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NASA Technical Memorandum 2001-210261

Canaveral National Seashore

Water Quality and

Aquatic Resource Inventory

July 2001

https://ntrs.nasa.gov/search.jsp?R=20010073452 2018-05-15T10:38:12+00:00Z

Canaveral National Seashore

Water Quality and Aquatic Resource

Inventory

Prepared by

C. R. Hall, J_A. Provancha, D.M. Oddy,

R.L. Lowers, and J.D. Drese

Dynamae Corporation

Mall Code Dyn-2

Kennedy Space Center, F! 32899
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Table of Contents

Section Page

o..

List of Tables ...................................................................................................................... ......... nx

List of Figures ............................................................................................................................. w

Summary ................................................................................................................................ xxvii

1.0 Introduction ........................................................................................................................ .. . 1

2.0 Water and Sediment Quality ................................................................................................ 1

2.1 Introduction ........................................................................................................................ 1

2.2 Methods ............................................................................................................................... 6

2.3 Results and Discussion ....................................................................................................... 9

2.3.1 Basic Physical and Chemical Parameters ...................................................................... 9

2.3.2 Total Metals ................................................................................................................. 20

2.3.3 Inorganic Chemistry .................................................................................................... 38

2.3.4 Organic Chemistry ....................................................................................................... 45

3.0 Light Attenuation ................................................................................................................ 47

3.1 Introduction ...................................................................................................................... 47

3.2 Methods ............................................................................................................................. 48

3.3 Results and Discussion ..................................................................................................... 52

4.0 Biota ...................................................................................................................................... 54

4.1 Seagrass and Other Submerged Aquatic Vegetation (SAV) ........................................ 54

4.1.1 Introduction .................................................................................................................. 54

4.1.2 Methods ....................................................................................................................... 54

4.1.3 Results and Discussion ................................................................................................ 60

4.2 Submerged Aquatic Vegetation Mapping ...................................................................... 60

4.2.1 Introduction .................................................................................................................. 60

4.2.2 Methods ....................................................................................................................... 60

4.2.3 Results and Discussion ................................................................................................ 61

4.3 Shellfish ............................................................................................................................. 61

4.3.1 Introduction .................................................................................................................. 61

4.3.2 Methods ..................................................................... ,,,-, ........ ,,................................... . 63

4.3.3 Results and Discussion ................................................................................................ 63

4.4 Demersal Fish Community ........................................................... , .................................. 67

5.0 Meteorology Io*llgIH.*o''*o'**'''''''''e*''lel''''''¢5"'J'_J J "'''_leo'gem'o*wj'm j''' ................................................ .... 68
5.1 Rain Volume and pH ....................................................................................................... 68

5.1.1 Introduction .................................................................................................................. 68

5.1.2 Methods ....................................................................................................................... 69

5.1.3 Results and Discussion ............................. , ......................................................... _........ 69

5.2 Wind .................................................................................................................................. 70

5.2.1 Introduction .................................................................................................................. 70

5.2.2 Methods ....................................................................................................................... 70

5.2.3 Results and Discussion ............................. ................................................................... 70

5.3 Solar Insolation ................................................................................................................ 71

5.3.1 Introduction .................................................................................................................. 71

5.3.2 Methods ....................................................................................................................... 71

5.3.3 Results and Discussion ................................................................................................ 71

6.0 Impoundments and Culverts .......................................................................................... 73

6.1 Introduction ...................................................................................................................... 73

6.2 Methods ............................................................................................................................. 73

6.3 Results and Discussion ..................................................................................................... 73

7.0 Summary and Recommendations ......................................... ......................................... 75

7.1 Water and Sediment Quality .......................................................................................... 75

7.2 Seagrass Transects ............................................................................... ,........................... 76

7.3 Fisheries ............................................................................................................................ 76

7.4 Sea Turtles ........................................................................................................................ 77

8.0 Acknowledgments ................................................................................................................ 78

9.0 Literature Cited ................................................................................................................... 79

Appendix A: Water and Sediment Chemistry ........................................................................ 82

Appendix B: Light Attenuation .............................................................................................. 193

Appendix C: Submerged Aquatic Vegetation ....................................................................... 208

Appendix D: Atmospheric Deposition ................................................................................... 220

Appendix E: Wind Tower Data Summaries ...................................... ':.................................. 245

Appendix F: Total Metals in Clams from Mosquito Lagoon .............................................. 271

Appendix G: Results From Impoundment Monitoring ....................................................... 277

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List of Tables

Table 1. Global Positioning System (GPS) coordinates for the Canaveral

National Seashore sampling stations. Water and sediment chemistry station

designations include a W. Light attenuation sampling stations include the

letter A, B, or C designating location along a transect.

Table 2. Parameters measured for water and sediment samples collected in

Mosquito Lagoon between 1991 and 1993.

Table 3a. Depth profile schedule used at each PAR Station in Mosquito

Lagoon prior to January 1993.

Table 3b. Depth profile schedule used at each PAR Station in Mosquito

Lagoon beginning January 1993.

Table 4. Number of collection periods for PAR measurements at each station

1991-1993.

Table 5. TotalSuspended Solids(TSS), Chlorophyll-A (CPA) and Color

resultsfrom samples collectedmonthly atrandomly selectedPAR stations.

Table 6. Global PositioningSystem (GPS) coordinatesforsubmerged

aquatic vegetation transects sampled in Mosquito Lagoon. Ends of transects

are designated A and B.

Table 7. Heavy metal concentrations (ug/g dry weigh0 in clams collected at

the six water quality stations in Mosquito Lagoon in 1993.

Table 8. Mercury concentrations in seatrout collected in Merritt Island

National Wildlife Refuge.

Table 9. Results of total and fecal coliform monitoring in Mosquito Lagoon.

Table A-I. Summary statistics for water quality samples collected for

Mosquito Lagoon. All samples and stations combined. Samples are

included only if values are above the method detection limits.

Table A-2. Descriptive statistics for physical/chemical parameters measured

at all Mosquito Lagoon water quality stations sorted by sample collection

date.

Table A-3. Descriptive statistics for physical/chemical parameters measured

at each Mosquito Lagoon water quality station for all sample collection

dates.

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Table A-4. Descriptive statistics for metals measured at all Mosquito

Lagoon water quality stations sorted by sample collection date.

Table A-5. Descriptive statistics for metals measured at each Mosquito

Lagoon water quality station for all sample collection dates.

Table A-6. Descriptive statistics for inorganics measured at all water quality

stations sorted by sample collection date.

Table A-7. Descriptive statistics for inorganics measured at each Mosquito

Lagoon water quality station for all sample collection dates.

Table A-8. Descriptive statistics for organics measured at all Mosquito

Lagoon water quality stations sorted by sample collection date.

Table A-9. Descriptive statistics for organics measured at each Mosquito

Lagoon water quality station for all sample collection dates.

Table A- 10. Summary statistics for sediment quality samples collected for

Mosquito Lagoon. All samples and stations combined. Samples are

included only if values are above the method detection limits

Table A-11. Descriptive statistics for metals measured in sediment at all

sampling stations sorted by sample collection date.

Table A-12. Descriptive statistics for metals measured in sediment at each

sampling station for all sample collection dates.

Table A-13. Descriptive statistics for inorganic and organic parameters

measured in sediment at all sampling stations sorted by sample collection

date.

Table A-14. Descriptive statistics for inorganic and organic parameters

measured in sediment at each sampling station for all sample collection

dates.

Table A-15. Results ofbivariate Spearman Rank Correlation analyses

between water quality sample variables for all stations and sample periods

combined.

Table A-16. Results of bivariate Spearman Rank Correlation analyses

between sediment sample variables for all stations and sample periods

combined.

Table D-1. John F. Kennedy Space Center rainfall totals, pH and

conductivity.

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109

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Table D-2. John F. Kennedy Space Center rainfall totals, pH, and

conductivity.

Table D-3. John F. Kennedy Space Center rainfall totals, pH, and

conductivity.

Table D-4. John F. Kennedy Space Center rainfall totals, pH, and

conductivity.

Table D-5. John F. Kennedy Space Center rainfall totals, pH, and

conductivity.

Table D-6. John F. Kennedy Space Center rainfall totals, pH, and

conductivity.

Table D-7. John F. Kennedy Space Center rainfall Totals, pH, and

conductivity.

Table D-8. John F. Kennedy Space Center rainfall totals (inches) fi'om 1983

through 1992.

Table D-9. John F. Kennedy Space Center rainfall totals (inches) from 1984

through 1993.

Table D-10. John F. Kennedy Space Center rainfall totals (inches) from

1984 through 1992.

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List of Figures

Figure 1. Canaveral National Seashore, Mosquito Lagoon and the north

Indian River estuarine systems in east central Florida. The region has high

biodiversity and an abundance of wetlands and seagrass beds supporting

high primary production.

Figure 2. Conceptual model of hydrologic pathways and processes

influencing the mass balances of water and chemicals in Mosquito Lagoon.

Inputs include atmospheric deposition, runoff, surficial aquifer leakage,

deep aquifer leakage, and transport through Haulover Canal and Ponce de

Leon Inlet.

Figure 3. Locations of surface water sampling stations utilized during the

water and sediment chemistry characterization program for Mosquito

Lagoon.

Figure 4. Bi-hourly water temperature (°C) data collected at the Canaveral

National Seashore boat dock in December 1991. Data were collected

utilizing a programmable Hydrolab data logger set at a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in 1.2 m of

water.

Figure 5. Water quality sample frequency distributions for conductivity

and salinity. There are no Class 11 criteria for conductivity or salinity.

Figure 6. Water quality sample frequency distributions for total alkalinity

and total dissolved solids. There are no Class 11 criteria for alkalinity or

dissolved solids.

Figure 7. Water quality sample frequency distributions for chlorophyll A

and color. There are no State criteria for these compounds.

Figure 8. Water quality sample frequency distributions for biological

oxygen demand (BOD) and chemical oxygen demand (COD). The Florida

Class II: Shellfish Propagation or Harvesting Criteria for Surface Water

Quality (62-302.530 F.A.C.) state that BOD should not exceed values that

depress dissolved oxygen below established limits, or produce nuisance

conditions. There is no criterion for COD.

Figure 9. Water quality sample frequency distributions for silver and

aluminum compared to the Florida Class 1I: Shellfish Propagation or

Harvesting Criteria for Surface Water Quality (62-302.530 F.A.C.).

Criteria concentrations are depicted by a vertical line.

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Figure 10. Water quality sample frequency distributions for beryllium and

boron compared to the Florida Class II: Shellfish Propagation or

Harvesting Criteria for Surface Water Quality (62-302.530 F.A.C.).

