Broad Creek
SR7 Mouth of Granville Creek
SR8 Beards Point (Glen Isle)
SR9 Head of South River
-------
IV - 38
-H-
SOUTH RIVER
1 MILE
Figure IV-4
-------
IV - 39
Table TV - 5
State of Maryland
Station Location List
Station Number
Location
SVO
SVBC
SVSC
SV1
SVCC
SVWC
SV2
SV3
SVk
SV5
SV6
SV7
SVSC1
SVSC2
Mouth of Severn River, off Greenbury Point,
Buoy R "8"
Mouth of Back Creek
Mouth of Spa Creek
Off of the Naval Academy Pier, Buoy C "17"
Mouth of College Creek
Mouth of Weems Creek
Approximately 200 yards upstream of the Route
50-301 bridge, 20-foot contour, raid-channel
Between Arnold Point and Brewer Point at Buoy "5"
Mouth of Little Round Bay off of St. Helena
Island, 20-foot contour
Round Bay off of Eaglenest Point, 20-foot
contour, mid-channel
Off of Carrollton Manor, mid-channel
Head of Severn River, Indian Landing, West Side
Spa Creek, mid-channel off Southgate Avenue
Hgad of Spa Creek
-------
SEVERN
RUN
IV - 40
STEVENS CR.
1 FORKED CR
fYANTZ CR
ROUND BAY
RINOOLD COVE
HOPKINS CR.
BREWER POND
SALTWORKS CR.
STATION LOCATION
SEVERN RIVER
t MILE
Figure IV-5
-------
IV - 41
vironmental Studies supports an extensive estuarine research program
in the Rhode River. One of these studies being investigated by
R. L. Cory, U. S. Geological Survey, involves biological, chemical,
and physical measurements of water quality in the Rhode River.
Time limitations on this report did not permit a review of water
quality related studies being carried out by the Chesapeake Bay
Center for Environmental Studies.
The following discussions are based on data from the Maryland
Departments of Water Resources and Health and Mental Hygiene and the
Annapolis Field Office. Maps prepared by the MDWR are presented to show
sampling station locations for the South and Severn Rivers.
BACTERIOLOGICAL CONDITIONS
The review of fecal coliform data for the 1971 sampling season
showed only one violation of standards at one sampling location in
the South River. During 1970, on July 21 and August 31, abnormally
high fecal coliform densities were recorded in the upper South
River. However, the high occurrence of bacteria was attributed to
heavy rains occurring just prior to the surveys.
The Maryland Department of Health and Mental Hygiene reports
that a total of 127 acres of oyster bars remain closed in the South
River above Cedar and Melvin Points. This area remains closed to
safeguard against possible failure of a package wastewater treatment
plant located in the upper portion of the South River. The reach of
the river below Cedar and Melvin Points was reopened to shellfish
-------
17-42
harvesting on February 26, 1968.
Water contact recreation standards were exceeded at several
sampling stations in upper and lower Severn River, including Spa
Creek, in 1971. Based on the available data, standards were contra-
vened on the following dates: June 16, July 7, and October 13, 1971.
The MDWR attributes the excessive fecal coliform densities in the
Severn River to wastewater treatment plant discharges from the City
of Annapolis, the United States Naval Academy, and defective septic
systems. The City of Annapolis provides only primary treatment to
its wastewater.
The entire Severn River is currently closed to shellfish harvest-
ing. The closure involves approximately 1,481 acres of public bars. In
addition to the sources of bacteria mentioned above, the construction
of new housing with its concomitant erosion contributes to the coliform
problem.
The Maryland Department of Water Resources reports that the
bacterial quality of the Magothy is relatively good as a result of
the correction of more than 100 septic tank and sewage violations.
Shellfish areas formerly closed have been reopened.
In the Rhode and West River system, 63 acres of private oyster
bars are closed. This includes bottom grounds in the West River above
the county wharf, which was closed in December 1965, and all of
Parish Creek, closed in April 1967. The MDWR reports that the bacterial
degradation is caused primarily by defective septic systems.
-------
IV -
DISSOLVED OXYGEN CONDITIONS
Dissolved oxygen measurements taken at water surfaces indicate
that the DO standards are currently being maintained in the South
and Severn Rivers. Contacts with personnel of the Maryland Department
of Water Resources affirm that the DO concentrations in the Rhode,
West, and Magothy Rivers are sufficient to support the beneficial
uses assigned to these streams.
The MDWR reports that in the South River, dissolved oxygen is
depressed below a depth of 5 feet in the months of July and August.
Algal blooms have been observed during this period in the upper reach
of the South River. Low dissolved oxygen concentrations below the
5-foot depth have also been recorded at stations in the upper Severn
River during the summer months of 1971. It is expected that the res-
piration processes of algae coupled with low reaeration rates are
affecting the oxygen-holding capacities of the water columns in the
South and Severn Rivers.
NUTRIENTS
The most significant nutrient concentrations observed in the South
River during the 1971 sampling surveys were measured on the July 6, 1971,
survey at the following stations:
-------
IV -
Table IV-6
Station
SR4
SR5
SR6
SR7
SR8
SR9
Temp.
°C
28.9
28.9
29.9
29.9
30.3
29.6
N02+N03
as N
mg/1
< .01
< .01
< .01
< .01
< .01
< .01
Chlorophyll
a
ug/i
60
54
78
246
72
90
T. Phosphorus
as PO^
mg/1
.54
.37
1.12
1.25
1.11
.99
TKN
mg/1
1.20
1.13
1.07
1.20
1.13
1.27
The above concentrations of chlorophyll a_and phosphates could
be expected with algal growth processes. Blooms of algae, believed
to be the plankton organism Massartia rotundata, have been observed
in the South River during the summer months of 1971 and as recently
as December 1971.
Abnormally high concentrations of chlorophyll a_, total P04, and
TKN were measured in the upper and the lower Severn River in the
vicinity of Annapolis during the 1971 surveys by the MDWR. While
the high concentrations were recorded in the upper Severn River
stations on July 7, 1971, excessive concentrations were measured in
Spa Creek at Annapolis on both the July 7 and the October 13, 1971,
sampling surveys. Plankton blooms, identified as Massartia rotundata,
were reported in the Severn River during 1971.
The 1967 surveys by the AFO included measurements of the various
-------
IV -
nutrient fractions. Occasional high concentrations of total dissolved
P04 with accompanying significant chlorophyll admeasurements were
reported in the Magothy, West, and Rhode Rivers during the 1967
surveys. Current information is needed in order to identify water
quality trends, especially in light of the recent, algal blooms re-
ported in these waters.
HEAVY METALS AND PESTICIDES
The MDWR analyzed water samples obtained from the Severn and
South Rivers for copper during the 1971 sampling seasons. Concentrations
were found to be less than 0.05 mg/1. The detectable limit in the
laboratory is oftentimes 0.05 rng/1 . Concentrations above this limit
could be significant with respect to the ability of shellfish to
concentrate heavy metals.
The MDWR did not analyze water samples for pesticides during
the 1970 and 1971 sampling surveys, nor has the Annapolis Field
Office monitored for pesticides in this study area.
WATER QUALITY TRENDS
Personnel of the MDWR conducted an aerial overflight of the middle
portion of the Bay on December 14, 1971, to determine the persistence
of algae in the Bay. The Department had received citizen reports of
reddish-brown water in many of the tributaries to the Bay. The over-
flight showed plankton blooms persisting in the Magothy, Severn, South,
and West Rivers. Biologists in tfae Maryland Department of Water Resources
-------
rv - 46
have tentatively identified the predominant organism in the bloom
as Massartia rotundata, a dinoflagellate, which generally constitutes
more than 90 percent of the total number of organisms present.
The algal blooms observed last summer (1971) in the South River
were also observed during the December 14, 1971, aerial overflight.
Algal blooms in the upper South River have been observed by residents
in the area during the summer months since 1968.
The extent cf the algal blooms in the Bay observed during the
aerial overflight is discussed in the summary section of Chapter XI.
-------
-------
IV - 47
F. MIDDLE CHESAPEAKE BAY IN THE VICINITY OF SANDY POINT
The portion of the Chesapeake Bay covered herein includes the
middle section of the Bay, from the vicinity of the Patapsco River
southward to the Severn River area. Surveys taken by the Annapolis
Field Office of EPA between 1968 and 1971 constitute the main basis of
the information contained in this chapter. Twenty-two stations on
eight transects in the Bay were monitored at regular intervals to
ascertain existing water quality conditions. Table IV-7 lists these
station locations. The two main purposes of the EPA surveys were:
(1) to determine and identify any existing water quality trends in this
area and (2) to determine baseline conditions in this area before the
introduction of a wastewater treatment plant discharging directly into
Bay waters in the vicinity of Sandy Point.
The proposed Sandy Point treatment plant will serve the 56.91
square mile Broad Neck Sewerage Service Area, located between Annapolis
and Glen Burnie. This area is now served by individual septic tanks
and, occasionally, raw sewage lines discharging into the surrounding
water areas (the Magothy and Severn Rivers, and Chesapeake Bay). The
proposed treatment plant will serve estimated populations of 70,000 by
1980 and 148,000 by the year 2000.
Construction of the Sandy Point plant, providing secondary treat-
ment of all wastes, will be in two stages: the first stage, to be com-
pleted and in operation by late 1972, will have a capacity of 8.8 MGD;
-------
IV - 48
the second stage, to be completed sometime before the year 2000,
will have a capacity of 19.0 MGD.
In 1962, the Chesapeake Bay Institute conducted a 20-day contin-
uous dye discharge study to determine the movement and dispersion of
an introduced contaminant into the Bay waters off Sandy Point. The
dye was released approximately 1,360 yards off the shoreline just
north of Sandy Point, near the location of the future sewage outfall
from the Sandy Point treatment plant. In this area of the Bay, tidal
currents are quite strong: greater than 3 knots on the ebb current
and up to 2 knots on the flood current. This causes dye (or waste
effluent) to concentrate in a narrow north-south aligned plume off-
shore Sandy Point. During ebb tide, the plume will extend down the
Bay towards the Bay Bridge; during flood tide, the plume will extend up
the Bay. Observations of the dye confirmed this, and at no time was
the dye plume observed to extend toward the shore at Sandy Point.
The total dissolved and suspended material in secondary treated
waste effluent is approximately 100 ppm (parts per million) including
15 ppm inorganic phosphate and 25 ppm inorganic nitrogen. This effluent
is considerably less dense than the surrounding Bay water, with an
average salinity of 6.97 ppt (parts per thousand) at the surface and
14,70 ppt at a depth of 40 feet. There fore, from a bottom discharge
point, the effluent wil1 rise toward the surface, and thus some degree
of initial dilution will occur. At the surface, the diluted effluent
will then become aligned in the north-south plume described above.
Natural surface concentrations of inorganic phosphate ranged from
-------
IV -
.043 to .089 mg/1 near the future Sandy Point waste outfall during
1971. The natural surface concentrations of inorganic nitrogen
ranged from .019 to .393 mg/1 in the same area during 1971. High
increases in nutrients (a 213 percent average greater inorganic
phosphate density and a 162 percent average greater inorganic nitrogen
density) are concentrated in a narrow plume, 100 yards wide and 600
yards long, located 1,200 yards offshore Sandy Point. Approximately
600 yards from shore, the average increases in nutrient densities
reduce to 21 percent for inorganic phosphate and 16 percent for inor-
ganic nitrogen.
Detrimental or harmful effects to Bay waters in the vicinity of
Sandy Point, due to waste effluent from the future treatment plant,
cannot be accurately predicted. High increases in nutrient concen-
trations will occur only in a relatively small area offshore Sandy
Point. Elsewhere, a high degree of dilution, due to the strong
tidal currents present, will reduce the relative increase in nutrients
to an acceptable level , compared to the concentration of nutrients
naturally present. However, the natural concentrations of nutrients
are already high and have shown a trend to increase in the last
few years. Also, operation of the wastewater treatment plant at the
planned ultimate capacity of 19.0 MGD will greatly increase the per-
centage of nutrients in the effluent. It is not known how much of an
increase in nutrients the Bay waters in this area can absorb before
harmful effects occtr, i.e., hypereutrophic conditions.
The above observations are based solely on the effects of in-
creases in nutrient concentrations. It has been assumed that bac-
-------
IV - 50
terial levels of the waste effluent will be below the level which would
constitute a danger to health. While a sufficient dilution of the
effluent nutrients is generally indicated, this may not be the case if
high bacterial levels are found in the effluent. High bacterial levels
would result in the closing of oyster bars in the area.
The greatest problem affecting general water quality in this por-
tion of Chesapeake Bay is that of increasing nutrient concentrations.
Both dissolved oxygen and coliform concentrations in this area are
well within the prescribed safe limits (dissolved oxygen concentration
greater than 5.0 mg/1 and coliform density less than 70 MPN/100 ml).
In addition, dissolved oxygen and coliform densities in the Sandy Point
area have shown no trends either to increase or to decrease in the
past three years. Dissolved oxygen concentrations have generally been
between 6.0 and 7.0 mg/1 while coliform densities have generally been
below 20 MPN/100 ml during this time. The large volume of water present,
its great assimilative capacity, and the strong tidal currents in
this area are responsible for these condition;,.
Nutrient concentrations have, however, greatly increased during
the last 3 years. The concentration of nitrate-nitrogen (as N) re-
mained stable between 1968 and 1971, but the concentration of total
phosphate (as P04) increased nearly 100 percent during the same time.
Concentrations of nitrate-nitrogen (as N) at the surface in the Sandy
Point area averaged .609 mg/1 and .461 mg/1 during April and May of
1968, the months of highest concentrations of this nutrient. During
-------
IV - 51
1971, concentrations of nitrate-nitrogen (as N) averaged .640 mg/1
and .479 mg/1 for the same months. It can be seen that nitrate-
nitrogen (as N) concentrations have remained relatively constant
between 1968 and 1971. However, the concentration of total phosphate
(as P04) showed a nearly twofold increase. Concentrations of total
phosphate (as PO,^) at the surface in the Sandy Point area averaged
.122 mg/1 and .104 mg/1 during June and July of 1968, the months of
highest phosphate (as P04) concentrations. In 1971, concentrations
of total phosphate (as P04) averaged .227 mg/1 and .217 mg/1 for the
same months. This near doubling of phosphate concentrations accounts,
in part, for the alarming rise in the chlorophyll a_ density during
this time. Surface concentrations of chlorophyll a_ averaged between
35.0 and 40.0 yg/1 during the summer months of 1968, 1969, and 1970.
However, in June 1971, chlorophyll ^concentrations averaged 153 yg/1,
a nearly fourfold increase. In addition, isolated algae blooms have
been observed in this area, as indicated by abnormally high chloro-
phyll a_ concentrations. On June 14, 1971, a chlorophyll ^density of
682.5 yg/1 was measured at Station 1, Transect G. This was attributed
to a high level of nutrients, in particular phosphorus (.662 mg/1),
at that time.
Average concentrations of nitrate-nitrogen (as N) in the Sandy
Point area are generally greatest in late winter and early spring, and
least during late summer. From a maximum average concentration in
February 1970 of "1.055 mg/1, the average concentration of nitrate-
nitrogen (as N) steadily decreased to a minimum of .007 mg/1 in August
-------
IV - 52
1970, 6 decrease of 1.048 mg/1 in a 6-month period. The average
concentration of inorganic phosphorus, however, remained constant
during this period. The decrease in the nitrate-nitrogen (as N)
concentration is partly the result of a decrease in the flow rate of
the Susquehanna River between late winter and summer. The concentration
of nitrate-nitrogen in the Susquehanna River is flow-dependent: a
high flow rate will tend to generate a "flushing action" in the river
causing large loadings of nitrate-nitrogen to enter the Bay. In
February 1970, when a high concentration of nitrate-nitrogen was
measured in the Sandy Point area, the flow rate of the Susquehanna
River was 64,233 cfs at the Conowingo Dam. The flow rate of the
Susquehanna River decreased to 17,850 cfs in August 1970, when a
low concentration of nitrate-nitrogen was noted. In addition, ut-
ilization of nutrients by plankton accounts for part of the decrease
in the concentration of nitrate-nitrogen during spring and summer.
Tables IV-8 and IV-9 summarize current nutrient and chlorophyll
a_ concentrations at the surface in the Sandy Point area during the
spring months of highest concentrations in 1971.
-------
IV - 53
Table IV-7
Transect Station
AA 1 Buoy RBC
2 Buoy R 28 C
A 1 Off tower at Windmill Point
2 Red Flasher "IOC"
3 Black and White buoy "13B"
B 1 Red Flasher "2" Magothy River
2 Red Nun "4C"
3 Black Flasher, bell "1"
C 1 Off house at Tydings-on-the-Bay
2 Red Flasher, bell "2C"
3 Edge of dumping grounds
D 1 Off Sandy Point
2 Red Flasher, gong "8"
3 South edge of dumping grounds
E 1 Off Hacketts Point
2 Red Flasher, gong "4"
3 Off Matapeake ferry slip
F 1 Tolly's Point, Buoy "33"
2 Mid-Bay
3 Brickhouse Bar, Buoy "20B"
G 1 Off Bembe Beach
2 Bay Buoy (bell)
-------
IV - 54
Station
AA 1
2
A 1
2
3
B 1
2
3
C 1
2
3
0 1
2
3
E 1
2
3
F 3
2
3
G 1
2
NHrN
mg/1
.109
.471
.116
.113
.162
.098
.127
.173
.140
.169
.185
.044
.069
.095
.055
.093
.156
.089
.116
.124
.105
.060
N02+NOo-N
mg/1
.661
.719
.661
.669
.621
.705
.698
.650
.664
.693
.641
.571
.615
.573
.631
.619
.552
.634
.622
.570
.657
.666
Table IV-8
April 1971
Inorganic P
mg/1
.041
.047
.052
.055
.066
.055
.054
.038
.056
.051
.043
.037
.045
.045
.044
.053
.041
.039
.036
.041
.042
.046
Chlorophyll a
vg/1
24.0
51.8
1.5
5.3
12.8
17.3
7.5
12.0
17.3
13.5
13.5
38.3
19.5
1.5
20.3
15.0
21.8
23.3
11.3
38.3
3.0
18.8
Organic
mg/1
.254
.264
-
-
-
.439
-
.016
-
-
-
.206
.067
.215
.149
-
.563
.728
.058
.307
.183
.734
N Organic P
mg/1
.062
.137
.027
.025
.051
.039
.006
.035
.043
.054
.032
.036
.023
.024
.023
.027
.021
.021
.032
.056
.022
.030
-------
IV - 55
Station
AA 1
2
A 1
2
3
B 1
2
3
C 1
2
3
D 1
2
3
E 1
2
3
F 1
2
3
G 1
2
NH3-N
mg/1
.141
.773
.484
.070
.057
.036
.225
.186
.093
.230
.145
.001
.002
.001
.002
.001
.003
.002
.004
.002
.003
.001
NOp+NOrf
mg/1
.175
.146
.188
.189
.106
.088
.082
.096
.086
.060
.096
.130
.089
.077
.010
.091
.088
.078
.098
.010
.031
.010
Table IV-9
June 1971
Inorganic P
mg/1
.032
.046
.065
.064
.037
.049
.068
.058
.069
.072
.042
.048
.050
.051
.053
.074
.041
.059
.063
.063
.143
.059
Chlorophyll a Organic N
yg/l
77.3
76.5
233.3
191.3
45.8
99,8
-
156.8
180.8
234.0
150.0
146.3
130.5
105.0
50.3
198.0
27.8
86.3
131.3
96.0
682.5
132.0
mg/1
.850
-
1.574
1.549
.526
1.114
1.644
1.108
2.389
2.100
1.731
.725
.762
.536
.437
1.172
.027
.649
.790
.581
4.022
.960
Organic P
mg/1
.133
,151
.324
.274
.082
.124
.240
.123
.248
.185
.199
.141
.129
.097
.056
.162
.036
.121
.128
.108
.519
.129
-------
-------
IV - 56
G. MIDDLE EASTERN SHORE AREA
1. CHESTER RIVER AREA
The Chester is the largest of the rivers in the upper section
of the Eastern Shore. The river forms the boundary between Kent
and Queen Annes Counties as it flows from its headwaters in Delaware to
the Bay. The Chester and its tributaries serve as the drainage
system for a 360 square mile area which has a population of slightly
less than 30,000.
Chestertown is the largest population center and has most of
the significant waste discharges in the basin. The discharges are
from the sewage treatment plant and the Vita Foods corporation plant
to Radcliffe Creek and from the Campbell Soup and Tenneco Chemicals
plants to Morgan Neck Creek.
Two other sewage treatment plants are located in the Chester basin,
The Centreville plant dischages to the Corsica River and Millington
discharges to the Chester River.
Three areas in the Chester basin are classified as Group A waters
and should be suitable for shellfish harvesting, water contact rec-
reation and propagation of fish, other aquatic life and wildlife.
These areas are: (1) Chester River and estuarine portions of creeks,
coves and tributaries (excluding Piney Creek, Winchester Creek and
Corsica River) from the mouth at the Chesapeake Bay to U. S. Route
213 Bridge, (2) Piney Creek and estuarine portions of coves and
tributaries from the mouth at the Chester River to the U. S. 50-301
-------
IV - 57
crossing, and (3) Corsica River and estuarine portions of tributaries
from the mouth at the Chester River to Earle Cove.
Three more areas are classified as Group C waters and should be
suitable for water contact recreation and propagation of fish, other
aquatic life and wildlife. These areas are: (1) Chester River and
creeks, coves and tributaries from the U. S. Route 213 Bridge to the
Maryland Route 313 Bridge, (2) Piney Creek and tributaries from
U. S. Route 50-301 crossing to its headwaters, (3) Corsica River and
tributaries from Earle Cove and from estuarine portions to its head-
waters. The last two classification areas are the Chester River and
triburaries from Maryland Route 313 Bridge to the Delaware State Line
and headwaters classified as Group B, to be used for public or munici-
pal water supply, water contact recreation and propagation of fish,
other aquatic life and wildlife; and all of Winchester Creek and its
tributaries classified as Group C water to be used for water contact
recreation and industrial water supply.
Only two water quality surveys were available for the Chester
River basin. One study conducted by the Annapolis Field Office (AFO)
in 1970 consisted of four sets of samples at 9 stations located
between the mouth of the Chester and Crumpton, Maryland. The
second investigation was done by the Maryland Department of Water Re-
sources (MDWR) and was apparently designed to study the effect of
municipal and industrial effluents on the Chester River, Radcliffe
Creek area. Station location lists for these studies appear in this
-------
IV - 58
report.
Another study currently in progress was instituted in November,
1971 as a joint effort of the Westinghouse Electric Corporation (Ocean
Research Laboratory and Ocean Research and Engineering Center) and
the Maryland Department of Natural Resources. This is intended to be
a comprehensive regional study which will investigate the transport
characteristics for pollutants as related to biological contamination
in the basin.
BACTERIOLOGICAL CONDITIONS
The only bacteriological data available is in the area around
Chestertown. The coliform densities in Radcliffe Creek are much greater
than the densities found in the Chestertown sewage treatment lagoon
effluents. Vita Foods Corporation also has a plant which discharges
to Radcliffe Creek and may contribute to the coliform problem.
Three areas in the Chester Basin have been closed to direct
shellfish harvesting due to bacterial pollution. The areas closed
and their locations are as follows:
Area
Chester River
Corsica River
Queenstown Creek
Number of
Acres Closed
108
10
Description of the
Area
All waters upstream from a line between
Ashland Landing and Quaker Neck Landing
All waters upstream from a line between
Ship Point and Wash Point
entire creek
-------
IV - 59
DISSOLVED OXYGEN CONDITIONS
Samples from two stations in the MDWR Radcliffe Creek area
study showed DO less than the 4.0 mg/1 allowable minimum. These
samples were taken in July when the water temperature was around
23° C. Samples taken at these same two stations in August at about
the same time of day when water temperature was 24° to 26° C had
DO's of 7.7 and 7.4 mg/1. Due to the seemingly inconsistent data,
no conclusive statement can be made as to whether or not there is
a DO problem.
In the AFO study no violations of the 4.0 mg/1 minimum were
found in the surface or 20-foot depth samples but two were found
at 40-foot depths in September when water temperatures were 25° C.
No sampling was done in July and August during this study and low
DO levels would be most likely to occur in these months.
NUTRIENTS
The AFO study was designed primarily as an investigation of
nutrient-salinity relationships in the estuary. Unfortunately,
sampling was suspended during the months of July and August when
algal blooms are most likely to occur due to high nutrient loadings.
In the September 4, 1970 sampling, the two uppermost stations at
Possum Point and Crumpton had chlorophyll a^ concentrations of 52.5
and 111.0 ug/1 respectively. This would indicate that excessive
bloom level algal problems may have existed during the summer. No
nutrient parameters were run on the September samples, thus precluding
the establishment of nutrient-phytoplankton correlations.
-------
IV - 60
OTHER
During the AFO survey in 1970, pH values ranged between 6.0 and
7.6 and were within the prescribed limits set in the water quality
standards. The samples taken in the MDWR investigation had signifi-
cantly higher pH values (ranging from 6.5 to 8.7) and on May 18, 1971
3 samples taken in Radcliffe Creek exceeded the upper limit of the
pH standard.
The Chester River cooperative study, mentioned previously,
will focus on pesticides and polychlorinated biphenyls in the en-
vironment and will also produce some data on heavy metals.
WATER QUALITY TRENDS
In response to a number of telephone calls in December, 1971,
the MDWR conducted an investigation of a reddish brown discoloration
of water in the Chesapeake Bay tributaries. Some samples were taken
from the western shore rivers and the discoloration was attributed
to the presence of a dinoflagellate tentatively identified as Massartia
Rotundata. This sampling led to aerial surveillance which disclosed
similar discoloration in a number of areas north of the Patuxent. The
Chester was the most severely affected river on the Eastern Shore
but was not as heavily discolored as the areas on the western side of
the Bay. Discoloration was recorded as far up the River as Cedar Point
and although no sampling was done in the Chester, the discoloration
was similar enough to assume that the plankton were probably the same
as those found in samples on the western shore.
-------
IV - 61
STATE OF MARYLAND
DEPARTMENT OF WATER RESOURCES
WATER QUALITY INVESTIGATION DIVISION
Chester River - Radcliffe & Morgan Creeks
Kent County
1971
Station Location List
Table IV-10
STATION
NUMBER LOCATION NEAREST TOWN
CH40 (S, B) Chester River. Red Num Buoy #40 Chestertown
near Chester River Country Club Dock
CH213 (S, B) Chester River. Chestertown Bridge Chestertown
RC1 Radcliffe Creek. At mouth- Chestertown
Flashing Light "41"
RC2 Radcliffe Creek. 50 yards from old Chestertown
sewage treatment plant, near old
effluent line
RC3 Chester River. Radcliffe Creek- Chestertown
upstream of sewage treatment plant
effluent
RC4 Chester River. Radcliffe Creek- Chestertown
Quaker Neck Road Bridge
E Chestertown Lagoon effluent Chestertown
NOTE: S= Surface sample
B= Bottom sample
-------
IV - 62
Anapolis Field Office - EPA
Chester River
Station
Number
1
2
3
4
5
6
7
8
9
Station Location
Table IV-11
Location
Love Point - Bell Buoy
Long Point - Buoy 9
Boxes Point - Buoy 14
Nichols Run - Buoy 16
Corsica River - Buoy 4
Milton Point - Buoy 28
Chestertown Beacon
Possum Point - Buoy 44
Crumpton - Buoy 58
List
Latitude
39°
38°
39°
39°
39°
39°
39°
39°
39°
04'
59'
02'
05'
04'
08'
12'
14'
14'
00"
36"
64"
12"
54"
18"
01"
27"
36"
Longitude
76°
76°
76°
76°
76°
76°
76°
76°
76°
16'
12'
12'
09'
06'
04'
04'
00'
56'
24"
48"
06"
54"
48"
24"
07"
32"
41"
-------
TV - 63
2. EASTERN BAY AREA
The Eastern Bay Area, a small drainage area (approximately 120
square miles) with a population of 11,500, consists of the Eastern
Bay, Wye and Miles Rivers and a number of smaller bays and creeks.
Most of the waters in this basin are estuarine, much of which are
closed to shellfish harvesting.
According to the latest Maryland Department of Water Resources
status report (November 1, 1970), the only waste discharges in the
area are from S. E. W. Friel Company in Wye Mills, Harrison and Jarboe
in St. Michaels and the St. Michael's sewage treatment plant. This
report also stated that legal action had been taken against Roger
Johnson for sediment pollution. Most of the sanitary waste in this
basin is treated ineffectively in septic tank systems. A secondary
level sewage treatment plant has been scheduled for construction at
Grasonville to reduce septic tank leaching.
The waters of the Eastern Bay drainage area have been given
two sets of use classification by the Maryland Department of Water
Resources. Eastern Bay and estuarine portions of tributaries, coves
and creeks (excluding St. Michaels Harbor and Wye East River) and
the Wye East River from the mouth to a point 2 1/2 miles above
Wye Landing are classified as group A waters to be used for shellfish
harvesting, water contact recreation, and propagation of fish, other
aquatic life and wildlife. All of the non-estuarine portions of
Eastern Bay, St. Michaels Harbor and the Wye East River from a point
2 1/2 miles above Wye Landing to their headwaters are group C waters
-------
IV - 64
suitable for water contact recreation and propagation of fish,
other aquatic life and wildlife.
The only parts of this area which have been adequately studied
are Miles River and St. Michaels Harbor. Monthly sampling was conducted
by the Department of Water Resources from April through August in both
1970 and 1971. Stations for these surveys were located in St. Michaels
Harbor, Oak Creek and near the entrances to both the creek and the har-
bor. A station location list for these studies is included in this
section.
BACTERIOLOGICAL CONDITIONS
Samples taken at the two stations located in the section of the
Miles River open for shellfish harvesting showed most coliform den-
sities ranging from about 3 to 10 mg/1 with a few isolated samples
having higher counts. In general, the results of the surveys support
the suitability of the water quality for shellfish harvesting.
Likewise, the sampling done in Oak Creek and St. Michaels Harbor
supports the conclusion that these waters are unfit for shellfish har-
vesting. An example of coliform densities in this area is given in
table IV-12.
-------
IV - 65
Table IV-12
Coliform Densities in Oak Creek and St. Michael's Harbor
June 28. 1971 July 19. 1971 August 16.1971
A
B
C
E
F
G
Coliform
MPN/100 ml
230
230
93
430
930
230
E. Coli
MPN/100 ml
93
93
23
230
93
93
Coliform
MPN/100 ml
230
430
93
2300
930
930
E. Coli
MPN/100 ml
93
230
43
430
210
430
Coliform
E. Coli
MPN/100 ml MPN/100 ml
430
430
930
2300
430
93
230
150
93
930
93
93
Station Locations
A, B, C - Oak Creek Transects E, F, G - St. Michaels Harbor Transects
The bacteria pollution in the Eastern Bay area is due primarily
to septic tank failure and subsequent leaching. Most of the shellfish
bed closings are in shoreline areas or narrow sections of the creeks
and rivers. Following is a list of areas where shellfish harvesting
is presently prohibited.
Table IV-13
Name of Area Description of Closed Portion
Warehouse Creek All
Thompson Creek All
Cox Creek All waters above confluence
with Thompson Creek
-------
IV - 66
Table IV-13 (Cont.)
Name of Area Description of Closed Portion
Leeds Creek All
St. Michaels Harbor All
Spencer Creek All
Little Neck Creek All
Newcomb Creek-Oak Creek All
Miles River All above Red Buoy #10
Wye East River All above line between Dividing
Creek and Quarter Cove including
tributaries
Kent Island Narrows All shoreline area from Wells
Cove to Long Point
DISSOLVED OXYGEN CONDITIONS
The section of the drainage basin sampled appeared to be relatively
free from signs of oxygen depletion. Only a few samples taken in
and near St. Michaels Harbor had dissolved oxygen levels below 4.0 mg/1.
These oxygen depressions were probably due to discharges from the
sewage treatment plant at St. Michaels coupled with poor transport
characteristics in the Harbor.
NUTRIENTS
Sampling done in July and August of 1970 and 1971 indicates
that an algal problem* did exist in the Oak Creek and St. Michaels
Harbor areas. Many of the chlorophyll concentrations found in 1970
-------
IV - 67
were between 50 and TOO yg/1 with some values above 100 yg/1.
In 1971, the severity of the algal problem (in terms of chlorophyll
a^ concentration) in St. Michaels Harbor was significantly decreased
from 1970 (69 yg/1 was the highest chlorophyll value recorded)
and no chlorophyll concentrations above 50 yg/1 were recorded in
Oak Creek.
There are not sufficient data to develop significant nutrient-
phytoplankton relationships. Total phosphate concentrations
associated with the algal blooms ranged from 0.2 to 2.5 mg/1
and the nitrite plus nitrate concentrations were always less than
0.01 mg/1. No other nitrogen fractions were reported.
*Algal problem measured in terms of chlorophyll ^concentrations
with 50 yg/1 as the max before occurence of excessive bloom conditions
-------
IV - 68
GENERAL
In viewing the nutrient-algal situation it appears that there
may have been an improvement in water quality conditions but that
the causes are not evident from the available data. More extensive
work would be necessary to develop more definite relationships.
Investigative activity in the Eastern Bay Area was concentrated
in only a small section of the Miles River. More work should be
undertaken in the Eastern Bay, Wye River and the other bays and
tributaries so that a better assessment of the overall basin conditions
can be developed.
-------
rv - 69
STATE OF MARYLAND
DEPARTMENT OF WATER RESOURCES
WATER QUALITY INVESTIGATION DIVISION
Miles River - Oak Creek Survey
Talbot County
August 3, 1970
Station Location List
Table IV-14
Station
Number Location
Al North Shcre, 1050 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
A2 Mid-stream, 1050 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
A3 South Shore, 1050 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
Bl East Shore, 550 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
B2 Mid-stream, 550 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
B3 West Shore, 550 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
Cl East Shore, 250 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
C2 Mid-stream, 250 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
C3 West Shore, 250 nautical yards above Maryland Route 33
bridge at mouth of Oak Creek.
7 Miles River, Flashing Light "7" off mouth of Oak Creek.
-------
IV - 70
Table IV-14 (Cont.)
Station
Number Location
N4 Miles River, Nun Buoy "4" off St. Michaels Harbor.
El Southeast Shore, upper end of St. Michaels Harbor,
450 nautical yards from Flashing Light at mouth.
E2 Mid-harbor, upper end of St. Michaels Harbor,
450 nautical yards from flashing Light at mouth.
E3 Northwest Shore, upper end of St. Michaels Harbor,
450 nautical yards from Flashing Light at mouth.
Fl South Shore, middle St. Michaels Harbor, 425 nautical
yards from Flahing Light at mouth.
F2 Mid-harbor, middle St. Michaels Harbor, 250 nautical
yards from Flashing Light at mouth.
F3 North Shore, middle St. Michaels Harbor, 175 nautical
yards from Flashing Light at moutn.
Gl Southeast Shore, mouth of St. Michaels Harbor, 300
nautical yards from Flashing Light at mouth.
G2 Mid-harbor, mouth of St. Michaels Harbor, 75 nautical
yards from Flashing Light at mouth.
G3 Northwest Shore- mouth of St. Michaels Harbor, 250
nautical yards from Flashing Light at mouth.
-------
IV - 71
3. CHOPTANK RIVER AREA
The Choptank is the largest river on the Eastern Shore draining
portions of Kent County in Delaware, and Talbot, Caroline and Dorchester
Counties in Maryland. The drainage area of the Choptank Basin is 795
square miles and has a population of 55,000 with two population
centers at Cambridge (14,000) and Easton (11,000). The tidal portion
of the river extends past Denton to a point slightly downstream from
Greensboro, Maryland.
The two largest wastewater discharges in the basin are 3.8 MGD
from a heavily overloaded primary treatment plant at Cambridge and a
2.5 MGD intermediate plant at Easton.
Other municipal treatment plants in the drainage area are primary
plants at East New Market and Trappe, an intermediate plant at Oxford
and secondary plants at Ridgely, Preston, Denton, Cambridge Sanitary
District Number 1 and Dorchester County Sanitary District Number 1.
The Denton plant provides no effluent chlorination and discharges
directly into the Choptank. The other facilities discharge to trib-
utaries of the Choptank.
The town of Greensboro has a population of 1300 and discharges
raw sewage to the Choptank. The town of Secretary (population 600)
is presently served by septic tanks.
There are a large number of industrial discharges to the Choptank
basin many of which were reported as not being in compliance with the
laws and regulations in the November 1, 1970 MDWR water quality status
-------
TV - 72
report. Detailed information about these discharges if available in
the industrial inventory which is discussed in the Data Inventories
section.
The estuarine portion of the Choptank River and its tributaries
form a complicated network of water use classifications consisting of
11 zones employing four different sets of water use categories. Five
of these zones are listed as Group A waters protected for shellfish
harvesting, water contact recreation, and propagation of fish, other
aquatic life and wildlife. These are:
1. The Choptank and estuarine portions of tributaries in Talbot County
from the mouth at the Chesapeake Bay to a line extending from Bow Knee
Point to Wright Wharf with the exception of Black Walnut Cove, San
Domingo Creek and Tred Avon River, which are listed separately,
2. Black Walnut Cove from the mouth at the Chesapeake Bay to a line
drawn from Battery Point to Bar Neck Point,
3. San Domingo Creek and estuarine portions of its tributaries from
the mouth at Broad Creek to the mouth of the cove to St. Michaels and
to non-estuarine boundaries,
4. Tred Avon River and estuarine portions of tributaries other than
Town Creek from the mouth at the Choptank River to Easton Point and
to non-estuarine portions of tributaries, and
5. The Choptank River, Lecompte Bay and all coves in Dorchester County
portion from the mouth to a line drawn between Bow Knee Point and Wrights
Wharf Road.
Another set of four zones are classified as Group C waters
-------
IV - 73
and can be used for water contact recreation and propagation of fish,
other aquatic life, and wildlife. These zones are:
1. Black Walnut Cove from a line drawn between Battery Point and
Bar Neck Point to all headwaters.
2. Cove of San Domingo Creek leading to St. Michaels from its mouth
to all headwaters.
3. Tred Avon River and all portions of tributaries from Easton Point
to all headwaters, and
4. Town Creek and all tributaries from the mouth at Tred Avon River
to all headwaters.
The last two classifications in the Choptank Estuary are for
Group C waters but with different water use specifications. All of
the creeks and tributaries in Dorchester County should be acceptable
for water contact recreation, propagation of fish, other aquatic life
and wildlife and agricultural water supply. The Choptank River and all
tributaries from a line extending between Bow Knee Point and Wright
Wharf to the Delaware line or to all Maryland Headwaters should be
acceptable for the three preceding uses and for industrial water supply.
A significant amount of water quality data has recently been
gathered in the Choptank basin. The Maryland Department of Water Re-
sources conducted studies in the upper Choptank in the spring, summer,
and fall of both 1970 and 1971. The Annapolis Field Office (AFO), EPA,
sampled on July 13-15, 1971, and again on August 5, 1971, as part of a
survey studying the major rivers on the Eastern Shore. Another study
was conducted cooperatively by AFO and the National Marine Fisheries
-------
IV - 74
Services (NMFS) Laboratory in Oxford, Maryland, in August, September,
and October of 1971. Station location lists for these studies are
included at the end of this section.
BACTERIOLOGICAL CONDITIONS
The bacteriological standards imposed on the waters of the Choptank
as a result of classifications in water use Groups A and C require a
maximum coliform density of 70 MPN/100 ml for Group A and a maximum
fecal coliform density of 240 MPN/100 ml for Group C. The number of
standards violations, particularly in Group A waters, is reflected in
the shellfish bed closings shown in the following table:
Table IV-15
Shellfish Bed Closings in the Choptank Basin
Name of Acres
Area Closed
Choptank River 4962
San Domingo Creek 23
Town Creek 4
Tred Avon River "149
La Trappe Creek 58
Tilghman Island 234
Description of
Area Closed
All waters upstream from a line
between Howell Pt. and Jenkins Creek.
Both "branches" from point which is
north of red day beacon "14"
Entire creek from mouth to all headwaters
All waters of Tred Avon and tributaries
upstream from a line from Long Pt.
to an unnamed cove on the opposite shore.
Entire creek from mouth to all headwaters
Area surrounding Tilghman Island marked
off by closure line buoys - includes
Front Creek, Back Creek, Knapp Narrow,
Pawpaw and Blackwalnut Coves and
Dogwood Harbor.
-------
IV - 75
No bacterial analysis was done on samples from the NMFS-AFO
study and the MDWR studies were in the upper Choptank, above waters
designated as Group A. The only available bacteriological data in
Group A waters are from the AFO-1971 Eastern Shore Survey.
Data from both AFO and MDWR studies showed many exceeding the
240MPN/100 ml fecal coliform standard between Choptank and Greensboro
where the water is classified as Group C. Excessive bacterial counts
were observed consistently at stations near Greensboro and Denton.
These results are not unexpected since waste from Greensboro receives
no treatment at all and the effluent from the secondary plant at
Denton is not chlorinated.
Much of the Group A water below Bow Knee Point is closed to the
intended use of shellfish harvesting (Table IV-15). Examination of
the bacterial data from the AFO survey corroborates the validity of
the closings (Table IV-16). Stations 8, 9, 10, and 11 each show
violations in at least 2 out of 3 samples. These stations all lie in
the area between Bow Knee Point and Howell Point where the shellfish
beds are presently closed. Samples taken at stations 12 (uppermost
station in the section of the Choptank open to shellfish harvesting),
13 and 14 (located in the lower Tred Avon River which is currently
open) indicated that bacteriological standards were being met and
verified the acceptability of the area for its intended use.
-------
IV - 76
Table IV-16
TOTAL COLIFORM DENSITIES AT STATIONS IN CHOPTANK WATERS PROTECTED
FOR SHELLFISH HARVESTING (MAXIMUM ALLOWABLE COLIFORM DENSITY 70 MPN/100 ml)
Station
Number
AFO 8
AFO 9
AFO 10
AFO 11
AFO 12
AFO 13
AFO 14
7/13/71
MPN/100 ml
330
80
330
790
60
20
20
7/14/71
MPN/100 ml
50
80
130
80
20
20
20
7/15/71
MPN/100 ml
490
20
330
No sample taken
ii
n
1!
-------
IV - 77
DISSOLVED OXYGEN CONDITIONS
Dissolved oxygen levels in the Choptank estuary are quite high
with many of the values from fall and spring samplings reported as
being close to saturation. As would be expected, the DO levels in
the summer are lower than in spring and fall but do remain well above
the required 5.0 mg/1 standard. Samples taken by MDWR on July 6 and
7, 1970 showed DO ranges from 5.5 to 8.2 mg/1 and 5.4 to 9.8 mg/1
respectively. On July 13, 1971 sampling was done independently by
both AFO and MDWR. The following table lists the observed DO values,
arranging the stations approximately according to the river profile.
-------
IV - 78
Table IV-17
DISSOLVED OXYGEN VALUES IN THE CHOPTANK RIVER ON JULY 13, 1971
Station Number D. 0. Value
(mg/1)
AFO 1 8.5
MDWR 11
MDWR 9
7.3
AF° 2 6.6
AFO 3 8>0
MDWR 9A 7j
MDWR 10 7J
AFO 4 2.7
7.1
MDWR 6 6-5
AFO 5 7i2
AFO 5A 7.6
MDWR 7 12.6
MDWR 5 37
AFO 6 8 g
MDWR 4 6 7
MDWR 3 74
AFO 7 7.5
MDWR 1 7 3
AFO 8 6 g
AFO 9 . 6.5
AFO 10 6>8
AFO 11
-------
IV - 79
Table IV-17 (Cont.)
Station Number p. 0. Value
(mg/1)
AFO 12 10.3
AFO 13 6.8
AFO 14 6.3
-------
rv - go
NUTRIENTS
Data from the AFO survey in July and August of 1971 indicate
nuisance level algal blooms (measured as chlorophyll ^concentrations)
in the upper reaches of the Choptank, above the confluence with
Hunting Creek. The blooms seem to be associated with total Kjeldahl
nitrogen (TKN as N) concentrations above 0.9 mg/1 and total phosphorus
(TP as PO.) concentrations above 0.3 mg/1 (see table IV-18). The
MDWR data also show high phosphorus concentrations in the same areas
during the July sampling runs with only a few high concentrations
occurring in the spring and fall studies.
The chlorophyll concentrations indicate that the most extensive
algal blooms occurred in the Denton area probably as a result of
enrichment from sewage and industrial waste. Samples from station 7
(below the Dover Bridge) consistently show TP and TKN concentrations
higher than those at station 6 which is upstream from the bridge.
This is due to the effluent from the Easton sewage lagoons which empty
into an unnamed tributary 0.8 miles southwest of Dover Bridge. The
nutrient increases are not inordinate and do not seem to influence
the algae situation significantly.
-------
IV - 81
Table IV-18
NUTRIENT - CHLOROPHYLL* RELATIONSHIPS IN CHOPTANK RIVER
August 5, 1971 July 14, 1971
Station
AFO 1
AFO 2
AFO 3
AFO 4
AFO 5
AFO 5A
AFO 6
AFO 7
AFO 8
AFO 9
AFO 10
AFO 11
AFO 12
AFO 13
AFO 14
Chlorophyll a
yg/i
103
73
80
48
28
30
28
22
33
14
38
17
10
13.5
11.3
TP
mg/1
.510
.519
.373
.361
.381
.410
.325
.433
.340
.242
.336
.204
.165
.142
.189
TKN
mg/1
1.49
1.68
1.33
.92
1.02
.96
.76
1.02
.56
.40
.94
.41
.75
.33
.52
Chlorophyll a
yg/1
150
171
121
105
80
97
73
66
35
17
15
48
30
16
13
TP
mg/1
.471
.450
.383
.326
.310
.313
.316
.333
.259
.165
.149
.214
.192
.117
.132
TKN
mg/1
1 .93
1.45
1.45
1.54
1.58
1.13
.95
1.34
.87
.66
.52
.66
.92
.54
.92
*Chlorophyll ^concentrations greater than 50 yg/1 indicate nuisance
level algal blooms.
-------
IV - 82
METALS
Metals analyses were run on three of the sets of samples taken in
1971. Samples taken on July 13, 1971 during the AFO Eastern Shore
survey were analyzed for zinc, lead, mercury, copper, chromium and
cadmium. Samples taken on August 2 and August 17, 1971 during the
AFO-NMFS cooperative study were analyzed for zinc, lead, cadmium,
chromium and copper.
Due to equipment sensitivity problems, the copper, chromium and
cadmium concentrations in the AFO samples were reported only as
being less than 0.1 mg/1 and the lead concentrations as being less
than 0.5 mg/1. The zinc and mercury concentrations in these samples
ranged from less than 0.005 mg/1 to 0.014 mg/1 and from less than
0/0005 yg/1 to 0.0020 yg/1, respectively.
Almost all of the cadmium and chromium concentrations in the NMFS-
AFO cooperative samples were reported at the lower detection limit
(0.001 mg/1). Many of the lead, zinc and copper values were also
reported as 0.001 mg/1. concentrations of lead, zinc and copper in
the NMFS-AFO samples are shown in the accompanying tables.
In general, the waters of the Choptank are relatively free from
contamination by heavy metals. Zinc concentrations significantly
above the fish toxicity level of 0.15 mg/1 were observed at stations
Ml, N2, N5, and N6 but only on one of the two days on which the
sampling was done. The lead concentrations fall mostly at the lower
detection limit (0.001 mg/1) with only 5 samples showing concentrations
-------
IV - 83
close to or in the fisn toxicity range of 0.1 - 0.2 mg/1. These
isolated instances of high metals concentrations are not sufficient
to indicate a metals problem.
-------
IV - 84
Table IV-19
CHOPTANK RIVER
Metal Concentrations for NMFS-AFO Samples Taken August 2, 1971
Station Depth (ft)
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
1
1
2
2
3
3
4
4
5
5
6
6
7
7
8
8
9
9
10
10
Range
1
16
1
9
1
29
1
58
1
13
1
26
1
13
1
13
1
49
1
13
Zinc
mg/1
.016
.299
.245
.245
.001
.160
.048
.140
.001
.129
.052
.106
.001
.158
.018
.074
.021
.066
.036
.093
.001 - .299
Lead
mg/1
. "K'56
.001
.001
.001
.001
.001
.001
.001
.001
.001
.078
.001
.001
.001
.078
.001
.001
.156
.001
.001
.001 - .156
Copper
mg/1
.025
.050
.050
.050
.001
.050
.001
.001
.001
.001
.001
.050
.001
.050
.025
.050
.001
.025
.001
.025
.001 - .050
-------
IV - 85
Table IV-20
CHOPTANK RIVER
Metal Concentrations for NMFS-AFO Samples Taken August 17, 1971
Station Depth (ft)
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
1
1
2
2
3
3
4
4
5
S
6
6
7
7
8
8
10
1
20
1
5
1
26
1
49
1
13
1
23
1
33
1
13
1
Range
Zinc
mg/1
.062
.026
.021
.018
.015
.007
.015
.016
.199
.120
.173
.092
.069
.130
.139
.066
.101
.007 - .199
Lead
mg/1
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.150'
,001
.001
.001
.001
.104
.001 - .150
Copper
mg/1
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
.001
-------
IV -
Table IV-21
ANNAPOLIS FIELD OFFICE STATIONS
CHOPTANK RIVER
Station Number Location
AFO 0 Headwaters of Choptank
AFO 1 Denton, Power Towers
AFO 2 Buoy 79
AFO 3 Buoy 70
AFO 4 Buoy 66
AFO 5 Mouth of Tuchahoe Creek
AFO 5A Fixed Bridge, Tuckahoe Creek
AFO 6 Buoy 60
AFO 7 Buoy 55
AFO 8 Buoy 41
AFO 9 Buoy 36
AFO 10 Buoy 30
AFO 11 Buoy 24
AFO 12 Buoy 19
AFO 13 Buoy 11M
AFO 14 Channel, Tred Avon River, Oxford, Maryland
Determinations: Temperature,*pht Total Phosphate, Inorganic Phosphorous,
To'ial Kjeldahl Nitrogen, Zinc, Nitrite + Nitrate, Ammonia,
DO, Total Organic Carbon, Lead, Chlorophyll, Mercury,
Coliform, Fecal Coliform, Copper,
Chromium, Cadmium.
*Field Determinations
-------
IV - 87
Table IV-22
NATIONAL MARINE FISHERIES LABORATORY STATIONS
CHOPTANK RIVER
Station
Number Location
N 1 Denton Bridge
N 2 Fowling Creek
N 3 Tuckahoe Creek at Bridge
N 4 Hunting Creek
N 5 Warwick River
N 6 Cambridge
N 7 Howell Point
N 8 Benoni Light
N 9 Cooks Point
N 10 Double Mills Point
Determinations: Inorganic Phosphorous, Nitrite & Nitrate, Ammonia,
Total Organic Carbon, Zinc, Lead, Cadmium, Chromium
and Copper.
-------
IV -
Table IV-23
STATE OF MARYLAND
WATER QUALITY INVESTIGATION DIVISION STATIONS
Choptank River
1970
Station Location List
STATION
NUMBER LOCATION
MDWR 1 Bridge at mouth of Hunting Creek
MDWR 2 Bridge on Hunting Creek above
Linchester Pond
MDWR EE1 Unnamed tributary receiving effluent
from Easton sewage lagoons, 0.8 mile
southwest of Dover Bridge
MDWR 3 Pier at boat basin in Choptank
MDWR 4 (S, B) Dover Bridge on Maryland Route 331
MDWR 5 (S, B) Choptank River at Ganey Wharf
MDWR 6 (S, B) Tuckahoe Creek at mouth
MDWR 7 Tuckahoe Creek at bridge in Hillsboro
MDWR 8 Tuckahoe Creek at bridge on Maryland
Route 404
MDWR 9 (S, B) Choptank River below mouth of Fowling
Creek
MDWR 9A (S, B) Downstream of Denton lagoon effluent
MDWR 10 (S, B) Choptank River at black day beacon,
1 mile downstream from Denton
-------
IV - 89
Table IV-23 (Cont.)
STATION
NUMBER LOCATION
MDWR 11 (S, B) Choptank River at Maryland Route 404
bridge in Denton
MDWR 12 (S, B) Choptank River at railroad bridge
upstream from Denton
MDWR 13 Bridge on River Road over Chicken
Branch tributary just south of Brick
Wall Landing
MDWR 14 Choptank River at Brick Wall Landing
MDWR 15 Forge Branch at bridge on Maryland
Route 480
MDWR 16 Choptank River at launching ramp
downstream from Greensboro
MDWR 17 Choptank River at bridge on Maryland
Route 313 just north of Greensboro
MDWR 18 Oldtown Branch at bridge on Maryland
Route 313
MDWR 19 Choptank River at bridge on Maryland
Route 287 east of Goldsboro
NOTE: S = Surface Sample
B= Bottom Sample
Stations not designated S or B are Surface
Determinations: *DO, BOD, Turbidity, Color, Suspended Solids,
Dissolved Solids, Total Solids, *Temperature,
*pH, *Salinity, Chlorides, Conductivity
(non-tidal stations), Coliforms and E_. coli,
Nitrite, Nitrate, and Total Phosphate.
* Field Determinations
-------
IV - 90
4. LITTLE CHOPTANK RIVER AREA
The Little Choptank River and its tributaries form a small pre-
dominately tida1 basin south of the Choptank River. The total drainage
area of the basin is less than 100 square miles and the population is
approximately 5,800. Madison Canning Company in Madison is the only
known industry in the basin and was listed as being in compliance with
laws and regulations by the Maryland Department of Water Resources.
The Little Choptank has been divided into two use classifications.
The river, including estuarine portions of creeks, coves, and tributaries,
from the mouth (a line drawn between Hills Point, and the northern tip of
Oyster Cove) to the head of all estuarine portions is classified as
Group A waters and may be used for shellfish harvesting, water contact
recreation, and propagation of fish, other aquatic life, and wildlife.
The Little Choptank River and its tributaries beyond the estuary are
classified in Group C and may be used for water contact recreation and
propagation of fish, other aquatic life, and wildlife.
General Water Quality Conditions
Data on water quality in this area is lacking but some pertinent
information is available. As was stated before., Madison Canning Comapny
is the only industry in the basin and reports the use of land waste dis-
posal techniques, hence, no discharge to the water.
On February 21, 1972, the Maryland Environmental Health Administration
opened approximately 30 percent of the 1,250 acres of shellfish beds which
had been closed due tc bacterial pollution. Now open for shellfish
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IV - 91
harvesting are "All of the waters of the Little Choptank River downstream
from a line extending from McKeil Point to Cedar Point, with the excep-
tion of Hudson Creek." The waters which remain closed are probably
affected by leaching from the septic tanks near the shoreline.
From the above information, it can be concluded that recently
there has been a significant improvement in at least the bacterial
quality of the water and that even through there is little pollution
creating activity in the basin, some water quality investigative work
would be desirable in this area.
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IV - 92
5. NANTICOKE RIVER AREA
The drainage basin formed by the Nanticoke River and its major
tributaries, Marshy Hope Creek and Broad Creek, serves an 815 square
mile area in Delaware and Maryland. The estuarine section of the basin
extends 35 miles from the mouth of the Nanticoke to Seaford, Delaware,
and includes portions of both Marshy Hope and Broad Creeks. The total
population of the basin is over 54,000 with the highest density areas
being the Laurel-Delmar (10,500) and Seaford (16,200) census divisions.
Of the discharges to the estuary, those at Seaford, Delaware, and
Federalsburg and Hurlock, Maryland are the most significant. At
Seaford, wastewater from a population of 7,000 receives primary treat-
ment only. This plant is scheduled for upgrading to secondary treat-
ment in October, 1972, and will serve as the main plant for a new
regional system. Secondary treatment is provided at Federalsburg but
the plant is heavily overloaded by industrial waste, accounting for
70 percent of the flow and 85 percent of the BOD load to the plant.
Plans have been made for expansion of this plant to accommodate the
needs of the area. Hurlock has a secondary plant which is operating
satisfactorily with an average daily flow of 1.0 MGD.
Other significant discharges to the Nanticoke are:
1. Raw sewage (0.1 MGD) from Sharptown, Maryland,
2. A large nylon manufacturing plant operated by Dupont at Seaford,
3. A secondary plant at Laurel which serves 2,500 people,
4. A secondary package plant at Vienna,
5. Delmarva Power and Light Company in Vienna,
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IV - 93
6. Maryland Chicken Processors, Inc. in Nanticoke, and
7. H. B. Kennerly & Sons, Inc. in Nanticoke.
Waters in the Nanticoke estuary have been assigned four use
classifications by the Maryland Department of Water Resources and
the Delaware Department of Natural Resources and Environmental Con-
trol. The Nanticoke River from the mouth (a line between Frog Point
and Stump Point) to a line between the mouth of Jacks Creek and Run-
away Point, including estuarine portions of creeks, coves, and trib-
utaries except Nanticoke Harbor is classified as Group A water and
may be used for shellfish harvesting, water contact recreation, and
propagation of fish, other aquatic life and wildlife. Nanticoke
Harbor is classified as Group C waters and may be used for water contact
recreation and propagation of fish, other aquatic life and wildlife.
The Main stem of the Nanticoke from the Jacks Creek - Runaway Point
line to the Maryland - Delaware boundary is classified as Group C
waters and may be used for water contact recreation; propagation of fish,
other aquatic life and wildlife; and agricultural water supply. The
Nanticoke estuary in Delaware is a single zone with designated uses
of industrial water supply after reasonable treatment, recreation,
and maintenance and propagation of fish, aquatic life and wildlife.
A number of surveys have been conducted in this area by the
Maryland Department of Water Resources and by the Annapolis Field
Office. Sampling was done by the Maryland Department of Water Resources
in May and August of both 1970 and 1971 and by AFO in the summers of
-------
IV - 94
1967 and 1971. Stat-'on location lists for these surveys are included,,
BACTERIOLOGICAL CONDITIONS
Surveys in 1967 by the Annapolis Field Office and in 1970 by the
Maryland Department of Water Resources, Water Quality Investigation
Division, both reported occasional violations of the 240 MPN/100 ml
fecal coliform maximum allowed in Group C waters. Average values for
fecal coliform counts in the Group C waters, however, were below the
maximum level at most stations. The coliform counts in the Group A
stations were above the maximum 70 MPN/100 ml value in almost all cases.
The same two agencies conducted surveys again in 1971 with sampling
by the Maryland Department of Water Resources on May 24-25 and August
30-31 and by Annapolis Field Office on July 20-22 and August 10-12.
Sampling by the MDWR in May indicated high fecal coliform values
in the Group C waters only near the Vienna Sewage Treatment Plant and
the Delmarva Power and Light Company fly ash lagoon. The only avail-
able data on the Group A waters was obtained during this sampling run.
Of the four samples taken in Group A waters, only one met the maximum
allowable coliform count of 70 MPN/100 ml. No valid conclusions can
be drawn regarding the suitability of the Group A waters for their pre-
scribed use since the amount of data is so limited. Samples taken on
August 30 and 31, 1971, showed violations of bacterial standards at
almost all of the stations in both Group A and C waters in the basin.
The 1971 AFO study indicates an even more severe coliform problem
than was seen in the MDWR 1971 study. Violations of the 240 MPN/100 ml
-------
IV - 95
fecal coliform maximum occur at all stations and the mean fecal coliform
counts (based on six samples) at all but two of eight stations exceeded
the maximum allowable level. The most significant incidents of bacterial
pollution are mean fecal coliform counts of 7,383, 3,641, and 1,898
MPN/100 ml at stations 1 (upstream from Seaford), 8 (Broad Creek, Laurel,
Delaware), and 5 (Broad Creek at Bethel, Delaware), respectively.
-------
IV - 96
DISSOLVED OXYGEN CONDITIONS
Dissolved oxygen levels in the Nanticoke Basin are generally
very good, with most values ranging from 6 to 8 mg/1. One exception
is the Nanticoke Harbor area where oxygen depressions were documented
at the end of August 1971. At this time, depressed values existed as far
up the river as the confluence with Marshy Hope Creek. Also in this
period, a fish kill involving a large number of menhadden was reported
in the harbor. Representatives of the Maryland Department of Water
Resources observed rich blooms of red algae upon which the menhadden were
presumably feeding, and sampling in connection with the kill exposed
the low DO values. No conclusive evidence has been found that would
definitely establish the cause of the kill, hence, no damage suits could
by instituted by the Maryland Department of Natural Resources. Dis-
charges from Maryland Chicken Processors, Inc. and H. B. Kennerly & Sons,
Inc. (an oyster processing plant) along with algae blooms and the poor
transport characteristics of the harbor probably contributed to the
low DO levels. Both of the above named companys have been put under
orders by the MDWR to provide adequate treatment for their waste.
-------
IV - 97
NUTRIENTS
Nutrient levels in the Nanticoke estuary remained quite low through-
out areas sampled. Total phosphate and ammonia nitrogen were lowest
with average concentrations ranging from .14 mg/1 to .56 mg/1 and .03
mg/1 to .6 mg/1, respectively. Nitrite plus Nitrate and Total Kjeldahl
Nitrogen (TKN) concentrations were slightly higher with some average
values for TKN greater than 2 mg/1. MDWR reports high nutient concen-
trations at the Vienna STP, the confluence with Marshy Hope Creek, and
near Quantico Creek where the shape of the river is severely constricted.
OTHER
THe pH values found in the Nanticoke all lie within the speci-
fied water quality standards range of 6.0 to 8.5 with most of the read-
ings grouped between 6.5 and 7.5.
Samples collected by AFO on July 21, 1971, were analyzed for
zinc, lead, mercury, copper, chromium and cadmium. The metal con-
centrations did not vary from station to station; measured values were:
zinc - .005 mg/1; lead - .50 mg/1; mercury - .0005 mg/1; copper - .100
mg/1; chromium - .100 mg/1; and cadmium - .ICO mg/1. The levels of zinc,
mercury, copper and cadmium all meet Public Health Service Drinking
Water Standards and are below the levels which have been found toxic to
fish and aquatic life. The lead concentrations (.50 mg/1) were
above the maximum allowed for drinking water (.05 mg/1) and the fish
toxicity level (0.1 to 0.2 mg/1). Chromium also occurred in concen-
trations above the maximum allowable for drinking water (.05 mg/1).
-------
IV - 98
Table IV-24
ANNAPOLIS FIELD OFFICE STATION LOCATIONS
NANTICOKE RIVER
STATION
NUMBER LOCATION
1 Upstream of Seaford, Delaware
2 Woodland Ferry, Delaware
3 Sharptown, Maryland
4 Vienna, Maryland
5 Broad Creek, Bethel, Delaware
6 Marshy Hope Creek, Brookview, Maryland
7 Marshy Hope Creek, Federalsburg,
Rt. 318 Bridge
8 Broad Creek, Laurel, Delaware
-------
IV - 99
Table IV-25
STATE OF MARYLAND
WATER QUALITY INVESTIGATION DIVISION STATION LOCATIONS
NANTICOKE RIVER
STATION STREAM MILES ABOVE
NUMBER CODE MOUTH* LOCATION
IS NAN 32.5 Just west of Maryland - Delaware line
on river bend at black Buoy #45
2S NAN 25.1 1/2 mile upstream from Buoy #38
(Wicomico County)
3S MAR ' . 28.8 Marshyhope Creek at Walnut Landing,
.5 miles above mouth of Marshyhope
Creek (Dorchester County)
3AS NAN 23.8 Nanticoke River at Delmarva Power
and Light Company effluent (Dorchest-
er County)
3BS NAN 23.7 Nanticoke River at Vienna Sewage
Treatment Plant (Dorchester County)
3CS NAN 23.9 Nanticoke River at Delmarva fly ash
lagoon effluent (Dorchester County)
4S NAN 23.6 Bridge at Vienna (Dorchester County)
5AS NAN 17.7 Athaloo Landing, Buoy #23 (Wicomico
County)
5S NAN 14.0 Penknife Point, Buoy #17 (Dorchester
County)
6S NAN 8.5 Off Tyaskin, Buoy #13 (Wicomico County)
7S WET 8.1 Wetipquin Bridge, Wetipquin Creek,
.8 mile above mouth (Wicomico County)
8S NAN 6.2 Jackson Harbor at Bivalve (Wicomico
County)
9S NAN 2.3 Nanticoke Harbor (Dorchester County)
* Based on distance from confluence
-------
IV - 100
6. WICOMICO RIVER - MONIE BAY AREA
Tidal action in the Wicomico River extends for 24 miles from the
mouth of the river tc dams at Salisbury, Maryland. The total drainage
area of the basin is 239 square miles and the population is approximate-
ly 44,500, of which 70 percent is concentrated in the vicinity of Sal-
isbury.
The largest discharge in the basin is from a heavily overloaded
secondary treatment plant at Salisbury which treats both domestic
(40 percent of volume) and industrial (60 percent of volume ) waste.
The plant's design parameters are 3.6 MGD flow and 187 mg/1 BOD load;
the actual loadings are 4.6 MGD flow and 411 mg/1 BOD. BOD removal
has been reduced to less than 70 percent because of the overloading
problem. Another secondary plant is being built at Fruitland where
2,000 people are presently being served by septic tanks.
At Salisbury, Mardel Byproducts Corporation, with inadequate
biological stabilization; and Petroleum Equipment Division of Dresser
Industries discharge to Mitchell Pond and the Wicomico River, respect-
ively. The Green Giant Company has a plant in Fruitland which employs
land disposal methods and J. I. Wells in Quantico discharges inade-
quately treated waste into the Wicomico. Mardel Byproducts and J. I.
Wells have been listed as not in compliance with Maryland laws and
regulations by the Department of Water Resources in the November 1, 1970,
status report.
Three sets of water use classifications have been accepted for this
area. The Wicomico river from the mouth to a point 1 mile above
-------
IV - 101
Mount Vernon wharf, and Monie Bay from the mouth to the head of the Bay
1/2 mile above Nail Point (both including estuarine portions of creek,
coves, and tributaries) are classified as Group A waters with shellfish
harvesting; water contact recreation, and propagation of fish, other
aquatic life and wildlife as the protected water uses. Tributaries
beyond both estuaries are Group C water with water contact recreation
and propagation of fish, other aquatic life and wildlife as the protect-
ed water uses. The main stem Wicomico River and all tributaries, ponds
and headwaters in Maryland from a point 1 mile above Mount Vernon
Wharf to all headwaters or the Maryland-Delaware State Line is designated
as Group C waters with water contact recreation; propagation of fish,
other aquatic life and wildlife; and agricultural water supply as
protected water uses.
Surveys by AFO in 1967 and 1971 and by the Maryland Department
of Water Resources in 1970 and 1971 provide the basis for evaluation
of the water quality conditions in this basin. Station Location lists
for these surveys are included.
-------
IV - 102
BACTERIOLOGICAL CONDITIONS
Bacterial pollution in the Wicomico River is widespread; at a
majority of the stations sampled, coliform densities averaged an
order of magnitute or more above the 240 MPN/100 ml standard set for
the prescribed water uses in the Group C waters.
Samples taken is Sharps Creek produced the highest bacterial
counts ranging from 16,090 MPN/100 ml to greater than 160,900 MPN/100
ml in 1967 and averaging 18,500 MPN/100 ml in 1971. This pollution
may be a result of seepage and overflows from the Green Giant land dis-
posal system and septic tank Teachings.
Coliform count in Salisbury area generally run from 2,400 to
54,000 MPN/100 ml. These high values are due to inadequate treat-
ment at the Salisbury treatment plant and a possible discharge from
Mardel Byproducts.
The waters designated for shellfish harvesting must not have
fecal coliform densities greater than 70 MPN/100 ml. Thus, the bac-
terial quality of the water is adequate for shellfish harvesting only
below a point 750 yards south of Clara Road in the lower section of
the river. According to a report by the Maryland Department of Water
Resources, 22 acres in the Wicomico have been closed to shellfish
harvesting.
No shellfish bed closings have been reported in Monie Bay,
thus indicating satisfactory bacterial quality in those waters.
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IV - 103
DISSOLVED OXYGEN CONDITIONS
Data from the 1967 AFO survey showed oxygen depressions in the
Salisbury area and in Sharps Creek. Samples taken above Salisbury
had more than adequate dissolved oxygen but an oxygen sag begins between
the Nancy Point and Harbor Point stations. (The overloaded Salisbury
treatment plant discharges between these stations). Further depres-
sion occurred at Gumbey Landing. Recovery is very gradual and DO
levels averaging 5.0 mg/1 are not reestablished until the White Haven
station.
Samples taken from Sharps Creek near Fruitland indicated that
severe depression of oxygen levels also existed in that area in 1967.
Low DO levels in Sharps Creek may be attributable to the oxygen demand-
ing waste entering the stream from the Green Giant land disposal system
and septic tank Teachings.
-------
IV - 104
NUTRIENTS
Nutrient values in the Wicomico estuary show relatively low
values throughout most of the basin. Samples at Harbor Point reflect
the impact of the Salisbury treatment plant with TKN values from 2 to
3 mg/1 and TP values from 1.2 to 2.2 mg/1. TKN and ammonia levels
averaging 1.93 mg/1 and .70 mg/T, respectively, are also considerably
higher in Sharp's Creek than in the rest of the basin.
Other than the two exceptions mentioned, the trend is a decrease
in nutrient concentrations at the stations downstream from Salisbury.
OTHER
Samples of shellfish from waters of the Wicomico and Monie Bay
have been analyzed for copper, zinc, cadmium and mercury as part of
a Maryland Department of Health and Mental Hygiene program. This
program will alwo include pesticide analysis in the 1972 fiscal year.
-------
IV - 105
Table IV-26
ANNAPOLIS FIELD OFFICE STATION LOCATIONS
WICOMICO RIVER
STATION NUMBER LOCATION
1 Nancy Point
2 Harbor Point, Fl 57
3 Gumby Landing, Buoy 51
3A Fl 47
4 Patricks Landing, Fl 45
5 Quantico Wharf
6 Collins Wharf, Buoy 30
7 White Haven, between Buoy 26 and 27
8 Webster Cove, Fl 18 and 19
9 Island Point, Nun 12
10 Wicomico Creek Ferry
11 Sharps Creek, River Road Bridge
12 Tonytank Creek Bridge
13 Beaverdam Creek, Shumaker Road Bridge
13A Beaverdam Creek, Route 12
14 Naylor Mill Road, North of Salisbury, Md,
-------
IV - 106
Table IV-27
STATE OF MARYLAND
DEPARTMENT OF WATER RESOURCES
Wicomico River Basin
STATION
NUMBER
MILES ABOVE
MOUTH
Wicomico County^
1970
Station Location List
LOCATION
NEAREST
TOWN
River Stations
1
2
3
4
4A
5
5A
6
7
8
9
Tributary
10
11
12
20.5
19.7
18.7
16.1
14.1
13.4
11.9
8.9
5.5
2.1
0.0
Stations
8.2 E 0.9
18.0 E 0.4
18.0 E 0.4
Nancy Point
Harbor Point, Buoy FL-57
Gumby Landing, Buoy FL-53
Patricks Landing, Buoy FL-45
Upper Ferry
Quantico Wharf (off J. I. Wells
effluent in the channel)
Kerod Landing
Collins Wharf
Whitehaven, Buoy FL-27
Webster Cove, Buoy FL-18
Island Point, Buoy FL-14
Wicomico Creek, bridge on Redden
Ferry Road
Sharps Creek, bridge on River Road
Tony Tank Creek, bridge on River
Salisbury
Salisbury
Fruitland
Si loam
Si loam
Quantico
Quantico
Trinity
White Haven
Mt. Vernon
Mt. Vernon
Trinity
Fruitland
Fruitland
Road
-------
IV - 107
Table IV-27 (Cont.)