Criteria concentrations are depicted by a vertical line. There is no Class il

criterion for boron.

Figure 11. Water quality sample frequency distributions for calcium and

cadmium. The Florida Class II: Shellfish Propagation or Harvesting

Criteria for Surface Water Quality (62-302.530 F.A.C.) criterion for

cadmium is _<9.3 ug/l. There is no criterion for calcium.

Figure 12. Water quality sample frequency distributions for chromium and

copper compared to the Florida Class II: Shellfish Propagation or

Harvesting Criteria for Surface Water Quality (62-302.530 F.A.C.).

Criteria concentrations are depicted by a vertical line.

Figure 13. Water quality sample frequency distributions for iron and

magnesium compared to the Florida Class 1I: Shellfish Propagation or

Harvesting Criteria for Surface Water Quality (62-302.530 F.A.C.).

Criteria concentrations are depicted by a vertical line. There is no criterion

for magnesium.

Figure 14. Water quality sample frequency distributions for nickel and

lead compared to the Florida Class 1I: Shellfish Propagation or Harvesting

Criteria for Surface Water Quality (62-302.530 F.A.C.). Criteria

concentrations are depicted by a vertical line.

Figure 15. Water quality sample frequency distributions for silicon and

zinc compared to the Florida Class If: Shellfish Propagation or Harvesting

Criteria for Surface Water Quality (62-302.530 F.A.C.). Criteria

concentrations are depicted by a vertical line. There is no criterion for

silicon.

Figure 16. Water quality sample frequency distributions for ammonia and

total Kjeldahl nitrogen (TKN). There are no Class II criteria for ammonia

and TKN.

Figure 17. Water quality sample frequency distributions for phosphate and

total phosphorus. Florida DEP criteria states that in no case shall nutrient

levels be altered in a way that causes an imbalance in natural populations

of flora or fauna.

Figure 18. Water quality sample frequency distributions for potassium and

sulfate. There are no state criteria for potassium or sulfate.

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Figure 19. Water quality sample frequency distributions for grease and oil,

and phenol compared to the Florida Class If: Shellfish Propagation or

Harvesting Criteria for Surface Water Quality (62-302.530 F.A.C.).

Criteria concentrations are depicted by a vertical line. The state criterion

for phenolic compounds is < 1.0 ug/1 unless higher values are shown not to

be chronically toxic.

Figure 20. Water quality sample frequency distributions for Total Organic

Carbon. There is no Class 1I criterion for total organic carbon.

Figure 21. Locations of underwater light attenuation sampling transects in

Mosquito Lagoon. Samples were collected on clear days between 10:00

and 14:00 h.

Figure 22. Locations of submerged aquatic vegetation sampling transects

in southern Mosquito Lagoon.

Figure 23. Locations of submerged aquatic vegetation sampling transects

in the Canaveral National Seashore and Mosquito Lagoon.

Figure 24. Locations of transects utilized to ground truth maps of the

distribution of submerged aquatic vegetation. Transects were located in

deeper regions to sample areas not readily observable on aerial

photography.

Figure 25. Monthly mean solar insolation values for the east central

Florida coastal region. Data were collected by the Florida Solar Energy

Center at Port Canaveral, Florida.

Figure 26. Locations of mosquito control impoundment sampling areas

along the eastern shoreline of Mosquito Lagoon.

Figure A-1. Seasonal dissolved oxygen (rag/l) concentrations collected on

Transect 1. Samples were collected between 10:00 and 14:00 h on clear

days with relatively calm waters as part of an investigation into underwater

light attenuation and seagrass bed distributions.

Figure A-2. Seasonal dissolved oxygen (mg/l) concentrations collected on

Transect 2. Samples were collected between 10:00 and 14:00 h on clear

days with relatively c_ waters as part of an investigation into underwater

light attenuation and seagrass bed distributions.

Figure A-3. Seasonal dissolved oxygen (mg/1) concentrations collected on

Transect 3. Samples were collected between 10:00 and 14:00 h on clear

days with relatively calm waters as part of an investigation into underwater

light attenuation and seagrass bed distributions.

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Figure A-4. Seasonal dissolved oxygen (rag/l) concentrations collected on

Transect 4. Samples were collected between 10:00 and 14:00 h on clear

days with relatively calm waters as part of an investigation into underwater

light attenuation and seagrass bed distributions.

Figure A-5. Seasonal dissolved oxygen (rag/l) concentrat/ons collected on

Transect 5. Samples were collected between 10:00 and 14:00 h on clear

days with relatively calm waters as part of an investigation into underwat_"

light attenuation and seagrass bed distributions.

Figure A-6. Seasonal salinity (ppt) concentrations collected on Transect I.

Samples were collected between I0:00 and 14:00 h on clear days with

relatively calm waters as part of an investigation into underwater light

attenuation and seagrass bed distributions.

Figure A-7. Seasonal salinity (ppt) concentrations collected on Transect 2.

Samples were collected between 10:00 and 14:00 h on clear days with

relatively calm waters as part of an investigation into underwater light

attenuation and seagrass bed distributions.

Figure A-8. Seasonal salinity(ppt)concentrationscollectedon Transect 3.

Samples were collectedbetween I0:00 and 14:00 h on cleardays with

relativelycalm waters aspartof an investigationintounderwater light

attenuationand scagrassbed distributions.

Figure A-9. Seasonal salinity (ppt) concentrations collected on Transect 4.

Samples were collected between 10:00 and 14:00 h on clear days with

relatively calm waters as part of an investigation into underwater light

attenuation and seagrass bed distributions.

Figure A-IO. Seasonal salinity (ppt) concentrations collected on Transect

5. Samples were collected between 10:00 and 14:00 h on clear days with

relatively calm waters as part of an investigation into underwater light

attenuation and seagrass bed distributions.

Figure A-11. October, 1991 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

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Figure A-12. November, 1991 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-13. December, 1991 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-14. January, 1992 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 ra of water.

Figure A-15. February, 1992 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-16. March, 1992 bi-hourly water temperature (°C) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-17. April, 1992 bi-hourly water temperature (°C) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 ra of water.

Figure A-18. May, 1992 bi-hourly water temperature (°C) data collected at

the Canaveral National Seashore boat dock. Data were collected utilizing

a programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

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127

128

129
Figure A-19. June, 1992 bi-hourly water temperature (°C) data collected at

the Canaveral National Seashore boat dock. Data were collected utilizing

a programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 em above the bottom in approximately 1.2 m

of water.

Figure A-20. July, 1992 bi-hourly water temperature CC) data collected at

the CanaveralNational Seashore boat dock. Data were collected utilizing

a programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 em above the bottom in approximately 1.2 m

of water.

Figure A-21. August, 1992 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling _terval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-22. September, 1992 bi-hourly water temperature (°C) data were

not reported due to instrument problems.

Figure A-23. October, 1992 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collectedutilizinga programmable Hydrolab data loggerwith a two hour

sampling interval.Probes were located30 - 40 cm above thebottom in

approximately 1.2m of water.

Figure A-24. November, 1992 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure Ao25. December, 1992 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 em above the bottom in

approximately 1.2 m of water.

Figure A-26. January, 1993 bi-hourly water temperature (°C) data

collectedatthe Canaveral National Seashore boat dock. Data were

collectedutilizinga programmable Hydrolab data loggerwith a two boia"

sampling interval.Probes were located30 - 40 cm above thebottom in

approximately 1.2m of water.

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v a_

Figure A-27. February, 1993 bi-hourly water temperature (°C) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-28. March, 1993 bi-hourly.water temperature (°C) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-29. April, 1993 bi-hourlywater temperature (°C) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 em above the bottom in

approximately 1.2 m of water.

Figure A-30. May, 1993 bi-hourly water temperature (°C) data collected at

the Canaveral National Seashore boat dock. Data were collected utilizing

a programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 = 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-31. October, 1991 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 = 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-32, November, 1991 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 em above the bottom in approximately 1.2 m

of water.

Figure A-33. December, 1991 bi-ho_ly salinity (ppt) data C0H&ted at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

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FigureA-34. January, 1992 bi-hourly salinity Oapt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

144

Figure A-35. Febuary, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water. 145

Figure A-36. March, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water. 146

Figure A-37. April, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water. 147

Figure A-38. May, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water. 148

Figure A-39. June, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water. 149

Figure A-40. July, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water. 150

xiii
Figure A-41. August, 1992 bi-hourly salinity (PP0 data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-42. September, 1992 bi-hourly salinity (ppt) data were not

reported due to instrument problems.

Figure A-43. October, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-44. November, 1992 bi-hourly salinity (PP0 data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-45. December, 1992 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-46. January, 1993 bi-hourly salinity (PP0 data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-47. February, 1993 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-48. March, 1993 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water,

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Figure A-49. April, 1993 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-50. May, 1993 bi-hourly salinity (ppt) data collected at the

Canaveral National Seashore boat dock. Data were collected utilizing a

programmable Hydrolab data logger with a two hour sampling interval.

Probes were located 30 - 40 cm above the bottom in approximately 1.2 m

of water.

Figure A-51. October, 1991 bi-hourly dissolved oxygen (rag/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figm'e A-52. November, 1991 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-53. December, 1991 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-54. January, 1992 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-55. February, 1992 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

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P g

Figure A-56. March, 1992 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-57. April, 1992 bi-hourly dissolved oxygen (mg/1) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-58. May, 1992 bi-hourly dissolved oxygen (mg/l) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-59. June, 1992 bi-hourly dissolved oxygen (mg/1) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 = 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-60. July, 1992 bi-hourly dissolved oxygen (mg/l) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-61. August, 1992 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure Ao62. September, 1992 bi-hourly dissolved oxygen (mg/l) data

were not reported due to instrument problems

Figure A-63. October, 1992 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

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FigureA-64. November,1992 hi-hourly dissolved oxygen (rag/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-65. December, 1992 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-66. January, 1993 bi-hourlydissolvedoxygen (rag/l)data

collectedatthe Canaveral National Seashore boat dock. Data were

collected utilizing a programmable Hydrolab data logger with a two hour

sampling interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-67. February, 1993 bi-hourly dissolved oxygen (mg/l) data

collected at the Canaveral National Seashore boat dock. Data were

collectedutilizinga programmable Hydrolab data logger with a two hour

sampling interval.Probes were located30 - 40 cm above thebottom in

approximately 1.2m of water.

Figure A-68. March, 1993 bi-hourlydissolvedoxygen (rag/l)data

collectedatthe Canaveral National Seashore boat dock. Data were

collectedutilizinga programmable Hydrolab data logger with a two hour

sampling interval.Probes were located30 - 40 cm above the bottom in

approximately 1.2m of water.

Figure A-69. April, 1993 bi-hourly dissolved oxygen (rag/l) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval.Probes were located30 - 40 cm above the bottom in

approximately 1.2rn of water.

Figure A-70. May, 1993 bi-hourly dissolved oxygen (rag/l) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

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w

Figure A-71. June, 1993 bi-hourly dissolved oxygen (mg/1) data collected

at the Canaveral National Seashore boat dock. Data were collected

utilizing a programmable Hydrolab data logger with a two hour sampling

interval. Probes were located 30 - 40 cm above the bottom in

approximately 1.2 m of water.

Figure A-72. Mean, standard deviation, and sample fre,quency

distributions for aluminum and boron in Mosquito Lagoon sediment

samples.

Figure A-73. Mean, standard deviations, and sample frequency

distributions for beryllium and calcium in Mosquito Lagoon sediment

samples.

Figure A-74. Mean, standard deviations, and sample frequency

distributions for cadmium and chromium in Mosquito Lagoon sediment

samples.

Figure A-75. Mean, standard deviation, and sample frequency

distributions for copper and iron in Mosquito Lagoon sediment samples.

Figure A-76. Mean, standard deviation, and sample frequency distributions

for potassium and magnesium in Mosquito Lagoon sediment samples.

Figure A-77. Mean, standard deviation, and sample frequency

distributions for manganese and nickel in Mosquito Lagoon sediment

samples.

Figure A-78. Mean, standard deviation, and sample frequency

distributions for lead and silver in Mosquito lagoon sediment samples.

Figure A-79. Mean, standard deviation, and sample frequency

distributions for zinc and pH in Mosquito lagoon sediment samples.

Figure A-80. Mean, standard deviation, and sample frequency

distributions for ammonia and total Kjeldahl nitrogen in Mosquito Lagoon

sediment samples.

Figure A-81. Mean, standard deviation, and sample frequency

distributions for nitrite and nitrate in Mosquito Lagoon sediment samples.

Figure A-82. Mean, standard deviation, and sample frequency

distributions for phosphate and total phosphorus in Mosquito Lagoon

sediment samples.

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XVlll
Figure A-83. Mean, standard deviation, and sample frequency

distributions for sulfate and total organic carbon in Mosquito Lagoon

sediment samples.

Figure A-84. Mean, standard deviation, and sample fi'equency

distributions for grease and oil, and phenols in Mosquito Lagoon sediment

samples.

Figure B-1. Light attenuation coefficients (K m q) measured at Transect 1

in southern Mosquito Lagoon between Summer 1991 and Spring 1993.

Attenuation was estimated using measures of scalar irradiance at varying

depths below the water surface.

Figure B-2. Light attenuation coefficients (Km q) measured at Transect 2

in southern Mosquito Lagoon between Summer 1991 and Spring 1993.

Attenuation was estimated using measures of scalar irradiance at varying

depths below the water surface.

Figure B-3. Light attenuation coefficients (K m q) measured at Transect 3

in southern Mosquito Lagoon between Summer 1991 and Spring 1993.

Attenuation was estimated using measures of scalar irradiance at varying

depths below the water surface.

Figure B-4. Light attenuation coefficients (K m _) measured at Transect 4

in southern Mosquito Lagoon between Summer 1991 and Spring 1993.

Attenuation was estimated using measures of scalar irradiance at varying

depths below the water surface.

Figure B-5. Light attenuation coefficients (K m q) measured at Transect 5

in southern Mosquito Lagoon between Summer 1991 and Spring 1993.

Attenuation was estimated using measures of scalar irradiance at varying

depths below the water surface.

Figure B-6. Average percent light available at different depths measured

at Transect 1 in southern Mosquito Lagoon between Summer 1991 and

Spring 1993. Percent light was estimated using measures of scalar

irradiance at varying depths below the water surface.

Figure B-7. Average percent light available at different depths measured

at Transect 2 in southern Mosquito Lagoon between Summer 1991 and

Spring 1993. Percent light was estimated using measures of scalar

irradiance at varying depths below the water surface.

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FigureB-8. Average percent light available at different depths measured

at Transect 3 in southern Mosquito Lagoon between Summer 1991 and

Spring 1993. Percent light was estimated using measures of scalar

irradiance at varying depths below the water surface.

Figure B-9. Average percent light available at different depths measured

at Transect 4 in southern Mosquito Lagoon between Summer 1991 and

Spring 1993. Percent light was estimated using measures of scalar

irradiance at varying depths below the water surface.

Figure B-10. Average percent light available at different depths measured

at Transect 5 in southern Mosquito Lagoon between Summer 1991 and

Spring 1993. Percent light was estimated using measures of scalar

irradiance at varying depths below the water surface.

Figure B-I 1. Average attenuation coefficient (K m "i) and 95% confidence

interval estimated for each sample station in Mosquito Lagoon between

Summer 1991 and Spring 1993. Attenuation was estimated using

measures of scalar irradiance at varying depths below the water surface.

Figure B-12. Average attenuation coefficient (K m "1) and depth estimated

for each sample station in Mosquito Lagoon between Summer 1991 and

Spring 1993. Attenuation was estimated using measures of scalar

irradiance at varying depths below the water surface.

Figure B-13. Average attenuation coefficient (K m °1) and estimated

percent light and maximum depth of submerged aquatic vegetation on each

sample transect in Mosquito Lagoon between Summer 1991 and Spring

1993. Attenuation and percent available light were estimated using

measures of scalar irradiance at varying depths below the water surface.

Figure B-14. Plot of relationship between percent light and attenuation

(Km "_) for sample stations having depths between 1.4 and 1.9 m.

Figure C-1. Percent coverage of shoal grass, Halodule wrightii, along 9

transects in Mosquito Lagoon. Percent cover was estimated at 5 m

intervals along a 50 m transect utilizing a lm2 plot frame.

Figure C-2. Percent coverage of manatee grass, Syringodiumfiliforme,

along 3 transects in Mosquito Lagoon. Percent cover was estimated at 5 m

intervals along a 50 m transect utilizing a lm 2 plot frame.

Figure C-3. Historic data on percent cover of submerged aquatic

vegetation at Transects 12 and 20, monitored by the NASA Biomedical

Office, in south Mosquito Lagoon between 1983 and 1993. Shoal grass,

Halodule wrightii, is the dominant species in this region.

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Figure C-4. Historic data on percent cover of submerged aquatic

vegetation at Transects 13 and 14, monitored by the NASA Biomedical

Office, in south Mosquito Lagoon between 1983 and 1993. Shoal grass,

Halodule wrightii, is the dominant species in this region.

Figure C-5. Historic data on percent cover of submerged aquatic

vegetation at Transects 21 and 22, monitored by the NASA Biomedical

Office, in south Mosquito Lagoon between 1983 and 1993. Shoal grass,

Halodule wrightii, is the dominant species in this region.

Figure C-6. Estimated trend lines for percent cover of submerged aquatic

vegetation on 5 transects in south Mosquito Lagoon. Transects monitored

by the NASA Biomedical Office, in south Mosquito Lagoon between 1983

and 1993. Shoal grass, Halodule wrightii, is the dominant species in this

region.

Figure C-7. Plot of relationship between percent cover of different types

of submerged aquatic vegetation and depth in Mosquito Lagoon. Note the

decrease in seagrass and increase in algae with depth.

Figure C-8. Plot of relationship between frequency of encounter of

different species types of submerged aquatic vegetation and depth in

Mosquito Lagoon.

Figure C-9. Frequency of occurrence of different density categories by

depth for manatee grass, Syringodiumfiliforme, coUected at the Mosquito

Lagoon transects in 1992.

Figure C-10. Frequency of occurrence of different density categories by

depth for shoal grass, Halodule wrightii, collected at the Mosquito Lagoon

transects in 1992.

,Figure C-I 1. Frequency of occurrence of different density categories by

depth for all algae species combined collected at the Mosquito Lagoon

transects in 1992.

Figure D-1. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the third quarter of 1991. Samples were collected at

the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon.

Figure D-2. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the fourth quarter of 1991. Samples were collected at

the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon.

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Figure D-3. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the first quarter of 1992. Samples were collected at

the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon. 233

Figure D-4. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the second quarter of 1992. Samples were collected

at the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon. 234

Figure D-5. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the third quarter of 1992. Samples were collected at

the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon. 235

Figure D-6. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the fourth quarter of 1992. Samples were collected at

the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon. 236

Figure D-7. Temporal rainfall volumes, average rainfall, and 95%

probability limits for the first quarter of 1993. Samples were collected at

the National Atmospheric Deposition site on Kennedy Space Center

approximately 5 miles southwest of Mosquito Lagoon. 237

Figure D-8. Temporal rainfall pHand conductivity for the third quarter of

1991. Samples were collected at the National Atmospheric Deposition site

on Kennedy Space Center approximately 5 miles southwest of Mosquito

Lagoon. 238

Figure D-9. Temporal rainfall pH and conductivity for the fourth quarter

of 1991. Samples were collected at the National Atmospheric Deposition

site on Kennedy Space Center approximately 5 miles southwest of

Mosquito Lagoon. 239

Figure D-10. Temporal rainfall pH and conductivity for the first quarter of

1992. Samples were collected at the National Atmospheric Deposition site

on Kennedy Space Center approximately 5 miles southwest of Mosquito

Lagoon. 240

Figure D- 11. Temporal rainfall pH_and conductivity for these_.nd quarter

of 1992. Samples were collected at the National Atmospheric Deposition

site on Kennedy Space Center approximately 5 miles southwest of

Mosquito Lagoon. 241

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f

Figure D-12. Temporal rainfall pH and conductivity for the third quarter

of 1992. Samples were collected at the National Atmospheric Deposition

site on Kennedy Space Center approximately 5 miles southwest of

Mosquito Lagoon.

Figure D-13. Temporal rainfall pH and conductivity for the fourth quarter

of 1992. Samples were collected at the National Atmospheric Deposition

site on Kennedy Space Center approximately 5 miles southwest of

Mosquito Lagoon.

Figure D-14. Temporal rainfall pH and conductivity for the first quarter of

1993. Samples were collected at the National Atmospheric Deposition site

on Kennedy Space Center approximately 5 miles southwest of Mosquito

Lagoon.

Figure E-1. Wind direction and speed measured at Haulover Canal bridge

during May 1991.

Figure E-2. Wind direction and speed measured at Haulover Canal bridge

during June 1991.