STATION MILES ABOVE
NUMBER MOUTH
Tributary Stations
15 20.7 W 0.5
13A 21.1 E 0.1
LOCATION
NEAREST
TOWN
13
14
21.1 E 2.5
14A 21.1 N 0.0
14B 21.1 N 0.5
14C 21.1 N 2.2
14D 21.1 N 3.0
21.1 N 2.8
14E 21.1 N 5.0
14F 21.1 N 4.8
14G 21.1 E 5.0
14E1 21.1 N 1.0
Mitchell Pond, bridge on Md. Rt. Salisbury
349
Beaverdam Creek, bridge on River- Salisbury
side Drive just above confluence
with Leonard Pond Run
Beaverdam Creek, bridge on Salisbury
Shumaker Road below Shumaker
Pond
Leonard Pond Run, bridge on Salisbury
East Main Street at the conflu-
ence with Beaverdam Creek
Johnson Pond, in pond just Salisbury
above the dam on Kd. Rt. 349
Middle Neck Branch, bridge Salisbury
on U.S. Rt. 13
Brewington Branch, bridge Salisbury
on U.S. Rt. 13
Leonard Pond Run, bridge on Salisbury
Nay!or Mill Road
Connelly Mill Branch., bridge Delmar
on Jersey Road
Leonard Pond Run, bridge im- Delmar
mediately downstream from Md. Rt.
13 bridge crossing Leonard
Pond
Beaver Dam Creek, Mt. Hermon Mt. Hermon
crossing
Woods Creek, Jersey Road Delmar
crossing
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IV - 108
7. MANOKIN RIVER AREA
The Manokin River drains a small wedge shaped area in the middle
of Somerset County, Maryland. The drainage basin is approximately
60 square miles in area and has a population of 2900. The only
known discharge to the Manokin is biologically treated domestic waste
from a Somerset County Sanitary District Plant at Princess Anne.
The Manokin River has been divided into three zones for water
use classifications. The Manokin River including estuarine portions
of creeks, coves and tributaries from the mouth (a line between
Pin Point and Hazard Point) to Sharps Point is designated as group A
waters with shellfish harvesting; water contact recreation; and
propagation of fish, other aquatic life and wildlife as the protected
use classifications. Manokin River tributaries beyond the estuary
(mouth of river to Sharps Point) are group C waters and are pro-
tected for water contact recreation; and propagation of fish, other
aquatic life and wildlife. The main stem of the Manokin River and
its tributaries from Sharps Point to all headwaters is also classi-
fied as group C waters and may be used for water contact recreation;
propagation of fish, other aquatic life and wildlife; and agricultur-
al water supply.
GENERAL WATER QUALITY CONDITIONS
The authors have no knowledge of any water quality investigative
work done in this area and were able to find only abstract information
regarding the water quality in the basin. Since no sampling data
is available, any theories advanced in this section come solely from
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IV - 109
subjective interpretation of non-analytical information.
Below are listed a number of facts that give some insight into
the water quality picture in the Manokin River.
1. The only discharge in the basin has adecuate secondary
level treatment (biological stabilization) and is reported as being
in compliance with the laws and regulations of the Maryland Depart-
ment of Water Resources.
2. None of the shellfish areas have been closed by the Maryland
Department of Health and Mental Hygiene.
3. A 1967 EPA* report on immediate pollution control needs for
the Eastern Shore made no mention of needs in the Manokin River Basin.
In view of the above statements the water quality in the Manokin
River should be satisfactory. Some intensive sampling should be done
in this area to measure the background levels of the most common
water quality paramenters. Since part of this basin is classified for
agricultural water supply use, pesticide sampling might also be infor-
mative.
* Then called FWPCA
-------
IV - 110
8. ANNEMESSEX RIVERS AREA
The Little and Big Annemessex Rivers combine to form one of
the smallest drainage basins on the Eastern Shore. The area drained
by these rivers is between 35 and 40 square miles and has a population
of about 5200. The two river systems, of which the Big Annemessex is
the northern-most, are connected by the Annemessex Canal. On the
Little Annemessex River there is a harbor at Crisfield which has been
extensively developed with marina facilities.
The major discharges in this basin are located at Crisfield on
the Little Annemessex River. Domestic waste from the town of Cris-
field receives only primary treatment (secondary treatment scheduled
to begin April, 1972} before discharge. Waste from Mrs. Paul's
Kitchens seafood packing plant (which will connect to the sewage
treatment plant in the future) presently receives only inadequate
primary treatment.
Two water use classifications have been specified for this
basin. The Big Annemessex River from the mouth to the bridge on
River Road; the Little Annemessex, (along with Broad Creek and
Daugherty Creek) from the mouth to a line drawn between channel markers
#11 and N-10 to all estuarine headwaters; and Jenkins Creek from the
mouth to the bridge on the road to Birdtown are all classified as Group
A waters with shellfish harvesting; water contact recreation; and
propagation of fish, other aquatic life and wildlife as water uses to
be protected. These water use areas include estuarine portions of
-------
IV - 111
creeks, coves, and tributaries. All other waters in this basin are
classified as Group C waters and may be used for water contact rec-
reation and propagation of fish, other aquatic life and wildlife.
Relatively little investigative work has been done in the Anne-
messex basin. Two surveys conducted by the Department of Water Resources
on September 3-4, 1968 and September 8, 1970 provide the only data
which could be located. A station location list and map are included.
BACTERIOLOGICAL CONDITIONS
Only one station in these two studies was located in the shellfish
harvesting area. Samples taken at this station in 1968 showed coli-
form counts of 430 and 93 MPN/100 ml but a sample taken in 1970
showed a value of only 15 MPN/100 ml which is well below the 70 MPN/100
ml maximum standard set for shellfish harvesting waters. Indications
are that all of the designated shellfish beds remain suitable for use.
The group C waters were generally acceptable for the designated
uses except near the two major discharges in the basin. The samples
taken in 1968 indicated the following values:
Station Sample Coliform E. Coli
Number Location Date MPN/100 ml MPN/100 ml
100 yards west of 9-3-68 240,000+ 46,000
4 sewage treatment
plant effluent, mouth 9-4-68 2,300 2,300
of Hop point
Channel next to Mrs 9-3-68 4,300 430
7 Paul's plant, below
mouth of Somers Cove 9-4-68 46,000 15,000
-------
IV - 112
The sample taken September 8, 1970 showed decreases in Coliform
to 430 MPN/100 ml and E. Coli to 150 MPN/100 ml at station 4 and decreases
in Coliform to 15 MPN/100 ml and E. Coli to 7.3 MPN/100 ml at station 7.
Since only one sample was taken at each station in 1970 any statement
regarding an improvement in water quality would be considerably biased.
DISSOLVED OXYGEN CONDITIONS
Only one of the samples taken in the 1968 and 1970 surveys fell
below the minimum DO value (4.0 mg/1). Since all of the sampling
was done in September, some depression of oxygen levels in the July -
August period may go un-noted, but the general quality of the water
from the oxygen standpoint appears to be satisfactory. The standards
for the group A and C water uses (minimum DO of 4.0 mg/1 and average
DO of 5.0 mg/1) are being met according to the data collected.
NUTRIENTS
Nutrient analyses were performed on the samples collected on
September 8, 1970. Total phosphate values reported in the estuary
were low, ranging from .05 to .28 mg/1, but high nitrogen levels were
found. Total Kjeldahl Nitrogen values ranged from .80 to 1.20 mg/1
with half of the samples showing levels above 1.00 mg/1.
OTHER CONDITIONS
No data on heavy metals or pesticides in this area is available.
-------
IV - 113
Table IV-28
STATE OF MARYLAND
DEPARTMENT OF WATER RESOURCES
WATER QUALITY INVESTIGATION DIVISION
Crisfield Harbor - Little Annemessex River Survey
Somerset County
September, 1971
Station Location List
STATION
NUMBER LOCATION
1 Middle of Somers Cove
2 Mouth of Somers Cove
3 1/4 mile north of Flashing Light "13A" west of
old brick icehouse
4 100 yards west of sewage treatment plant effluent,
north of Hop Point
5 Mouth of Annemessex Canal, Beacon No. 18
6 Beacon No. 2
7 Channel next to Mrs. Paul's plant, below mouth of
Somers Cove
8 Red Nun Buoy #12
9 Red Nun Buoy #8
*10 Annemessex Canal, approximately one mile north of
Flashing Light "18"
*11 Annemessex Canal, approximately two miles north of
Flashing Light "18"
*12 Mouth of Annemessex Canal, north end at Flashing
Light. "5"
-------
IV - 114
Table IV-28 (Cont.)
STATION
NUMBER LOCATION
*13 Mouth of Acre Creek at Flashing Light "3"
*14 Mouth of Doughterty Creek at Big Annemessex River
at Flashing Light "1"
* These stations were added for the 1970 survey.
-------
CRISFIELD HARBOR IV ' 115
LITTLE ANNEMESSEX RIVER SURVEY
STATION LOCATIONS
14
ISLAND
POINT
NAUTICAL MILE
-------
IV - 116
H. LOWER EASTERN SHORE AREA
(POCOMOKE RIVER)
The Pocomoke River is the primary drainage for a 488 square mile
area located in a sparsely populated (population approximately 16,700)
portion of the Delmarva Peninsula. The largest part of the Pocomoke
drainage area lies in Maryland with the tidal influence extending 23
miles from Pocomoke Sound to a point slightly above Snow Hill, Maryland.
Major discharges to the Pocomoke River occur at the two population
centers in the basin, Snow Hill and Pocomoke City, Maryland. Primary
treated domestic waste from the town of Snow Hill, inadequately treated
poultry processing waste from Maryland Chicken Processors, Incorporated,
and inadequately treated vegetable canning waste from W. T. Onley Com-
pany are all discharged into the River at Snow Hill. Waste from
Johnson Meat Products Company, Campbell Soup Comapny and Mason Can-
ning Company, as well as domestic waste receive secondary treatment
before being discharged at Pocomoke City.
Three water use classifications are specified for the Pocomoke
estuary. The Virginia portion of Pocomoke Sound and the Virginia
tributaries are classified as II-B waters and are generally satisfact-
ory for use as public water supply, primary contact recreation;
propagation of aquatic life; and other beneficial uses. The Maryland
sector of Pocomoke Sound including estuarine portions of creeks,
coves and tributaries (except Fair Island Canal) is included in group
-------
rv - 117
A water with uses specified as shellfish harvesting; water contact
recreation; and propagation of fish, other aquatic life and wildlife.
The Pocomoke River and all its Maryland tributaries is classified as
group C water with uses including water contact recreation; propagation
of fish, other aquatic life and wildlife; agricultural water supply; and
industrial water supply. Specific standards associated with the various
water use classifications are discussed in the following sections.
Data from surveys by the Annapolis Field Office (1967 & 1971)
and the Maryland Department of Water Resources (1971) were used in
evaluating the water quality of this basin.
BACTERIOLOGICAL CONDITIONS
Bacterial water quality in the Pocomoke River is generally poor
and examination of the data showed that many of the samples had fecal
coliform values greatly in excess of the 240 MPN/100 ml standard set
for waters in the C use classification. As would be expected, bacterial
quality is at its worst immediately downstream from the population and
industrial centers at Snow Hill and Pocomoke City.
Most of the fecal coliform values around Snow Hill range between
700 and 5400 MPN/100 ml with no apparent change in levels between
1967 and 1971. Bacterial pollution in this area is mainly attribut-
able to the reduced effectiveness of chlorination when coupled with
primary treatment and the inadequacy of treatment for poultry process-
ing waste
In the case of Pocomoke City, a distinct improvement in bac-
-------
IV - 118
terial quality occurred between 1967 and 1971. Eight (8) samples
taken in 1967 showed most fecal coliform counts ranging from 2700 -
54000 MPN/100 ml with three of the samples having values greater than
10,000 MPN/100 ml. In 1971, six (6) samples produced counts of 490,
490, 2400, 2400, 70 and 9180 MPN/100 ml. This improvement is attributed
to the secondary treatment plant in Pocomoke City which began opera-
tion in 1970 and treats part of the city's industrial waste as well
as domestic waste.
The standards in Pocomoke Sound were established by both Vir-
ginia and Maryland to allow harvesting of shellfish in ths area. This
requires that coliform counts average less than 70 MPN/100 ml (in
Virginia no more than 10% can be greater than 230 MPN/100 ml) and
additionally, in Virginia only, chloride concentrations must not
exceed 800 mg/1. Due to violation of these standards shellfish beds
have been closed in both Maryland and Virginia waters.
An improvement of the bacterial quality of the water led the
Maryland Department of Health and Mental Hygiene to reopen shellfish
harvesting beds from Tulls Point to and including Marumsco Creek in
January, 1970. Beds from Marumsco Creek up the Sound to the end
of the group A waters at the mouth of the Pocomoke River remained closed,
In November, 1971, shellfish areas in Marumsco Creek were closed,
but areas further up the Sound were opened. The beds now open in
Marumsco Creek area form a wedge bounded by a line between number 6
light and a point 500 feet west of Rumbley Point and a line between
number 6 light and number 1 light.
-------
IV - 119
As reported in Water Control Board Publications of 1967 and
1971, there has been no change in the Virginia area (1,485 acres)
closed to shellfish harvesting. The data collected by AFO in 1967
and 1971 reinforces the decision of the Water Control Board in not
opening any shellfish beds as no improvement in the bacterial quality
of the water can be detected.
-------
IV - 120
DISSOLVED OXYGEN CONDITIONS
A Maryland Department of Water Resources survey conducted April
19-21, 1971 showed DO levels in the River well above the 5.0 ppm
average required for this water use classification.
However, sampling at the same stations from July 12-14, 1971 indi-
cated a severe oxygen deficiency throughout the entire stream.
The data collected by AFO in July and August of 1967 showed a
distinct oxygen sag starting at Snow Hill with partial recovery at
Milburn Landing. At Pocomoke City waste loadings caused a further
oxygen depletion and full recovery from the sag did not occur until
Shell town.
The 1971 study conducted in July, August and September by AFO
further manifested the greater efficiency of the Pocomoke City treat-
ment plant. The data shows an oxygen sag beginning at Snow Hill with
little or no recovery at Milburn Landing. But, instead of a second
sag farther downstream, significant recovery appears at the Pocomoke
City station and almost total recovery is realized at Puncheon Landing.
Samples taken in Pocomoke Sound and its smaller tributaries all
showed satisfactory DO levels with most values reported being well
above 5.0 ppm.
NUTRIENTS
The Maryland Department of Water Resources reports above normal
background values for nutrients in the River. Most of the yearly
averages for Total Phosphate were approximately 1.00 mg/1 and Total
-------
IV - 121
Kjeldahl Nitrogen averages ranged from .80 mg/1 to 1.5 mg/1.
Nutrients were reported as being exceptionally high in the water
near Maryland Chicken Processors, Incorporated, where yearly averages
were: Ammonia - 7.52 mg/1; Total Phosphate - 30.0 mg/1; and
Total Kjeldahl Nitrogen - 29.0 mg/1.
Data collected by AFO in 1971 indicated that Total Kjeldahl
Nitrogen (TKN) was the only nutrient parameter which was slightly
above normal in the Pocomoke Sound and its tributaries. About
half of the samples collected in this area had TKN values greater
than 1.00 mg/1. Total Phosphate levels rarely exceeded .500 mg/1
and ammonia levels were predominantly below .100 mg/1.
OTHER
No data on metals or pesticides in the waters of the Pocomoke
has been discovered, but some work has been done on metals in shell
fish. The Maryland Department of Health and Mental Hygiene has
established a program for monitoring copper, zinc, cadmium and mercury
in shell fish with some of the work being done in Pocomoke Sound.
This program is to be continued in conjunction with the administration
of Maryland's food laws and is to be expanded to include pesticide
analyses during fiscal 1972.
-------
IV - 122
Table IV-29
STATE OF MARYLAND
DEPARTMENT OF WATER RESOURCES
WATER QUALITY INVESTIGATION DIVISION
Pocomoke River
Worcester County
Station Location List
STATION
NUMBER
1
2
3
4
5
6
7
8
9
10
STREAM
CODE
POK
POK
POK
POK
POK
POK
POK
POK
POK
POK
MILES ABOVE
MOUTH*
32.6
31.2
31.6
31.0
30.9
29. C
25.5
23.0
19.6
17.5
LOCATION
Pocomoke River at Hallet
Heights (mouth of Purnell
Branch)
Pocomoke River at W. T. Olney
(just south of Md. 12 Bridge-
Plant - effluent about 1/3
mile downstream of bridge)
Bridge on Maryland 12
Pocomoke River at Snow Hill
Sewage Treatment Plant
Pocomoke River at Maryland
Chicken Corporation
Pocomoke River at mouth of
Nassawango Creek
Pocomoke River at mouth of
Corker's Creek
Pocomoke River at Mil burn
Landing
Pocomoke River at mouth of
Dividing Creek
Pocomoke River at Johnson's
NEAREST TOWN
Snow Hill
Snow Hill
Snow Hill
Snow Hill
Snow Hill
Snow Hill
Snow Hill
Pocomoke r^ ty
Pocomoke City
Pocomoke City
Meat Products
-------
Table IV-29 (Cont.)
IV - 123
STATION
NUMBER
11
12
13
14
15
16
STREAM
CODE
POK
POK
POK
POK
POK
POK
MILES ABOVE
MOUTH*
17.1
16.6
16.5
16.0
14.6
11.8
LOCATION
Pocomoke River at Pocomoke
Provision Company (between
old and new bridge)
Pocomoke River at Ralph
Mason Company (water tower)
Pocomoke River at the
Campbell Soup Company (down-
stream of electric tower at
big grey tank with yellow
band)
Pocomoke River at mouth of
Union Branch
Pocomoke River at Puncheon
Landing
Pocomoke River at 2.8 miles
NEAREST TOWN
Pocomoke City
Pocomoke City
Pocomoke City
Pocomoke City
Pocomoke City
Pocomoke City
17
18
19
20
21
22
23
POK
downstream of Puncheon
Landing
9.8 Pocomoke River at 4.8 miles
downstream of Puncheon
Landing
Hall Bridge, Cedarhall Wharf
Road Crossing
Pitt's Creek, Colona Road
Crossing
Town Bridge, Maryland 756
Crossing
Willow Grove Creek, U.S.
113 Crossing
Mattapone Creek, U.S. 113
Crossing
Corker's Creek, U.S. 113
Crossing
Pocomoke City
St. James
St. James
Pocomoke City
Willow Grove
Betheden Church
Betheden Church
-------
IV - 124
Table IV-29 (Cont.)
STATION
NUMBER
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
STREAM
CODE
MILES ABOVE
MOUTH*
LOCATION
Purnell Branch, U.S. 113
Crossing
Pocomoke River, Porter's
Crossing Road
Dividing Creek, River
Road Crossing
Dividing Creek, unnamed
road crossing
Pusey Bridge, Whiteburg
Road Crossing
Dividing Creek, Dentson
Dam Road Crossing
Nassawango Creek, Mt. Olive
Road Crossing
Nassawango Creek, Maryland 12
Crossing
Nassawango Creek, Old Furnace
Road Crossing
Nassawango Creek, Red House
Road Crossing
Nassawango Creek, Nassawango
Road Crossing
Pocomoke River, Whiton
Crossing Road
Pocomoke River, Maryland
374 Crossing
Pocomoke River, Purnell
Crossing Road
Pocomoke River, Logtown
Road Crossing
NEAREST TOWN
Snow Hill
Snow Hill
Pocomoke City
Whiteburg
Whiteburg
Olivet Church
Colburne
Rolling Hills
Furnace
Nassawango Creek
Snow Hill
Whiton
Burbage Crossing
Purnell Crossing
Mt. Pleasant
-------
Table IV-29 (Cont.)
IV - 125
STATION STREAM
NUMBER CODE
39
40
Wicomico County
41
42
43
44
45
46
47
48
Somerset County
49
50
51
MILES ABOVE
MOUTH* LOCATION
Pocomoke River, U.S. 50
Crossing
Pocomoke River, Sheppard
Crossing Road
Pocomoke River, North Folk,
Bethel Road Crossing
Burnt Mill Branch, U.S. 50
Crossing
Gordy's Bridge, unnamed
crossing
Adleurs Pond, Maryland
350 Crossing
Nassawango Creek, Mt.
Herman Road Crossing
(Maryland 350)
Wango Branch, Wango Road
Crossing
Beaverdam Creek, Johnson's
Road Crossing
Horsebridge Creek, Johnson's
Road Crossing
Marimisco Creek, Marimisco
Road Crossing
East Creek, Tulls Road Cross-
ing
Johnson's Creek, Phoenix
NEAREST TOWN
Wil lards
Bethel
Bethel
Willards
Wil lards
Powell vi lie
Wango
Wango
Wango
Wango
Marimisco
Tulls Corner
Bedsworth
Church Road Crossing
-------
IV - 126
Table IV-29 (Cont.)
STATION STREAM MILES ABOVE
NUMBER CODE MOUTH* LOCATION NEAREST TOWN
52 Johnson's Creek, Maryland Hopewell
667 Crossing
53 Pocomoke River, end of Shelltown
Wharf Shelltown
* Based on distance from confluence
-------
IV - 127
Table IV-30
EASTERN SHORE STUDY - AFO
POCOMOKE RIVER
STATION NUMBER LOCATION
1 Porters Crossing
2 Snow Hill
3 Mil burn Landing
4 Pocomoke City
5 Puncheon Landing
6 Rehobeth
7 Cedar Hall Wharf
8 Shell town, Maryland
9 East of Fair Island
10 Opposite Persimmon Point
11 Fair Island Channel
12 Robin Hood Bay
13 Rumbly Point
14 Marumsco Creek
15 Bullbegger Creek
16 Pitts Creek
17 Hoi dens Creek
-------
IV - 128
I. PATUXENT RIVER AREA
The Patuxent River Basin covers an area of 963 square miles,
stretching for 110 miles from the headwaters in upper Howard and
Montgomery Counties, Maryland, to its mouth at Chesapeake Bay. Major
tributaries of the Patuxent are the Little Patuxent and the Western
Branch, with drainage areas of 160 and 110 square miles, respectively.
The three regions of the Patuxent River are:
(1) Upper Patuxent - Frederick County line to Fall Line at Laurel;
Little Patuxent Branch - Frederick County line to Savage,
(2) Middle Patuxent - Fall Line to Queen Anne's Bridge, and
(3) Lower Patuxent (tidal estuary) - Queen Anne's Bridge to mouth
at Chesapeake Bay.
The upper region of the Patuxent River lies entirely in the Piedmont
Plateau geological area, while the middle and lower regions, located
below the Fall Line, lie in the Coastal Plain.
All areas of the Patuxent River are classified as Water Use III
(water contact recreation) and Water Use IV areas (propagation of fish
and aquatic life). In addition, the following areas are designated as
Water Use II areas (municipal water supply): Patuxent River headwaters
to Rocky Gorge Reservoir; middle Patuxent River and tributaries; and
Little Patuxent River and tributaries. Also, the lower portion of the
Patuxent River, from Deep Landing to the mouth of the Patuxent, is
designated as Water Use I area (shellfish harvesting). The most strin-
-------
IV - 129
gent water quality standards in the Patuxent River, those for shellfish
harvesting, call for an average daily dissolved oxygen concentration
of 5.0 mg/1 and a maximum coliform density of 70 MPN/100 ml.
BACTERIOLOGICAL CONDITIONS
At the present time, a severe lack of information exists concern-
ing coliform bacteria concentrations in all areas of the Patuxent
River. This shortage is especially serious in the lower Patuxent
River region where careful monitoring of bacteriological conditions
is essential. Below Deep Landing (River Mile 29.35), a shellfish har-
vesting area, a coliform density of 70 MPN/100 ml must not be exceeded.
Table IV-31 summarizes the most recent coliform concentration data
available.
-------
IV - 130
Table IV-31
PATUXENT RIVER BACTERIOLOGICAL DATA
DECEMBER 15, 1970
RIVER MILE COLIFORM
MPN/100 ml
22.90 39
32.20 1,500
41.75 4,300
45.20 21,000
54.88 24,000
60.74 4,300
63.67 93
63.70 23
66.37 430
71.50 230
75.00 430
80.00 93
-------
IV - 131
From the above data, it appears that the coliform density standard
is upheld in the shellfish harvesting area. The coliform density tends
to decrease as one moves downstream from maximum coliform densities
found at approximately River Mile 50. The extremely high coliform
densities at River Miles 45.20 and 54.88 can be attributed to the large
wastewater outputs from treatment plants at Laurel Parkway (2.60 MGD),
Bowie-Belair (1.90 MGD), and Fort Meade (2.10 MGD). However, 106 acres
(5 public, 101 private acres) are now closed to oyster production out of
a total of 14,804 acres available in the Patuxent River. The closed
areas are located in the lower portion of the Patuxent River and include
Back Creek, Mill Creek, and St. John Creek.
More surveys of the entire Patuxent River Basin need to be made to
determine if current water quality standards are being maintained at the
required levels.
DISSOLVED OXYGEN CONDITIONS
Dissolved oxygen concentrations in the Patuxent River, from River
Mile 19.4 to 60.74, ranged from a high of 7.81 mg/1 to a low of 4.54 mg/1
on September 1, 1970. On September 5, 1968, dissolved oxygen values
ranged from 9.4 mg/1 to 5.5 mg/1 in the same area. The low dissolved
oxygen values noted in September 1970 are partly the result of a high
nitrogenous oxygen demand (NOD) at this time. A maximum TKN value of
1.242 mg/1 was found at River Mile 60.74, resulting in a NOD value of
5.6 mg/1. The dissolved oxygen concentration appears to have degraded
-------
IV - 132
between 1968 anc! 1970, although this may be the result of a low-flow
rate during fall 1970. Insufficient information concerning flow rates
exists in order to make a definite statement regarding dissolved oxygen
concentration trends in the Patuxent River. Table IV-32 presents
a more detailed summary of dissolved oxygen concentrations in the
Patuxent River between 1968 and 1971.
It can be seen that dissolved oxygen values generally are lower in
the upper region of the river, gradually increasing moving downstream.
The higher dissolved oxygen concentrations observed in the spring, as
compared to fall values, are attributed to greater flow rates in the
spring than in the fall. Table IV-33 presents detailed dissolved
oxygen concentration data during the late spring and summer months of
1970. Dissolved oxygen concentrations, with some exceptions, were
generally greater than 5.0 mg/1. However, any degradation of water
quality in the Patuxent River will result in the serious contravention
of the dissolved oxygen standard of 5.0 mg/1.
-------
IV - 133
Table IV-32
PATUXENT RIVER DISSOLVED OXYGEN CONCENTRATIONS
(mg/D
River Mile
19.40
22.90
23.90
25.25
26.65
27.35
29.35
31.85
34.35
38.25
41.45
42.80
44.50
45.20
47.45
54.88
60.74
9/5/68
-
9.4
8.0
-
8.8
8.6
8.2
7.2
7.3
8.0
-
7.8
-
6.4
5.5
-
_
5/13/70
11.87
10.96
-
10.42
-
10.09
-
8.19
-
6.46
6.15
-
-
5.02
5.16
4.98
4.94
9/1/70
4.54
5.35
-
5.62
-
5.85
-
5.35
-
6.58
7.81
-
-
5.38
5.92
5.76
4.97
5/17/71
9.4
9.6
9.8
8.8
8.5
8.8
8.5
9.0
7.0
7.3
7.3
7.7
-------
IV - 13-4
Table IV-33
PATUXEN RIVER DISSOLVED OXYGEN VALUES - 1970
(mg/1)
River Mile
19.4
22.9
25.0
27.3
28.5
31.9
32.2
38.4
41.75
45.20
47.45
48.60
52.50
54.88
60.74
6/11/70
9.63
9.92
9.59
9.27
10.71
7.82
6.27
7.11
8.23
5.27
4.75
5.64
5.53
5.40
4.58
6/29/70
8.13
3.34
9.35
8.36
8.91
7.89
7.73
10.22
9.27
4.91
5.58
5.96
6.19
6.44
6.35
7/27/70
10.10
9.11
12.63
8.05
8.54
8.28
6.43
6.62
6.89
3.84
4.94
5.42
5.96
5.88
5.66
9/1/70
4.54
5.35
5.62
5.85
5.03
5.35
6.37
6.58
7.81
5.38
5.92
5.57
6.11
5.76
4.97
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IV - 135
NUTRIENTS
Recent data indicate that nutrient concentrations in the Patuxent
River have greatly increased in the last few years. A summary of
average nutrient concentrations in 1967 and 1970 is outlined in Table
IV-34.
Table IV-34
PATUXENT RIVER NUTRIENT CONCENTRATIONS
River N02 + N03 as N T. Phosphorus as P04
Mile 1967 1970 1967 1970
(mg/1)
47.45 1.448
54.88
60.74 1.500
In the above region, nitrate-nitrogen (as N) concentrations have
increased an average of 25 percent since 1967, while total phosphorus
(as PO.) concentrations have increased an average of 44 percent from
1967 to 1970. The proceeding observations are based on average nutrient
concentration values obtained by mathematically averaging four to
eight samples taken throughout each year (1967 and 1970).
Table IV-35 (nitrate-nitrogen) and Table IV-36 (total phosphorus
as POj detail nutrient concentration data in the Patuxent River during
the year 1970. It can be seen that both nitrogen and phosphorus con-
centration levels are greater in the upper region of the river, and
gradually decrease downstream. In general, nutrient values are highest
mg/1)
1.569
1.985
2.006
(mg/1)
1.433
2.003
2.487
(mg/1)
2.091
2.753
3.685
-------
IV - 136
Table IV-35
PATUXENT RIVER
+ N03 i
(mg/1)
N02 + N03 as N
River Mile
19.4
22.9
25.0
27.3
28.5
31.9
32.2
38.4
41.75
45.20
47.45
48.60
52.50
54.88
60.74
2/18/70
-
.383
.512
.584
.819
.841
.973
.975
.959
.901
.907
.924
.911
.901
.891
5/13/70
.065
.071
.084
.097
.269
.462
.572
.654
.743
1.070
1.420
1.550
1.490
1.490
1.410
7/27/70
.050
.041
.041
.041
.090
.162
.314
.447
.521
1.031
1.186
1.321
1.748
1.802
1.928
9/1/70
.001
.001
.001
.001
.001
.001
.001
.001
.121
1.350
2.160
2.330
2.550
2.840
2.680
11/23/
-
.141
_
-
-
-
.623
.726
.942
1.240
1.240
1.220
1.270
1.270
1.270
-------
IV - 137
Table IV-36
PATUXENT RIVER
Total Phosphorus as P04 (mg/1)
River Mile
19.4
22.9
25.0
27.3
28.5
31.9
32.2
38.4
41.75
45.20
47.45
48.60
52.50
54.88
60.74
2/18/70
-
.175
.204
.246
.422
.363
.681
.795
1.120
.173
1.540
1.570
1.660
1.660
1.980
5/13/70
.171
.320
.371
.519
.582
.489
.542
.451
.619
1.297
1.643
1.989
2.259
2.141
2.649
7/27/70
.272
.272
.256
.337
.344
.372
.367
.506
.711
1.467
1.111
1.270
1.889
1.556
2.444
9/1/70
.400
.440
.462
.490
.427
.416
.394
.572
.622
1.783
3.765
3.248
3.963
4.128
5.119
11/23//
-
.229
-
-
-
-
.487
.853
1.486
2.422
1.783
1.872
2.202
2.367
3.160
-------
IV - 138
during the fall months and least during the summer. Maximum values
of 2.840 mg/1 and 5.119 mg/1 for nitrate-nitrogen (as N) and total
phosphorus (as PO.), respectively, were found on September 1, 1970.
It appears that nutrient concentrations in the middle and upper regions
of the Patuxent River greatly exceeded the recommended maximum
concentrations of nitrogen (.5 mg/1) and phosphorus (.33 mg/1)
during most of 1970 (Reference 4). These nutrient concentrations
are far above the level that may stimulate excessive algal growth in
the river.
Chlorophyll a_ concentrations provide one means of measuring the
standing crop of algae in a water body. A chlorophyll a_ concentration
greater than 50 ug/1 indicates an algal standing crop of "bloom"
proportions (Reference 4). In the upper region of the river, River
Mile 45.20 to 60.74, chlorophyll ^concentrations during 1970 ranged
from 5.83 to 19.76 mg/1. The absence of excessive algal growths in
the upper Patuxent River is attributed to excessive turbidity in this
area. Large amounts of suspended material in the water limits
light penetration, thereby limiting utilization of available nutrients
and inhibiting the growth of algae. However, several algal blooms
have occurred in the lower Patuxent River. If corrective measures
are not taken, large-scale algal blooms, such as occur yearly in the
Potomac River, could become a fact in the Patuxent River. The in-
creasing nutrient concentrations should be checked by more efficient
wastewater treatment methods in order to prevent nuisance algal growths.
It has been estimated that by 1980, 95 percent of the nitrogen and 96
-------
IV - 139
percent of the phosphorus will have to be removed from wastewater
before discharge in order to meet water quality standards in the
Patuxent River.
HEAVY METALS
No significant surveys of heavy metal concentrations in the Patux-
ent River have been conducted to data. However, present indications
are that the amounts of most metals in the river are either slight
or are comparable to levels in most major rivers in North America. The
only known exception to this is found in the vicinity of Chalk Point
(River Mile 25.0), near the site of the steam electric power plant
which began operation in 1964. High copper concentrations and green-
ing in oysters were found near the cooling water outfall at Eagle
Harbor, 2 miles upstream from Chalk Point. These detrimental effects
were greatest near the outfall, and steadily decreased downstream
from Eagle Harbor. At times, copper levels in oysters taken from the
economically important shellfish harvesting area just south of Chalk
Point have exceeded the recommended limits for human consumption
and have resulted in the loss of commercial oyster sales. The source
of the high copper levels has been attributed to corroding condenser
tubes in the power plant.
-------
IV - UO
The information contained in this chapter has been obtained from the
following sources:
1. Natural Resources Institute, "Patuxent Thermal Studies,"
Summary and Recommendations, January 1969.
2. Governor's Patuxent River Watershed Advisory Committee,
"The Patuxent River, Maryland's Asset, Maryland's Responsibility,"
July 1968.
3. Flemer, D. A., Hamilton, D. H., Keefe, C. W., and Mihursky, J. A.,
Chesapeake Biological Laboratory, "The Effects of Thermal Loading and
Water Quality on Estuarine Primary Production," December 1970.
4. Federal Water Pollution Control Administration, "The Patuxent
River, "Water Quality Management Technical Evaluation, September 1969.
5. Federal Water Pollution Control Administration, "Water Quality
and Pollution Control Study, Patuxent River Basin," CB-SRBP
Working Document No. 15, May 1967.
6. State of Maryland, Department of Water Resources, "Patuxent
River Study," 1970-71.
7. "Patuxent Estuary Study," EPA, AFO, 1970, unpublished.
-------
PATUXENT RIVER BASIN
IV - 1-41
PARKWMT
LEGEND
• -WASTE WATER DISCHARGES
A-ESTABLISHED OAOINO STATIONS
• —WATER SUPPLY INTAKES
T— TEMPORARY GAGING STATIONS
KEY
L W.R. GRACE and CO.
2. JOHNS HOPKINS RESEARCH CENTER
3. PATUXENT WATER SUPPLY (W.S.SC.)
4. MO. and VA. MILK PRODUCERS ASSC.
5. SAVAGE MD. (HOWARD CO.)
6.-8. MD. HOUSE OF CORRECTION WATER SUPPLY
7 MD. HOUSE OF CORRECTION S.T.R
& MD.CITV (ANNE ARUNDELCO.)
10. FT. MEADE WATER SUPPLY
IL FT. MEADE (2)
\Z. LAUREL MD.- PARKWAY (W.S.S.C.)
13. FT. MEADE (I)
K NAVAL ACADEMY DAIRY
15. PATUXENT MD. (ANNE ARUNDEL CO.)
1C. BOWIE-BEL AIR
II ANDREWS AIR FORCE BASE
I*. UPPER MARLBORO
I a WESTERN BRANCH PLANT (W.S.S.C.)
20. PEPCO-CHALK POINT STEAM ELECTRIC PLANT
SCALE
10
IS
20
IN MILES
-------
IV - 142
J. POTOMAC RIVER STUDY AREA
Existing water quality conditions in the Potomac River were
determined for the tidal portion of the River which extends from
Chain Bridge in Washington, D. C., 112 miles southeastward to the
Chesapeake Bay. The tidal portion of the Potomac River is shown
in figure IV-8.