Figure E-3. Wind direction and speed measured at Haulover Canal bridge

during July 1991.

Figure E-4. Wind direction and speed measured at Haulover Canal bridge

during August 1991.

Figure E-5. Wind direction and speed measured at Haulover Canal bridge

during September 1991.

Figure E-6. Wind direction and speed measured at Haulover Canal bridge

during October 1991.

Figure E-7. Wind direction and speed measured at Haulover Canal bridge

during November 1991.

Figure E-8. Wind direction and speed measured at Haulover Canal bridge

during December 1991.

Figure E-9. Wind direction and speed measured at Haulover Canal bridge

during January 1992.

Figure E-10. Wind direction and speed measured at Hanlover Canal

bridge during February 1992.

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FigureE-11. Wind direction and speed measured at Haulovcr Canal

bridge during March 1992.

Figure E-12. Wind direction and speed measured at Haulovcr Canal

bridge during April 1992.

Figure E-13. Wind direction and speed measured at Haulovcr Canal

bridge during May 1992.

Figure E-14. Wind direction and speed measured at Haulover Canal

bridge during June 1992.

Figure E-15. Wind direction and speed measured at Haulov_ Canal

bridge during July 1992.

Figure E-16. Wind direction and speed measured at Haulover Canal

bridge during August 1992.

Figure E- 17. Wind direction and speed measured at Haulover Canal

bridge during September 1992.

Figure E-18. Wind direction and speed measured at Haulover Canal

bridge during October 1992.

Figure E-19. Wind direction and speed measured at Haulover Canal

bridge during November 1992.

Figure E-20. Wind direction and speed measured at Haulover Canal

bridge during December 1992.

Figure E-21. Wind direction and speed measured at Haulover Canal

bridge during January 1993.

Figure E-22. Wind direction and speed measured at Haulovcr Canal

bridge during February 1993.

Figure E-23. Wind direction and speed measured at Haulover Canal

bridge during March 1993.

Figure

bridge

Figure

bridge

Figure

E-24. Wind direction and speed measured at Haulover Canal

during April 1993.

E-25. Wind direction and speed measured at Haulover Canal

during May 1993.

F-1. Concentrations of aluminum and cadmium in whole clams

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Ixlv
collected at the Mosquito Lagoon surface water and sediment chemistry

stations.

Figure F-2. Concentrations of chromium and copper in whole clams

collected at the Mosquito Lagoon surface water and sediment chemistry

stations.

Figure F-3. Concentrations of iron and lead in whole clams collected at

the Mosquito Lagoon surface water and sediment chemistry stations.

Figure F-4. Concentrations of manganese and nickel in whole clams

collected at the Mosquito Lagoon surface water and sediment chemistry

stations.

Figure F-5. Concentrations of silver and zinc in whole clams collected at

the Mosquito Lagoon surface water and sediment chemistry stations.

Figure G-1. Monthly water level and salinity measurements for

Impoundment V-I on the east side of Mosquito Lagoon. Data were

collected between 1990 and 1993.

Figure G-2. Monthly dissolved oxygen and temperature measurements for

Impoundment V-1 on the east side of Mosquito Lagoon. Data were

collected between 1990 and 1993.

Figure G-3. Monthly water level and salinity measurements for

Impoundment County Line on the east side of Mosquito Lagoon. Data

were collected between 1990 and 1993.

Figure G-4. Monthly dissolved oxygen and temperature measurements for

Impoundment County Line on the east side of Mosquito Lagoon. Data

were collected between 1990 and 1993.

Figure G-5. Monthly water level and salinity measurements for

Impoundment T-44 on the east side of Mosquito Lagoon. Data were

collected between 1990 and 1993.

Figure G-6. Monthly dissolved oxygen and temperature measurements for

Impoundment T-44 on the east side of Mosquito Lagoon. Data were

collected between 1990 and 1993.

Figure G-7. Monthly water level and salinity measurements for

Impoundment T-38 on the east side of Mosquito Lagoon. Data were

collected between 1990 and 1993.

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Figure G-8. Monthly dissolved oxygen and temperature measurements for

Impoundment T-38 on the east side of Mosquito Lagoon. Data were

collected between 1990 and 1993. : 285

xxvi
Summary

r

Mosquito Lagoon is a shallow bar built estuary located on the east central Florida Coast.

The lagoon and associated watershed cover approximately 327 km 2 (79422 acres). The lagoon

occupies 159 km 2 (37853 acres). Water depths average approximately 1 m. This gives the

lagoon an estimated volume of approximately 1.6x 10sin 3. A large portion of the relatively

undisturbed watershed is owned and managed by the federal government as Canaveral National

Seashore, the Merritt Island National Wildlife Refuge, and the NASA Kennedy Space Center.

This report contains results of a water resources inventory that included water and sediment

chemistry, underwater light attenuation, distribution and composition of submerged aquatic

vegetation beds, demersal fish sampling, and meteorological data summaries for the region.

Generally, water quality of Mosquito Lagoon is considered good. In part this is a result

of the low level of watershed development in the region. Three major forces, gravity, wind, and

radiation control water movement influencing the mass balance or concentrations of chemicals in

the various components of the system at any given instance. Influences of tidal action and the

Atlantic Ocean through Ponce de Leon Inlet are limited primarily to the northern reaches of the

Lagoon and the northern section of Canaveral National Seashore. Water quality in the southern

region of the lagoon is affected by evapotransporation, rainfall, discharges from mosquito control

impoundments, and exchange with the Indian River Lagoon through Haulover Canal.

Groundwater seepage into and out of the lagoon also influences water quality along with

biological processes.

Salinity data collected for the lagoon typically range between 20 ppt and 35 ppt. The

lowest value recorded was 4.5 ppt and the highest value was 37 ppt. Lower values are associated

with areas of fresh water discharge while higher values can be observed during periods of low

rainfall and high evapotransporation. A slight gradient of 2-3 ppt was observed between the

northern and southern reaches of the lagoon. Stations 1 and 2 in the south averaged 25 ppt while

northern stations averaged 28 ppt. This gradient most probably represents influences of Ponce

de Leon Inlet. Salinity values are positively correlated with total dissolved solids, conductivity,

and specific compounds as expected.

Lagoon water temperatures fluctuate 2-3°C over a 24 h period. Summer temperatures

typically range between 27 and 3 I°C and winter temperatures range between 15 and 23°C. Cold

front passage in late fall and winter can rapidly alter water temperature by 5-10°C or more in a

short period of time. The highest temperature recorded was 33.4°C and the lowest temperature

was 8.8°C following passage of a winter storm.

Dissolved oxygen concentrations displayed a high degree of variability when monitored

continuously at the Canaveral National Seashore boat dock. Values ranged from a low of 0.4

mg/1 to a high of 15.3 mg/i. Extended periods of readings below the Florida Department of

Environmental Protection criteria of 4.0 mg/l were observed in fall and spring months suggesting

high system respiration and oxygen demand. In contrast, results of daytime dissolved oxygen

sampling at the six water and sediment chemistry stations found values always above 5.0 mg/1.

Without continuous monitoring the periods of low dissolved oxygen would not have been

documented.

Results of metals analyses suggest the need for additional evaluation to understand

chemical dynamics and processes that control water concentrations and chemistry within the

lagoon. Several metals such as antimony, arsenic, molybdenum and mercury were reported as

below detection limits for all samples. In contrast, metals of concern such as cadmium, copper,

xxvii
chromium, silver, and zinc were found to be periodically above the Florida Department of

Environmental Protection criteria for Class rl and Class HI surface waters. Specific sources for

these metals are not readily identifiable and little is known about their partitioning withindifferent components of the lagoon system. Chemical analyses for pesticides and herbicides in

water and sediments were consistently reported as below detection.

The ability of light to penetrate the water column and reach the bottom is important to

overall system primary production. Light drives the photosynthetic process occurring in

phytoplankton, benthic algae, and submerged aquatic vegetation. Results of the light attenuation

study showed a high degree 0f variability between different regions of the lagoon. The minimum

attenuation value was 0.3 m "_at Station 3A. Maximum attenuation of 1.69 m "l was measured at

Station 4A. The high attenuation at Transect 4 is the result of tidal influences, turbulent mixing,

and the resulting increased turbidity. The average scalar attenuation for all stations and seasons

was 0.92 m "I. Primary factors influencing the underwater light field include sun angle, water

color, bottom color, and total suspended sediments or turbidity. Stormwater runoffwith its

nutrient and particulate load is recognized as a potential source for these parameters. Daily

rainfall amounts for the study period ranged between 0 and 2.95 inches. The mean rainfall

volume for the 207 recorded rainfall days was 0.44 in. Rainfall pH ranged between 3.85 and

7.06 pH units.

Results of submerged aquatic vegetation sampling at select transects found the system

dominated by two species, shoal grass (Halodule wrightii) and manatee grass (Syringodium

filiforme). Seagrass beds were less dense and reduced in distribution in the northern regions of

Canaveral National Seashore where tidal fluctuations and high turbidity are most evident.

Submerged aquatic vegetation was most abundant in the shallow southern regions of the lagoon

with shoal grass most abundant in shallow areas and manatee grass increasing in importance in

deeper areas. The central basin of the lagoon was found to be devoid of seagrass. Drift algae

were present in deeper areas.

Fish community sampling at five stations produced 49 species. The fish fauna consisted

of a few specimens that were numerically dominate and a larger number of increasingly rare

species. The bay anchovy often composed over 90% of the catch. Although a small species, the

bay anchovy often predominates in biomass because of sheer abundance. Other numerically

common species were silver perch, pinfish, pigfish, spot, croaker, Gulfpipefish, silver jermy, and

code gob),. Large specimens are relatively rare in trawl collections. When they are caught,

however, they may dominate in biomass due to their large size. Typical examples were the

butterfly ray, blunt-nose stingray, and hardhead catfish. Community composition varied from

station to station and between sampling periods. Although this variation was often of large

magnitude, most of it proved to be statistically random and insignificant. The patterns of

variation that appeared to be consistent and statistically significant over the two year period

were: 1) Stations 1 and 2 were highly correlated and were very similar in community

composition. (2) Station 4 was consistently uneorrelated with any other station and had a

different community composition. (3) The silver jenny was more abundant in 1991 than in 1992.

(4) The spot was more abundant in 1992 than 1991. (5) Rare species were encountered more

often at the northern stations than at the southern stations. Important environmental

considerations that appear to infhenee community composition are habitat diversity and

proximity to ocean access (Stations 1 and 2) and drift algae density (Station 4).

xxviii
The following recommendations are provided based on results of this project.

1) Continue to develop information necessary to quantify the water budget for Mosquito

Lagoon. This should be accomplished at a level of detail that will allow for creation of a

simple mass balance model that can be used to support management decisions. One area

needing immediate attention is the rate and quality of groundwater leakage into and or

out of Mosquito lagoon.

2) Develop iv.formation on the relationship between sediment chemistry and the chemistry

of the overlying water column with emphasis on the exchange rates and controlling

factors for metals and other ions. Define sources of metals in the environment and

develop management strategies if possible..

3) Work closely with the St Johns River Water Management District and Volusia County

staffto develop and participate in a joint interagency monitoring program that includes

Canaveral National Seashore. Participate in the St Johns River Water Management

Districts Pollution Load Reduction Program.

4) Develop a working adaptive water resources management strategy that defines the goals

of the CNS with regard to water quality issues. Set specific objectives and priorities.

5) Continue monitoring the species composition and abundance of submerged aquatic

vegetation by use of transect sampling and aerial photography or other remote sensing

methods.

6) Work with State and federal programs to continue monitoring fish communities in

Mosquito Lagoon with emphasis on critical periods in the early life history.

7) Establish a protocol for monitoring tissue concentrations of metals in shellfish and their

relationships to concentrations in sediments and the water column.

8) Support development of a multi-agency program to monitor seaturtle use of Mosquito

Lagoon with emphasis on species composition, health and abundance.

xxix
_L- qll
Canaveral National Seashore

Water Quality and Aquatic Resource Inventory

1.0 Introduction

This report covers Phase II of an Interagency Agreement IA 5000-0-9504 between the

National Park Service at Canaveral National Seashore and the National Aeronautics and Space

Administration at the John F. Kennedy Space Center. The study design was based on results of a

comprehensive literature review and information search reported in the "Mosquito Lagoon

Environmental Resources Inventory" (Provancha et al. 1992), which represented Phase I of the

project. Phase II covered two years of data collection based on information needs identified

through literature review.

Mosquito Lagoon is a shallow, bar built, barrier island estuary located on the east coast of

central Florida north of Cape Canaveral. Figure 1 shows the study area with the southern

boundary at 28 42.44 N and the northern boundary in the vicinity of Turtle Mound at 28 57.30 N.

Our objective was to provide a more comprehensive baseline database for water quality and

select biological resources that exist in Mosquito Lagoon with emphasis on the Canaveral

National Seashore. This baseline characterization program developed information on the

following topics:

• meteorology (rainfall, air temperature, wind speed and wind direction);

• water and sediment chemistry, temperature, salinity, and light attenuation;

• seagrasses (species composition, relative abundance, distribution maps)

• fish community data (species composition, relative abundance with comparisons to

historical data).

Information derived in Phase II was used to recommend monitoring programs for

implementation by the National Park Service personnel at Canaveral National Seashore (CNS).

2.0 Water and Sediment Quality

2.1 Introduction

Review of existing information on Mosquito Lagoon and Canaveral National Seashore

revealed several issues. There is a lack of long-term (greater than 10 years) data with consistent

variables and analytical procedures. Implementation of a monitoring program, coordinated by

the St. Johns River Water Management District, in 1989 for 135 sites in the Indian River Lagoon

continues to address this problem. However, several site-specific questions remain unanswered.

The majority of existing and historic sample stations are concentrated around the communities of

Edgewater and New Smyrna and do not provide adequate descriptions of water quality

conditions inside the CNS boundary.
Figure 1. CanaveralNationalSeashore,MosquitoLagoonandthenorth

IndianRiverestuarinesystemsin eastcentralFlorida. Theregionhashigh

biodiversityandanabundanceof wetlandsandseagrassbedssupporting

highprimaryproduction.
This study focused on development of baseline characterization data for water quality in and

around CNS.

Interpretation of water quality data requires an understanding of the water budget and

basic hydrodynamic processes that influence the mass balance, distribution and concentration of

chemicals within Mosquito Lagoon. Factors controlling water quality operate across a variety of

spatial and temporal scales each of which must be considered during sampling, analyses, and

interpretation. These factors are summarized in Provancha et al. (1992) and Woodward Clyde

(1994) and generally are represented by the water budget of the system.

Components of a basic water balance or water budget equation for Mosquito Lagoon can

be developed as shown in equation 1:

V=P+R+G-E+T+H (1)

V = instantaneous total lagoon volume

P = precipitation on the lagoon surface

R = watershed surface runoff and discharges to the lagoon (all sources)

G = groundwater seepage to/or from the lagoon

E = evapotranspiration from lagoon

T = tidal exchange between the ocean and lagoon through Ponce de Leon Inlet

H = water exchange with the Indian River Lagoon through Haulover Canal

In its simplest form, the equation states that the lagoon volume, V, is controlled by direct

precipitation on its surface plus runoff and surface input from point and non-point source

discharges, plus or minus groundwater seepage, minus evapotranspiration, pins or minus flow

through Haulover Canal, and plus or minus tidal exchange with the Atlantic Ocean. This

conceptual model is presented graphically in Figure 2. The major unknown in the equation is the

volume of groundwater movement into or out of the system. Basic order of magnitude estimates

for the other components of the water budget are available in the literature (Provancha et al.

1992, Woodward Clyde 1994).

Three forcing functions, gravity, radiation, and wind, serve as major controlling factors

affecting water movement and the mass balance or concentrations of chemicals in the system.

Gravity drives the major contributions or fluxes such as rainfall, stormwater runoff, and

groundwater seepage, tidal exchange and density stratifications. Wind serves as a source of

energy for advective mixing and movement, influencing several aspects of the mass balance

equation such as transport through Haulover Canal and Ponce de Leon inlet. Radiation (light and

heat) drives density dependent mixing events, evapotranspiration rates and biological processes

such as photosynthesis, respiration, and microbial decomposition. Water levels within south

Mosquito Lagoon average about 0.2 m above mean sea level, rising and falling in an annual

cyclic pattern in response to the annual rise and fall of sea level (Provancha et al. 1992).

3
Atmosphere Evapotranspiration

Wet De Dry Deposition

Inputs

Atlantic Ocean

Inlet

Point Sources

Nonpoi uito Lagoon Losses

Surficial Aquifer Haulover

Watershed

Infiltration Upward leakage

Indian River

Deep Aquifer

Figure2. Conceptual model of hydrologicpathways and processes influencingthe mass

balances of water and chemicals inMosquito Lagoon. Inputsinclude atmospheric

deposition,runoff,surficialaquiferleakage,deep aquiferleakage,and transportthrough

Haulover Canal and Ponce de [,conInlet.

4
Water levels in Mosquito Lagoon reach highs in October and November, and lows in

April and May. The estimated average 0.2 m difference in hydraulic head between south

Mosquito Lagoon and the Atlantic Ocean generates a net long-term flux of water out of the

lagoon through Ponce de Leon inlet onto the near-shore continental shelf (Provancha et al. 1992;

Woodward Clyde 1994). Influences of the tidal connection at Ponce de Leon Inlet are significant

when considering system hydrodynamics on a time scale of hours or days, especially in the

vicinity of the pass. Daily tidal cycles serve as water and energy exchange mechanisms resulting

in mixing of estuarine and oceanic waters as well as suspension of sediments and other lowdensity materials. At the inlet, mean tidal range is 0.7 m with tidal influences extending

approximately 10-15 km into Mosquito Lagoon (Provancha et al. 1992). Tidal fluctuations in the

Canaveral National Seashore area range from 50 cm at the north end to less than 2 cm at the

south end (Grizzle 1988). Daily tidal influences have not been measured at the south end of

Mosquito Lagoon.

On a long-term basis there is a net seaward flow of water and materials through Ponce de

Leon Inlet to the Atlantic Ocean (Woodward Clyde 1994). However, during high temperature

periods, high evaporation from the lagoon surface can result in lowering of water levels

producing a prolonged (days to weeks) net inward flux of seawater to replace estuarine water

losses. Near the inlet, water quality appears oceanic during these periods. In south Mosquito

Lagoon hyper-saline conditions may develop with salinities approaching and exceeding 40 ppt.

Superimposed on the daily tidal cycle near the inlef and the annual cycle in sea level that

influences the entire system are effects of wind driven circulation processes. Wind forcing on

the water surface tends to push water in the direction of the wind causing it to set up or set down.

For example, southeasterly breezes tend to push water in the Indian River and Mosquito Lagoon

to the north. This produces a difference in elevations between the two lagoons with water in the

Indian River being "set up" in its north basin and water in the south end of Mosquito Lagoon

being "set down" by the wind. This difference in water surface elevations generates a net flux

through Haulover Canal from the Indian River Lagoon to Mosquito Lagoon. In contrast, large

volumes of oceanic water may be transported into Mosquito Lagoon during extreme high tide

periods associated with storms in the Atlantic. These wind driven circulation processes are of

great importance when assessing results of water quality sampling in the Indian River and

Mosquito Lagoon (Woodward Clyde 1994).

Influences of storms on estuarine water quality and ecosystem productivity are poorly

documented in the scientific literature. Flint (1985) suggests that extreme weather events may be

responsible for controlling long-term productivity of estuarine and near-shore ecosystems by

producing major perturbations in biogeochemical processes and disrupting nutrient sinks,

analogous to fire or floods in terrestrial ecosystems. During March 1993, east central Florida

experienced westerly winds in excess of 40 knots for more than 24 hours in what was termed by

the media as the storm of the century. These winds lowered regional water levels and exposed

large areas of seagrass beds and sediments to the atmosphere and low air temperatures. This

exposure to the atmosphere alters the oxidation-reduction potential in surface sediments and can

cause a die off and detachment of large areas of seagrass blades and macroalgae. This resulting

pulse of organic matter and nutrients impacts the detritus base of the food chain in the lagoon

and near shore continental shelf. Quantitative assessments of the significance of these types of

events on system dynamics have not been conducted and the role in overall system productivity

and water quality is poorly understood.
_t' V

2.2 Methods

Water and sediment chemistry, microbiological samples, and basic field parameters were

collected at six stations in Mosquito Lagoon (Figure 3). Station 1, near Gallinipper Point, has

been sampled as part of Kennedy Space Center (ICSC) long-term monitoring since 1984. Station

2, located south of Eldora, represents the southeastern section of the park. Station 3 was located

in the Brickhouse Cove area of the west central region of the park. Station 4 was located in the

northeast section ofthe park near Turtle Mound and the associated urbanized region of the

barrier island. Station 5 was located in the southwest section of the park near Oak Hill, an area

of possible contamination sources. Station 6 was located at the northwest end of the park.

Coordinates for these stations are presented in Table 1.