From the Key Bridge vicinity, below the Fall Line, downstream
to the District of Columbia-Prince Georges County (Md.) line, water
quality standards have been established to support the water uses of
recreational boating, maintenance of fish life, and industrial water
supply. From the District of Columbia-Prince Georges County line to
Point Lookout, where the Potomac River discharges to the Bay, water
contact recreation, propagation of fish, other aquatic life and wild-
life, and industrial water supply uses are permitted. Shellfish
harvesting is an allowable use of the Potomac Estuary from Upper Cedar
Point to Point Lookout, except in areas where such use is prohibited
by Maryland and Virginia health officials. The water quality criteria
necessary to support the beneficial water uses in the Potomac Estuary
are listed in Chapter III.
BACTERIOLOGICAL CONDITIONS
The highest fecal coliform densities in the Potomac Estuary are
found in the upper portion of the estuary near Washington. The fecal
coliform standard of 1,000 MPN/100 ml (geometric, mean) established for
-------
POTOMAC ESTUARY
SAMPLING STATIONS
IV -
LEGEND
A MAJOR WASTE TREATMENT PLANTS
• GAGINC STATION
POTOMAC RIVER AT WASHINGTON D.C.
A DISTRICT OF COLUMBIA
B ARLINGTON COUNTY
C ALEXANDRIA SANITARV AUTHORITY
D FAIRFAX COUNTY- WESTGATE PLANT
E FAIRFAX COUNTY- LITTLE HUNTING CREEK PLANT
F FAIRFAX COUNTY—D06UE CREEK PLANT
G WASHINGTON SUBURB SANITARY COMMISSION — PISCATAWAY
H ANDREWS AIR FORCE BASE- PLANTS NO. I AND 4
I FORT BELVOIR—PLANTS NO. I AND 2
J PENTAGON
LEGEND
I KEY BRIDOC
IA FLETCHER'S •OATHOUSC
2 I4TH STREET BRIDGE
3 MAINS POINT
4 BELLEVUC
t WOOOROW WILSON BRIDGE
8 BROAD CREEK
7 PISCATAWAV CREEK
• DOOUE CHEEK
• HALLOWING POINT
10 INDIAN HEAD
II POSSUM POINT
12 SANDY POINT
IS SMITH POINT
14 MARYLAND POINT
15 NANJCMOV CREEK
ISA MATHIAS POINT
16 ROUTE 301 BRIDGE
17 MACHODOC CREEK
IS KETTLE BOTTLE SHOALS
(•A MOUTH OF WICOMICO RIVER
20 KINCOPISCO POINT
21 RAGGED POINT
22 PINEY POINT
23 POINT LOOKOUT
24 SMITH POINT
23 POINT LOOKOUT
29
10
SCALE IN MILES
Figure IV-8
-------
IV - 144
the Key Bridge to the D.C.-Prince Georges County (Md.) line segment was
consistently contravened during 1971 according to sampling data of the
Government of the District of Columbia, Department of Environmental
Services. In the vicinity of Roosevelt Island, the results of samples
taken during the summer months of June, July, and August reveal fecal
coliform densities ranging form a low of 3,300 MPN/100 ml to a high of
350,000 MPN/100 ml, with a mean of about 150,000 MPN/100 ml. The high
densities are attributed mainly to untreated sewage being discharged
into the upper estuary as a result of inadequate sewerage and the
exceeding of capacity at the District of Columbia Water Pollution Con-
trol Plant (Blue Plains).
Fecal coliform densities in the vicinity of Fort Washington show
a decrease from the above figures. From Indian Head downstream to
Maryland Point, the fecal coliform counts are within the standard of
240 MPN/100 ml established for the estuarine reach from the D.C.line
to Upper Cedar Point.
From Upper Cedar Point to the Bay, the Potomac River and its
estuaries are designated shellfish waters. There are currently about
29,000 acres of oyster beds in the Potomac Estuary and its embayments.
For shellfish harvesting, the most probable number (MPN) of coliform
organisms should be less than 70 per 100 ml of sample. Except for
isolated areas, the bacterial quality of these waters remains within
the above limits. These isolated areas are discussed below.
Areas currently closed to shellfish harvesting in Virginia estuaries
-------
IV - U5
of the Potomac are located in King George and Westmoreland Counties and
include portions of Upper Machodoc, Monroe, and Mattox Creeks. Four
of the condemned areas total approximately 1,868 acres of river
bottom out of an approximate total of 15,162 acres. Inadequate waste-
water treatment plants, marinas, subdivision build-up, and human
activities are cited by the Virginia State Water Control Board as
reasons for the closures.
The following oyster bars are prohibited for shellfish harvesting
in St. Mary's County, Maryland:
Breton Bay - 53 acres public, 8 acres private. Order
issued November 1, 1971.
St. Mary's River - 23 acres public. Order issued January
17, 1972.
Neale Sound - 2 acres private. Order issued August 1960.
Upper St. Catherine Sound - 39 acres public, 15 acres private.
Order issued November 1, 1971.
Charleston Creek - Conditions not suitable for prior use as
oyster storage area. Order issued November 1, 1971.
Head of St. Clement Bay - 120 acres public, 23 acres private.
Order issued November 1, 1971.
Canoe Neck Creek - 19 acres private. Order issued November
1, 1971.
St. Patrick Creek - 83 acres private. Order issued November
1, 1971.
The November 1, 1971, closings can be attributed to faulty septic
-------
IV - 146
systems of individual dwellings and present management practices with
regard to livestock. It should be noted, however, that on January 17,
1972, the acreage of oyster bars closed in St. Mary's River was reduced
from 178 to 23 acres by the Maryland Department of Health and Mental
Hygiene as a result of sewage violation corrections.
Bacterial densities in the Upper Potomac Estuary have been
determined routinely by the District of Columbia, Department of
Sanitary Engineering (now Department of Environmental Services),
since 1938. While total coliform counts at Three Sisters Island,
below the Fall Line, have remained fairly constant for the past
20 years at about 2,000 MPN/100 ml during the summer months, the
total coliform density in the estuary increased tc over 2,000,000
MPN/100 ml near the Blue Plains Wastewater Treatment Plant in 1966.
When year-round chlorination began in 1970, the total coliform den-
sity decreased to less than 7,000 MPN/100 ml (Figure IV-9).
Bacterial densities, however, remain high in the estuary along
the Georgetown waterfront due to the overflow of mixed sanitary and
storm sewage from the overloaded sewage treatment system. Figure
IV-10 indicates current fecal coliform densities in the vicinity of
Roosevelt Island. Activations of the Potomac Pumping Station in May
1972 and the closure of the so called "Georgetown Gap" in September 1972
will shift these overflows downstream. By 1973, expansion of the
sewage treatment facilities at Blue Plains should abate the overflows.
Although continuing interim construction will reduce the frequency
of combined sewer overflows, they cannot be completely eliminated until
-------
IV - 147
II- 001 83d)
SMStNVOUO WHQJTOD
(I-CO BUI
SWNWHO HHOfXO
11*001
SHSMRMO mttfioo
Figure IV-9
-------
FECAL COLIFORM DENSITIES
ROOSEVELT ISLAND
IV - 148
100,000 -
10,000 =
2 ^
3 2
o 9
u x
u e
1,000 -
100 -
10
350,000 (MPN)/IOO«I
1971
1969
I I I I I
JAN. FEB. MAR. APR. MAY JUN.
! I I I I
JUL. AUG. SER OCT. NOV.
DEC.
Figure IV-LO
-------
IV - 149
storm and sanitary sewers are separated, perhaps after the year 2000.
A possible alternative to separation is the retention and treatment of
combined system and separate system overflows.
DISSOLVED OXYGEN
The dissolved oxygen (DO) standard extablished for the Potomac
Estuary requires a minimum DO concentration of 4.0 mg/1 with a daily
average of 5.0 mg/1. This standard is maintained in the middle and
lower reaches of the estuary, but is contravened during the summer
months in the upper estuary in the vicinity of the major waste
discharges.
The following DO concentrations represent surface conditions at
sampling stations in the middle and lower portions of the estuary.
Dissolved oxygen concentrations are not seriously affected by waste
discharges in this area.
-------
Table IV-37
IV - 150
STATION
Indian Head
(30.60 mi. below
Chain Bridge)
Smith Point
(46.80 mi. below
Chain Bridge)
U.S. Route 301 Bridge
(67.40 mi . below
Chain Bridge)
Piney Point
(99.20 mi. below
Chain Bridge)
SAMPLING
DATE
6-29-71
7-29-71
8-25-71
9-28-71
6-29-71
8-25-71
9-28-71
6-28-71
7-29-71
8-25-71
9-27-71
6-28-71
8-02-71
8-24-71
9-27-71
WATER TEMPERATURE
°C
28.5
27.3
28.0
23.1
27.8
26.5
24.4
28.3
26.7
27.6
24.1
27.5
26.9
27.2
23.6
DO
mg/1
7.43
4.51
12.25
6.61
4.15
8.50
9.27
8.75
7.95
8.74
7.81
9.04
9.73
7.53
8.45
-------
IV - 151
As indicated above, DO concentrations exceed, for the most part,
the standard of 5.0 mg/1. Only at lower water depths, where reaeration
is restricted by salinity stratification, are depressed oxygen concen-
trations observed.
In the upper reach from Chain Bridge to Indian Head, Maryland, a
total domestic wastewater flow of approximately 325 MGD is discharged
into the upper Potomac estuary. Eighteen facilities currently serve
approximately 2.5 million people in the Washington Metropolitan Area
with the largest facility being the Blue Plains plant of the District
of Columbia (Table IV-38). Of the 325 MGD, 42, 23, and 35 percent come
from Maryland, Virginia,, and the District of Columbia, respectively.
An anlysis of loading trends since 1913 indicates that waste-
water volumes have increased eightfold, from 42 to 325 MGD (Table IV-39)
Of major significance has been the increase in ultimate oxygen demand
(UOD) loadings. The carboaceous UOD increased from 84,000 Ibs/day
in 1913 to about 297,000 Ibs/day in the late 1950's. With the con-
struction of secondary treatment facilities, including completion of
the Blue Plains plant of the District of Columbia, the carbonaceous
loading was reduced to 110,000 Ibs/day. The nitrogenous loading
has increased steadily from 1913 to the present loading of 254,000
Ibs/day which exceeds the current carbonacous loading of 204,000
Ibs/day. This results in a total oxygen demand loading of over 450,000
Ibs/day. The instream oxidation of this load results in low DO con-
centrations, often less than 1.0 mg/1 during the summer (Figure IV-11).
Interim chemical treatment to reduce the biochemical oxygen demand,
-------
IV - 152
suspended solids, and phosphorus in the Blue Plains effluent is
scheduled to begin in June 1972.
As shown in Figures IV-11 and IV-12, the most seriously depressed
oxygen concentrations occur in the vicinity of the Woodrow Wilson
Bridge, 12.1 miles below Chain Bridge, downstream from the Blue Plains
plant, the major waste discharge source in the upper estuary.
Under varying flow conditions dissolved oxygen levels remain depressed,
indicating that high water temperatures during the summer have a
greater influence than freshwater inflow on the ability of the upper
estuary to retain dissolved oxygen. While freswater inflows have
been more uniform in recent summer months, the loadings requiring in-
stream oxidation have increased each year. This is evident by the
fact that since 1960 the increase in wastewater volumes and the continued
increase in nitrogenous UOD have resulted in a total oxygen demand-
ing load to the estuary similar to that which occurred before the
secondary treatment facility was completed in the late 1950's.
There are 82 wastewater point source discharges into the mid-
dle and lower reaches of the Potomac Estuary and their tributaries.
The estimated BOD, total phosphorus as P, and nitrogen as N are 4,000,
500, and 1,000 Ibs/day, respectively. Although the discharges appear
numerous, the dissolved oxygen standard is maintained in this portion
of the estuary as manifested by the data set forth earlier in this re-
port.
NUTRIENTS
While bacterial densities and dissolved oxygen concentrations
-------
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-------
Ta 1< IV-39
PRESENT WASTEWATER LOADINGS
WASHINGTON i.JJTROPOLITAK AREA
a
•H OJ ^ t> ^1 TN O ^
22$ 3 tf 8 8 B
° -j-U] O O O O O
i> Sn rH
Cu i i ^— '
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d) Qj \, >fr 00 -* O
II S -*" "4
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•n m p>
P.QO O ~J- O cr\ O
OiejT) OJ rH OJ O OJ
° j>m O O O o' o'
fH Q f
01 O rH
-P o? Q Q O irv O
01 IT TJ O O "^ OJ O
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•P O
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OJ T3 O 0^ 00 O °0
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f^ ~£
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VD -4- o ->*•
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Fairfax-Hunting Creek 3
Fairfax -Dogue Creek 2.
Fort Belvoir No. 1 0.
Fort Belvoir No. 2 2
Fairfax-Lower Potomac***
o r-o o^ o
OJ Q to O
O O O »r\
O 0 O 0
O O «A iTv r\
VD o r^ o
O rH O OJ
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Naval Ordnance Station
Indian Head
Site I 0
Site II 0
Site III 0.
Site IV 0.
TOTALS 325.
* Based on 100 gpcpd
** Based on dry weather flow to
*** Under construction
-------
io H
IV - 155
8 -
6 -
4 -
2 -
TIME PERIOD
SEPT. 10-15. 1965
FLOW s 970 cfs
TEMP. = 24.5* C
to
i
15
l
20
I
25
l
30
I
35
I
40
T
45
T
50
6
ci
10 H
8 H
6 H
4 H
2 H
TIME PERIOD
SEPT. 7- 13, 1966
FLOW= 185 cfs
TEMP. = 27.0'C
10
15
20
i
25
30
I
35
40
1
45
I
50
10 H
8 H
6 -\
4 H
2 -\
TIME PERIOD
SEPT. 20-21. 1967
FLOW =1,800 cfs
TEMR= 22.0* C
i i i i ii 1 1 i i
5 10 15 20 25 30 35 40 45 50
MILES BELOW CHAIN BRIDGE
Figure IV-11
-------
10 -
8 -
6 -
4 -
2 -
IV - 156
TIME PERIOD
AUG. 19-22, 1968
FLOW = 2,800 cfs
TEMR = 27.5"C
l
10
15
T
20
\
25
T
30
T
35
T
40
I
45
T
50
6
Q
10 -
8 -
6 -
4 -
10 -
8 -
6 -
4 -
2 -
TIME PERIOD
OCT. 16, 1969
FLOW = 2,200 cfs
TEMP = 19.0* C
2 -
v — s
T 1 1 1 1 1 1 1
0 5 10 15 20 25 30 35
40 45 50
TIME PERIOD
SEPT. 28-30,1970
FLOW= 1,480 cfs
TEMR=25.5'C
I T T I I I I I
5 10 15 20 25 30 35 40
MILES BELOW CHAIN BRIDGE
45 50
Figure IV-12
-------
IV - 157
remain as water quality problems in the Potomac Estuary, nutrient in-
puts to the estuary are also incluencing a great portion of the estuary.
Detailed analyses of the freshwater inflow from the upper Potomac
River Basin at Great Falls, Maryland, were conducted during the period
from June 1969 to August 1970 to determine the nutrient contribution
of the water entering the tidal system. Based on average monthly
flows for the 15-month study period, the results were as follows:
Parameter
Monthly Average
TP04 as P04
P (Inorganic)
TKN as N
N02 + N03 as N
NH3 as N
TOC
(Ibs/day)
23,000
9,900
35,000
57,000
6,000
267,000
Percent Contribution to Bay
(TbsTdaT]
33%
27%
23%
25%
27%
The percent of nutrient input to the Chesapeake Bay and its tidal
estuaries by the Potomac River is based on a study of the nutrients
contributed from the following rivers: Susquehanna, Rappahannock, Pa-
munkey, Mattaponi, James, and Chickahominy. The Potomac is the second
largest contributor of nutrients to the Bay, outranked only by the
Susquehanna River.
The major sources of nutrients in the Potomac Estuary are the
Washington Metropolitan Area wastewater discharges. Under low-flow
conditions, approximately 90 percent of the nitrogen and 96 percent of
the phosphorus are from treated waste effluents. At median freshwater
-------
IV - 158
inflows, approximately 60 to 82 percent of the nitrogen and phosphorus,
respectively, are from these wastewater discharges.
The total phosphorus from wastewater discharges has increased
about 22-fold, from 1,100 Ibs/day in 1913 to 24,000 Ibs/day in 1970,
while total nitrogen loadings have increased from 6,400 to 60,000
Ibs/day. The greater increase of phosphorus reflects not only an
increase in population but also the increased use of detergents. The
current carbon loadings are about 100,000 Ibs/day, approximately the
same as they were in the mid-1940's.
The concentrations and forms of phosphorus and nitrogen in the
Potomac Estuary area are a function of wastewater loadings, temperature,
freshwater inflow, and biological activity. As shown in Figure IV-13,
inorganic phosphorus concentrations varied considerably, at the six
stations sampled, from March 1969 through September 1970. The concen-
tration at Hains Point, located at the upper end of the tidal excursion
of the major wastewater discharges, was fairly uniform, averaging about
0.3 mg/1 during 1969 and 1970. The data for 1971 show an average of
about 0.4 mg/1 in this area. At Woodrow Wilson Bridge, located below
the Blue Plains wastewater discharge, the inorganic phosphorus concen-
tration increased appreciably with concentrations over 2.5 mg/1 during
periods of low flow such as those that occurred in the period July to
October 1969 and September 1970. The remaining four downstream
stations had inorganic phosphorus concentrations progressively smaller.
The total phosphorus concentration closely parallels that of
inorganic phosphorus. In the upper reach, the ratio of total phosphorus
-------
IV - 159
INORGANIC PHOSPHATE CONCENTRATION as
POTOMAC ESTUARY
M9-BT7D
JAN FEB.
MAINS POINT
MILES BELOW CHAIN BODGE * 7.M
JW. AUG. SEP.
a«-
12-
10-
28-
2.6-
2A~
22-
20-
12 -
10-
oe-
(Xfi-
tt4-
02-
WOODROW WILSON BRIDGE
MILES BELOW CHAM BRIDGE = 12.10
T—-—i———i———r
JAN FEB
MAY JUN. JUL AUG
OCT NOV. DEC JAN. FEB.
W69 i—l-» 1970
APR. ' MAY ' JUN. ' JUL. ' AUG.
U -
12-
LO -
c
0.4-
IND1AN HEAD
MILES BELOW CHAIN BRIDGE = 30.60
FEB. MAR APR
JUN ' JUL. AUG SEP OCT. MOM DEC JAN. ' FEB.
APR. ' MAY ' JUN. ' JUL. ' AUG.
SMITH POINT
MILES BELOW CHAIN BRIDGE = 46.80
APB. MAY JUN. JUL. AUG SEP. OCT. NOV. DEC
301 BRIDGE
MILES BELOW CHAIN BRIOGE = 67.40
MAY JUN. JUL. MJG. SEP. OCT. NCW DEC JAN. FEB.
PINEY POINT
MLES BELOW CHAM BffiDGE -. 9020
MAY JUN. JUL AUG. ' SEP. r OCT. NOV. ' DEC I JAN. F
APR. ' MAX
Figure IV-13
-------
Li -
ts-
L4-
1.0 -
=,-
0.3-
02-
ai -
MAINS POINT
ML£S BEU3W CHAIN BROGE < 740
NITRATE and NITRITE NITROGEN as N
POTOMAC ESTUARY
069-1970
IV - 160
JAM. TO
APR MAY JUN. JUL
OCf NOV
APR. MW JIM JUL
zs-
2.0-
16-
J">-
04-
04-
O2-
WOODROW WILSON BRIDGE
ML£S MLOW CHAIN BRIDGE & 12-10
AWI ' MM F JIM ' JUL. ' AUG. ' XR T
ae-
05-
JAN FEB MA* APR MAV JUN JUL AUG 5EI
INOIAN HEAD
MILES BELOW CHAIN BRIDGE = 30.60
JAN. FIB MAR
JIM. JUL AUG
OCT NOV
DEC I Ji
m» i I i tq
AUG SEP
SMITH POINT
MILES BELOW CHAIN BRIDGE * 46.80
0-3-
0.2-
01 -
JAN. FU
JUN JUL AUG S£P
U -
to-
CL8-
0.6-
r °-7"
' QJ>-
05-
a4-
OJ-
02-
ai -
301 BRIDGE
MILiS BELOW CHAIN BRDGE « 87.40
0 '-
QO-
JAN FEB. MAA APR. MAY JUN
RNEY POINT
MILES BELOW CHAW BRIDGE - 99.20
FO. MMt APR.
JUN. JUL.
AUG. Sff.
Figure IV-14
-------
AMMONIA NITROGEN « N
POTOMAC ESTUARY
low-WTO
IV - 161
HAMS POKT
MLES mOH CHAIN WOOE » 740
' ' ' ' ' '
' ' ' '
OCT. im DEC. wi
WOOOROW WILSON BRIDGE
MLES BOON CHAIN BRCGE • E.IO
OCT. NOT DEC I Mi FO.
INDIAN HEAD
MLES BELOW CHAIN BRIDGE * 3040
OCT. NOV DEC. I JAN. FEB.
SMITH POINT
MILES BELOW CHAM BRIDGE * 40.80
APR. ' tux ' ~JM. '
. ' OCT. NO* OCC JAN. FEB. MM) ' APS ' MAV ' JUN
301 BRIDGE
MLES BEICW CHAN 9ROGE • 67.40
MA. JUL. ' AUO. '
OCT NOV. ' DEC I JAN. FTB
WNEY PONT
MLES BELOW CHAM MDGC •
SCK OCt NOV. DEC. JAM. FEB.
APR. UAY JUN. JUL AUG SEP.
Figure IV-15
-------
IV - 162
to inorganic phosphorus ranges from 1.1 to 1.5. The ratio is higher
in the middle reach, normally varying from 1.5 to 2.0 with the ratio
in the lower reach having a range of approximately 2.0 to 2.5.
The concentration of nitrite (NO^) and nitrate (N0j nitrogen
at Mains Point and Woodrow Wilson Bridge varies almost inversely with
that of phosphorus (Figure IV-14). The NOp+NO, concentration was highest
in July and August 1969 and during the spring months of 1970. The in-
crease of N0p+N03 at Indian Head, as compared to Woodrow Wilson Bridge
in May-June 1969, September-November 1969, and July 1970, was a result
of the conversion of ammonia from the wastewater treatment plant dis-
charges to NO.,. The extremely low concentrations of N02+N03 in the
summer months at Smith Point was caused by uptake by algal cells. Dur-
ing winter months algal utilization is lower, thus the concentrations
of nitrates are high, as in January and April 1970. At Piney Point,
concentrations of N02+N03 were usually less than 0.1 mg/1 during 1969,
1970, and 1971.
The concentration of ammonia nitrogen is also affected by flow
and temperature conditions. Although large quantities of ammonia are
discharged into the Potomac near Woodrow Wilson Bridge from wastewater
treatment facilities, the ammonia at Indian Head during the summer
months is low because of nitrification.
During the summer and early fall months, the average ranges of
pH, alkalinity, and free dissolved C02 (measured by titration) for the
five stations in the upper and middle reaches were:
-------
IV - 163
pH
limits)
7.5
7.0
7.2
7.5
7.5
- 8.0
- 7.5
- 8.0
- 8.2
- 8.0
ALKALINITY
(mg/1
80
90
70
60
65
as CaCO-J
- 100
- no
- 90
- 85
- 85
C00
(mg/T)
2
8
6
2
7
- 4
- 12
- 10
- 8
- 8
Table IV-40
FREE DISSOLVED
LOCATION
Chain Bridge
W. Wilson Bridge
Indian Head
Maryland Point
Rte. 301 Bridge
In the vicinity of the Woodrow Wilson Bridge, the increase in
both alkalinity and C0? with a corresponding decrease in pH is attributed
to wastewater discharges. The decrease in both alkalinity and C0? with
a corresponding increase in pH at the Indian Head and Maryland Point
stations is due to algal growths. In the lower estuary, the increased
alkalinity and C0? values and decreased pH values are caused by the
smaller algal standing crops in this area.
HEAVY METALS
Recent detection of heavy metals in sediments of the Potomac
River Estuary has raised sufficient concern to include the accumulation
of metals as a water quality problem requiring additional study and
analysis.
A cooperative program of the Annapolis Field Office and the U.S.
Naval Ordnance Station laboratory in Indian Head, Maryland, was initi-
ated to determine the occurrence of heavy metals in the Potomac Estuary
and bottom sediment Sediment analyses were made during August and
-------
IV - 16/i
September 1970, and again in April 1971. While small concentrations of
zinc and manganese were detected in the overlying waters of the estuary,
considerable amounts of various heavy metals were found in the sediment
by acid extraction determination.
From the sediment analyses presented on the following pages it is
evident that the concentrations of lead, cobalt, chromium, cadmium,
copper, nickel, zinc, silver, barium, aluminum, iron, and lithium in
the upper estuary in the area immediately above the Woodrow Wilson
Bridge are greater than the metal concentrations measured above and
below this area. Of the metals measured in April 1971, all showed in-
creases in concentrations in this area but the concentrations were
lower than those detected in August and December of 1970.
At Possum Point and the Route 301 Bridge, 38.0 and 67.4 miles
below Chain Bridge, respectively, the incidence of metals in the
sediment again increased significantly. While there were increases
in the qua!tities of most metals at the two sampling stations, the
following showed the greatest increased concentrations when compared
to the initial determinations made in August 1970: barium, lead, iron,
strontium, lithium, cobalt, magnesium, chromium, nickel, and potassium.
At the Route 301 Bridge sampling station, copper showed a sharp increase
in April 1971, to 731 ppm, while at Possum Point the April 1971 amount
was lower than that of December 1970.
Although mercury is not included in the data set forth at the end
of this section, sediment samples were analyzed for mercury. The con-
centration of mercury was found to be below the detection limit in
-------
IV - 165
practically all samples analyzed. Exceptions were noted at Piscataway
Creek, Hallowing Point, Indian Head, Possum Point, and Sandy Point
during December 1970, at which time the concentrations measured were
26.2, 5.0, 5.0, 5.6, and 4.7 ppb, respectively.
Arsenic, antimony, boron, bismuth, lanthanum, molybdenum, selenium,
tin, and zirconium were included in the list of metals to be measured.
However, the concentration of these metals was found to be below the
detection limit in all samples.
Heavy metals in the Potomac Estuary are chemically bound in bottom
sediment and require heat and an acid-induced low pH in the laboratory
procedure employed to extract them from the sediment samples. These
metals, and the possibility of their remineralization into the over-
lying water, must be considered in the disposal of dredged spoil. Dredg-
ing operations involving deepening and widening of the channels near
Washington, construction of piers and marinas, etc., disturb the
sediments and require disposal of the dredged spoil. Should dredged
material containing high concentrations of potentially toxic metals
be deposited in open waters of the estuary during high-flow conditions,
colloidal suspension of the fine clay sediments with adsorbed metals
could be transported downstream to economically important shellfish
growing areas. The metals could then be taken up by filter-feeding
organisms which pump water through their digestive systems with probable
accumulations of metals occurring in these organisms.
A more detailed report entitled "Heavy Metals Analyses of Bottom
Sediment in the Potomac Estuary", which discusses possible sources of
-------
IV - 166
5ooo r
40001—
(3
I
sooo f--
20001—
1000 h-
CALCIUM
- • Augutt '70
-O December '70
9085 ppm
10
20
30
50 60
Miles Below Chain Bridge
90
100
10001
800
BARIUM
— • August'70
O Decernber '70
600
I
400
200
_L
_L
I
10 20 30 40 50 60
Miles Below Chain Bridge
70
80
90
100
Figure IV-16
-------
IV - 167
100
80
60 -
40
20
731 ppm
COPPER
— —-. • August '70
.. O December '70
-—^T.4 April'71
10 20 30 40 50 60
Miles Balow Chain Bridge
70
80
90
SILVER
— — — • August '70
—— O December '70
10 20 30 40 50 60
Miles Below Chain Bridge
70
80
90 100
Figure IV-17
-------
IV - 168
10
B
8
7
6
CD
°- 5
IRON
•• August '70
-O December '70
I
J_
\
10 20 30 40 50 60
Below Cham Bridge
70
30
90
100
?00
180
160
140
120
i
MOO
L
80
60
40
20
0
LEAD
• August '70
——— O December '70
A April '71
^_ /
f
10
20
30
40 50 60
Miles Below Chain Bridge
80
90 100
Figure IV-18
-------
500
400
STRONTIUM
•—• Auguit '70
— O December '70
IV - 169
300
200
100
10 20 30 40 60 60
Mile* Below Chain Bridge
70 80 90 100
50
40
LITHIUM
• • August '70
-O December '70
30
20
10
I
I
10 20 30 40 SO 60
Miles Below Chain Bridge
70 80 90 100
Figure IV-19
-------
IV - 170
30
20
10
COBALT
Auguil '70
December '70
I
I
•»
_J
10
20
30
40
50 60
*r Cham Bridge
70
80
90
100
10,000
8,000
f
6,000
4,000
2,000
MAGNESIUM
• August'70
—— O December '70
V
_L
I
I
100
10 20 30 40 60 60
Mitel below Chain Bridge
70
80
90
Figure IV-20
-------
IV - 171
6000
4000
c
3000
2000
1000
MANGANESE
— — — • August '70
O December '70
I
10 20 30 40 50 60
MilAL BfttaMfcCfctti* ttudtti
70
80
90
100
ALUMINUM
•—— • August '70
— " O December '70
10 20 30 40 50 60
Mils* B^pf Chain
70
80
90
100
Figure IV-21
-------
IV - 172
4000
3000
|2000
a
1000
POTASSIUM
- • August '70
- O December '70
--i ----- r
10
20 30
40 50 60
Miles Below Chain Bridge
70 80 90 100
1000
800 -
600
400
200
ZINC
• August'70
——— O December '70
A April'71
10 20 30 4ff 50 60
Milts Below Chain Bridge
70 80 90 100
Figure- IV-22
-------
IV - 173
100
80
60
40-
20-
VANADIUM
•—•• AIIQIIII '70
— O December '70
—-A April '71
10 20 30 40 50 60
Miles below Chain Bridge
70
80
90
100
CADMIUM
—— — • August'70
——— O December '70
-—-A AprH'71
10
20
30
40 60 60
Miles Below Chain Bridge
70
80
90
100
Figure IV-23
-------
ioor
so
60
u
40
20i
IV - 174
rHUOMIlIM
-• Auyubt '70
-O December '70
-A April '71
0
1
10
1
20
1
30
1
40
1
50
1
60
70
80
90
V
100
Chain Bridge
NICKEL
• August '70
O December '70
A April '71
20
30
40 50 60
Miles Below Cham Bridge
70
80
90 100
Figure IV-24
-------
IV - 175
heavy metals in the bottom sediment and recommends further studies,
is available from the Annapolis Field Office of EPA, Annapolis, Maryland.
CHLORINATED HYDROCARBON PESTICIDES
During August 5 to 11, 1969, samples obtained from six stations
in the Potomac Estuary and a 24-hour composite sample of the final
effluent from the Blue Plains Vlastewater Treatment Plant were analyzed
for pesticides. The estuary stations sampled are as follows:
STATION
Chain Bridge
Arlington Memorial Bridge
Woodrow Wilson Bridge
Piscataway
Indian Head
U. S. Route 301 Bridge
MILES FROM CHESAPEAKE BAY
106.5
100.7
94.4
89.0
77.5
46.3
The pesticide compounds for which the samples were analyzed and
the minimum detectable concentrations for each are presented in Table
IV-41.
None of these compounds were detected in any of the six estuary
samples or in the 24-hour composite of the final effluent from the
Blue Plains facility.
Since there is considerable agricultural use of insecticides
and herbicides within the Potomac River Basin at certain times of the
year, and because of the limited data available, further surveys to
include those seasons of use are needed.
-------
IV - 176
Table IV-41
PESTICIDES ANALYZED AND
MINIMUM DETECTABLE LIMITS
COMPOUND MINIMUM DETECTABLE CONCENTRATION
ng/1*
Dieldrin 5
Endrin 5
DDT 10
DDE 5
Heptachlor 5
Heptachlor Epoxide 5
Aldrin 5
BHC 5
Endosulphan 5
Chlordane (Tech.) 25
Toxaphene 1,000
Methoxychlor 25
* ng/1 = nanograms/liter
-------
IV - 177
WATER QUALITY TRENDS
The Potomac tidal system is saline in the lower reach with the
middle reach brackish and the upper reach fresh water. These differ-
ences in salinity as well as nutrient enrichment by wastewater discharges
have a pronounced effect on the ecology of the estuary. Under summer
and fall conditions, large populations of blue-green algae (a pollution
tolerant phytoplankton), mainly Anacystis sp. are prevalent in the
freshwater portion of the estuary. Large standing crops of this alga
occur, especially during periods of low flow, forming green mats of
cells. The blue-green algae are apparently not readily grazed by the
higher trophic forms and therefore are often considered a "dead end"
of the normal food chain.
The large populations of blue-green algae have been observed from
Woodrow Wilson Bn'dge dcwnstream to Potomac River Route 301 Bridge
during the months of June through October. In September of 1970, after
a period of low-stream flow and high temperatures, the algal mats
extended upstream beyond Hains Point and included the first nuisance
growth within the Tidal Basin. The effects of the algal blooms in the
middle estuary are (1) an increase of over 490,000 Ibs/day in total
oxygen demand, (2) an overall decrease in dissolved oxygen due to
algal respiration in waters 12 feet and greater in depth, (3) creation
of nuisance and aesthetically objectionable conditions, and (4) re-
duction in the feasibility of using the upper estuary as a potable
water supply source because of potential toxin, taste, and odor problems.
-------
IV - 178
In the saline portion of the Potomac Estuary, the algal popu-
lations are not as dense as in the freshwater portion. Nevertheless,
at times large populations of marine phytoplankton, primarily the
algae Gymnodinium sp., Massartia sp., and Amphidin^um sp., occur
producing massive growths known as "red tides."
On February 28 and 29, and March 1, 1972, Dr. Donald Lear,
Annapolis Field Office, observed extremely widespread "red tides"
in the Lower Potomac Estuary. In Neale Sound, behind Cobb Island
at the mouth of the Wicomico River, in Charleston Creek (a tributary
to the Wicomico River), the Wicomico River itself, St. Catherine's
Sound, Whites Neck Creek (tributary to St. Catherine's Sound), the
Potomac River itself in this area, Dukeharts Channel, St. Clements
Bay, St. Patrick Creek, Canoe Neck Creek, and the Potomac River in
the vicinity of Piney Point (about 15 or 20 miles downstream) all
showed evidence of red tide conditions. Dr. Lear reported that water
temperature at the time of the observations was 10 to 12°C and that
the causative organism was presumably due to the phytoplankter Massartia.
This organism is not uncommonly encountered in the lower Bay in late
summer and early fall, but is always associated with warm water conditions,
In the winter of 1971, a few blooms of Massartia were recorded in the
vicinity of Morgantown and in the reaches immediately adjacent to the
Morgantown area. The 1^71 blooms were few and remarkable because they
had not been noted before.
-------
IV - 179
The effect of the increases in nutrient loadings from wastewater
since 1913 on the dominant plant forms in the upper estuary has been
dramatic (Figure IV-25). Several nutrients and other growth factors
have been implicated as stimulating this, with nitrogen and phosphorus
showing promise of being the most manageable.
The historical plant life cycles in the upper Potomac Estuary can
be inferred from several studies. Gumming [1] surveyed the estuary
in 1913-1914 and noted the absence of plant life near the major waste
outfalls with "normal" amounts of rooted aquatic plants on the flats
or shoal areas below the urban area. No nuisance levels of rooted
aquatic plants or phytoplankton blooms were noted.
In the 1920's, an infestation of water chestnut appeared in the
waters of the Chesapeake Bay including the Potomac Estuary. This
infestation was controlled by mechanical removal [2].
In September and October 1952, another survey of the reaches
near the metropolitan area made by Bartsch [3] revealed that vegetation
in the area was virtually nonexistent. No dense phytoplankton blooms
were reported although the study did not include the downstream areas
where they were subsequently found.
In August and September 1959, a survey of the area was made by
Stotts and Longwell [4]. Blooms of the nuisance blue-green alga
Anacystis were reported in the Anacostia and Potomac Rivers near
Washington.
In 1958 a rooted aquatic plant, water milfoil, developed in the
Potomac Estuary and created nuisance conditions. The growth increased
-------
IV - 180
*D Noaavo oiNvoao
u.