Table 1. Global Positioning System (GPS) coordinates for the Canaveral

National Seashore sampling stations. Water and sediment chemistry station

designations include a W. Light attenuation sampling stations include the

letter A, B, or C desi _nating location along a transect.

Location

CNS1A

CNS1B

CNSIC

CNS1W

CNS2A

CNS2B

CNS2C

CNS3A

CNS3B

CNS3C

CNS3W

CNS4A/CNS2W

CNS4B

CNS4C

CNS4W

CNS5AJCNS5W

CNS5B

CNS5C

CNS6W

Latitude Longitude

28 42 27.00618 80 42 52.3016

28 42 27.90976 80 42 23.08577

28 42 29.59069 80 41 48.84447

28 41 13.9033 80 40 29.1598

28 44 9.79526 8 0 44 33.65264

28 44 16.81208 80 44 5.09409

28 44 18.04776 80 43 32.6989

28 51 14.08643 80 49 13.56059

28 51 17.34338 80 49 2.09203

28 51 24.81714 80 48 35.25331

2855 4.83162 80 51 39.1558

28 54 9.65259 80 49 7.46075

28 54 37.3500 80 49 20.4960

28 55 24.9636 80 49 34.2408

28 56 43.95463 80 50 17.33822

28 52 01.1000 80 50 4.22331

28 52 24.4455 80 50 4.32287

28 52 45.0815 80 50 16.13092

28 56 33.51459 80 52 9.79602

Water and sediment samples were collected and analyzed _cording to procedures

outlined and approvedby the State of Florida as part of their State Labq:atory Certification

Program. These methods generally followed procedures from the EPA'Methods for Chemical

- 6
Figure3. Locationsof surfacewatersamplingstationsutilized duringthe

waterandsedimentchemistrycharacterizationprogramfor Mosquito

Lagoon.
• q

Analysis of Water and Waste (EPA-600/4-79-020, revised March 1983). All samples, except the

1993 sediment samples, were processed through the State Certified chemical laboratory of Post,

Buckley, Schuh and Jernigan Inc., Orlando, Florida. The NASA Biomedical Office

Environmental Chemistry Laboratory at John F. Kennedy Space Center processed all sediment

samples collected in 1993. Microbiological samples were processed by the NASA Biomedical

Office Environmental Microbiology Laboratory using Florida DHRS Certified procedures.

Parameters monitored during the characterization program are listed in Table 2.

Table 2.

between 1991 and 1993.

Parameters measured for water and sediment samples collected in Mosquito Lagoon

Basic

PhysicalChemical

Conductivity (CON)

Total Suspended Solids

(TSS)

Total Dissolved Solids

(TDS)

Chlorophyll A (CPA)

Total Alkalinity (TAK)

Salinity(SAL)

Turbidity (TB)

Color (COL)

pH

Chemical Oxygen

Demand (COD)

Biological Oxygen

Demand (BOD)

[norganics Organics Metals

OrthoPhosphate (PO4)

Total Phosphorus (TP)

Magnesium (Mg)

Phenols (PILE)

Total Organic

Carbon (TOC)

Grease and Oil

Arsenic (As)

Mercury (Hg)

Silver (Ag)

Total Kjeldahl Nitrogen

(Trd,0

Nitrate (NO3)

Nitrite (NO2)

Ionized Ammonia

(NI-h)

Calcium (Ca)

Potassium (K)

Sulfate (SO4)

Herbicides

Pesticides

Cadmium (Cd)

Zinc (Zn)

Iron (Fe)

Aluminum (Al)

Boron 03)

Beryllium (Be)

Copper (Cu)

Molybdenum (Mo)

all

Nickel (Ni)

Lead if'b)

Silicon (Si)

Chromium (Cr)

Manganese (Mn)

Antimony, (Sb)

The six surface water stations were sampled on 12 occasions beginning in July 1991,

following a bimonthly schedule. Sediment sampling also followed the bimonthly schedule but

began in September 1991. Pesticide samples were collected three times during a six month

period from September 1991 to February 1992. Total and fecal coliform samples were also

collected bimonthly, beginning in September 1991 with one collection missed in March 1993 as

a result of equipment failure. Parameters measured in the field included temperature, DO, pH,

CON, oxidation-reduction potential (ORP), and SAL, using a Hydrolab Datasonde 3. At one

fixed station, data on CON, SAL, DO, pH, and temperature were collected every two hours. The

site was located approximately ten miles south of Ponce de Leon Inlet at the CNS boat dock in

Mosquito Lagoon. Sampling began on 8 October 1991 and continued for 608 days yielding
ar _¢

6,252 bi-hourly records. Probes were mounted approximately 35 em above the bottom in an area

approximately 1.2 m deep. Datasondes were typically in the field for fourteen days before being

replaced with a calibrated unit. Instruments were returned to the laboratory for data "

downloading, cleaning, and calibration.

Data analyses were conducted following an approach that included development of basic

descriptive statistics and bivariate correlations. Basic descriptive statistics were calculated to

characterize the statistical nature of the parameters. In this phase of the analysis the variability

of the data was defined and the need for data transformations, parameter deletions or the use of

nonparametric procedures were determined. The second phase of the analysis involved

determination ofbivariate measures of association between parameters to define interdependency

and covariance. The ultimate goal of the analysis procedure was definition of the statistical

nature of the data for use as a baseline with future goal specific monitoring or research activities.

2.3 Results and Discussion

Results of chemical analyses and field monitoring are presented in tabular and graphical

form in Appendix A. Tables A-1 to A-9 list results for surface water chemical analyses in

summary form sorted by sample date and station. Tables A-10 to A-14 present statistical

summaries for sediment analyses sorted by sample date and station. Tables A-15 and A-16

contain results of the nonparametrie Spearman Rank Correlation analyses. Figures A-I to A-10

display results of DO and SAL data collected on five transects as part of a light attenuation

study. Figures A-11 to A 71 show the temporal pattern of SAL, DO and temperature for the bihourly data collected at the CNS boat dock. Figures A-72 to A-84 present frequency

distributions of sediment chemical analyses. All analyses for herbicides, pesticides, Hg and Mo

were below the analytical procedure detection limits utilized by the chemistry laboratory or had

too few readings to analyze. These parameters are not discussed further.

2.3.1 Basic Physical and Chemical Parameters

2.3.1.1 Dissolved Oxygen (DO)

Dissolved oxygen is a critical and essential constituent for maintenance of biological

resources in aquatic systems. The Florida Department of Environmental Protection (DEP)

Quality Criteria for Surface Water Quality (FAC 62-302.530) state, that for Class II Waters used

for propagation or harvesting of shellfish DO levels shall not average less than 5.0 mgO in a 24

hour period and shall never be less than 4.0 mg/l. Normal daily and seasonal fluctuations above

these levels shall be maintained. Factors that directly control DO levels include temperature,

SAL, photosynthesis, BOD and COD. Gas exchange accompanies metabolic processes when

organic substances are synthesized or decomposed. The rate at which oxygen is consumed in the

water column is a function of mineralization of organic matter by bacteria as well as respiration

of aquatic plants and animals. Increases in dissolved carbon dioxide typically follow decreases

in oxygen levels. This in turn may alter the pH of water by formation of carbonic acid.

Conversely, photosynthetic activity in benthic algae, seagrass, macroalgae and phytoplankton

9
can liberate large quantities of oxygen into the water column, under proper growth conditions,

reversing the cycle.

Results ofbi-hourly data collection at the CNS boat dock are presented in Appendix A,

Figures A-51 to A-71. Three trends are present in the data. A short term, 24 hour daily

fluctuation is present that corresponds to the daily cycle ofpbotosynthesis and respiration. A

general longer term trend of higher values during cool months and lower values during warm

months is present that is directly related to the inverse relationship between temperature and

dissolved gases in water. Year to year differences are present, especially when comparing

winter/spring 1991-1992, to winter/spring 1992-1993.

Also important in the data set are the large number of readings and the extended periods

of measured values below the 5 mg/l 24-hour average and the 4 mg/l minimum DEP criteria.

Readings were consistently below the criteria between October 9, 1991 and November 24, 1991,

March 9 to March 18,1992, April 1 to April 27, 1992 and May 1 to July 8, 1992. In contrast,

extended periods of relatively high DO occurred in July 1992, October 1992, and November

1992 and between January and March 1993. During these periods values were consistently

above 8 mg/l. The sudden increase in DO in July from about 1 mg/1 to 11 mg/l was associated

with an influx of oceanic water through Ponce de Leon inlet. Salinity at the site increased from

18 ppt to almost 30 ppt in a two-hour period. Dissolved oxygen readings reached super

saturation levels of 197.2% with the highest recorded reading of 15.3 mg/l on March 2, 1993.

Th0 lowest value was recorded on August 25, 1992 at only 5.7% saturation or 0.37 rag/1.

Results of DO sampling at 15 stations associated with the underwater light attenuation

study are presented in Appendix A, Figures A-1 to A-5. These results display little deviation

between stations for the mid-day samples where all data were collected between 1000 h and

1500 h. All values in this data set are in compliance with the DEP criteria for DO of no values

below 4 mg/l. All transects and stations followed a general trend of maximum temperatures in

fall 1991 and relatively constant readings for the rest of the sampling with minimum values in

summer 1992.

2.3.1.2 Temperature

Results of water temperature measurements are presented in Appendix A, Figures A-11

to A-30. Two major temporal cycles are present in the data. On a daily basis, water

temperatures fluctuate about 2-3°C. Summer temperatures, June through August, generally

range between 27 and 31 degrees while winter temperatures, December through February,

typically range between 15 and 23°C. Spring and fall are transitional periods. The passage of

high-pressure cold fronts during fall and winter can have dramatic influences over water

temperature. Figure 4 displays effects of the passage of distinct frontal systems showing rapid

cooling of the water by typically 5-10°C and the gradual return to more average conditions over

the next 5 to 6 days. The influences of frontal system passage appear most commonly in data

10
35

.31

7..7

22

F--

i

............................................................................................................................ . ............................................................. ...............................................

t

J

7 L ilifd L_ItlJi;JlIll IdIIl illli IdHtfllll_ ill aHHLQ_QmlglllW I,Liltl_lUI#Ill _lttidllW[ll_i _ mt_lil III_lll_i Ill IIIitlltll]4lit H_HIIH_nIBHIdL;U_tli_ _dlt_ai li_ii_hIJiillllHIfl_4ill JUill_lilfliltlIfil_lil _ _IUIHHi I_lillP,I lil lllutltit I_lUltfld_ _lt_l_ii IHIIIIIliSll LUJlitlldlHIdl_l

} 2 ,3 4 5 67 8 9 10 11 12 13 14. 15 16 t718 lg 20 21 22 23 24- 25 26 27 28 29 30 31

Date

Figure 4. Bi-hourly water temperature (°C) data collected at the Canaveral National

Seashore boat dock in December, 1991. Data were collected utilizing a programmable

Hydrolab data logger set at a two-hour sampling interval. Probes were located 30 - 40

cm above the bottom in 1.2 m of water.