U-
LJ
(J
O
3
o
o
UJ 5
o
z
u
a:
z
UJ
LJ
UJ
Ct
I-
tr
LU
LJ
CO
o
6
N *D N39OH1IN 1V1O1
(
-------
IV - 181
to major proportions by 1963, especially in the embayments from Indian
Head downstream [5].
These dense strands of rooted aquatic plants, which rapidly in-
vaded the stream, dramatically disappeared in 1965 and 1966. The
decrease was presumably due to a natural virus [6],
Subsequent and continuing observations by the Annapolis Field
Office have confirmed persistent massive summer blooms of the blue-
green alga Anacystis in nuisance concentrations of greater than
50 yg/1 from the metropolitan area downstream at least as far as
Maryland Point [7]. Chlorophyll a_ determinations (a gross measure of
algal standing crop) in the upper reach and in the middle and lower
reaches of the Potomac Estuary are presented in Figures IV-26 and
IV-27, respectively.
Chlorophyll a_ at Indian Head and Smith Point for 1965-1966 and
1969-1970, as presented in Figures IV-26 and IV-27 respectively,
indicate that algal populations have not only increased in density but
have become more persistent over the annual cycle. At both stations,
higher values of chlorophyll were measured during the 1969-1970 sampl-
ing cruises. The occurrence of a spring bloom of diatoms was observed
in 1969 and 1970. This had not been observed during the 1965-1966 cruises,
These biological observations over the years appear to indicate
a species succession. The initial response to a relatively light
overenrichment [2] was the growth of water chestnut which, when removed,
allowed the increasing nutrient load to be taken up into the rooted
aquatic plant, water milfoil (Myrioph.yllum spicatum). The die-off of
-------
MAINS POINT
ML£S BELOW CHAW BROGE = 7.6O
CHLOROPHYLL a
POTOMAC ESTUARY
UPPER REACH
IV - 182
MAR APR. MAV JIN. JUL AUG. SEP OC
JUR JUL. AUG. SEP
PISCATAWAY CREEK
MILES BELOW CHAIN BRIDGE = 18.35
JUN JUL. ' AUG. ' SEP.
INDIAN HEAD
MILES BELOW CHAIN BRIDGE = 30.60
JUN. JUL. AUG. SEP. OCX MK D&. I JAN.
MW ' JUN. ' "ML. "" AUG. ' S0>. '
Figure IV-26
-------
SMTTH PONT
MLES BELOW CHAM BMOGE > 4640
CHLOROPHYLL a
POTOMAC ESTUARY
MODLE tut LOWER REACH
iX
IV - 183
AUG. iff. OCT.
DEC JAN. FES.
JUN. JU.. AUG. SEP.
3(» BRIDGE
MLES BELOW CHAM BRIDGE * S7.40
JAN m. MAfi AMI MW JIM. Juu
3£P. OCT NW
' «' 1
nm •«-(-»
JAN. FEB.
WO
JUN. JUL. AUG. SCR
WNEY POINT
MLES BELOW CHAM BRIDGE = 99.20
JAM ' FEB.
IV-27
-------
IV - 184
water milfoil then allowed the nutrients to be competitively selected by
the blue-green alga Anacystis. Since Anacystis is apparently not uti-
lized in the normal food chain, huge mats and masses accumulate, die
off, and decay.
From the above considerations, it would appear that nuisance
conditions did not develop linearly with an increase in nutrients.
Instead, the increase in nutrients appeared to favor the growth and
thus the domination by a given species. As nutrients increased further,
the species in turn was rapidly replaced by another dominant form. For
example, water chestnut was replaced by water milfoil which in turn
was replaced by Anacyctis.
Figure IV-25 indicates that the massive blue-green algal blooms
were associated with large phosphorus and nitrogen loading increases
in the upper reaches of the Potomac River tidal system. The massive
algal blooms have persisted since the early 1960's even though the amount
of organic carbon from wastewater discharges has been reduced by almost
50 percent.
Laboratory and controlled field pond studies by Mulligan [8] have
shown similar results. Ponds receiving low-nutrient additions (phosphor-
us and nitrogen) contained submerged aquatic weeds. Continuous blooms
of algae appeared in the ponds having high nitrogen and phosphorus
concentrations. An important observation in Mulligan's studies was
that when the water quality was returned to its original state by re-
duction of nutrient concentrations, the ecosystem also reverted to its
previous state. This observation was also supported by studies of Ed-
-------
IV - 185
mondson [9] on Lake Washington and Hasler on the Madison, Wisconsin
lakes [10].
-------
IV - 186
REFERENCES
1. U. S. Public Health Service, "Investigation of the Pollution
and Sanitary Conditions of the Potomac Watershed," Hygienic
Laboratory Bulletin No. 10U, Treasury Department, February 1915-
2. Livermore, D. F. and W. E. Wanderlich, "Mechanical Removal of
Organic Production from Waterways, " Eutrophication: Causes,
Consequences, Correctives,1' National Academy of Sciences,
3. Bartsch, A. F., "Bottom and Plankton Conditions in the Potomac
River in the Washington Metropolitan Area," Appendix A, A report
on water pollution in the Washington metropolitan area, Interstate
Commission on the Potomac River Basin, 195^--
h-. Stotts, V. D. and J. R. Longwell, "Potomac River Biological
Investigation 1959>" Supplement to technical appendix to Part VII
of the report on the Potomac River Basin studies, U. S. Department
of Health, Education and Welfare, 1962.
5. Elser, H. J., "Status of Aquatic Weed Problems in Tidewater Maryland,"
Spring 1965 , Maryland Department of Chesapeake Bay Affairs, 8 pp
mimeo, 1965-
6. Bayley, S. H. Rabin, and C. H. Southwick, "Recent Decline in the
Distribution and Abundance of Eurasian Watermilfoil in Chesapeake
Bay," Cioesapeake_Sci_ence, Vol. 9, No. 3, 1968.
7. Jaworski, N. A., D. W. Lear, Jr., and J. A. Aalto, "A Technical
Assessment of Current Water Quality Conditions and Factors Affecting
Water Quality in the Upper Potomac Estuary," CTSL, FWPCA, MAR,
U. S. Department of the Interior, March 19o9- (No_w Annapolis Field
Office, Region III, Environmental Protection Agency)
8. Mulligan, H. T., "Effects of Nutrient Enrichment on Aquatic Weeds
and Algae," The Relationship of Agriculture to Soil and Water Pollution
Conference Proceedings, Cornell University, January 1970.
9. Edmonson, W. T., "The Response of Lake Washington to Large Changes
in its Nutrient Income," International Botanical Congress, 1969.
10. Hasler, A. D., "Culture Eutropni cation is Reversible," Bioscience,
Vol. 19, No. 5, May 1969.
-------
IV - 187
K. RAPPAHANNOCK RIVER AREA
The tidal effects on the Rappahannock River extend for ap-
proximately 110 miles, up to the Fall Line, in the vicinity of
Fredericksburg, Virginia. The total drainage area of the Basin
is 2,715 square miles. The major industry in the tidal area is the
American Viscose Division, FMC Corporation, at Fredericksburg.
Water uses assigned to the Rappahannock Estuary are primary
contact recreation (prolonged intimate contact; considerable risk
of ingestion); propagation of fish, shellfish, and other aquatic life;
and other beneficial jses. The uses are protected by Class II stan-
dards, including bacteriological standards for primary contact rec-
reation and shellfish uses. The standards are delineated in the ap-
propriate section of this chapter.
BACTERIOLOGICAL CONDITIONS
Degradation of bacteriological conditions in the Rappahannock
Estuary can occur downstream of the City of Fredericksburg during
low-flow periods as a result of secondary treated wastes discharged
by the City and the FMC Corporation. The bacterial quality varies
with river flows and tides. For the lower range of flows (less than
500 cfs), when freshwater inflow is insufficient to overcome tidal
effects, wastes accumulate in the estuary creating degraded bacterial
and dissolved oxygen conditions. Sampling data of the Virginia Water
Control Board obtained during June, July, and August of 1971 show a
-------
IV -
fecal coliform count range of less than 100/100 ml to 2100/100 ml in
a reach extending from the Route 3 Bridge at Fredericksburg to a
point about 5 miles downstream. From a total of nine samples taken
during this period, four of the samples contained a fecal coliform
density of less than 100/100 ml.
Except for the short stretch noted above the estuary below
Fredericksburg is suitable to support primary contact recreation uses.
Fecal coliform counts were less than 100/100 ml during the summer
months of 1971 .
The latest available report on shellfish growing areas by the
Virginia State Water Control Board lists six areas in the Rappahannock
River Basin condemned for the direct maketing of shellfish. The con-
demned areas total approximately 2,363 acres out of an estimated total
of 69,008 acres, or roughly 3 percent, of the available oyster bars.
The 2,363-acre figure represents an approximate increase of 1,254 acres,
or 1 percent, over the 1967 figures. Jurisdiction for closing oy-
ster bars lies with the Virginia State Department of Health.
Oyster beds currently condemned and the reasons for their
condemnation are listed below:
Rappahannock River (1,045 acres): Windmill Creek - marina
pollution, sewage treatment facilities, etc.; below Ur-
banna Creek - animal pollution, sewage treatment facili-
ties, etc.
Carter's Creek (590 acres): industrial activity, marinas,
residences, etc.
-------
IV - 189
Urbanna Creek (297 acres): sewage treatment plant, marinas,
commercial docks, etc.
Broad Creek (81 acres): marinas, commercial docks,
residences, etc.
Eastern Branch of Corrotoman River (350 acres): lack of
sewage treatment facilities.
DISSOLVED OXYGEN CONDITIONS
The Virginia Water Control Board reported that the DO concen-
trations during the summer of 1971 averaged 8.2 mg/1 in the vicinity
of the Route 3 Bridge at Fredericksburg. In this area the DO con-
centration averaged 7.4 mg/1 during the summer of 1968. Below Fred-
ericksburg at River Mile 105.3, based on the results of four surveys,
the DO averaged 3.4 mg/1 in the summer of 1971. In the same vicinity
DO concentrations of 2.3 mg/1 and 5.2 mg/1 were recorded in the summers
of 1965 and 1968, resoectively.
From the Route 301 Bridge at Port Royal, Virginia, downstream to
the Bay at Windmill Point, DO standards are maintained. A review of
sampling data obtained in the summer of 1971 showed average DO con-
centrations of 8.9, 7.3, and 7.4 mg/1 at River Miles 78, 56, and 43,
respectively. The standard established for the Rappahannock Estuary
requires a daily DO concentration average of 5.0 mg/1.
The Middle Atlantic Region, Federal Water Quality Administration
(now Region III, EPA), conducted a field survey on the Rappahannock
River in the vicinity of Fredericksburg, Virginia, from April through
July 1970. The field survey was initiated to gather data in order to
-------
IV - 190
reevaluate the water quality aspects of the proposed Salem Church Re-
servoir of the U. S. Army Corps of Engineers. A total of 16 stations
were sampled weekly from the Fall Line at Fredericksburg downstream to
the Route 301 Bridge at Port Royal, Virginia. The following parameters
were measured: water temperature, DO, BOD5, and pH. The results of the
dissolved oxygen determinations are briefly discussed below.
The limited amount of field data collected during the 1970
field survey showed depressed dissolved oxygen concentrations below
the City of Fredericksburg, in the vicinity of Bernard Bar, and in
the area of Route 301 Bridge, Port Royal, Virginia (see Figures IV-28
through IV-30). Although the City of Fredericksburg and the FMC Cor-
poration provide secondary treatment to its sewage and process water,
respectively, instream oxygen demand from the treated effluents ap-
parently results in an oxygen sag in the vicinity of Bernard Bar, es-
pecially during the low-flow summer conditions. The mean monthly flows
entering the estuary at Fredericksburg during June and July 1970 were
521 and 774 cfs, respectively, while the 1970 mean yearly flow was
1,360 cfs. In addition, the FMC Corporation discharges approximately
20 MGD of spent cooling water, which receives no treatment, upstream
from Bernard Bar. The oxygen sag found 20 or .30 miles downstream
from Fredericksburg (Figures IV-28 through IV-30) was not evaluated in
the study.
NUTRIENTS
The Annapolis Field Office made a determination of the nutrient
input from the freshwater portion of the Rappahannock River Basin
-------
IV - 191
UJ
LL
O
X
Q.
OXYGEN
SOLVED
-
5
£
UJ
>
£
ANNOCK
RAPPAH
UJ
£
(A
Q
-1
UJ
u!
FWQA 1
(6/4/70)
sj
*1
I
e
p
•
i
o
p
tt
I
O
I
P
M
u
U)
to
UJ
£
UJ
O
-o
~2
N39AXO
Figure IV-28
-------
IV - 192
2
»»
(ft
p
0)
I
ui
I
in
y
K
UJ
p
tt
S
o
•i
N39AXO
Figure IV-29
-------
IV - 193
(l/»«0 N39AXO QBAIOSSIQ
Figure IV-30
-------
IV - 194
at the Fall Line (River Mile 110.3) for the period June 1969 to
August 1970. Based on average monthly flows for the 15-month study
period the results were as follows:
AVERAGE MONTHLY % INPUT TO
PARAMETER CONTRIBUTION BAY
(Ibs/day) (Ibs/day)
T. P04 as P04 1,600 2%
P (Inorganic) 900 2%
TKN as N 3,900 3%
N02 + N03 as N 3,600 M
NH3 as N 600 1%
TOC 29,000 3%
The following table of nutrient data is intended to show nutrient
concentrations at several randomly selected sampling stations main-
tained by the Virginia Water Control Board. Valid conclusions can-
not be drawn as the data is not sufficiently extensive, nor is it
correlated with flow rates.
-------
IV - 195
Table IV-42
STATION
LOCATION
(river mile)
108
103
78
56
43
29
18
8
DATE
6-22-70
7-26-70
9-03-70
6-02-71
7-02-71
7-21-71
8-08-71
6-22-70
9-03-70
6-02-71
7-02-71
7-21-71
8-08-71
4-13-70
5-27-70
2-05-70
4-13-70
5-27-70
4-13-70
5-27-70
4-13-70
5-27-70
4-13-70
5-27-70
2-10-70
5-27-70
9-28-70
TOTAL
PHOSPHORUS AS P
(mg/TJ
.1
.1
< .1
< .1
< .1
< .1
.1
.18
< .1
< .1
< .1
< .1
.20
< .05
< .05
.05
.1
< .05
< .05
.05
.05
.50
< .05
.05
< .05
.05 '
.3
NITRATE
NITROGEN AS N
fing/TJ
.19
.53
.07
.78
.39
.24
.52
.17
.15
.78
.39
.39
.45
.22
.24
.20
.35
.01
.30
.03
.50
.05
.01
.02
.12
.05
.05
The Virginia Water Control Board collected limited nutrient data
during the 1960's and has provided summaries of the analyses of this
data. At the Route 301 Bridge, Port Royal, Virginia (River Mile 79),
-------
IV - 196
the average minimum and maximum nitrate-nitrogen concentrations during
1962 were .02 and .28 mg/1, respectively, based on 10 sets of data.
For most sampling stations, however, yearly concentration averages are
obtained from very limited data. Phosphorus concentration data is re-
ported for only three stations in the data summaries covering the 1960's,
HEAVY METALS
The Virginia Water Control Board sampled for mercury, lead, and
arsenic during the summers of 1970 and 1971. For the most part, the
data is limited to one set for either 1970 or 1971 and available only
for the upper or middle reaches of the estuary. However, the concen-
trations measured in water samples were less than the detectable limits
for the three metals in most samples. The concentrations most fre-
quently observed were: less than .0005 ppm for mercury, less than
.010 ppm for lead, and less than .005 ppm for arsenic.
Huggett et al. analyzed zinc, copper, and cadmium concentrations
in a paper entitled "Utilizing Metal Concentration Relationships in
the Eastern Oyster (Crassostrea virginica) to Detect Heavy Metal
Pollution," VIMS Contribution number 431, Virginia Institute of Marine
Science, October '1971. The study analyzed the distribution of zinc,
copper, and cadmium in oysters from Virginia's major rivers. In the
Rappahannock Estuary these metals were distributed in the oyster as
follows:
Zinc: 400 - 800 ppm, Lowery Point (below Tappahannock, Va.)
to Jones Point; 0 - 400 ppm, Jones Point to Bay.
-------
IV - 197
Copper: 25 - 500 ppm, Lowery Point to Bowlers Wharf; 0-25 ppm,
Bowlers Wharf to Bay.
Cadmium: 1.0 - 1.5 ppm, Totusky Creek to Bowlers Wharf;
0.6 - 1.0 ppm, Bowlers Wharf to Jones Point; (also Cor-
rotoman River), < 0.6 ppm, Jones Point to Bay.
PESTICIDES
The Virginia Water Control Board analyzed water samples in June
and July of 1971 in order to detect the presence of chlorinated
hydrocarbon and phosphorus based pesticides. The chlorinated and
thio-phosphate groups were measured at less than .1 ppm at all sampl-
ing stations selected for review. This recent data will provide some
basis for detecting increases in pesticide concentrations.
WATER QUALITY TRENDS
Water quality remains generally good in the Rappahannock Estuary.
Contributing factors to the maintenance of water quality standards
are the apparent absence of intensive development within the basin
drainage area and the provision of secondary treatment of wastewater
at Fredericksburg, the major population center in the basin. However,
a more sufficient data base must be established in order to identify
any water quality trends. This will necessitate intensive and
extensive monitoring of nutrients, pesticides, and heavy metals.
Although the sparse data on metals and pesticides show concentrations
in the water as negligible, bottom sediment data could show accumu-
-------
IV - 198
lations of greater significance. The remineralization of metals
by disturbing bottom sediment is a growing concern where shellfish
are economically important, as in the case of the Rappahannock
Estuary.
-------
IV - 199
L. YORK RIVER AREA
The York River is formed by the confluence of the Mattaponi
and Pamunkey Rivers, its two principal tributaries, at West Point,
approximately 35 miles from its mouth. The entire York River is
tidal. The Pamunkey and Mattaponi Rivers are tidal from West Point
for distances of about 51 and 37 miles, respectively. The major
water-using industry in the study area is the Chesapeake corporation,
located in the Town of West Point, which produces draft pulp, liner
board, and draft paper.
Water uses assigned to the York River tidal system by the Common-
wealth of Virginia include primary contact recreation; propagation of
fish, shellfish and other aquatic life; and other beneficial uses.
The uses are protected by Class II water quality .standards, including
bacteriological standards for primary contact recreation and shellfish
harvesting uses.
The following discussions of existing water quality conditions in
the York Estuary are based largely on data provided by the Virginia Water
Control Board.
BACTERIOLOGICAL CONDITIONS
During the summer months of 1970 fecal coliform counts were found
to be less than 100/100 ml in the York River from a point approximately
4.5 miles below West Point to its mouth. Monitoring stations were
sampled on a frequency of once a month over a-two-to three month period.
The primary contact recreation standard prohibits'a fecal coliform
-------
IV - 200
density in excess of a log mean of 200/100 ml (multiple-tube
fermentation or MF count).
Currently, there are eight shellfish areas in the York River
closed to harvesting by the Virginia State Department of Health.
The condemned areas total approximately 5,092 acres out of an
estimated total of 18,653 acres, or about 27 percent of the avail-
able oyster bars. The 27 percent figure reflects improved bacterial
conditions, since nearly 39 percent of the available acreage was
closed in 1967.
Of the estimated 5,092 acres closed, 4,675 acres are located in
the main stem of the York River. These areas are in the vicinity of
the Town of West Point, the Naval Warfare School, Gloucester Point,
the City of Yorktown, and the Naval Weapons Station at Yorktown. The
largest closure is located in waters adjacent to and below the Town
of West Point. The reasons for condemnation of this area include
industrial discharge, sewage discharges, marinas, and residential areas
on the shoreline discharging raw and partially treated sewage. Indus-
trial discharge from the Chesapeake Corporation constitutes the most
significant pollution source affecting the closure of shellfish bars
in the vicinity of West Point. The remaining closures are in Timber-
neck Creek (112 acres) and Sarah's Creek (305 acres).
DISSOLVED OXYGEN CONDITIONS
The following table gives the results of dissolved oxygen measure-
ments for 1971.
-------
IV - 201
Table IV-43
RIVER MILE DATE TIME DO CONCENTRATION
tatute Mile)
31.48
28.10
11.14
2.92
1.88
6-28-71
8-01-71
6-28-71
8-01-71
8-23-71
6-28-71
8-01-71
8-23-71
6-28-71
8-01-71
8-23-71
8-01-71
8-23-71
1200
1200
1220
1210
1320
1250
1305
1350
1340
1325
1440
1345
1430
(mg/1)
5.8
6.4
6.2
7.4
5.8
6.5
9.8
6.6
6.0
7.0
8.1
7.6
8.8
-------
IV - 202
As shown by the available data, the DO standard of 5.0 mg/1
was not contravened on the dates at the specific hours listed above.
However, during the summer months of 1970 at River Mile 0.92 on the
Pamunkey River, immediately below the Chesapeake Corporation discharge
output, the following [)0 concenrations were measured: 3.6 mg/1
(July 26), .80 mg/1 (Aug. 12), and 5.0 mg/1 (Aug. 24). No DO data
was available at this sampling location for the summer months of 1971.
The Chesapeake Corporation at West Point discharges its effluent,
which includes spent cooling water, to the Pamunkey River about 1-mile
upstream from its confluence with the York River. The effluent, about
25 MGD, is characteristically high in BOD (30,000-35,000 Ibs/day). The
assimilative capacity of the upper York River has thus far precluded
serious oxygen depletions except for the degradation in the Pamunkey
River noted above. Increases in the strength of the current wastewater
loadings could exceed the present capacity of the upper York River
to assimilate this effluent.
The Chesapeake Corporation has constructed a small pilot plant
to determine the most efficient method of treating its wastes. The
Virginia Water Control Board has established a compliance date of
October 1973 for the Chesapeake Corporation to provide adequate treat-
ment of all its wastewater.
NUTRIENTS
The Pamunkey and Mattaponi Rivers were included in the detailed
study by the Annapolis Field Office of the nutrient contribution to
-------
IV - 203
the Chesapeake Bay from its major tributary watersheds. These two
rivers provide the most significant freshwater flows to the York
River tidal system. The following table sets forth the average concen-
tration of nutrients for the two rivers measured during the period of
July 1969 to August 1970. The sampling stations were located above the
Fall Lines in freshwater areas.
Table IV-44
Pamunkey
River at
Hanover, Va.
Mattaponi
River at
Beaulahville,
Virginia
TP04
as P04
mg/1
.18
Inorganic
P
mg/1
.13
TKN as
N
mg/1
.53
N02+NOs
as N
mg/1
.19
NH3 as
N
mg/1
.12
TOC
mg/1
6.15
.16
.13
.58
.11
.07 8.08
-------
IV - 204
Nutrient data collected during 1970 and 1971 by the Virginia
Water Control Board is presented below.
Table IV-45
STATION LOCATION
(Statute river miles)
Mattaponi River -
Mile 1.34
Pamunkey River
Mile 0.92
York River -
Mile 31.48
York River -
Mile 28.10
York River -
Mile 11.14
York River -
Mile 2.92
DATE
2-10-70
3-19-70
4-17-70
5-07-70
8-24-70
9-10-70
6-28-71
2-10-70
3-19-70
4-17-70
5-07-70
8-12-70
3-19-70
4-14-70
5-07-70
8-24-70
9-10-70
6-28-71
3-19-70
4-17-70
5-07-70
3-19-70
4-17-70
5-07-70
3-19-70
5-07-70
TOTAL
PHOSPHATES AS P
(mgTTI
05
00
05
01
10
.10
.10
.05
.10
.05
.05
.40
.10
.05
.05
.10
.10
.10
.05
.05
.05
.10
.05
.05
.10
.05
NITRATE NITROGEN AS N
.25
.02
.34
.01
.03
.18
.19
.19
.01
.17
.02
.06
.01
.01
.02
.02
.05
.19
.01
.05
.04
.01
.10
.02
.01
.01
The Mattaponi River and Pamunkey River data set forth above
was obtained from sampling stations located on the two streams a
short distance from their confluence with the York River.
-------
IV - 205
As shown above, nutrient data was collected only at two of the
monitoring locations during 1971 and only on one occasion. No
nutrient data was reported for the York River stations for 1968 or
1969. Nutrient monitoring should continue on a more frequent basis
to identify any nutrient trends in the York River Estuary.
HEAVY METALS
The following table indicates the concentrations of several
heavy metals detected in water samples during 1970 and 1971. A
blank space in the table indicates no measurement of that metal at the
given location.
Table IV-46
Station Location Date Concentration in ppm (or mg/1)
Chromium Zinc Copper Mercury Manganese Lead Arsenic
Mattaponi River 9-10-70 - <.0005 -
Mile 1.34 6-28-70 - - - <.0005 - .110 <.005
Pamunkey River 3-19-70 .010 .010 .020 - .150
Mile 0.92 4-17-70 .030 .030 .020 - .110
5-07-70 .040 .010 .020 -
York River 9-10-70 - <.0005 -
Mile 31.48 6-28-70 - - - .0014 - .010 .005
York River 9-10-70 - <.0005 -
Mile 28.10
York River 9-10-70 - <.0005 -
Mile 11.14
York River 9-10-70 - - - <.0005 -
Mile 2.92
Huggett, et al. analyzed oysters in 1971 from the York River to
-------
IV - 206
determine the distribution of zinc, copper, and cadmium in the oysters.
(See Rappahannock River section of this chapter for further information.)
Zinc was found to be uniformly distributed in the oysters in concen-
trations from 400 to 800 ppm from Terrapin Point, about 5 miles below
West Point, to the mouth of the York. The highest concentrations of
copper, 50 to 100 ppm, were detected in oysters collected between
Terrapin Point and Mount Folly. Oysters containing from 1.5 to 2.0 ppm
of cadmium were taken from Puritan Bay and the mouth of Queen Creek.
These were the highest concentrations of copper and cadmium found in the
York River, although both metals were found in oysters from other
areas of the estuary. Further information on these studies can be
obtained from the Virginia Institute of Marine Science.
PESTICIDES
Of the sampling stations reviewed for the York River study area,
pesticide data was reported for two stations only. At River Mile 1.34
on the Mattaponi River, water samples collected June 28, 1971, contained
concentrations of 1.00 ppm pesticides for both the chlorinated and
thio-phosphate groups. Downstream at River Mile 31.48 on the York
River, water samples contained less than .100 ppm for both pesticide
groupings on June 28 and August 1, 1971. Continuous monitoring of
pesticides should be included in ongoing sampling programs for the York
River.
WATER QUALITY TRENDS
Although 27 percent of the available oyster bars are currently
-------
IV - 207
closed in the York River, this figure represents improved bacterial
conditions since 1967. Sanitary surveys during 1967 resulted in the
closure of nearly 39 percent of the available acreage. Compliance
by the Chesapeake Corporation with pollution abatement order should
further reduce the amount of oyster bars now closed downstream from
the Town of West Point.
-------
-------
IV - 208
M. JAMES RIVER AREA
1. JAMES RIVER
The James River, the most southerly major tributary stream, is
approximately 340 statute miles in length and provides 16 percent of the
freshwater inflow to the Bay. There is a total fall of 988 feet
from the headwaters near Iron Gate, Virginia to the fall line sep-
arating the Piedmont and Coastal Plain at lower Richmond, Virginia.
From Richmond the James is a tidal estuary that joins the Bay at
Hampton Roads, a distance of approximately 107 statute miles over which
the fall in river level is negligible (less than 10 feet). The mean
freshwater discharge is approximately 7,500 cfs with recorded extremes
of 329 and 325,000 cfs.
Industry in the James Estuary is concentrated in three areas:
Richmond, Hopewell, and the Norfolk-Newport News area. A thorough
account of the historical, meteorological, economic, population,
industrial, and transportation aspects of the James Estuary are
contained in a recent report, "The Tidal James", by John B. Pleasants
of the Virginia Institute of Marine Science.
The James Estuary, in Virginia water quality standards, is classi-
fied as Class I IB waters from the mouth at the Old Point Comfort-Fort
Wool line to the fall line at Richmond. This includes the Chickahominy
River to Walker's Dam and the tidal waters of the Appomattox River.
These waters shall be satisfactory for primary contact recreation,
the propagation of fish and other aquatic life, and other beneficial
uses. In addition, the estuarine segment from the Old Point Comfort-
-------
IV - 209
Fort Wool line to Barrets Point (mouth of Chickahominy River) is as-
signed the special bacteriological standard (70 MPN/100 ml coliforms)
to protect the shellfish bars in this area, many of which, however, are
condemned for direct marketing because of contravention of the standard,
The following discussions of existing water quality conditions
are based on data provided by the Virginia Water Control Board, the
Virginia Institute of Marine Science, and inhouse data of the Annapolis
Field Office of EPA.
BACTERIOLOGICAL CONDITIONS
From October 14 through 30, 1969, the Federal Water Pollution
Control Administration, Middle Atlantic Region (now, EPA, Region III)
conducted an intensive water quality survey of the James Estuary between
Richmond and Hopewell. Samples were collected each day at slack low
tide and analyses were run for total coliform, fecal coliform, dissolved
oxygen, temperature, biochemical oxygen demand, nutrients, chemical
oxygen demand, total carbon, and metals. Figure IV-31 shows the 1969
sampling locations.
The bacteriological results of the October 1969 survey are presented
in graphic form in Fig. IV-32. Results are given as the most probable
number of bacteria (MPN). These data indicated that the fecal coliform
levels in the James River were acceptable for all water uses during
October at Boulevard Bridge and Mayo's Island. Immediately below these
areas and downstream from the Richmond and Henrico County wastewater
treatment plants the standard for primary contact (200 MF/100 ml fecal
-------
IV - 210
coliforms) recreation was contravened. Data of the Vigim'a State
Water Control Board (VWCB) for the 1971 summer sampling season show that
excessive bacterial counts still preclude contact recreation water uses
in the upper estuary f^om the Richmond wastewater treatment plant out-
fall downstream to Bermuda Hundred less than two miles north of Hopewell.
From sampling Station 168 below Goode Creek, downstream to Duch Gap,
a distance of approximately 10 miles, fecal coliform densities (MPN) av-
eraging up to 80,000/100 ml were recorded on May 6, 1971. Fecal coliform
densities averaged less than 5,000/100 ml on June 13, 1971, and tended
to decrease on subsequent sampling runs, although bacterial counts still
exceeded the standard for primary contact recreation. The Annapolis
Field Office (AFO) recorded excessive fecal coliform counts in this same
segment of the James River during the fall of 1971. At a station below
Goode Creek on October 19 and November 2, 3, and 4, the densities were:
2,400/lOOml, 2,100/100 ml, 91,800/100 ml, and 790/100 ml, respectively.
Below the Richmond Deepwater Terminal the counts were 240,000/100 ml,
17,200/100 ml, 870/100 ml, and 5,400/100 ml on the respective sampling
dates. During the October 1969 intensive survey fecal coliform den-
sities averaged about 25,000/100 ml in this segment of the estuary.
The high fecal coliform densities described above were mainly due
to discharges by the City of Richmond of raw wastes to Goode Creek
which then entered the estuary. On February 28, 1972, an intercepting
sewer was connected to the Richmond treatment plant which diverted 2 MGD
of previously discharged raw wastes from the Goode Creek area. The
VWCB advises that this recent hook-up eliminates the last raw discharge
-------
IV - 211
t- «
t/> -
o
* 7
Figure IV-31
-------
FECAL COLIFORM DENSITIES
VS
RIVER MILE
OCTOBER 14 — 30.1969
IV - 212
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RCCOMMENDEO LIMIT FOR
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RECOMMENDED LIMIT FOR
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126
RECOMMENDED LIMIT FOR
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Figure IV-32
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IV - 214
from the City of Richmond to the James River. It should be noted, how-
ever, that the existing combined sewers (sewers which carry both storm
water and sewage) will still result in the bypass of raw wastes to
the estuary during periods of high runoff following heavy rains when
the sewage treatment plants' hydraulic capacities are exceeded. The
extent of bacterial degradation in the James estuary at and below Rich-
mond will have to be assessed during the 1972 sampling season.
From Turkey Point downstream to Windmill Point, a distance of
approximately 12 statute miles, the bacterial levels steadily decrease.
The great dilution capacity of the estuary at Hopewell and the absence
of unchlorinated domestic waste in this reach appears to influence the
bacterial recovery of the estuary.
The estuary from Windmill Point downstream to the ESSO pier at
Newport News, a distance of approximately 62 statute miles, showed no
serious bacterial degradation during the 1971 VWCB sampling runs.
Sampling frequency amounted to one sampling run per month from May
through September, except for July when two sampling runs were made.
Except for occasional moderately high levels, fecal coliform densities
were found to be less than 100/100 ml in this stretch of the estuary.
The most recent published report on shellfish growing areas by
the Virginia Water Control Board lists eleven areas in the James River
Basin condemned for the direct marketing of shellfish. The condemned
areas total approximately 46,727 acres out of an estimated total of
93,062 acres available. Jurisdiction for closing shellfish areas lies
with the Virginia State Department of Health.
-------
IV - 215
The larger areas closed to direct marketing of shellfish are as
follows: James River below Hog Island, 3,392 acres; Pagan River,
2,270 acres; Nansemond River, 1,980 acres; Willoughby Bay, 1205 acres;
and the Hampton Roads area of the James River including the Elizabeth
River, 36,275 acres. The large closures in the Hampton roads area are
due to several reasons, including: the large population density, num-
erous marinas, dockage of naval vessels, industrial activities, and
numerous wastewater treatment plant discharges. This latter problem is
discussed in detail in the Elizabeth River section.
DISSOLVED OXYGEN CONDITIONS
Table IV-47 presents DO concentrations measured by the VWCB during
the late spring and mid-summer months of 1971. Dissolved oxygen concen-
trations in the mainstem of the James River, with few exceptions, were
greater than the standard which requires a daily average of 5.0 mg/1 and
a minimum of 4.0 mg/1. The highest DO concentrations were recorded dur-
ing the May 11, 1971 sampling run when water temperatures were favorably
low for DO maximum concentrations. In the 100 mile reach below Richmond
the temperature averaged 18.9°C (66°F) during the sampling on May 11, 1971.
Generally, the resu'.ts of the July 23 and August 3, 1971 sampling runs
show decreased oxygen concentrations. The average water temperature at
the sampling stations on August 3, 1971 was 29.3°C (84.6°F) or 10.4°C (18.6°F)
greater than the May 11, 1971 average temperature. The higher water tem-
peratures would result in a decrease in the oxygen holding capacity of
the water and an acceleration of biological activity relating to oxygen-
consuming decomposition of organic wastes and detritus.
-------
IV - 216
Table IV-47
SAMPLING
STATION
Esso Pier, Newport News
(Statute mile 7.77)
Rt. 17-1-258 Bridge
(13.54)
Byoy 12
(20.54)
Buoy 24, Mulberry Point
(26.07)
DATE
797T
5-11
6-14
7-05
7-23
8-03
5-11
6-14
7-05
7-23
8-03
5-11
6-14
7-05
7-23
8-03
5-11
6-14
7-05
7-23
8-03
DO
ing/1
8.4
9.0
7.8
6.8
3.8
8.6
8.0
6.7'
7.2
4.2
8.8
6.6
8.0
8.2
8.4
10.0
7.0
8.0
6.4
8.6
TEMP
°C
18.3
23.3
24.4
25.0
25.6
18.9
25.0
25.6
25.6
26.1
20.0
25.6
26.1
26.1
27.8
18.9
26.7
26.7
26.1
27.8
-------
IV - 217
Table IV-47 (Cont.)
SAMPLING
STATION
Buoy 43, Hog Point
(34.27)
Swarm Point
(42.92)
Buoy 74, Brandon Po'int
(56.22)
Buoy 86, Windmill Point
(69.34)
DATE
1971
5-11
6-14
7-05
7-23
8-03
5-11
6-14
7-05
7-23
8-03
5-11
6-14
7-05
7-23
8-03
5-11
6-14
7-03
7-23
8-03
DO
mg/1
11.2
7.8
8.0
-
8.4
10.0
7.2
8.0
7.0
8.0
7.0-
4.6
5.8
4.2
6.4
9.8
7.4
6.5
7.4
7.0
TEMP
°C
21.1
26.1
26.1
26.7
28.3
21.7
26.7
26.1
25.6
28.9
20.6
27.2
28.9
27.2
30.0
21.1
27.8
27.8
27.8
29.4
-------
IV - 218
Table IV-47 (Cont.)
SAMPLING
STATION
Rt. 156 Bridge, Jordan
Point (77.44)
Buoy 118 Below American 5-06
Tobacco (80.01)
Buoy 126
(81.61)
Byoy 150, Dutch Gap
(94.84)
DATE
197T
5-13
6-27
7-05
7-08
7-23
8-03
5-06
6-13
7-05
7-23
8-03
5-06
6-13
7-05
7-23
8-03
5-06
6-13
7-05
7-23
8-03
DO
rng/1
6.4
5.0
7.8
6.0
8.0
6.0
10.2
6.2
7.4
8.6
6.8
8.0
6.2
6.0
7.0
9.0
7.0
6.0
8.0
7.0
5.0
TEMP
^C~
23.3
30.0
30.6
27.8
27.8
30.0
16.7
25.6
28.9
28.3
30.0
16.7
23.3
27.8
28.3
30.6
16.7
24.4
27.8
28.3
30.6
-------
IV - 219
SAMPLING
STATION
Buoy 155, Dutch Gap
(96.76)
Buoy 157
(98.34)
Table IV-47 (Cont.)
Buoy 166, Below Deep
Water Terminal (103.22) 6-13
Buoy 168, Below
Goode Creek
DATE
1971
5-06
6-13
7-05
7-23
8-03
5-06
6-13
7-05
7-23
8-03
5-06
6-13
7.23
8-03
5-06
6-13
7-23
8-03
DO
mg/1
9.2
6.5
8.0
7.0
5.0
6.2
6.0
8.2
4.0
5.0
7.8
8.0
6.4
6.0
10.0
8.0
6.6
6.2
TEMP
°C
17.2
23.9
28.3
28.3
32.8
17.2
28.3
28.9
28.3
29.4
17.2
23.3
28.3
30.6
17.2
23.3
28.3
30.6
-------
IV - 220
The Virginia Institute of Marine Science (VIMS) collected slack
water samples at successive stations upstream from the mouth of the
James Estuary on several occasions between June and December 1971.
Dissolved oxygen measurements and 5-day BOD determinations were taken
at the surface and at the bottom of the water column. The purpose of
these field studies was to determine the existing water quality of the
estuary below Richmond by evaluating the degree of deoxygenation caused
by the biochemical breakdown of organic matter accompanying the waste
discharges entering the estuary.
Figures IV-34, IV-35, and IV-36 show the results of low water
slack runs made by VIMS on June 11, August 10, and September 8, 1971.
Oxygen sags resulting from instream biological breakdown of waste are
apparent from the graphs, and show a much more frequent contravention
of the 4.0 mg/1 standard than indicated in Table IV-47 above. The
oxygen sags tend to become elongated due to the ebbing of the tide.
The tidal influence appears more pronounced in the vicinity of Hopewell
where the estuary widens. As expected, bottom waters tended to be lower
in DO than surface waters; with a few noteworthy exceptions, the differ-
ence was only about 0.5 mg/1.
The initial oxygen sag begins about 5 miles below the discharge
point of the City of Richmond's wastewater treatment plant, and extends
approximately 12 nautical miles downstream to the, vicinity of Turkey
Island. During the August 10 and September 8, 1971 low water slack
runs, DO was depressed to 3.0 mg/1 near the confluence of Falling Creek
-------
IV - 221
Figure IV-34
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IV - 223
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IV - 224
with the estuary. Higher freshwater dilution flows and colder water
temperatures prevented a significant DO depression during the June 11,
1971 run. Freshwater flows recorded at Richmond for the 3-day periods
preceding the August arid September runs averaged 5,728 and 7,689 cfs
lower, respectively, than the average 3-day flow recorded prior to
the June run.
Table IV-48 summarizes most of the significant sources of organic
loadings to the James Estuary from Richmond to Hopewell. The most
pronounced influence on the segment discussed above is the high organic
loading exerted on the .estuary by the Richmond Sewage Treatment Plant
(STP). While secondary treatment facilities are slated for operation
in October 1972, this facility currently provides only primary treat-
ment to approximately 40 MGD of wastewater and exerts a 5-day BOD
loading of 38,364 Ibs/day. Even with secondary treatment, combined
sewers in Richmond will result in the bypass of storm and sanitary
wastes to the estuary following periods of heavy rainfall. Other
sources of organic loadings above Turkey Island are the Henrico County
STP, Richmond Deep Water Terminal STP, Chesterfield County's Falling
Creek STP, and duPont Company's STP. The Henrico County STP provides
secondary treatment and discharges to Gillies Creek just below Richmond.
From Turkey Island to several miles downstream, the estuary begins
to recover from the oxygen sag downstream from the Richmond STP. However,
as shown in Figures IV-34, IV-35, and IV-36, an elongated oxygen sag then
occurs and extends from Hopewell downstream to the vicinity of the
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IV - 226
entrance of the Chickahominy River, a distance of about 20 nautical miles.
A combination of poorly treated domestic wastes from the Colonial Heights,
Hopewell, and Petersburg areas and heavy organic industrial effluent
from the Hopewell area contribute to this oxygen sag. As shown by Table
IV-48, Colonial Heights, Petersburg, and Hopewell currently provide
primary treatment only. The Petersburg Sewage Treatment Plant, which
is overloaded by about 700,000 gallons per day, and the Colonial Heights
STP discharge to the Appomattox River, while the Hopewell STP discharges
to Bailey Creek. The Appomattox River in the vicinity of the Route
10 Bridge at Hopewell showed no serious DO depression during the 1971
sampling season; Bailey Creek, where it is traversed by Route 10, 0.6
mile upstream from its confluence with the James contained no DO at
all except in cold weather.
Bailey Creek, in addition to recurring domestic wastes from
Hopewell and Fort Leeb receives a heavy industrial effluent from
several industries. These discharges enter the James River (Bailey
Bay) below the Route 10 Bridge sampling station operated by the VWCB.
The largest organic loadings to Bailey Bay are from Continental Can
Company and Hercules Powder Company which discharge 39,840 and 39,400
Ibs/day of 5-day BOD, respectively. The results of the 1971 monitoring
by the VWCB at the Route 10 Bridge were as follows:
-------
IV - 227
DATE
1-18-71
2-14-71
3-13-71
4-28-71
5-13-71
6-27-71
7-08-71
8-02-71
_£HL
10.0
5.5
>10.0
0.0
>10.0
8.2
6.7
8.9
TEMP
°F
44
39
64
64
77
98
82
90
DO
mg/1
4.0
6.0
0.0
0.0
0.0
0.0
-
0.0
BOD
mg/1
250
146
195
230
-
380
-
200
The above data strongly demonstrate that the current industrial
loadings to Bailey Bay are a significant factor in the depressed DO
concentrations noted between Hopewell and the confluence of the
Chickahominy River. Although not shown above, fecal coliform stan-
dards at this station were greatly exceeded, with values recorded
in excess of 80,000 MPN/100 ml, indicating inadequacy of domestic
sewage treatment.
The remaining oxygen sag, determined at low water slack, is
downstream from Jamestown Island near the mouth of College Creek.
The organic loadings from several small treatment plants in the
Jamestown area and the treated wastes from Williamsburg which are
discharged into College Creek could have influenced the lower DO
concentrations in this section. The 1.82 MGD of wastewater from
Williamsburg, previously treated at the College Creek plant, has
-------
IV - 228
recently been diverted to the newly constructed Hampton Roads Sani-
tation District's Williamsburg Plant, located near the Camp Wallace
Military Reservation. Plans call for connecting the existing small
plants in the Jamestown area to the new Williamsburg Plant.
The Virginia Institute of Marine Science also made runs at high
water slack conditions, Figures IV-37, IV-38, and IV-39. The evidence
of DO depression is similar to the low water slack runs discussed above,
except that oxygen demanding material tends to become concentrated
following high tide conditions. During flood tide, pollutants move
upstream resulting in a backup and concentration of wastes rather
than a dispersal. This effect is more pronounced in the upper estuary
during low freshwater inflows. As with the low water slack runs, the
lowest DO concentrations were recorded when flows were low and water
temperatures high. The oxygen sag near Hopewell is closer to the waste
outfalls following the flood tide.
Figures IV-40 and IV-41 show biochemical oxygen demand (BOD) data
for bottom and surface water conditions obtained during high water
slack. No BOD data were available for the low water slack runs.
The Virginia Institute of Marine Science found these data to be in-
conclusive, as they often failed to coincide with DO deficits for the
same sampling stations. However, BOD peaks were apparent below Rich-
mond, Hopewell, and College Creek. The BOD surges at nautical River
Miles 76 and 60 seem to manifest first, the high BOD discharge from the
City of Richmond's primary plant and second, the heavy organic indus-
trial loadings flowing from Bailey Bay at Hopewell.
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IV - 229
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Figure IV-38
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IV - 231
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IV - 232
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IV - 234
NUTRIENTS
Surveys of the James Estuary were conducted during the spring and
summer months of 1970 and 1971 by the Virginia Water Control Board and
in November 1971 by the Annapolis Field Office (AFO) of EPA. The AFO
carried out a detailed study of nutrient contributions to the Bay from
the James and Chickahominy River as part of its "Chesapeake Bay Nutrient
Input Study." The only other available data containing nutrient concen-
trations were taken by the Virginia Institute of Marine Science in an
intensive study from 1965-1966. These sources constitute the basis of
the information contained in this section.
In September 1966, nitrate-nitrogen concentrations (as N) ranged
from .028 to 1.246 mg/1 between River Miles 13.54 and 98.34. The highest
values, 1.078 and 1.246 mg/1, were found at River Miles 56.22 and
69.34, downstream from the industrial discharges at Hopewell (Statute
River Mile 80.01). Inorganic phosphorus (as P) and organic phosphorus
(as P) ranged from .016 to .372 mg/1 and .031 to .271 mg/1, respectively,
in the same area as above. The highest phosphorus values were recorded
at River Mile 98.34. In addition, chlorophyll a_ values of 92.0 and
86.0 yg/1 were found at River Miles 69.34 and 98.34, respectively,
well above the 25 yg/1 level generally considered as acceptable. In
terms of algal blooms, previous studies in the Potomac Estuary have
shown that chlorophyll a_ values in excess of 50 yg/1 are indicative
of nuisance conditions.
Nutrient data taken in August and November 1971 did not differ
appreciably from concentrations found in September 1966. While the
-------
IV - 235
levels of nitrate-nitrogen were higher in August 1971 than in Sep-
tember 1966, the concentrations of both inorganic and organic
phosphorus (as P) were lower than the September 1966 levels. However,
the nitrate-nitrogen concentration decreased in November 1971 and the
inorganic phosphorus (as P) level increased, as compared to September
1966 levels. Although chlorophyll a_ values were low in November 1971
(varying from 1.5 to 24.9 yg/1), no other recent chlorophyll a_ data
exists. This precludes any statement concerning algal growth in the
James Estuary during periods of high nutrient concentrations.
In 1971 nutrient concentrations were greatest during the late
spring and early summer months, in particular the May-June period.
Concentrations of both inorganic and organic nutrients in May 1971
are given in Table IV-50. The concentrations of ammonia-nitrogen
and nitrate-nitrogen tended to increase downstream from Hopewell,
while inorganic phosphorus (as P) levels increased downstream from
Richmond (River Mile 107.95). The latter increase is due to primary
treated domestic wastes from the City of Richmond, while the nitrogen
increases are due to industrial wastes discharged into Bailey Creek,
just downstream from Hopewell. During 1971, ammonia-nitrogen concen-
trations and total Kjeldahl nitrogen (TKN; includes ammonia) in Bailey
Creek were excessively high, with NH_ as N varying from a low of 2.00
mg/1 to a high of 11.00 mg/1 and TKN varying from 7.0 mg/1 to 14.0 mg/1
at the Rt. 10 bridge, 0.6 mile from the confluence of Bailey Creek
with the James River. The high nitrate-nitrogen concentrations down-
stream from Hopewell could reflect the oxidation of NH~ to nitrate-
-------
IV - 236
nitrogen due to the abundance of oxygen in the mainstem area. Discharges
into the Appomattox Ri \/er and from American Tobacco Company, directly
into the James downstream from the mouth of the Appomattox, may account
for the high nitrate-nitrogen levels in the James River downstream
from River Mile 77.44. Insufficient data exist at this time to deter-
mine the impact of the Appomattox River on nutrient levels in the James
River. Also, the high organic and inorganic phosphorus (as P) levels
found in Bailey Creek are not reflected in increased values in the James
River downstream from Hopewell. High dilution in this area could ac-
count for the lower P levels.
Nutrient concentrations in James River bottom sediment in the
summer of 1971 are shown in Figures IV-42 and IV-43. (Note: All River
Mile locations for sediments are given in nautical miles.) While TKN
does not exhibit a definite pattern, total phosphorus concentration
maxima occur at River Miles 5, 30, 37, and 40. No correlation between
nutrient concentrations in surface water and bottom sediment of the
James River can be found.
A lack of sufficient nutrient and chlorophyll a_ concentration
data prevents making a definite statement regarding any related water
quality problems in the James River. Chlorophyll a^ data taken during
periods of high nutrient concentrations are essential in order to deter-
mine if any nuisance algal growths exist, as both nitrogen and phosphorus
levels in the upper James River are present in amounts which could
support excessive algal growths. In addition, the nutrient loadings
originating from municipal and industrial sources should be determined.
-------
IV - 237
I 2 3 4 5 24 25 26 27 28
E 500
2'9 3'0 37! 3T2 i
3*7 3'8 3'9 4*0
42 57 58 59 60 61 66 67 70
71 72 73 75 77 78 79 80 84
JAMES RIVER (MILES FROM MOUTH)
-------
IV - 238
200-
100-
24 25 26 27 28
41 42 57 58 59 60 61 66 67 70
71 72 73 75 77 78 79 80 84
JAMES RIVER (MILES FROM MOUTH)
Figure IV-43
-------
IV - 239
An initial step in determining nutrient sources to the James
Estuary was taken by AFO during 1969-1970. Detailed analyses of the
freshwater inflow from the James River at Route 147 Bridge (West Rich-
mond) and from the Chickahominy River at Route 60 Bridge were conducted
during the period from June 1969 to August 1970 to determine the nutrient
contribution of the water entering the tidal system. The Appomattox
River was not included in this intensive study. The following table
presents the average concentration of nutrients based on average
monthly flows for the two rivers measured during the 15-month period
of June 1969 to August 1970.
Table IV-49
TPO,
AS PD4
mg/1"
.20
.57
INORGANIC
P AS PO,
mg/1 4
.13
.39
TKN AS
N
mg/1
.64
.73
NOp+NO,,
AS N J
mg/1
.66
.25
NH~
AS N
mg/1
.13
.07
TOC
mg/1
5.51
10.53
James River
Chickahominy
River
Average monthly contributions in pounds per day for the two rivers
can be found in the report "Chesapeake Bay Nutrient Input Study,"
Technical Report Number 47, by the Annapolis Field Office of EPA.
-------
IV - 240
Table IV-50
James River
Nutrient Concentrations
May 1971
Statute
River Mile
7.77
13.54
20.54
26.07
34.27
41.27
42.92
56.22
69.34
77.44
80.01
81.61
94.84
96.76
98.34
103.22
106.18
107.95
NH--N
J
mg/1
.600
.500
.300
.070
.380
.060
.070
.310
.600
3.900
.620
.030
.600
.550
.600
.500
.400
.130
N00+N00-N
L. J
mg/1
.190
.310
.450
.700
.800
.900
.850
.950
.650
.600
.300
.500
.250
.400
.510
.450
.400
.350
Inorganic P
as P
mg/1
.060
.010
.010
.010
.100
.060
.030
.030
.030
.100
.070
.070
.100
.100
.140
.140
.100
.010
Organic N
mg/1
-
-
-
.130
.420
.240
.230
.490
.400
.700
.280
.570
.200
.050
.000
.000
.000
.070
Organic P
mg/1
.040
.090
.090
.090
.000
.040
.070
.070
.070
.000
.030
.030
.000
.000
-
-
.000
.090
-------
IV - 241
PESTICIDES
Both chlorinated hydrocarbon and thio-phosphate pesticides were
found in surface waters of the James River during the late spring and
summer months of 1971 (May-July). Total concentrations of each of the
above general categories of pesticides were less than 0.100 yg/1, the
minimum detectable laboratory limit for those parameters employed at the
time the analyses were made. The chlorinated hydrocarbon pesticides
Dieldrin, DDE, DDT, and Lindane were also monitored, with the fol-
lowing range of concentrations measured:
Dieldrin .007 - .030 yg/1
DDF. <.020 - .030 yg/1
DDT <.030 - .060 yg/1
Lindane .030 - - yg/1
The United States Public Health Service standards for public and
municipal water supplies at the raw water intake were, at no time,
contravened by any of the above pesticides. The maximum allowable
concentrations of these pesticides are:
Dieldrin .017 trig/I
DDT .042 mg/1
Lindane .056 mg/1
Currently, no standard exists for DDE, although it appears that this
pesticide is also present in only very small amounts.
In general, pesticides in the James River were found at levels
far below the point at which they would constitute a hazard to health.
-------
IV - 242
Although the tidal James Estuary is not now used as a public or
municipal water supply, studies are currently underway to determine
the feasibility of such a water use for the upper Estuary.
HEAVY METALS
The Virginia State Water Control Board monitored the following
heavy metals in the James River during April, May, and September 1970,
and June 1971: arsenic, cadmium, chromium, copper, iron, lead, manganese,
mercury, and zinc. The range of concentrations of the above metals were
found as follows:
Arsenic < .005 mg/1
Cadmium < .010 mg/1
Chromium < .010 - .040 mg/1
Copper < .010 - .140 mg/1
Iron .600 mg/1
Lead < .010 mg/1
Manganese < .010 - .100 mg/1
Mercury < .0005 - .0076 ppm
Zinc < .010 - .080 mg/1
Concentrations of six of the above metals (arsenic, cadmium, chromium,
copper, lead, and zinc) were, at all times, less than the standards the
United States Public Health Service has set for the raw water intake of
public and municipal water supplies. The water supply raw water intake
standard was contravened in the case of iron and manganese, for which
-------
IV - 243
the standards are 0.3 mg/1 and 0.05 mg/1, respectively. The standard
for manganese was contravened four times out of a total of 16 samples,
while the standard for iron was contravened on the only occasion this
metal was monitored. In general, heavy metal concentrations in the
main stem of the James Estuary are satisfactory, except between River
Miles 77.44 and 98.34 where higher concentrations of some metals are
found.
High heavy metal concentrations, in particular chromium, iron,
manganese, and zinc, were found at Creek Mile 0.65 in Bailey Creek
0.6 mile from its confluence with the James Estuary at River Mile 77.
The following heavy metal concentrations were found during 1970 and
1971 at River Mile 0.65 in Bailey Creek:
Arsenic < ,005 mg/1
Cadmium < .010 mg/1
Chromium < .010 - .060 mg/1
Copper .010 - .050 mg/1
Iron .900 - 1.700 mg/1
Lead .020 - .030 mg/1
Manganese .120 - .140 mg/1
Mercury < .0005 ppm
Zinc .070 - .340 mg/1
A number of industries discharge significant amounts of wastes into
Bailey Bay, including Continental Can Co., Hercules Powder Co., Allied
Chemical Co., and Firestone Co.
-------
IV - 244
During the summer of 1971 concentrations of lead, mercury, and
*
zinc in the bottom sediment of the main channel of the James River
were monitored. This survey was conducted by the Virginia Institute
of Marine Science in order to identify those dredging spoils which
would violate water quality criteria for open water disposal. The
following limits for heavy metal concentrations have been set by EPA
for open water disposal of spoil materials:
Lead 50 ppm
Mercury 1 ppm
Zinc 50 ppm
Figures IV-44, IV-45, IV-46 delineate the concentrations of the
above heavy metals in the bottom sediment of the James River (Note:
River Mile locations in the remainder of this section are given in
nautical miles). The criterion for lead was contravened at only one
location, River Mile 82.0, about three miles below Richmond City's
sewage treatment plant, where a concentration of 55 ppm was found.
The concentration of mercury in the sediment was found to be satisfac-
tory throughout the James River, never exceeding 1.0 ppm. However, the
concentration of zinc in the James River sediment exceeded the spoil
material disposal criterion in a large portion of the river, in parti-
cular between River Miles 25.0 (in Channel SW of Hog Island) and 64.0
(opposite Bailey Creek), and between River Miles 71.0 and 74.0 (in vi-
cinity of Dutch Gap). Most zinc concentration values fell within a
range between 50 and 240 ppm. At River Mile 72.0, a maximum concentra-
tion of 708 ppm of zinc was found in the James River sediment. In the
-------
IV - 245
paper "Utilizing Metal Concentration Relationships in the Eastern Oyster
(Crassostrea virginica) to Detect Heavy Metal Pollution," VIMS no. 431,
October 1971, oysters in the lower portion of the James River (below
River Mile 25) were reported to contain concentrations of zinc ranging
from 800 to 1600 ppm. However, no correlation between the levels of
zinc in bottom sediment of the James River and the zinc levels in James
River oysters has been found.
-------
IV - 246
E
Q.
0.
LJ
-J
501
0
50
40-
30'
10-
50-i
40-
30^
20
IOH
I 2 3 4 5 24 25 26 27 28
29 30 31 32 33 36 37 38 39 40
41 42 57 58 59 60 61 66 67 70
71 72 73 75 77 78 79 80 84
JAMES RIVER (MILES FROM MOUTH)
Figure 11-44
-------
E
Q.
Q.
o
a:
u
0.81
0.6-
0.4-
0.2-
IV - 247
I.O-i
0.8-
0.6-
0.4-
0.2-
0.4-
5 ?4 25 26 27 28
32 33 36 37 38 39 40
41 42 57 58 59 60 61 66 67 70
0.2-
71 72 73 75 77 78 79 80 84
JAMES RIVER (MILES FROM MOUTH) Figure IV_45
-------
IV - 248
Q.
a
U
Z
M
72 73 75 77 78 79 80 84
50-
JAMES RIVER (MILES FROM MOUTH)
Figure IV-46
-------
IV - 249
2. ELIZABETH RIVER
The Elizabeth River, an estuary with sluggish tidal cycles
inhibiting the inflow of fresh water, is an example of an excessively
utilized waterway in regard to waste assimilation. Due to (1) the
relatively shallow nature of the Elizabeth River (2) low dispersion
and transport characteristics and (3) intense industrial, commercial
and domestic development, the Elizabeth River's ability to assimilate
the diverse waste input from these sources is extremely limited.
The three main branches of the Elizabeth River - the Eastern Branch,
Western Branch and Southern Branch - are characterized by heavy in-
dustrial , commercial and domestic pollution problems. In addition
to domestic waste discharged by sewage treatment plants and toxic
wastes discharged by a variety of industrial concerns, the area is
plagued by frequent spills and waste discharges from the extensive
shipyard and docking facilities therein.
On the Eastern Branch are located shopbuilding and drydock facilities,
an automobile assembly plant, an electric power plant, and several ship-
ping docks which contribute to the waste input of the river. The
Southern Branch, the most industrialized and longest branch of the
Elizabeth River, is characterized by a variety of industrial and com-
mercial concerns: cement plants, creosote treatment plants, ship-
building and drydock facilities, food processing plants, power plants,
chemical plants, and U. S. Navy shipyards. On the Western Branch, the
least industrialized branch of the Elizabeth River, are located
-------
IV - 250
a chemical manufacturing company and shipyards. The Main Branch houses
shipping terminals, coal loading yards, an oil terminal, and sewage
treatment plants.
INDUSTRIAL DISCHARGES
In March, 1972, the Annapolis Field Office conducted field inves-
tigations of major industries known to be discharging significant quanti-
ties of wastes into the Elizabeth River. Effluent samples and receiving
water samples opposite the discharges were obtained. This information
is presently being analyzed and will be published at some later time.
BACTERIOLOGICAL
In 1967 twelve areas in the James River Basin were condemned
by the State Health Department for the direct marketing of shellfish.
These condemned areas represented approximately 91% of the available
shellfish harvesting acreage in the state of Virginia. The entire
Elizabeth River was included as one of the original condemned areas
for the location of oyster beds. Condemnation of these areas was
based on several factors: high population density, sewerage system
with 30 pump stations, heavy boat activities (commercial and military
docks), numerous marinas, location of refineries and oyster processing
plants, and heavy shipping activities.
Based on 1971 data the State Health Department has condemned
eleven areas in the James River Basin for direct marketing of shellfish.
These condemned areas total 46,727 acres as compared to 42,170 acres
-------
IV - 251
which were condemned in 1967. However, the condemned areas of 1971
represent approximetely 50% of available acreage for shellfish har-
vesting on the James River Basin. This decrease in the percentage of
condemned areas is not to be construed as a decrease in the amount of
condemned acreage. It is, rather, due to an increase in the total
available shellfish harvesting acreage from a 1967 level of 46,335
acres to a 1971 level of 93,062 acres.
Based on a water quality survey of the Elizabeth River during
November, 1971 by AFO, fecal coliform counts (MPN) varied from 330/100
ml to 54,200/100 ml at station L-28 (Western Branch, Elizabeth River).
The following table presents the total coliform and fecal coliform
levels for the sampling period at stations in the Main Branch, Western
Branch, Eastern Branch, and Southern Branch of the Elizabeth River.
-------
Table IV-51
ELIZABETH RIVER
IV - 252
STATION
NUMBER
L-28
L-29
L-31
L-33
L-34
STATION
DESCRIPTION
Western Branch
Elizabeth River
Norfolk Reach
Eastern Branch
Elizabeth River
Eastern Branch
at Pescara Creek
Southern Branch
at St. Helena
Southern Branch
Paradise Creek
DATE
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11 -04-71
11-02-71
11-03-71
11-04-71
COL I FORM
MPN/100 ml
1300
54200
490
5420
2400
24000
17200
17200
34800
16090
24000
17200
-
9180
_
FECAL COL I FORM
MPN/100 ml
1300
54200
330
9180
3480
9180
17200
10900
9180
16090
24000
17200
-
5420
_
-------
IV - 253
As can be seen in the preceding chart, extremely high total and
fecal coliform counts were detected at every station. In every case
the specific bacteriological water quality criteria assigned to shell-
fish areas was violated (i.e. 70 total coliform organisms MPN per 100
ml).
During 1969, 1970, and 1971 the VWCB monitored portions of the
Eastern and Southern Branches of the Elizabeth River. The following
table gives the coliform levels detected sporadically at three locations
for the 1968, 1969, 1970, and 1971 sampling runs.
-------
Table IV-52
EASTERN BRANCH, ELIZABETH RIVER
IV - 254
RIVER
MILE
0.07
4.62
STATION
DESCRIPTION DATE
09-09-68
02-03-69
07-24-69
04-21-70
Alternate Route 58- 05-05-70
460 Bridge 11-22-70
Chesapeake, Virginia 05-11-71
06-14-71
07-06-71
09-02-71
06-28-68
07-24-68
Route 13 Bridge
08-22-68
Norfolk, Virginia
09-09-68
02-03-69
04-28-69
07-24--69
04-21-70
TOTAL COL I FORM FECAL COL I FORM
MPN/100 ml MPN/100 ml
430
4300
43000
230
4600
930 0
930 700
1300
430 <100
>11000 600
30
430
91
750
23000
930
1500
2400
-------
IV - 255
Table IV-52 (Cont.)
RIVER
MILE
4.62
2.03
STATION
DESCRIPTION DATE
05-05-70
11-22-70
Route 13 Bridge 05-11-71
Norfolk, Virginia 06-14-71
07-06-71
08-22-68
09-09-68
02-03-69
Beltline Railroad 04-21-70
Bridge 05-05-70
Norfolk, Virginia 10-27-70
(Southern Branch) 11-22-70
05-11-71
06-14-71
07-06-71
TOTAL COL I FORM
MPN/100 ml
11000
4300
930
-
430
430
230
930
930
11000
11000
930
1500
-
430
FECAL COL I FORM
MPN/100 ml
-
400
200
700
300
-
-
-
-
-
-
0
100
1600
<100
-------
IV - 256
MUNICIPAL DISCHARGES
The discharges emanating from two primary treatment plants on
the Elizabeth River contribute to the widespread water quality problems
associated with this river.
The Hampton Roads Sanitation District Commission operates several
sewage treatment plants with nearly sixty pumping stations, the majority
of which affect the water quality of the Elizabeth River. Occasionally
these pumping stations overflow and raw untreated sewage enters the
Elizabeth River. This situation contributes significantly to the high
levels of coliform bacteria in the receiving waters.
A recurring eutrophication problem in the Elizabeth River is
alledgedly the result of two plants - the Lamberts Point and Army
District Sewage Treatment Plants. Quantities of algae rivaling
those found in the upper Potoomac Estuary were evidenced in photographs
of the Elizabeth River taken by a resident of the area.
The Hampton Roads Sanitiation District Lamberts Point Treatment
Plant serves a population of 220,000 and has a design capacity of
24 MGD. At the present time this primary plant is utilized at a
25 MGD rate. Based on 1971 data the plant provides only 20% BOD
removal and discharges approximately 24,000 Ibs/day of BOD into the
Elizabeth River.
The Hampton Roads Sanitation District Army Base Treatment Plant
serves the James River north of the Lamberts Point Treatment Plant.
The plant has a design capacity of 11 MGD and is presently being
-------
IV - 257
utilized at a 12.3 MGD rate. Based on 1971 data the plant provides
28% BOD removal and discharges 11,300 Ibs/day of BOD into the receiving
waters.
Based on the Municipal Waste Quality Inventory and Waste
Facilities Needs Data Report compiled by EPA in cooperation with the
Virginia State Water Control Board the following TableIV-53 is a list
of Hampton Roads Sanitation District Treatment Plants.
Two additional treatment plants not listed in the Municipal
Waste Facility Inventory and Waste Facilities Needs Data Report
are in operation on the Main Branch and Southern Branch of the
Elizabeth River. A 15 MGD primary treatment plant is in operation
at Pinner Point on the Main Branch. This plant is not well operated
and, as a result, frequent overflows of untreated sewage into the
Elizabeth River are not uncommon. A 2 MGD sewage treatment plant
is in operation at Great Bridge (State Highway Number 168) on the
Southern Branch of the Elizabeth River.
-------
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IV - 259
NUTRIENTS
The domestic and industrial waste input to the Elizabeth River
contributes not only to high levels of coliform bacteria and toxic
industrial wastes but also to progressive stream fertilization which
ultimately leads to excessive algal growth. High nutrient levels,
especially nitrogen and phosphorus, contribute to dense algal growth
and resultant stream deterioration.
In November 1971 the Annapolis Field Office, EPA, Region III,
conducted an intensive water quality survey of the James and Elizabeth
Rivers. The data from this study are presented in the following
table:
-------
Table IV-54
ELIZABETH RIVER SURVEY
November, 1971
Annapolis Field Office
IV - 260
STATION
L-26
L-27
L-28
L-29
L-30
L-31
L-32
L-33
L-34
SECCHI
DISK
inches
36
42
35
44
40
36
36
30
24
42
48
40
42
30
34
36
36
36
30
34
24
36
36
30
27
48
27
DATE
TEMP T. PO
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
11-02-71
11-03-71
11-04-71
7.30
7.20
6.80
7.10
7.20
6.70
7.15
7.10
6.70
7.15
7.20
6.65
7.10
7.20
6.55
7.25
7.00
6.60
7.20
7.00
6.55
7.10
6.90
6.60
7.00
6.80
6.80
Pi
TKN
mg/1 mg/1 mg/1
22.87 0.404
23.30 0.352
20.14 0.309
22.78 0.409
23.07 0.403
20.90 0.241
23.2 0.373
23.2 0.341
20.64 0.276
23.03 0.459
23.04 0.386
21.06 0.451
23.12 0.440
23.15 0.481
21.31 0.528
23.18 0.438
23.10 0.462
21.50 0.418
23.30 0.404
23.40 0.425
21.00 0.574
23.73 0.432
23.72 0.366
21.70 0.462
24.00 0.462
23.67 0.405
22.04 0.561
0.408 0.790
0.332 0.610
0.334 0.830
0.337 0.840
0.290 0.670
0.306 0.870
0.354 0.960
0.252 0.920
0.244 1.200
0.435 1.010
0.326 0.800
0.354 0.980
0.406 1.080
0.364 0.830
0.371 1.010
0.427 1.060
0.354 0.890
0.365 1.120
0.392 1.120
0.355 0.940
0.346 1.060
0.470 1.100
0.336 1.210
0.363 1.000
0.418 1.130
0.332 1.030
0.413 1.100
N00+N0.
WT
0.390
0.371
0.373
0.360
0.328
0.348
0.336
0.302
0.354
0.334
0.300
0.327
0.315
0.319
0.331
0.303
0.309
0.324
0.291
0.308
0.327
0.290
0.315
0.310
0.290
0.302
0.314
-------
IV - 261
Table IV-54 (Cont.)
ELIZABETH RIVER SURVEY
November, 1971
Annapolis Field Office
STATION NH2 DO BODr TOC TC CHLOROPHYL CONDUCTIVITY SALINITY
mg/T mg/1 mg/T mg/1 mg/1 yg/1 y mhos ppt
0.343 6.23 1.48 5.49 20.04 6.0 18.35 11.60
L-26 0.396 6.69 1.19 7.12 21.13 - 19.18 12.06
0.378 7.28 1.28 9.49 23.50 - 18.65 12.45
0.343 5.29 - 5.41 19.62 7.5 19.28 12.18
L-27 0.348 6.48 - 6.72 20.35 - 19.40 12.30
0.652 6.56 - 10.39 24.24 - 20.00 13.30
0.516 5.87 1.60 6.29 20.04 9.8 17.82 11.24
L-28 0.512 6.09 1.41 8.22 21.61 - 18.40 11.90
0.594 6.77 1.96 12.30 25.54 - 18.14 12.00
0.520 5.03 1.56 8.01 22.42 4.5 19.22 12.10
L-29 0.427 1.33 - 8.26 22.17 - 20.15 12.74
0.537 6.25 1.12 11.41 25.24 - 20.14 13.20
0.506 4.77 - 11.27 23.96 8.3 19.45 12.24
L-30 0.463 - - 10.02 24.64 - 20.25 12.85
0.598 5.30 - 14.74 27.65 - 19.93 13.10
0.598 4.33 1.50 12.76 25.72 3.0 19.34 12.12
L-31 0.463 - 0.74 11.60 26.10 - 19.75 12.55
0.517 5.71 0.94 15.21 28.01 - 19.40 12.66
0.702 4.23 - 10.42 23.83 6.8 18.20 11.44
L-32 0.515 5.02 - 4.43 23.60 - 19.20 12.00
0.755 5.30 - 23.07 33.84 - 17.70 11.58
0.506 4.52 1.68 15.30 26.94 12.0 19.34 12.00
L-33 0.488 5.02 1.49 7.36 25.15 - 19.76 12.33
0.494 6.31 1.13 19.42 31.12 - 20.00 12.88
0.500 4.27 - 17.99 28.83 6.8 18.18 11.24
L-34 0.441 4.76 1.41 10.03 27.35 - 18.50 11.50
0.502 5.01 - 22.41 33.45 - 18.53 11.90
-------
IV - 262
During 1969, 1970 and 1971 the VWCB monitored portions of
the Eastern and Southern Branches of the Elizabeth River. Sporadically
high nutrient levels were detected at three stations. The following
table presents the nutrient data collected by the VWCB.
-------
IV - 263
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IV - 264
Sediment data for the Elizabeth River beginning off Craney Island
in the Elizabeth River Channel and extending down the Southern Branch
of the Elizabeth River is presented in Figure IV-47. Although these
data, collected by the Virginia Institute of Marine Science in the
summer of 1971, are not extensive they do illustrate some areas where
high concentrations of total Kjeldahl nitrogen, COD, volatile solids
and total phosphorus have been detected.