I1
collected between November and April. Passage of the storm of the century in March 1993

produced a 14°C decline in water temperature during a 48-hour period with values falling from

about 23°C to 9°C. The highest temperature recorded during the project was on July 27,1992

reaching 33.4°C, while the lowest recorded temperature was on March 15, 1993 at only 8.8 °C.

2.3.1.3 Salinity (SAL), Conductivity (CON), and Total Dissolved Solids (TDS)

Virtuallyallnaturallyoccurring elements of the earth'scrustcan be found insome

concentrationdissolvedin seawater. Concentrations ofdissolvedsubstancesin fleshand

estuarineecosystems are a functionof relationshipsthatexistbetween the body of water and its

watershed characteristics.Inland waters,riversand streamsare generallyhigh inCO3, SO4, Ca,

and Mg with lesseramounts ofNa and CI (Reid 1961). Relativeconcentrationsoftheseions

depend primarilyon soilcharacteristicsand geology of thewatershed. Oceanic constituentsare

virtuallyconstantand includeprimarilyNa (30.4%) and Cl (55.2%) and to a much lesserdegree

Mg (3.7%) and SO4 (7.7%). The chemical composition and distributionof ions inMosquito

Lagoon are the end resultof mixing of normally dissimilarwaters including rainfall,watershed

runoff,industrialdischarges,groundwater leakage,transportfrom the Indian River through the

Haulover Canal and the tidalinfluenceof the AtlanticOcean.

Three relatedmeasures of dissolved constituentsinMosquito Lagoon are SAL, CON, and

(TDS). TotalDissolved Solidsare measured by evaporatinga filteredquantityof water atlow

temperature. The driedresiduecontainsboth the inorganicand organic materialsdissolvedin

the sample. Ignitionofthe residueathigh temperature elirninatcsthe volatileorganics,and

decomposes bicarbonateswith the lossof carbon dioxide.Only the inorganicsaltsexpressed as

mg/l TDS remain. The totalweight of the ioniccomponent expressed as a proportionof the

originalsample interms of partsper thousand (ppt)isthesalinity.The salinityof the open ocean

generallyranges between 33 ppt and 38 ppt with an averagevalue of 35 ppt. The average

salinityof softfleshwater is0.065 ppt and of hard freshwater is0.3 ppt. From thisitisapparent

thathigh estuarinesalinitiesarcderived almost entirelyfrom seawater while low salinities

representareasof high freshwater influence.

A thirdand simple method tomeasure the amount of dissolved ionizedmaterialsis

through thedeterminationof electricalconductance. This parameter closelyapproximates the

residueinsolutionand generallyishighly correlatedwith TDS and salinity.By definition

conductance isthereciprocalof theresistancemeasured between two electrodes.Measurements

aregenerallyexpressed inmicro-mhos per centimeter(umhos/cm) at25°C and arecalledspecific

conductance.

Salinityvalues,collectedwith the Hydrolab Datasonde 3, atthe CNS boat dock, are

presented in Appendix A, Figures A-31 to A-50. The highest measurement was recorded on

May 8, 1993 reaching 40 ppt, and the lowest measurement of 18.3 ppt was recorded on July 7,

1992. Salinity readings higher than oceanic values generally result from low rainfall and high

evaporation in the lagoon during warm dry periods of late spring. :

Early in the study (October - November 1991), SAL at the CNS boat dock site increased

from about 25 ppt to about 32-'35 ppt and remained in this range for most of the following six

months. During the period between June and September 1992, in what is commonly referred to

as the wet season, salinities at the boat dock were noticeably lower with most values between 20

and 30 ppt. In the following months values varied more than in the previous year.

12
Salinitydata,collectedduringthelight attenuationstudyareshown graphically in

Figures A-6 through A-10. As with the DO data, SAL variation along transects was small.

Transects 1 and 2 appear similar with Transect 2 having slightly lower values possibly as'a

function of lower salinity waters moving from the Indian River Lagoon through Haulover Canal

to Mosquito Lagoon. In summer 1991 data on Transect 2 were almost 4 ppt lower than Transect

1 in south Mosquito Lagoon and 2-3 ppt lower than Transects 3, 4 and 5 north of Haulover

Canal.

Results of SAL measurements from the six bimonthly monitoring stations are presented

in Tables A-1 to A-3, providing additional spatial and temporal information about the lagoon.

Salinity measurements were variable across all seasons and stations ranging from a reported low

of 4.5 ppt at Station 2 in July 1992 to a high of 37 ppt at Stations 2 and 4 in June 1993. The low

value of 4.5 ppt appears to be an outlier, however the possibility of sampling a freshwater lens

does exist and the data were retained in the dataset. The majority of SAL measurements ranged

between 20 and 35 ppt with an overall average of 27 ppt and a standard deviation of 6.8 ppt or

about 24% of the mean value. Figure 5 shows the sampling distribution of the SAL data.

Average salinities at Station 1 and Station 2 were 25 ppt while Stations 3 through 6 averaged 27

to 28 ppt. Salinities at the southern two sites were generally 2-3 ppt less than the northern

stations, similar to results observed in the underwater light attenuation study. This salinity

gradient may be partially attributed to station locations relative to Haulover Canal and Ponce de

Leon Inlet with associated oceanic tidal influences.

A summary of CON and SAL measurements is presented in Figure 5. The average CON

measurement for the bimonthly water quality stations was 47,077 umhos/cm with a standard

deviation of 4,484 umhos/cm or only about 10 % of the mean, a value that is similar to the

estimate for TDS. The minimum CON value of 39,900 umho/cm was observed at Station 5 on

September 22, 1992. The maximum value of 59,900 umho/cm occurred at Station 2 in

conjunction with the elevated TDS measurement of June 16, 1993. As with TDS and SAL the

average CON value at Station I in south Mosquito Lagoon was lower than observed at the

northern sites.

Across all stations and sample periods TDS averaged 32,612 mg/l with a standard

deviation of 2,966 mg/l. The minimum value of 25,960 mg/l was collected at Station I in

November 1991, corresponding to a period of low salinity (16 ppt) and low conductance (40,230

umho/cm). The maximum TDS value of 40,500 mg/l was collected at Station 4 on June 16,

1993. Results of TDS measurements for each station and sample period are summarized in

Table A-1 to A-3 and are presented graphically in Figure 6.

The relationships between CON, SAL and TDS are apparent since each is a

measurement that involves the total ionic concentration in the sample. Results of non-parametric

Spearman Rank Correlation analysis (Table A-15) indicated significant positive correlations

between CON and TDS (r = 0.7228, p < 0.001), CON and SAL (r = 0.3808, p = 0.001), and

TDS and SAL (r = 0.2935, p = 0.013). The correlations between CON and SAL, and TDS and

SAL, although significant, were not as strong as expected based on the chemical relationships

that exist between the parameters.

13
t

16t

14

12

w = --

Std. Dev= 4484.24

Mean = 47076.9

N = 71.00

Conductivity (umhos/cm)

0 I

It.

[ " I "_ _ ....

5.0 10.0 15.0 20,0 25.0 30.0 35,0

7.5 12,5 17.5 22.5 27.5 32.5 37.5

Std. Dev= 6.84

Mean = 26.7

N = 71.00

Salinity (ppt)

Figure 5. Water quality sample frequency distributions for condtietivity and salinity.

There are no Class II criteria for conductivity or salinity.

14
50

10,

0__ .

g _ m w

_.o " _.o r_.o 600.0

393.0 45O.O 550.0

100.0 200.0

150.0 250.0

Total Alkalinity (mg/I as CaCO3)

Std. Dev= 60.30

Mean = 139.4

N = 71.00

_1 _ Std. Dev- 2965.94

_N= 71.00

Total Dissolved Solids (mg/I)

Figure 6. Water quality sample fi'equency distributions for total alkalinity and total

dissolved solids. There arc no Class H criteria for aikalimty or dissolved solids.

15
2.3.1.4 Total Alkalinity (TAK) and pH

The chemistry of marine waters is different from fi'esh water because of the large volume

of dissolved minerals present. Total alkalinity (TAK) is the sum total of components dissolved in

water that tend to elevate pH above a value of about 4.5 units. It is a measure of water's capacity

to neutralize strong acids through the hydroxide, carbonate and bicarbonate ion system.

The average pH value for water quality samples collected at the six sample stations

combined was 8.41 units with a standard deviation of 0.28 units. The minimum value observed

was 7.98 units from Station 4 and the maximum value was 9.04 units at Station 1. The average

for each station ranged between 8.3 and 8.6 units. The pH levels exceeded the 8.5 unit State of

Florida criteria at all six stations in July 1991, March 1992 and May 1992. Stations l, 2, and 5

also had values higher than the limit in July 1992. The high value observed at Station 1, which is

located in a shallow seagrass bed, is subject to high photosynthetic and respiration rates.

Results from the Spearman Rank Correlation analysis indicated pH was significantly

correlated with several parameters. There were weak negative correlations with Al (r = -0.3016,

p = 0.020), color (r = -0.3406, p = 0.004), and BOD (r = -0.3170, p = 0.011). Significant

positive correlations were found between pH and Cu (r = 0.8815, p < 0.001), TAK (r = 0.2952, p

= 0.012), and TOC (r = 0.4836, p < 0.001). Sediment pH values ranged between 6.82 at Station

1 on March 2, 1992 and 8.58 at Station 4 on May 5, 1992. The average sediment pH was 7.75.

Sediment pH was significantly correlated with Ag (r = .9355, p < .001), A1 (r = .2525, p = .042),

Fe (r = .1809, p = .0149), NH4 (r = .3846, p = .002), NO3 (r = -.3723, p ---.043), and TSS (r =

.4065, p = .0el).