Total Kjeldahl nitrogen concentrations in the sediment vary from
1000 ppm near Craney Island to nearly 35,000 ppm (3.5%) at nautical
mile 14 in the Southern Branch of the Elizabeth River (Intracoastal
Waterway in the vicinity of State Highway 168). Organic loadings
from treatment plant effluents are indicated by high total Kjeldahl
nitrogen concentrations. High TKN concentrations in sediment may be
indicative of the direct influence of the six treatment plants on the
Elizabeth River.
The chemical oxygen demand and volatile solids percentage in the
sediment increase nearly uniformly from mile zero (at Craney Island)
to mile 14 (Southern Branch - Intracoastal Waterway). This steady in-
crease from Craney Island Reach to the Southern Branch (State Route 168)
is indicative of the buildup of biologically resistant matter. The
intense industrial development and corresponding deposition of toxic
matter into the Elizabeth River is no doubt a contributing factor
to the condition illustrated in Figure IV-47.
Total phosphorus concentration in the sediment varies from
-------
IV - 265
VOLATILE SOLIDS
3 4
ELIZABETH
RIVER (MILES FROM MOUTH)
Figure IV-47
-------
IV - 266
approximately 10 ppm to 300 ppm. Peak values were detected at numerous
stations in the Elizabeth River.
Lead, mercury, zinc and copper concentrations in the sediment are
illustrated in figure IV-48. Due to sluggish tidal cycles which inhibit
the fresh water inflow, the suspended matter introduced into the
waterway via natural conditions and heavy industrial loading renders
the bottom sediment toxic. High levels of mercury (3 ppm), lead (500 ppm),
zinc (1200 ppm) and copper (300 ppm) were detected by the Virginia
Institute of Marine Science.
-------
600 -i
IV - 267
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400-
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-------
-------
IV - 268
N. LOWER CHESAPEAKE BAY
For the puposes of this discussion, the lower Bay area includes
all open waters of the Bay from Smith Island seaward to the Atlantic
Ocean.
Whaley et al., Chesapeake Bay Institute, The Johns Hopkins University,
conducted 24 surveys of the upper Chesapeake Bay and several of its
tributary rivers during 1964, 1965, and 1966. The primary purpose of
this study was to inventory the distributions of the various forms of
phosphorus and nitrogen. The results of this study were recently
reported by Dr. Donald W. Pritchard, Director of the Chesapeake Bay
Institute (CBI Contribution Number 154).
The Bay sampling stations, in the study mentioned above, extended
from the mouth of the Susquehanna River seawerd to a point in the Bay
just below the mouth of the Potomac River. Some of these earlier
studies are compared with more recent data discussed in the upper Bay
and Sandy Point sections of this report.
The Chesapeake Bay Institute has conducted more recent studies
which included surveys of nutrient distribution throughout the entire
length of the Bay. These surveys were conducted on a monthly basis from
April 1969 through May 1971. The samples are still being analyzed with
results expected during fall of 1972. Once interpreted, this data
should provide a general picture of nutrient distribution in the lower
Bay, heretofore not known, as well as a basis for determining changes
in nutrient concentration in the middle and upper Bay.
-------
-------
V - 1
CHAPTER V
DATA EVA....I ITION AND INVENTORIES
A. DATA EVALUATION
It is estimated that approximately 50 institutions and federal
and state agencies are involved in data collection and analysis in the
Chesapeake Bay or its tidal tributaries.
The nature of this report and the resources available to the authors
precluded a comprehensive inventory of all sources of "water quality"
data. Major emphasis was placed on obtaining current data from the reg-
ulatory agencies involved in monitoring programs to assure compliance with
water quality standards. Those agencies were: the Annapolis Field Office,
EPA; the Virginia Water Control Board; the Maryland Department of Water
Resources; the District of Columbia Department of Environmental Services;
and the Maryland Department of Health, which monitors shellfish waters.
Other sources of data, collected by various institutions, were utilized
in attempts to identify possible water quality trends for a particular
estuarine area and as a supplementary nature where data were limited. Flow
data from the U. S. Geological Survey were sought to relate, for example,
depressed dissolved oxygen concentrations under low-flow conditions.
Monitoring data of the regulatory agencies of the District of
Columbia, Maryland, Virginia, and the Environmental Protection Agency
showed contraventions in numerical water qualtiy standards for the
particular time the sample was taken. Standards for which numerical
criteria were adopted are: pH, temperature, dissolved oxygen, and bacteria
-------
V - 2
(fecal and/or total coliform). Monitoring, for the most part, was con-
ducted during the critical high temperature periods. Two to three sets
of data usually were available for the summer months of June, July, August,
and September. Although attempts are made to collect data at slack water
tide (high or low), the limited manpower and resources of the agencies
did not always permit the correlation of data collection with tidal stages.
Where data collection was correlated with tidal stage and freshwater flows,
it is limited to a sub-estuary of the Bay, for example, the upper Potomac
Estuary.
Parameters for which there are no required numerical stream or eff-
luent standards, but are considered essential for predicting water quality
effects on the Bay are discussed below. The following discussion pertains
to data from the regulatory agencies .
Pesticides^;
The Virginia Water Control Board (VWCB) began sampling for pesticides
in the Rappahannock, York, and James Estuaries in its routine survey
during the 1970 sampling season. Detection and identification of pest-
icides is generally by the two major categories, chlorinated hydrocarbons
and thio-phosphates. However, specific chlorinated-hydrocarbon com-
pounds were isolated for the James River. The Maryland Department of
Water Resources (MDWR) does not currently monitor pesticides in its rou-
tine surveys. The Maryland State Department of Health (MDH) checks shell-
fish for pesticide content when contamination is expected.
The District of Columbia Department of Environmental Services (DCDES)
does not monitor pesticides in the Washington area of the Potomac River.
-------
V - 3
The Annapolis Field Office (APO) of EPA now has an in-house cap-
ability for pesticide analysis and will begin inclusion of pesticide mon-
itoring during intensive surveys of water quality problem areas. Prior
to this, pesticide samples-were sent to the Beltsville Laboratory for
analysis.
There is a need for expansion of current pesticide detection pro-
grams, especially in the economically important shellfish areas. Poly-
chlorination biphenyl (PCB) should also be monitored. The WCB did
include PCB's in its James River surveys. Intensive surveys should be
carried out to establish background levels for pesticides and PCB's,
followed by routine monitoring to detect changes in concentrations and
significant sources.
Heavy Metals:
The MDWR samples for metals in special studies, such as power plant
effluent effects and proposed sites for power plants. In the case of
the Calvert Cliff plant, radiation levels were measured off-shore of the
construction site. With fev exceptions, metals are not routinely mon-
itored by MDWR. The MDH analyzed shellfish for metal content when con-
tamination was expected. The WCB began monitoring for metals during
1970. In 19TO, the following metals were sampled in the James Estuary:
arsenic, cadmium, chromium, copper, iron, lead, manganese, mercury, and
zinc. The AFO has a metals analysis capability and has recently increased
its monitoring of metals in both water and bottom sediment. The DCDES
does not sample for metals.
There is a need for intensive surveys to ascertain background levels
-------
V - 4
of metals, especially in shellfish, waters. This should be followed up
by periodic monitoring to note any buildup of metals.
Nutrients:
All the agencies discussed herein routinely monitor for the various
nutrient fractions of nitrogen and phosphorus. Only MDWR and APO include
measurements of chlorophyll a to determine standing crops of phyto-
plankton.
There is a critical need to establish nutrient-phytoplankton rela-
tionships in areas, such as the upper Chesapeake Bay and the Potomac
Estuary, where organic pollution is believed to be causing accelerated
eutrophication with its accompanying dissolved oxygen depletions. Cur-
rantly, nutrient monitoring is neither intensive nor extensive. Nutrient
data obtained in the various tidal tributaries are not correlated with
the net inflow at the mouth of the Bay, which is required to assess the
effects of nutrients on the Bay proper.
Data Needs;
As previously mentioned, data collection and analysis is estimated
to be scattered among some SO institutions and federal and state agencies.
The intricate patterns of tides and currents have historically restricted
investigators to small areas of more manageable proportions. In some
instances, such as the upper Potomac Estuary, enough data were collected
and interpreted to allow simulation studies of the effects of waste
discharges on the receiving waters. Studies have been limited, however,
to predictions of water quality in defined areas of tidal tributaries to
the Bay. The conspicuous absence of historical data throughout the Bay
-------
V - 5
on a systematic basis prevents the prediction of the effects of wastes
discharged in a particular estuary or Susquehanna River contributary
loadings on other segments of the Bay.
A knowledge of water quality of the entire Bay is essential. Water
quality sampling over an extended period of time, and as frequently as
possible, is needed for all tidal tributaries of the Bay and the Bay it-
self. Sampling in the tidal tributaries should occur at slack water
tide with freshwater inflows recorded. Concurrent slack water sampling
boat runs up the entire main channel of the Bay would be a vital element
of this program. The resulting data from the tidal tributaries would
then be integrated, with the slack water runs data, to give an overall
picture of the water quality conditions of the Bay for the sample period.
-------
V - 6
B. DATA INVENTORIES
Two "basic types of data were used in the formulation of this report:
l) water quality monitoring data (including reports interpreting data),
and 2) inventories of waste discharges (including data from waste dis-
charge sampling). Since the volume of information acquired and used was
extensive, it was impractical to include all of the data in the report.
Therefore, it was determined that this data should be compiled and made
easily accessible to those interested in further or more detailed exam-
ination of the water quality in the Bay. In order to provide this access,
a computerized data storage and retrieval system (STORET), developed by
the Environmental Protection Agency and its predecessor agencies, will
be utilized. As well as serving as a repository for the data collected
during this study, STORET will serve as the source for much of the infor-
mation collected in future studies.
The following paragraphs are intended to give the reader a brief
description of the types of data available in, and the capabilites of,
the STORET system. Anyone desiring a more detailed knowledge of STORET
or wishing to obtain copies of available data may contact the Surveillance
Branch of the EPA Region III Office, 6th and Walnut Streets, Philadelphia,
Pennsylvania 19106.
Water Quality Data
The STORET system was c>riginally conceived as a method for central
storage of water quality data. Hence, this is the most sophisticated
of the subsystems that comprise STORET. Water quality data collected by
-------
V - 7
EPA, U. S. Geological Survey, and state and other participating agencies
has been stored over the last few years and was available for interpre-
tation during this study. The data which was gathered by the authors
from sources cited throughout the text will also be computerized in STORET
as soon as possible, manpower and resources permitting.
Water quality data is stored in the STORET system by unique station
number which is identified by either mileage from the mouth of the river
(River Mile Indexing) or latitude and longitude. Within the station
designation, data is stored by date, time and depth to further identify
its origin. The samples are characterized by physical, chemical and
radiological parameters which are virtually limitless and number more
than 500. There has been some difficulty in classifying biological
parameters for use with the system but work in this area will continue.
The Virginia Water Control Board also operated a computerized data
storage and retrieval system which handles all of the data collected in
Virginia. The Maryland Department of Water Resources is presently
working on a system for computerizing their water quality data.
Municipal Waste Inventory
The Municipal Waste Inventory became the second subsystem in STORET
based on the Public Health Service inventory of 1968. A continuous up-
dating procedure has since been developed by EPA and the various states
to keep the inventory as current as possible and to include information
on future waste treatment needs. The states initially provided a listing
of all present or planned sewage treatment plants and now periodically
update the information carried in each waste facility record. EPA has
-------
V - 8
taken responsibility for the computerization of the data and for pro-
viding it to interested parties as well as to the states.
Information about each plant is stored under a unique identification
number which represents the plant by state, city and facility codes. Data
is stored in three separate sections for each plant. The first section
contains identification data and shows, among other things, the county
and community in which the plant is located, receiving waters, latitude
and longitude of the ouofall, and census statistics. The second section
describes the physical plant and includes the type of sewer system employed,
population served by the plant, type of treatment, actual and design flows
and loads, percentage removals of organics and nutrients, and the kinds
of equipment used in the treatment process. The third section is entitled
"Waste Facilities Needs Data" and contains information on cost and type
of new construction required and schedules for completion of new projects.
Industrial Waste Inventory
The industrial inventory was the last of the subsystems added to
STORET and was primarily designed to store information on implementation
of new facility construction by industries. Since this inventory listed
only industries with construction needs, it did not meet the requirements
of this study. The basic format of this inventory was modified and the
inventory was expanded to include all of the industries which have filed
for permits to discharge with the Corps of Engineers. The existing
record format contained information on the county and city where the
plant is located, the receiving waters, schedules of new construction,
waste discharge flows, and latitude and longitude of discharges. The
-------
V - 9
modifications were instituted to acquire the flexibility to include
information on the type of waste being discharged and the type of treat-
ment presently employed.
A more elaborate vaste inventory system (RAPP) based totally on the
Corps of Engineers permit applications is currently being developed.
When this new inventory is completed (probably January 1973) the modified
inventory developed for this report will be obsolete and will be replaced
by the RAPP system.
-------
-------
ACKNOWLEDGMENTS
The authors, Thomas H. Pheiffer, Daniel K. Donnelly, and
Dorothy A. Possehl of the Annapolis Field Office, Region III, EPA,
wish to express their appreciation to those who assisted in the pre-
paration of the report.
Special thanks go to Michael E. Bender, Virginia Institute of
Marine Science: A. W. Madder, Virginia State Water Control Board;
William M. Sloan, Maryland Environmental Services; John R. Longwell,
Maryland Department of Water Resources; Samuel Fowler, Maryland De-
partment of Health and Mental Hygiene; and Carol Feister, The Johns
Hopkins University.
The authors also wish to acknowledge the assistance of all staff
members of the water chemistry laboratories of the institutions and
federal and state agencies who contributed data for this report.
Without their analysis of water samples, data would not be available
for presentation.
-------
-------
EPA-903/9-73-OO2-a
SUMMARY AND CONCLUSIONS
from the
forthcoming
Technical Report 56
"Nutrient Enrichment
and
Control Requirements
in the
Upper Chesapeake Bay"
Annapolis Field Office
Region III
Environmental Protection Agency
-------
EPA-Q03 -'9-73-O02 -a
Annapolis Field Office
Region III
Environmental Protection Agency
SUMMARY AND CONCLUSIONS
from the
forthcoming
Technical Report 56
'Nutrient Enrichment and Control Requirements
in the
Upper Chesapeake Bay"
Leo J. Clark
Daniel K. Donnelly
Orterio Villa, Jr.
August 1973
-------
ABSTRACT
The upper portions of the Chesapeake Bay and its tidal tributaries
are currently suffering from an insidious eutrophication problem as
evidenced by the increased frequency and persistence of undesirable
algal blooms and the dramatic changes in the Bay's natural flora which
have recently been experienced. Water quality monitoring data collected
between 1968 and 1971 have shown an upward trend in phosphorus levels
and indicated that inorganic nitrogen may presently be the growth rate-
limiting nutrient since it is almost nonexistent during peak bloom
conditions. Moreover, utilizing a combination of historical field data
and laboratory data to estimate biological uptake requirements led to
the conclusion that phosphorus was being recycled at least twice during
the algal growing season in the upper Chesapeake Bay.
In order to limit the maximum algal standing crop to 40 pg/1
chlorophyll a_, it was determined that total phosphorus and inorganic
nitrogen concentrations should not exceed 0.12 mg/1 (PCty) and 0.8 mg/1,
respectively. The achievement of these concentrations necessitates
the institution of a considerable abatement program in the two areas
responsible for most of the nutrient contributions to the upper Chesa-
peake Bay, namely the Susquehanna River Basin and the Baltimore metro
area. A quasi-verified dynamic estuary water quality model was used
to ascertain the maximum allowable phosphorus and nitrogen loadings
from both areas to maintain the aforementioned criteria for three
different Susquehanna flow conditions (10,000, 30,000 and 50,000 cfs).
For the two lower flow conditions a 70 percent reduction in the
existing phosphorus load would be required from both the Susquehanna
Basin and the Baltimore area. During the high flow condition a
reduction of over 90 percent of the point source discharges in the
Susquehanna must be realized to achieve the phosphorus criterion.
Nitrogen is considerably less manageable in the Susquehanna Basin
than phosphorus, especially during higher flow periods. Nitrogen
control may be a feasible alternative under extremely dry weather
conditions, but concentrated slugs of nitrogen associated with storm
water runoff would undoubtedly contravene the criterion because of
the Bay's exceptionally long flushing time.
-------
PREFACE
This report is intended to serve as an interim document
for disseminating the Annapolis Field Office's technical information
on the upper Chesapeake Bay. The report presents a series of
conclusions and graphically displayed supportive data relevant
to the current eutrophication problem in the upper Bay. The authors
hope to have a full report elaborating on these findings
completed in the near future.
-------
-------
1
The Annapolis Field Office of the U. S. Environmental Protection
Agency initiated a routine water quality monitoring program in the
upper Chesapeake Bay during 1968 in order to evaluate the effects
of a wastewater discharge from the proposed Anne Arundel County
Sandy Point Sewage Treatment Plant (STP) near Annapolis, Maryland.
This monitoring effort has continued to the present time and has
expanded in scope to include the following objectives: investigation
of recent trends resulting in the present eutrophic state of the
upper Bay; delineation of major nutrient inputs to the upper Bay;
mathematical model development to establish allowable loadings for
these inputs under varying flow conditions so as not to exceed a given
algal bloom condition; compilation of sufficient statistically
valid data which would allow management decisions to be made in
accordance with desired objectives. Results of AFO studies and related
data collected by other interested agencies are summarized as follows:
1) The Susquehanna River is the major contributor of
freshwater to the upper Chesapeake Bay and is the
primary factor influencing the Bay's salinity regime
and inorganic silt load. The Susquehanna exhibits a
classical hydrograph of high spring flows, often
exceeding 100,000 cfs, and flows of 10,000 cfs or
less during the summer and fall months.
2) The net advective velocities and travel times throughout
the upper Chesapeake Bay system vary directly with
Susquehanna River flows. The theoretical times required
-------
for a particle of water leaving the Susquehanna
River to reach the vicinity of Annapolis, Md., a
distance of approximately 32 miles, based upon a "plug
flow" analysis are given below for several sustained
flow conditions:
Susquehanna Flow Travel Times
(cfs) (days)
10,000 125
30,000 40
50,000 25
100,000 12
3) Sampling data collected from six transects (A through F)
along the Chesapeake Bay between the entrance to Baltimore
Harbor and the Severn River (see Basin Map in Appendix)
indicated that nitrogen and phosphorus concentrations
within each transect were relatively uniform, both
laterally and vertically, and spatial differences from
one transect to the next were generally small. Spatial
concentration gradients between these transects were
more pronounced for chlorophyll due to the effects of
wind and tide action causing blooms to occur as discrete
patches rather than as a uniform mixture.
4) Compositing all of the transect data collected since
1968 revealed the following:
-------
-------
a) Maximum concentrations of total phosphorus
(as PCL) exceeded 0.2 mg/1 during the late
summer and fall periods of 1969, 1970 and
1971. Minimum concentrations (0.08 - 0.12 mg/1)
were consistently found during the spring.
Total phosphorus concentrations in the upper
Chesapeake Bay have generally shown an
upward trend from 1968 to 1971.
b) Inorganic phosphorus concentrations during the
period 1969 to 1971 varied from about 0.04 mg/1
to 0.18 mg/1. Temporal variations in concentration
paralleled those observed for total phosphorus
with only slight differences in phasing noted.
c) Spatial differences in total phosphorus
concentrations were not extreme in the upper
Chesapeake Bay. Summer data collected from
1969, 1970 and 1971 generally showed concentrations
increasing between the Sassafras River and
Baltimore Harbor and remaining relatively high
downstream of Baltimore Harbor.
d) Total nitrogen (TKN + NOO and inorganic nitrogen
(NH., + NO,) concentrations varied from 0.5 mg/1
O O
to 1.2 mg/1 and from 0.05 mg/1 to 1.0 mg/1,
respectively, during the study period. Both
parameters exhibited similar seasonal variations
-------
with maximum concentrations observed in the
winter and spring and minimum values in the
summer.
e) Of the two components comprising inorganic
nitrogen, the nitrate form was predominant
(0.6 mg/1 vs. 0.3 mg/1 ammonia nitrogen)
during algal non-bloom periods while both
were minimal during peak bloom periods. This,
coupled with the fact that the Susquehanna
River water entering the Bay is highly nitrified
(refer to table on page 10), would appear to
indicate that (1) the nitrification reaction
(NH3+N03) is comparatively insignificant in the
Bay and (2) inorganic nitrogen may be the algal
growth rate-limiting nutrient at the present
time.
f) Organic nitrogen levels were greatest (0.4 -
0.5 mg/1) during periods of maximum algal
blooms. Background amounts (0.1 - 0.2 mg/1)
of refractory organic nitrogen compounds were
continuously present throughout the upper Bay.
g) Neither total nor inorganic nitrogen exhibited
a clearly defined upward trend between 1968 and
1971, however, adequate data were not available
to establish the critical pre-bloom concentrations
-------
of these parameters during the period Dec. 1970 -
April 1971.
h) Summer concentrations of inorganic nitrogen in
the upper Chesapeake Bay showed a substantial
decrease between the Sassafras River and Bush
River. During the maximum bloom periods of 1971
a continued, but more gradual, decrease in
concentrations were observed between Bush River
and Annapolis whereas prior years with lower
bloom intensities showed a rise in inorganic
nitrogen opposite Baltimore Harbor.
i) Both maximum and average chlorophyll concentrations
measured in the upper Chesapeake Bay under summer
conditions have showed a significant rise between
1968 and 1971 as indicated in the following table:
Year Max Chloro Avg Chloro
TygTT) (yg/D
1968 50 37
1969 50 30
1970 60 50
1971 188 100
j) During the critical bloom years of 1970 and 1971
drastic increases in chlorophyll were observed
in the Bay opposite Baltimore Harbor; maximum
chlorophyll levels persisted for approximately
-------
5 miles longitudinally and then decreased
sharply between the Magothy and Severn Rivers.
5) There have been subtle but important changes in the
biological conditions of the upper Chesapeake Bay area
which should be recognized and which may add support
to several conclusions drawn strictly from chemical
data.
a) Tidal portions of upper Bay tributaries such as
the Sassafras, Bohemia, Elk and Northeast Rivers
have been experiencing a change in flora which
is probably indicative of accelerated eutrophi-
cation. During the early 1960's sizeable blooms
of water chestnut and subsequently Eurasian
water milfoil were observed in these areas on
several occasions. By 1968 a succession from
green to blue-green algae had already occurred.
Extensive blue-green algal blooms composed of
Anacystis , Anabaena and Osci1latoria now inhabit
many portions of the Sassafras, Elk and Northeast
Rivers with increasing frequency, intensity
and duration.
b) The upper portions of the Bay proper including
both mesohaline and freshwater areas have recently
experienced a dramatic disappearance of the
normal rooted aquatic plants. This may have serious
-------
repercussions as a prelude to further adverse
biological successions. Moreover, these rooted
plants have served as a nutrient "trap" especially
in areas such as the Susquehanna flats. Without
their biological utilization of nutrients, greater
proportions of nutrients will be available to
the undesirable forms of algae if inputs remain
the same.
c) Ecological trends in the Bay's upper tributaries
have closely paralleled those documented for the
Potomac Estuary. A similar process is probably
underway in the upper Chesapeake Bay itself. Visual
observations of profuse algal blooms are being
recorded with greater frequency and persistence
and corroborate the rising trends shown by the
chlorophyll data previously presented. Of
major importance is the fact that the recent
elevated levels of chlorophyll are in part due
to increasing standing crops of undesirable
blue-green forms of algae.
While chlorophyll may not be the ideal
indicator for assessing the standing crop of
algal communities, it is nevertheless one of the
few effective tools currently available which
allows us to develop rational nutrient
limitations.
-------
6) Evaluation of pertinent data collected at each station
within the six transects indicated that maximum chlorophyll
levels were accompanied by low concentrations of inorganic
nitrogen and phosphorus. Conversely, high concentrations
of these nutrients were noted when chlorophyll levels
were relatively low.
7) Based upon a euphotic zone with a depth of 15 feet and
9 3
a total volume of 25.5 x 10 ft between transects
A and F, and the elemental composition analysis performed
on algal cells from the Potomac Estuary, the following
zonal nitrogen and phosphorus loads would theoretically
be required to yield the indicated bloom concentration,
as measured by chlorophyll a_, assuming complete utilization
by the cells and no re-cycling of the nutrients:
Chlorophyll Inorg. Phosphorus (PCO Inorganic Nitrogen
(ug/1)(Ibs)^ (Ibs)
30 140,000 500,000
40 190,000 650,000
50 240,000 800,000
100 475,000 1,600,000
8) Historical field data collected by AFO and the Chesapeake
Biological Institute (CBI) were utilized to estimate
nutrient losses that may have resulted from biological
uptake by the algal cells. Loading differences for
inorganic nitrogen and phosphorus measured in the
Chesapeake Bay zone between transects A and F during
-------
pre-bloom and peak-bloom conditions (the difference
representing nutrient uptake) are summarized in the
table below:
Inorganic Inorganic
Year Chlorophyll Phosphorus (PCL) Nitrogen
1965*
1968
1969
1970
1971
(ug/D
40
37
30
50
100
(Ibs)
150,000
**
150,000
250,000
400,000
(Ibs)
1 ,400,000
1,400,000
1 ,000,000
1 ,800,000
**
* CBI data
** Inadequate data to establish pre-bloom loading
condition
9) A comparison of the data shown in the previous two tables
reveals a favorable agreement between phosphorus loads
required to yield a given bloom as estimated from
laboratory and historical field data. In the case of
nitrogen, however, loadings determined from field data
were consistently double those derived from the
laboratory elemental analysis data.
10) This over-utilization of nitrogen coupled with:
(1) the fact that measured increases in organic
nitrogen from pre-bloom to peak-bloom periods confirmed
laboratory estimates of inorganic nitrogen uptake
requirements to support such blooms and (2) the extremely
-------
10
low phosphorus loss rates in the upper Chesapeake Bay
as estimated by two independent methods reinforces the
argument espoused by Dr. Donald Pritchard of the
Chesapeake Bay Institute, that phosphorus was being
recycled at least twice during the algal growing season.
11) A considerable quantity of nitrogen and phosphorus data
has been collected from the Susquehanna River at
Conowingo Dam between 1969 and 1972. Several regression
analyses were performed with this data in an attempt to
relate nutrient loadings with streamflow. The results
of these regression analyses, all of which were
statistically valid, are presented in the following table:
Susq
Flow TPCL Inorg P TN_ Inorg N N(33
(cfs) Ibs/day
10,000 7,500 3,500 80,000 58,000 40,000
50,000 50,000 30,000 400,000 300,000 250,000
100,000 120,000 75,000 800,000 600,000 530,000
12) Based on the above loadings it can be concluded that
the Susquehanna water was highly nitrified and that the
inorganic fractions represented an appreciable proportion
of the total nitrogen and phosphorus at all flows.
13) Regression analyses performed separately with the 1969
and 1971 total nitrogen and phosphorus data revealed
distinct loading increases for both parameters during the
-------
-------
11
two year period. A comparison of these Susquehanna
loadings is given in the table below:
Flow Total Phosphorus Total Nitrogen
(cfs) (Ibs/day) (Ibs/day)
1969 1971 1969 1971
10,000 6,500 8,500 75,000 82,000
50,000 60,000 75,000 370,000 420,000
100,000 150,000 190,000 750,000 850,000
14) An attempt was made to compare predicted nutrient
loadings for Susquehanna River inputs with those
loadings actually observed in a finite volume of the
Chesapeake Bay between transects A and F during the 3 year
study period. This nutrient accountability analysis was
based upon appropriate travel and displacement times
along the upper Bay for successive parcels of Susquehanna
water. The following conclusions were drawn from this
analysis:
a) The average measured total phosphorus load was
about 400,000 Ibs whereas the average expected
load from the Susquehanna was 500,000 Ibs.
Comparable values for inorganic phosphorus were
240,000 and 280,000 Ibs respectively.
b) The average total nitrogen load measured in
the Bay was 2,000,000 Ibs whereas the average
expected load from the Susquehanna was 4,000,000
-------
12
Ibs. Comparable values for inorganic nitrogen
were 1,000,000 and 3,000,000 Ibs respectively.
c) The expected total phosphorus loading in the
Bay was a function of Susquehanna River flow
and varied from about 350,000 Ibs (@ 6,000 cfs)
to 600,000 Ibs (@ 100,000 cfs). Inorganic
phosphorus behaved in a similar fashion, but
varied between 150,000 and 400,000 Ibs.
Comparable ranges for both parameters were
observed in the Bay during the study period.
d) The expected total and inorganic nitrogen
loadings in the Bay (4,000,000 and 3,000,000
Ibs respectively) were constant regardless of
Susquehanna flow. The increased daily loadings
during high flow periods were completely
negated by the shorter displacement times.
e) Phosphorus appears to behave more conservatively
than nitrogen on an annual basis since approximately
80-90 percent of the Susquehanna phosphorus
contribution was actually measured in the
Bay whereas less than 50 percent of the
nitrogen load was accounted for. Phosphorus
accountability exceeded 100 percent on several
occasions during the low flow summer and fall
periods and reached a minimum (65 percent) during
high flow periods. These extremes would
-------
13
indicate (1) the presence of an additional
phosphorus source and (2) the effects of greater
silt loads and increased phosphorus adsorption
and deposition rates generally accompanying high
flows.
15) The following table delineates average phosphorus loadings
from the Baltimore Metro Area based upon a combination
of Maryland Environmental Service (MES) data*,
information contained in the Federal industrial permit
applications, and actual sampling data:
Source Flow Total Phosphorus
(mgd) (Ibs/day as P04)
Municipal 20 4,000
Industrial 750 35,000
Other --- 1 ,000
Totals 770 40,000
16) The following table presents a similar delineation
of total and inorganic nitrogen loadings in the
Baltimore Metro Area utilizing the same data sources:
^Published in report entitled "Water Quality Management
Plan for Patapsco and Back River Basins"
-------
14
Source Flow Total Nitrogen Inorganic Nitrogen
(mgd) (Ibs/day) (Ibs/day)
Municipal 20 5,000 3,000
Industrial 750 65,000 54,000
Other --- 5,000 3,000
Totals 770 75,000 60,000
17) Water quality data collected by MES were used to eval-
uate nutrient and chlorophyll distributions in the main
channel of Baltimore Harbor during the summer growing season.
In general, the nitrogen and phosphorus concentrations
measured in the Harbor were greater than concentrations
observed in adjacent reaches of the Chesapeake Bay and
reflected the sizable loadings currently discharged from
various municipal and industrial sources. Specifically -
a) Total phosphorus concentrations in the inner Harbor
varied between 0.4 and 0.6 mg/1. The outer Harbor
exhibited relatively constant although somewhat
lower (0.25 - 0.35 mg/1) phosphorus levels.
b) Total nitrogen and inorganic nitrogen concen-
trations in the Baltimore Harbor above Sparrows
Point averaged about 1.75 mg/1 and 1.0 mg/1,
respectively. Near the mouth of the Harbor,
concentrations decreased to about 1.0 mg/1 and
0.5 mg/1, respectively.
c) Maximum chlorophyll levels (70 - 100 ug/1) were
measured between Sparrows Point and the Chesapeake
-------
-------
15
Bay. Chlorophyll values ranging from about
60 to 80 yg/1 were measured in other portions
of the Harbor.
18) Average phosphorus concentrations found across the mouth
of Baltimore Harbor were consistently 0.04 mg/1 higher
than concentrations found in the adjacent open Bay. A
similar comparison performed for inorganic nitrogen also
indicated that concentrations at the mouth of Baltimore
Harbor were consistently higher than comparable data
from the Bay proper.
19) Considering the following - (1) that nitrogen and espe-
cially phosphorus loadings to Baltimore Harbor are quite
high, actually exceeding Susquehanna loadings to the Bay
during low flow periods, (2) a considerable body of data
shows consistently higher levels of these nutrients in
the outer Harbor than in nearby areas of the Bay, (3) the
possibility of recycling of nutrients from the grossly
contaminated bottom sediments in Baltimore Harbor and
(4) the significant exchange characteristics between the
Harbor and Bay - it appears reasonable to surmise that
the Harbor adversely affects the waters of the Bay. Any
nutrient management program undertaken for the protection of
the upper Chesapeake Bay must include adequate control not
only of discharges in the Susquehanna Basin but from the
Baltimore Metro Area as well.
-------
16
20) In order to limit the algal standing crop to 40 yg/1
chlorophyll a_, an acceptable bloom condition based upon
historical observations in the Chesapeake Bay and adopted
criteria for the Potomac Estuary, total inorganic phosphorus
and nitrogen loadings in the euphotic zone between
transects A and F should not exceed 200,000 Ibs. and
1,400,000 Ibs. respectively. Converting these loadings
to equivalent concentrations yields the following -
Phosphorus - 0.12 mg/1 as PO.
Nitrogen - 0.8 mg/1
These limiting nutrient levels were derived from
historical field data, model simulation studies and
correlations with nutrient-phytoplankton relationships
developed for the Potomac Estuary.
21) The EPA Dynamic Estuary Water Quality Model has been
adapted to the Chesapeake Bay and its tidal tributaries
upstream from Annapolis, Md. with a network comprised
of 74 junctions and 88 channels. The model proved
capable of simulating the hydrodynamic behavior of
the upper Bay as evidenced by the accurate predictions
of average tidal ranges and phasing at several USC
& GS stations.
22) A review of the available field data indicated
three steady state simulation periods with different
-------
17
flow and algal bloom characteristics as shown below:
Period Susq Flow Chlorophyll
(cfs) (yg/1)
May - July, 1970 23,000 50
Aug - Oct, 1970 10,000 30
April - May, 1971 50,000 20
23) Salinity data collected during two of these flow
periods (10,000 and 50,000 cfs) were used to calibrate
and verify the advection and dispersion components of
the model. The model was then used to simulate total
phosphorus and inorganic nitrogen distributions for
determination of loss or uptake rates. In addition, one
simulation was made during the high bloom period in an
attempt to mathematically link chlorophyll with inorganic
nitrogen. The results of these model studies are summarized
as follows:
a) The model accurately simulated total phosphorus
during the Aug - Oct (1970) and April - May (1971)
periods when loss rates of 0.008 and 0.015/day,
respectively, were assumed. The increased rate
during the latter period probably resulted from
the greater adsorption and deposition potential
of the higher Susquehanna flow. Both rates were,
however, much lower than expected.
b) Inorganic nitrogen was also accurately simulated
on two separate occasions contingent upon the
-------
18
proper selection of uptake rates for first order
kinetics. The rates obtained from the model
(0.055 and 0.010/day) appeared to be highly
dependent upon existing chlorophyll levels.
c) For the high bloom period of 1970 and using
the uptake rate of 0.055/day for inorganic
nitrogen, the model satisfactorily simulated
the chlorophyll distribution observed in the
Chesapeake Bay. Since the model assumed an
immediate growth response corresponding to
any loss of inorganic nitrogen, phasing differences
between observed and predicted profiles did
exist; however, total masses compared
favorably.
24) Follov/ing calibration and limited verification, the
Dynamic Estuary Model was used to perform a series of
alternative runs for determining allowable total
phosphorus and inorganic nitrogen loadings from the
Susquehanna River and the Baltimore Metro Area to
achieve the previously indicated nutrient criteria
throughout the upper Chesapeake Bay. The results
obtained from these model runs for three different
Susquehanna flow conditions (10,000, 30,000 and
50,000 cfs) are presented in the tables following.
-------
19
Bait. Metro Area
20,000 Ibs/day
10,000 Ibs/day
5,000 Ibs/day
Allowable Loadings
Phosphorus (PO.)
(Susq. Flow = 10,000 cfs)
Susq. Basin
3200 Ibs/day (.06 mg/1)
7000 Ibs/day (.13 mg/1)
(not a viable alternative)
(Susq. Flow = 30,000 cfs)
Bait. Metro Area
20,000 Ibs/day
10,000 Ibs/day
5,000 Ibs/day
Susq. Basin
16,000 Ibs/day (.10 mg/1)
21,500 Ibs/day (.135 mg/1)
23,000 Ibs/day (.145 mg/1)
(Susq. Flow - 50,000 cfs)
Bait. Metro Area
20,000 Ibs/day
10,000 Ibs/day
5,000 Ibs/day
Susq. Basin
35,000 Ibs/day (.13 mg/1)
36,000 Ibs/day (.135 mg/1)
38,000 Ibs/day (.14 mg/1)
-------
20
Bait. Metro Area
40,000 Ibs/day
30,000 Ibs/day
20,000 Ibs/day
Allowable Loadings
Nitrogen
(Susq. Flow = 10,000 cfs)
Susq. Basin
32,000 Ibs/day (.60 mg/1)
35,000 Ibs/day (.66 mg/1)
39,000 Ibs/day (.73 mg/1)
(Susq. Flow = 30,000
Bait. Metro Area
40,000 Ibs/day
30,000 Ibs/day
20,000 Ibs/day
Susq. Basin
103,350 Ibs/day (.65 mg/1)
111 ,300 Ibs/day (.70 mg/1)
119,250 Ibs/day (.75 mg/1)
Bait. Metro Area
40,000 Ibs/day
30,000 Ibs/day
20,000 Ibs/day
(Susq. Flow = 50,000 cfs
Susq. Basin
186,000 Ibs/day (.69 mg/1)
194,000 Ibs/day (.72 mg/1)
200,000 Ibs/day (.75 mg/1)
-------
-------
21
It should be noted that the Baltimore loadings were not
predicated on the protection of Baltimore Harbor waters,
otherwise more stringent loadings would probably have
been required.
25) In view of the uncertainty in defining the various
reactions responsible for conversion of organic forms
of phosphorus to inorganic forms (and vice versa);
the almost immediate utilization of regenerated phosphorus
by phytoplankton as hypothesized by Dr. Pritchard and
somewhat substantiated by data presented in this
report; and the low apparent loss rate for phosphorus,
allowable phosphorus loadings from the Susquehanna Basin
and the Baltimore area were developed for total and
not inorganic phosphorus.
26) Inorganic nitrogen was treated as a conservative
parameter in all of the model production runs. Since
the criteria, hence the allowable loadings, apply
primarily during pre-bloom periods this appeared to be
a reasonable assumption.
27) There was insufficient field data available to calibrate
or verify adequately the mathematical model for a
Susquehanna River flow of 100,000 cfs and the effects
of this extreme flow condition on the nutrient distri-
bution in the upper Chesapeake Bay could not be
properly evaluated.
-------
22
28) Special model runs were prepared to investigate the
effects of the Sandy Point STP discharge on the
phosphorus concentrations in nearby areas of the
Chesapeake Bay. Assuming present plant design capacity
(4.2 mgd - wastewater flow; 40,000 - population served)
and the realization of adequate phosphorus control in the
Susquehanna Basin and the Baltimore area, the model runs
demonstrated that the effects of the Sandy Point STP
discharge would be minor and the phosphorus criteria in the
Chesapeake Bay could still be achieved for either Susquehanna
River flow. Any future expansion of this facility,
however, would require a thorough investigation to determine
the necessity for and extent of nutrient removal.
29) As stated previously, it is quite possible that inorganic
nitrogen is presently the rate-limiting nutrient in the
upper Chesapeake Bay; however, it is reasonable to
expect that phosphorus can be made the rate-limiting
nutrient if adequate control measures are instituted.
Phosphorus is more manageable in the Susquehanna Basin
than nitrogen, especially during higher flow periods.
Nitrogen control may be a feasible alternative under
normal dry weather conditions, but concentrated slugs of
nitrogen occurrina from natural runoff durina short-term
localized storms would probably cause the maximum
allowable nitrogen concentrations previously established
-------
23
to be exceeded during the long retention periods
resulting from slow net seaward transport.
30) A mass balance analysis was performed on all nutrient
data collected in the lower Susquehanna Basin from
June 1971 to June 1972. The results obtained from
this analysis were used to estimate the degree of
controllability of nitrogen and phosphorus during
various seasons and flow conditions. For the three
Susquehanna flows investigated, the following tables
depict the effects of different reductions of all point
source discharges on the river loadings at Conowingo:
Est. Total
% Reduction Phosphorus Load
(Ibs/day)
10,000 cfs
0
50
70
90
0
50
70
90
0
50
70
90
8,300
5,700
4,600
3,800
30,000 cfs
27,100
23,000
21 ,500
20,000
50,000 cfs
46,000
41 ,000
40,000
38,500
Est. Inorganic
Nitrogen Load
(Ibs/day)
57,000
53,000
50,000
47,000
187,500
183,500
182,500
180,000
309,000
305,000
303,000
301 ,000
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24
31) Assuming sustained Susquehanna River flows of 10,000
and 30,000 cfs and utilizing the previous two tables,
a reduction in the existing phosphorus load from both
the point source discharges in the lower Susquehanna
Basin and the Baltimore area of 70 percent will be
required to achieve the 0.12 mg/1 total phosphorus
concentration limit in the Chesapeake Bay. If a
sustained flow of 50,000 cfs is assumed, it is
doubtful whether this criteria can be attained
unless over a 90 percent reduction at each of the
point source discharges in the lower Susquehanna
Basin and the Baltimore area is realized. It is
important to recognize that the Susquehanna River
becomes increasingly significant in terms of a
phosphorus management program during higher flow
periods, especially for protection of the extreme
upper reaches of the Bay. Unfortunately, the
controllable percentage of the phosphorus load in
the Susquehanna Basin decreases dramatically for
such flow periods.
-------
APPENDIX
-------
UPPER CHESAPEAKE BAY
Al - SAMPLING STATION
ANNAPOLIS
-------
HYDROGRAPH
SUSQUEHANNA RIVER AT CONOWINGO DAM
1968- 1971)
150 —i
140 —
130 —
120 —
110 —
100 —
90 —
80 —
I 70
3
U-
60 —
50 —
40 —
30 —
20 —
10 —
r
< UJ ^ '
-t u_ Z '
1968
1969
1970
1971
-------
CROSS SECTIONAL AREAS
UPPER CHESAPEAKE BAY
(CB1 DATA)
100 H
90 H
80 H
70 H
h- 60 -\
u_
ui
cc
50 H
40
30 H
20 H
10 H
I
2
4
I
6
I
8
10
I
12
I
14
:e
i
2C
22 24 26 28 3C 32 34 36
MILES BELOV SUSQ. RIVER
-------
ADVECTIVE VELOCITIES vs, SUSQUEHANNA RIVER FLOW
UPPER CHESAPEAKE BAY
2.0 -i
1.8 -
O
o
q
u
O
ZOQOOOcfs
1 6 -
1 4 -
o
Q)
t^.
1.2 -
U
O
LJ
> 0.8 -
h-
u
LJ
Q
** 0.6 -
0.4 -
0.2 -
0.0 -
c
lOQOOOcfs
75,000 cfs
50,000 cfs
30,000 cfs
lOjOOO cfs
O
O
O
O
O
O
o
o
00
O
1 1 1 I 1 1 1 1 1 I 1 1 1 I |
•) 2 46 8 10 12 14 16 18 20 22 24 26 28 30 32
MILES BELOW SJSQUEHANNA RIVER
-------
-------
TRAVEL TIMES vs. SUSQUEHANNA RIVER FLOW
UPPER CHESAPEAKE BAY
120 -
CO
1
UJ
0 2 4 6 8 10 12 14 16 18 20 22 24 26 28 30 32 34 36
10
MILES BELOW SUSQ. RIVER
-------
TEMPORAL PHOSPHORUS DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT A
(AVERAGE DATA FOR TRANSECT)
o>
E
1.50 —
1.40 —
1.30 —
1.20 —
1.10 —
100 —
.90 —
80 —
.70 —
.60 —
.50 —
40 —
.30 —
.20 —
.10 —
0
LEGEND
TPO4
P,
zoiJjO:j;z_iOo-i->u
->U-2-><(/)OZO
1968
2 a>% a:
1969
1970
1971
-------
TEMPORAL PHOSPHORUS DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT B
(AVERAGE DATA FOR TRANSECT)
t*
E
.50
140
I 30 —'
1.20
1.10 —
1.00 —
.90 —
.80 —
.70 —
.60 —
50 —
40 —
.30
.20
.10
LEGEND
TP04
Pi
1 1
Z m J fc > 2
< ui < i < D
-> u. Z < S -j
1968
1969
1970
1971
-------
TEMPORAL PHOSPHORUS DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT C
(AVERAGE DATA FOR TRANSECT)
\
1.50 -
1.40 —
1 30 —
1.20 —
I 10 —
1.00 —
.90 -
.80 -
.70 —
.60 —
.50 —
.40 —
.30 —
.20 -
.10 —
0
LEGEND
TP04
Pi
zm* 9= 5
< i
- - -, ^ 0. >- > u.2<5->~}z-Ji3 Q^v- >O
u.2<2->->< *nO ZO
I £ Q. H > O
i 3 uj y O u
> 4 (n O Z O
1968
1969
1970
1971
-------
TEMPORAL PHOSPHORUS DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT D
(AVERAGE DATA FOR TRANSECT)
X
0>
E
1.50 —
1.40 —
1.30 —
1.20 -
1.10 —
1.00 —
.90 —
.80 -
.70 —
.60 —
.50 —
.40 —
.30 —
.20 —
10 -
LEGEND
TPO4
Pi
I O CX I- > U
, D UJ U O u
< in O z o
1968
.
->u.Z-»< tnO ZQ
1969
z CD J| a >• z
-> " Z < Z R
1970
1971
-------
TEMPORAL PHOSPHORUS DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT E
(AVERAGE DATA FOR TRANSECT)
1.50 —|
1.40 —
1.30 —
1.20
I 10 —
100 —
.90 —
V
0>
E
.80
.70 —
.60
.50
.40 —
30 —
.20
.10 —
LEGEND
TP04
Pi
.
Z->«oza
1968
z co J a > z
TU! Z < S T
1969
1970
1971
-------
TEMPORAL PHOSPHORUS DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT F
(AVERAGE DATA FOR TRANSECT)
N
o>
E
1.50 —
1.40 —
1.30
1.20
1.10 -
100 —i
.90 -
.80 -
.70 -
.60 —
.50 —
.40 —
.30 —
.20 -
10 —
LEGEND
TP04
Pi
z a, °^
->4Oza
z m <* cr> z
< ul < Q-l 3
1968
1969
1970
1971
-------
TOTAL PHOSPHORUS CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA FOR ALL TRANSECTS)
40 -i
.36 H
32 H
28 H
~ .24 H
- .20 H
c?
I- .16 H
12 H
.08 H
.04 H
.00
isiSi^ftgig
1968
n TT i i i i iTTTiiITTiTTTiiiiiTm
1969
1970
1971
-------
INORGANIC PHOSPHORUS CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA FOR ALL TRANSECTS)
.40 -i
.36 -
.32 -
.28 -\
8 20 -
.16 -
.12 -
08 -
04 -
.00
1968
1 1 1 1 1 1 1 1 1 1 1
1969
1 1 1 1 1 1 1 1 1 1 1
1970
1971
Z CO 5 IT % Z
< UJ < OL < 3
-> u. S < S ->
-------
r- °
L
cr
•
O
to
o
O.
D
(O
u
CD
in
Q.
CO
o>
UJ
L(M
I
OJ
-------
TEMPORAL NITROGEN DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT A
(AVERAGE DATA FOR TRANSECT)
\
o>
E
150 —
140 —
1.30 —
120 —
no —
1.00 —
90 —
.80 —
.70 —
.60 —
.50 —
40 —
.30 —
ao —
.10 —
LEGEND
TKN
NO2+N03
NH3
Z a>cr z _/ O a. I- > u
.
. Z <
1968
[< Z->-)4«OZQ
1969
T1 I II I
* u! I < S T
1970
1971
-------
TEMPORAL NITROGEN DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT B
(AVERAGE DATA FOR TRANSECT)
o>
e
1.50 -
1.40 -
1.30 —•
1.20 -
I 10 —•
1.00 -
90 —
.80 -
.70 —
.60 —
.50 -
.40 —
.30 —
.20 —
.10 -
0
LEGEND
TKN
N02+ N03
NH3
s? <•>
MINI
1968
1969
1970
1971
-------
TEMPORAL NITROGEN DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT C
(AVERAGE DATA FOR TRANSECT)
o»
1.50 —
140 —
1.30 —
1.20 —
I 10 —
1.00 —
.90 —
.80 —
.70 —
.60 —
50 —
.40 —
.30 —
.20 —
.10 —
LEGEND
TKN
NO2+ N03
NH3
I I I II I II I I I
1968
-
kJU O
c/lO Z
1969
I I I II I I I I I I
1970
I 1 I I 1 II I I I I
1971
I I I I I I
z cb z
-------
TEMPORAL NITROGEN DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT D
(AVERAGE DATA FOR TRANSECT)
\
o>
£
1.50 —\
1.40 -
1.30 -
1.20 —
I 10 —
1.00 —
.90 -
.80 —
.70 —
.60 —
.50 —
.40 _
.30 -
.20 -
10 -
LEGEND
TKN
• N02 + NO3
NH3
I 1 I
1 <
.
i Si o
> u
Ou
z o
Zm
1968
1969
1970
1971
-------
TEMPORAL NITROGEN DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT E
(AVERAGE DATA FOR TRANSECT)
o>
1.50 —|
1.40 -
1.30 -
1.20 —|
I 10 -
100 -
.90 -
.80 -
.70 -
.60 -
50 —
.40 —
.30 -
.20 -
.10 -
LEGEND
TKN
N02+ NO3
NH3
I I
MINIUM
z ta i
< u :
z m it z
< S < a. < D
1968
1969
1970
1971
-------
TEMPORAL NITROGEN DISTRIBUTION
UPPER CHESAPEAKE BAY
TRANSECT F
(AVERAGE DATA ' FOR TRANSECT)
1.50 —I
1.40 —
1.30 —
.20
LEGEND
TKN
NO2 + N03
NH3
1.10 —
1.00 —
.90
.80 —
.70 —
.60 —
.50 —
.40 —
.30 —
.20 —
.10 —
1968
1969
>z-iOa.t->ti
1970
> u. s « z s^ < m o z Q
1971
z a> a a; > z
< u < Q.< 3
->u. Z < S -i
-------
1.50 —|
1.40 -
1.30 -
1.20 —
1.10 -
1.00 —
.90 —
.80 —
o>
6 .70 —I
.60 —
.50 —
.40
.30
.20 —
.10
TOTAL NITROGEN CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA)
1 1 1 1 1 1 1 1 1
1968
1969
1970
1971
I I I I I I
z cb 2 a: > z
< UI< i < 3
-i u. 3. < 3. -i
-------
INORGANIC NITROGEN CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA)
\
o>
1.50 —i
1.40 -
1.30 —
1.20 —
1.10 —
1.00 —
.90 —
.80 —
.70 —
.60 —
.50 -
.40 —
.30 —
.20 —
.10 —
1 1 1 1 1 1 1 1 1 1 1
1968
1969
1970
1 1 1 1 1 1 1 1 1 1 1
1971
-------
1.50 1
1.40 —
1.30 —
1.20 —
1.10 —
1.00 -
.90 —
.80 —
.70 —
.60 —
.50 —
.40 —
.30 —
.20 —
.10
TOTAL KJELDAHL NITROGEN CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA)
1968
1969
II 1 I II M 1 1 1
1970
1 1 1 1 1 1 1 1 1 1 1
1971
I I M I I
z m * ? >; z
< u < 5 < 3
-» u. 2 < 2 -*
-------
AMMONIA NITROGEN CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA)
1.0 -i
.9 -
.8 -
.7 -
.6 -
.5-
.4 -
.3 -
.2 -
I I I I I I I M I I
TU-2
-------
1.50 —
1.40 —
1.30 -
1.20 —
1.10 —
1.00 —
.90 —
.80 -
.70 —
.60 —
.50 —
.40 -
.30 -
.20 —
.10 —
NITRATE NITROGEN CONCENTRATIONS
UPPER CHESAPEAKE BAY
(AVERAGE DATA)
T I I I I M I I I
1968
I I I I I 1 I I I I I
Za>ocor>z_JOQ-*~ > *•
u.2<2->->O Z O
1969
I I M I I I I I I I
zmuca:>zjOQ;Hg(j
•>u-Z<OZo
1970
1 IT I 1 I MI
1971
I I I I I 1
z ob 5 a 2:2
< U <
-------
,- o
o
99
cr
\-
co
^7 GO
LJ LJ
O ^
rv Ld
K!
zS
o5
Q.
CO
_ C\J
C7)
(O
O)
a o
f-
O)
O
i
I
LJ > UJ
§ ^ §
-)—>-)
I
(O
00
C\J
•
at
a
CO
_ O
to
CD
CO
- 00
<£>
-------
CHLOROPHYLL a, CONCENTRATIONS
0>
150 —
140 —
130 —
120 —
110 —
100 —
90 —
80 —
70 —
60 —
50 —
40 —
30 —
20 -
10 —
i i ,i i i i i .1 -i i i .1 i i ii i i i .1 i i
'
1968
1969
.' ' .' i UJ •'•_•' i .'.
: B o: at >-z jO£[»- >u
)u. 2 < 2 ~> -> < z
< UJ <0. < 3
-> u. Z4 Z ->
-------
o
«•
hs
CVJ
fO
O
H
D
CD
£ >
*~ <
CO CD
O uJ
_l
_J
>
I
CL
UJ
a
UJ
§5
O a
-I UJ
I Q-
0 9:
5
a
co
O)
(O
g>
H-"
a
UJ
CO
i
UJ
Z
~)
I
o
«•
• 1
1
'1
1
1
1
I
\
\
\
\
\
\
\
'-. \
•
•
F
g>
o (D
r- 3
g> <
3"i
-> ->
i
1
1
1
1
i i i i *
o o o o o
CVJ O CO
cr
6
«/)
D
Wl
-S^
0
_i
UJ
CD
CO
-2J
2
_ CVJ
- CO
-
-------
(M
p ~
3 *g
U %*
> Luhj
CL CO
< z
CO <
LU 0£
I I-
U -
CO
CC
O
I
CL
CO
O
CL
U
Ct I
U O)
CL (O
CL O)
D ~
.00
.10 \
—• o>
E
I
tO
O
a
10
y
z
tr
O
2
•8
(D
a:
O
«*
8 8
i 8 8
o
03
O
r-
o
IO
o o
(V —
-------
oo
oo
o|
OD
CL
o
cr
V H
LtJ O
> < t/>
^5
Z CL <
•S x
1 o>
E
I
u
O
O
cc
O co •"
O \$ R
tr pj g>
h- O T
Z
o>
o^S
y
z
<
o
o oc
-<* o
z
cr
O
Z
'(M
.
-------
-------
PHOSPHORUS AND NITROGEN LOADINGS
UPPER CHESAPEAKE BAY
BETWEEN TRANSECTS A & F
(volume = 45 x I09 ft3)
TOTAL NITROGEN
INORGANIC NITROGEN
TOTAL PHOSPHORUS (as PO4)
INORGANIC PHOSPHORUS (as PO4)
M
-Q
4000 -
3600 -
3200 -
2800 -
2400 -
2000 -l
1600 -
1200 -
800 -
400 -
TTIiii i i i r
IT r i n
M I I T F 1 .11 I J H IF I I II .11 I
1968
1969
1970
1971
-------
CO
a:
a.
0
u
-o
c
o
o
a
^ -
Z P
< <
O LJ
LJ
D S
g Si
TJ
O
m
O
a
to
O
<
O
o I
•" a
a O
« O
cr X
o ^
z o
cr
O
a.
\-
U
\v_
o
o
I
o
00
•D30
' 'AON
•100
j'idJW
^ Ainr r-
" 'AON
UDO
^ _
_ -oid
'AON
130
jwnr
XV H
xinr
* 3Mnr
ATM
•AON
•J.OO
'•ld3S
; -onv
'1.DO
~ -onv us
_
•AON
[-JLOO
[_ Ainr io
3Nnr o*
AVH —
•WdV
-B3J
•330
'AON
•1DO
" 'Ld3S
•onv
xinr
•O30
" 'AON
" '100
"•ld3S
"
AVH
I 'Hdt
_ 'WVW
•AON
M.d 35
•onv 0
Ainr ,n
3Nnr en
O
(O
O
(\J
10
o
(I/6*)
-------
Q
Z u.
LJ
^ 1
>
-j- lO
a. h
O LJ
cc w 5
O 5 b
_i < <
i ^ °
U o
Z u-
•o S <
UJ
LJ LU
o m
o ^
cc <
• fin
-o
o
O
LJ
<
u
z -y
O Z
+ °
«. ^
i I
o
•030
" "AON
"'100
'AON
*"'1DO
"•ld3S
'AON
' '130
3wnr
xvw
•030
'AON
~MOO
""•onv
"~ xinr
~3Nnr
~ AVW
" -a**
" -83J
" 'Nvr
~ 'AON
~ 'J.OO
~Ud3S
~-onv
"* 3Nnr
2 'HdV
" 'fl3J
" 'AON
' '130
'•onv
" Ainr
'
'AON
" '100
"•Idas
AVW
HdV
•330
"AON
' 'J.3O
'•ld3S
;-DHV ^.
Ainr 10
' 3Nnr o>
' AVW —
' 'ddV
•AOM
" 'IDC
"•idas
'onv -
Ainr ^
~ awnr en
•AON
' "iOO
'
I
o
OJ
o
o
I
o
00
I
o
(O
I
o
I
o
I
o
CO
o
(O
I
o
O
OJ
O
(I/6*)
-------
I
(fi
-z.
o
U QD
^ <
Q. CO
O 1
o
LJ
CC
-------
REGRESSION ANALYSIS
TOTAL PHOSPHORUS LOAD vs FLOW
SUSQUEHANNA RIVER at CONOWINGO
(1969-72 DATA)
UOOO.QOO -,
loo.ooo H
x
o
-Q
I
*
O
a
10x100 H
1,000-
CORRELATION COEF. ; 0.94
t- 28.10
* It
D. F. -- 95
1,000
10,000
1 ' I
100,000
1^)00.000
FLOW- cfs
-------
REGRESSION ANALYSIS
INORGANIC PHOSPHORUS LOAD vs FLOW
SUSQUEHANNA RIVER at CONOWINGO
(1969-72 DATA)
1,000.000-1
100,000-
10,000-
1.000-
CORRELATION COEF. ; 0.89
* - 18.78**
D. F. : 90
100-
1,000.000
I " '
100,000
10,000
1,000
FLOW - cfs
-------
REGRESSION ANALYSIS
TOTAL NITROGEN LOAD vs FLOW
SUSQUEHANNA RIVER AT CONOWINGO, MARYLAND
(1969-1972 DATA)
10,000,000 -
1,000,000 -
o
-o
I
z
100,000 -
10,000
IjOOO
i T i i r n
10,000
CORRELATION COEF. = 0.96
t = 31.60* *
D.F = 90
i i i i r
100,000
500,000
FLOW - cfs
-------
REGRESSION ANALYSIS
TOTAL INORGANIC NITROGEN LOAD vs FLOW
SUSQUEHANNA RIVER AT CONOWINGO, MARYLAND
(1969-1972 DATA)
10,000,000 -
IjOOO.OOO -
m
jQ
I
Z
100,000 -J
10,000
CORRELATION COEF. - 0.95
+ = 28.52* *
D.F = 87
I I I I T I I I I
IjOOO IOX)00
I I T
1 I I Ml
100,000
1 1 I
500,000
FLOW -cfs
-------
REGRESSION ANALYSIS
TOTAL KJELDAHL NITROGEN LOAD vs FLOW
SUSQUEHANNA RIVER AT CONOWINGO, MARYLAND
(1969-1972 DATA)
10,000,000 -
1,000,000 -
I
z
100,000 -
10,000
CORRELATION COEF = 0.86
t = 16.47* *
D.F. - 94
I I I I I ! I T I
1,000 10,000
I I I
I I I I I 1
100,000
I I \ \
SOOjOOO
FLOW -cfs
-------
REGRESSION ANALYSIS
NITRATE NITROGEN LOAD vs FLOW
SUSQUEHANNA RIVER AT CONOWINGO, MARYLAND
(1969-1972 DATA)
10,000,000 -|
(,000,000 -)
o
z
100,000 H
10,000
CORRELATION COEF. - 0.93
I = 23.54"
D.F =91
~ I I I I I I I 11
1,000 10,000
I I I I I I I
100,000
I III
500,000
FLOW - cfs
-------
REGRESSION ANALYSIS
TOTAL PHOSPHORUS LOAD VS FLOW
SUSQUEHANNA RIVER at CONOWINGO
( 1969 and 1971 DATA)
1,000,000 -i
100,000 H
a
-o
O
a
10,000 H
1.000 •
1969 DATA
Correlation Coef = 0.98
ttt" = 23.42 •*
D. F. = 27
1971 DATA
Correlation Coef = 0.90
wt" = 8.94 **
D. F. = 21
i
(1969 DATA)
1,000
10,000
1 ' I
100,000
1
1.000,00
FLOW- cfs
-------
REGRESSION ANALYSIS
TOTAL NITROGEN LOAD VS FLOW
SUSQUEHANNA RIVER at CONOWINGO
(1969 and 1971 DATA)
10000000 -
IJOOO.OOO -
a
-o
m
I
z
100.000 -
10,000 •
1969 DATA
Corrtlation Co«f
u»" = 11.80 **
D. F. = 24
1971
Corrtlation Co«f
" t " = 6.72 * *
D. F. = 21
= 0.93
(1969 DATA)
i
1,000
10.000
100.000
1000.000
FLOW- cfs
-------
MILES BELOW SUSQUEHANNA RIVER
TRANSECTS
36 34 32 30 28 26 24 22 20 18 16 14 12 10 8 6 4 20 DATE
i I i i i i i i i i i i i i I i
DEC, 1967
JAN 1-31 daOOOcfs)
JAN 1-31 [I8,000cfj)
FEB 2-6 (I00,000cf>)
JAN 1-31 (I8,000cfi) FEB 2-6 (lOQOOOcfs)
FEB 7-11 BQOOOcfj)
FEB 2- 6 (I00,000cfs
(SQOOOcf ')
FEB 12-29 «8,000<:f3)
FEB 2 -6 IIOQOOOcf.)
rEB 7~' '
ISOjOOOcfs)
FEB I2~29
Il8,000cfs)
MAR 1-18 (I8,000cfs)
MAR 19-31 UOQOOOrfs)
MAR 19-31 UOO.OOOcfs
APRILI-12 (50,000cfi)
APRIL 1-12 (50,000cf»
APRIL I3-MAYI3 (2QOOOcfs)
APRIL 13-MAY 13 (2QOOOcf«)
MAY 14-28 BQOOOcfs)
MAY 14 -28 (60,000cfs)
MAY29 -JUNE 6 (100,000 cfs)
JUNE 7 -JULY 6 {40,000 cfs)
JUNE 7- JULY 6 (40,000cfs)
JULY 7-31 (I2000cfs)
1/31/68
2 /6/68
2/11/68
2/29/68
3/18/68
3/31/68
4/12/68
/ /
5/13/68
5/28/68
6/6/68
7/6/68
7/31/68
33
m
r-
m
TJ
O
co
C H
? i
m co
s 9
Oi •••
oS rn
' >
5 -n
CD
^ >
m co
CD
co
co
-------
MILES BELOW SUSQUEHANNA RIVER
1 BAY 1
I TRANSECTS I
36 34 32 30 28 26 24 22 20 18 16 14 12 10 8 6 4 2 0 DATE
11
I I I I I I I I i_
I I I
JUNE 7 -JULY 6 (40;000cf»)
JULY 7-3l(l2pOOcf,J AUG I - 31 (6000cf»l
JUNE 7 - JULY 6 UQOOOcf,)
JULY 7-31 AUGI-31
SEPT l-30U4000cfs)
JUNE 7- JULY 6
140,000 cf,)
JULY7-3,
U2,000cf»)
AUG 1-31
BDOOcfsl
s£pT ,,
OCT 1-31 (7,000cf,l
JULY 7-31
(I2,000cfs)
AUGI-31
BOOOcf.)
SEPT 1-31
U4,000cfi)
OCT 1-31
TOOOrfi)
NOV 1 — 18 (20,000cfs)
SEPT ,-30 04.000C,,,
NOV 19-22 (I00,000cf»)
NOV 1 9 ~22
,100,000 cf.)
NOV 23- DEC 15 (45,000 cf.)
NOV 23- DEC 15
(45,000 cf,)
DEC 16- JAN 31 (20,000 cf,)
DECI6-JAN3I (20,000cfs)
FEB 1-12 (40,000cfj|
DECI6-JAN3I
,o^^«« ,,
(20,000 cfs)
FEB 1-12 (40,000cfj
FEB 13-MARCH 23 (15,000 cf,)
FEB 1-12
.40,000 cf,,
FEB13-MARCH23
,15,000 cf.)
24'3' (70'°00cf5)
FEB 13 -MARCH 23(15£>00cfs) MARCH 24-31 (70,000cfs)
APRIL 1-6 (40,000cf,l
MARCH 24 -31 (7QOOOcW
APR'L ' ~6
(4O,OOOcfs)
APRIL 7-10 (95,000cfsl
8/31/68
9/30/68
10/31/68
11/18/68
11/22/68
12/15/68
1/31/69
2/12/69
3/23/69
3/31/69
4/6/69
4/10/69
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MILES BELOW SUSQUEHANNA RIVER
36 34 32 30 28 26 24 22 20 18 16 14 12 10 8 6 4 2 C
I I i I 1 I 1 1 i 1 I I 1 1 1 | 1
APRIL 7-10
(95,000 cfs)
Isoioolh?
MAY 1-31 (33,000
MAY 1-31 (33,000cfs)
JUNE 1-30 (I9,000cfs)
JUNE 1-30 JULY 1-
(19, 000 cfs) (10,000
JULY 1-22 J(JLY 23
UO.OOOcfs)
JULY 23 -AUG 10 (2
AUG 11-31 SEPTI-3
(13,000 cfs) (6,OOCtfs
(3,000 cfs) l6,OOOcfs)[6,OOOc
APRIL 11-30 (SO.OOOcfs)
MAY 1 - 31 ,33,000cf.)
cfs JUNE 1 -30 (I9,000cfs)
JUNE 1-30 (laOOOcfsl JULY 1-22 (I0j000cf§)
JULY '"22 JULY23-AUGIO (28,000cfs)
(10,000 cfs)
JULY23-AUGIO (28,000cfs) AUG 11-31 (I3,000cfs)
cfs
-AUG 10 I28,000cfs) AUG II -31 (I3,000cfj SEPT 1-31 (6,000cf.)
8,000cf.) AUG "-31 SEPT '-3I OCTI-NOV8 (6,000 cfs)
(13,000 cfs) (6,000 cf»)
CK:^NOe' NOV 9 - 31 (30,000cfs)
(6,000cfs)
NOV 9-31 (30,000cfs) DEC 1 - 10 (IB.OOOcfs)
NOV 9-31 ,30,000cf»)
DEC 11-22 I50,000cfs)
DECHO DEC II -22(50,000cfs)
:i8,000cfs
DEC 23-FE8 2 (20,000cf»)
) DATE
4/31/69
5/31/69
6/31/69
7/22/6S
8/10/69
8/31/69
9/31/69
1 1 /8/69
11/31/69
I2/IO/6S
12/22/6
2/2/70
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MILES BELOW SUSQUEHANNA RIVER
36 34 32 30 28 26 24 22 20 18 16 14 12 10 8 6 4 2 0 DATE
I i I i i I I I I I i I I I i I I
DEC23-FEB2
(20,000 cf»)
FEB 3-14 (lOO.OOOcfj)
FEB 3-14 (I00,000cfs)
FEB l5-28(40,000cfi)
FEB 15-28
140,000 cfs)
MAR 1-27 (40,000cfs)
MAR28-APRILI9(l50,OOOcfs)
MARCH 28 - APRIL 19
(150,000 cfi)
APR 20-31 (88,000cfi)
APRIL 20-31 (88£>00cfs)
MAY 1-15 (40POOcfs)
MAY I- I5(40,000cfs)
MAY 16-31 (40,000 cfs)
MAY 16 -31 (40,000cf!)
JUNE 1-30 (20,000cfs1
JUNE I -30(2QOOOcfs)
JULY I -31 (20,000cfs)
JUNE 1-30 (2QOOOcfs) JULY 1-31 (20,000cfs)
AUG 1-31 (lOjOOOcfs)
JUNE 1-30
(20,OOOcW
JULY I -31 (20,000 cfs)
AUG I —31 (10,000cfcl
SEPT I -30 (8,000cfs)
JULY i -31 (20,000cfs)
AUG 1-31
(10,000 cW
SEPT 1-30 (6,000cfsl
OCT 1-15 (8.0OO cfs I
2/14/70
2/28/70
3/27/70
4/19/70
4/31/70
5/15/70
5/31/70
6/30/70
7/31/70
8/31/70
9/30/70
10/15/70
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MILES BELOW SUSQUEHANNA RIVER
36 34 32 30 28 26 24 22 20 18 16 14 12 10 8 6 4 2 0 DATE
1 1 1 1
1 1 1 1 1 1 1 1 1 1
OCT H5(8,000<:fs)
1
AUG 1-31 SEP 1-30 j
(10,000 cf») BjOOOrfO
OCT 16 - NOV 13 (3QOOOcfs)
NOV 14-22 (lOO.OOOcf.)
NOV 23 - DEC 13 (40,000cfs)
DEC 14 -31 (45000cf
DEC 14-31
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NOV 14 - 22 (I00,000cfi)
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MAR !7-23(l35,OOOcfs)
MAR 17-23 (I35,000cf
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APR 5 -2C (80POOcfs)
11/13/70
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MILES BELOW SUSQUEHANNA RIVER
36 34 32 30 28 26 24 22 20 18 16 14 12 10 8 6 42 0 DATE
1 1
I
II I I I I i 1
APR 5-20(80,000
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APR 2 0 - MAY 8
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WOjOOOcfi)
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TOTAL NITROGEN & PHOSPHORUS LOADINGS
CHESAPEAKE BAY BETWEEN TRANSECTS A and F (45 x I0fft»)
28 - 37 MILES BELOW SUSQUEHANNA RIVER
ESTIMATED N LOAD FROM SUSQUEHANNA RIVER
ESTIMATED P LOAD FROM SUSQUEHANNA RIVER
OBSERVED LOADS
4000-
3600-
3200-
2800-
2400
2000
1600
1200
800-
400-
I 1 I 1 I I I I .1 I I I I I M I
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1968
1969
1970
1971
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COMPARISON OF TOTAL PHOSPHORUS CONCENTRATIONS
IN
TRANSECTS WITHIN CHESAPEAKE BAY
AND
TRANSECT ACROSS MOUTH OF BALTIMORE HARBOR
AVERAGE TPCU IN BAY
AVERAGE TPO4 AT MOUTH OF BALTIMORE HARBOR
.28
.24
.20 -
.16 -
.12 -
.08 -
.04 -
. .M-l .1 U
1968
1969
1970
1971
-------
COMPARISON OF INORGANIC NITROGEN CONCENTRATIONS
IN
TRANSECTS WITHIN CHESAPEAKE BAY
AND
TRANSECT ACROSS MOUTH OF BALTIMORE HARBOR
AVERAGE INORG. N IN BAY
AVERAGE INORG. N AT MOUTH OF BALTIMORE HARBOR
1.20 n
.10 -
i.oo -
.90 -
.80 -
.70 -I
0> -60 -
E
.50 -
.40 -
.30 -
.20 -
.10 -
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1968
1969
1970
1971
-------
TIDAL DATA
FOR
HYDRAULIC VERIFICATION
Upper Chesapeake Bay
Actual Predicted Actual Phasing Predicted Phasing
Station Junction Range Range (H.W.) (L.W.) (H.W.) (L.W.)
(ft.) (minutes)
Susq. River at 7 1.7 2.0 +330 +372 +354 +408
Havre de Grace
Pooles Island
Baltimore
Fort McHenry
Sandy Point
Charleston
Northeast River
TolChester Beach 47
Love Point,
Chester River
Susq. River at 5 2.1 2.2 +368 +434 +366 +432
Port Deposit
34
53
70
10
47
62
1.2
1.1
0.8
1.9
1.2
1.1
1.3
1.2
0.9
2.1
1.2
1.1
+179
+128
+43
+346
+144
+105
+185
+146
+51
+374
+158
+106
+186
+126
+ 54
+ 354
+ 168
+ 114
+192
+ 114
+ 42
+ 396
+ 168
+ 102
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