2.3.1.5 Total Suspended Solids (TSS) and Turbidity (TB)

Suspended solids are the organic and inorganicparticles in suspension in the water

column. Turbidity is a term that is applied to waters containing suspended matter that interferes

with the passage of light through the water or in which the depth of light penetration or photic

zone is reduced. Turbidity may be caused by a variety of materials including colloidal particles,

eroded soil, organic flocculants, and microscopic organisms. Suspended solids and TB can

interfere with commercial and recreational use of waters through alteration of aesthetics and

productivi_. Irnp_ts 0f_ _d suspend¢_[i_s can occur in the watercolurnn_d _ areas of

sedimentation. Effects include reduced primary production, smothering of fish and shellfish

spawning sites, increased mortality of eggs and juvenile fish, disruption of feeding success, and

reduction of secondary production. Often, suspended solids contribute 'to the BOD of waters and

may serve as adsorption sites for metals and other pollutants, concentrating them in areas of

sedimentation. The State of Florida has not issued criteria for total suspended solids but

historically set a limit on TB of no increase above background levels in excess of 29 NTU (62-

302.530 F.A.C.).

Results of total suspended solids (TSS) measurements are presented in Table A-1 to A-3.

16
Total suspended solids averaged 61.49 rag/1 with a standard deviation of 67.02 mg/l. The

minimum value of 16.0 mg/l was observed at Station 1 on Match 31, 1993. The maximum value

of 350 mg/1 occurred at Station 3 on November 16, 1992. Station averages ranged betweeh 32.8

and 74.3 mg/1 with the lowest average being at Station 1 in south Mosquito Lagoon. Highest

average values of 74.3, 71.6, and 70.4 mg/l occurred at Stations 6, 4, and 3 respectively. These

northern stations are believed to experience the largest tidal influences.

Mean TB, averaged across all sites and sample periods, was 6.15 NTU with a standard

deviation of 4.34 NTU or 76% of the mean value. The minimum value of 0.928 NTU occurred

at Station 5 on January 19, 1993. The maximum value of 22.6 NTU occurred at Station 4 on

September 22, 1992. The high value is below the "not to be elevated more than 29 NTU" criteria

once used by the state in regulating TB. As with TSS, Station 1 in south Mosquito Lagoon

displayed the lowest average value of 3.14 NTU. Station 4 had the highest average of 8.79 NTU

when all samples periods are combined. Based on all samples, TB and TSS were significantly

positively correlated (r = 0.4536, p < 0.001) as expected.

.... ]_,aa_mati-bii_tiae-eb-rr_iat-ion table (l_bqe A-IS) showing bivariate relationships

between TSS and other parameters suggests several trends. TSS is positively correlated with

SAi__, (_ON and total disso]ved_li-ds. Thesep_ametersare in general higher at the northern

stations and are directly influenced by tidal exchange at Ponce de Leon Inlet. TSS is positively

correlated with A1, Si, Ca, Fe and SO4. These are common components of the lagoon sediment

that may be suspended in the water column by tidal action, wind driven turbulent mix!ng, and

man's activities. TSS was positively correlated with nutrients (nitrite, total phosphorous and

total Kjeldahl nitrogen), color, and CPA.

2.3.1.6 Chlorophyll A (CPA)

Chlorophyll A measurements from the water column can provide a good indication of the

overall biological status of an aquatic system. Chlorophyll based primary production links the

inorganic world to the organic world through photosynthesis (Gross 1972). Extreme low

ehlorophyU values (low phytoplankton production) may indicate nutrient limitations while

extreme high values can be indicative of eutrophication. Results of chlorophyll analysis are

shown in Figure 7 and Tables A-1 to A-3. The Florida DEP does not provide criteria for

chlorophyll concentrations. During this sampling the minimum value of 2.70 mg m "3 was

recorded for Station 4 on March 1992 while the maximum of 53.40 mg m -3 was recorded for

Station 5 in July 1992. For all stations and all sample periods the average value was 10.34

mg/m 3. These results are similar to previously reported values (Woodward-Clyde 1994).

Chlorophyll concentrations were positively correlated with A1 (r = 0.5178, p = 0.001), BOD (r =

0.4577, p = 0.002), Ca (r = 0.4165, p = 0.003), COD (r = 0.2327, p --- 0.104), COL (r = 0.5384, p

< 0.001), Si ( r = 0.6703, p < 0.001), TB (r = 0.6598, p < 0.001), TKN (r = 0.5038, p < 0.001),

TSS (r = 0.4391, p = 0.001). These relatively strong correlations with color, TB, and total

suspended solids are expected responses to phytoplankton abundance in:the water column.

Similarly, increasing phytoplankton abundance would result in increases in Si and TKN in the

water column. Significant negative correlations were observed with Cu (r = -0.6524, p = 0.021),

GO (r -- -0.3446, p = 0.037), pH (r ffi -0.2737, p = 0.054), PHE (r -- -0.3256, p -- 0.029), and SO4

(r = -0.2940, p = 0.038).

17
o. w

2.3.1.7 Color (COL)

The Florida DEP does not provide criteria for color in Class II or Class 1TIwaters. Color

is a measure of the optical property of a water sample based on wavelength dependent absorption

and scattering by materials in solution or suspension. As such it is sensitive to the presence of

compounds that absorb and scatter photons in the visible 400 to 700 nm wavelength region that

corresponds to the region of photosynthetic activity. Examples of materials that influence color

include natural metallic ions (Fe and Mn), suspended sediments, phytoplankton, and humic

acids. The ability of light of select wavelengths to penetrate the water column is critical to the

production of healthy communities of submerged aquatic vegetation, phytoplankton and benthic

algae. Results are summarized in Figure. 7. The minimum value recorded was 5.00 pt co units

occurring on February 3, 1992, March 2 1992, January 19, 1993, and March 31, 1993 at Stations

1, 2, 3, and 6. The maximum value of 50.00 pt co units occurred on September 18, 1991 at

Station 4. The mean for the two-year period was 21.59 pt co units with a standard deviation of

11.26 pt co units. Station 4, influenced most by tidal activity, displayed the highest average value

of 28.75 pt co units while Station 5 at the southwest end of the park had the lowest average value

of 10.47 pt co units. Station 1, at the south end of Mosquito Lagoon, averaged 16.11 pt co units.

Results of bivariate correlation analyses are presented in Table A-I 6. Color was significantly

positively correlated with AI (r = 0.3531, p = 0.007), BOD (r = 0.3033, p = 0.016), Con (r =

0.2445, p = 0.043), CPA (r = 0.5384, p < 0.001), NH4-N (r = 0.3184, p = 0.013), Si (r = 0.6314,

p < 0.001), TB (r = 0.7757, p < 0.001), TKN (1"= 0.3297, p = 0.006), TP (r = 0.3747, p = 0.002),

TSS (r = 0.4626, p < 0.001), and Zn (1"= 0.5397, p = 0.003). Color was significantly negatively

correlated with Cd (r = -0.3996, p = 0.008), NI (r = -0.4436, p = 0.044), pH (r = -0.3406, p =

0.004), and TOC (r = -0.4091, p < 0.001).

2.3.1.8 Biological Oxygen Demand (BOD)

Biological oxygen demand is an indication of the biological activity present in the water

column. The test is analogous to a wet oxidation bioassay in which living organisms (primarily

bacteria) serve as the medium for oxidation of organic matter. Florida DEP criteria state that the

BOD shall not be increased to exceed values that would cause oxygen to be depressed below

limits established for the subject class. In no case shall BOD be great enough to produce

nuisance conditions. Measured BOD values ranged between 1.0 mg/l and 7.0 mg/l with an

average of 2.48 mg/l (Figure 8). Maximum values were reported at Stations 4 and 5. BOD was

significantly correlated with COL (r = 0.3033, p = 0.016), CPA (r = 0.4577, p = 0.002), K (r ffi -

0.2588, p = 0.039), Ni (r = -0.5095, p = 0.022), NO2 (r = 0.4562, p = 0.002), pH (r = -0.3170, p =

0.01 l), PO4 (r = -.4924, p = 0.007), Si (r = 0.3384, p = 0.017), TB (r = 0.4605, p < 0.001), TKN

(r = 0.3747, p ffi 0.002), and TSS (r = 0.3361, p = 0.007). Biological oxygen demand was not

measured in sediments.

18
20

.%.\\\'q

10,_

o _\_',_

5.0

®

_\\\.,x

x',.\\\_

_\-_-_,N. _, .\-,.\'x.\',,,

x\\\\"_

\\\\\'_

10.0 15.0 20.0 25,0 30.0 35.0 40.0 46,0

ChlorophyllA (rag/m3)

B - m

50,0 55.0

Std. Dev = 7.75

Mean = 10,3

N= 50.00

14-

0 I

0:

10,

0

_)2)22

10,0 20,0 30.0

®

40.0 50.0

Std. Dev= 11.26

Mean = 21,6

N = 69.00

Color (pt co units)

Figure 7, Water quality sample frequency distributions for chlorophyll A

and color. There are no State criteria for these compounds.

- 19
2.3.1.9 Chemical Oxygen Demand (COD)

Chemical oxygen demand is a measure of the oxygen required to oxidize all compounds

present in the water column within the constraints of the test procedure. This measure includes

many chemicals that are resistant to biological oxidation and in general is typically larger than

BOD. The Florida DEP does not provide criteria for COD. Chemical oxygen demand values

ranged between 355.0 mg/l and 9300.0 mg/l with a mean value of 1141.96 mg/l. The minimum

and maximum values were both recorded from Station 1. Chemical oxygen demand was

significantly correlated with Ca (r = 0.3370, p = 0.004), CON (r = 0.2887, p = 0.015), Cr (r =

0.3719, p = 0.006), Mg (r = 0.2982, p = 0.012), NH4-N (r = 0.4948, p < 0.001), TB (r = 0.2324, p

= 0.051), and Zn (r = 0.4361, p = 0.020). Chemical oxygen demand was not measured in

sediment samples.

2.3.2 Total Metals

Metals are naturally occurring elements that may be beneficial, troublesome or toxic

depending on their form or concentration. Concentrations in estuarine surface waters and

sediments are related to watershed soil characteristics, seawater concentrations, atmospheric

inputs, and anthropogenic inputs from point and non-point source discharges, Metals in

estuarine and coastal environments are known to react strongly with particulates and organics in

the water column and at the water sediment interface. These reactions include adsorption,

desorption, complexation, and chelation processes. Factors that control partitioning of metals

between the bottom environment and overlying water column include pH, SAL, oxidation and

reduction potentials, mount and type of organic matter present, particle grain size distributions,

biological activity, temperature, and physical mixing (Manahan 199 I). Effects of exposure to

metals can include altered metabolic and physiologic rates, reduced fecundity, increased risk of

cancer formation, reduced survival of larvae, juveniles and adults, and altered mental capacity.

In an effort to _zehfiman and ecosystem rifl_ the Florida Department of Environmental

Protection has established concentration criteria for different surface water quality classifications

or uses. For this assessment we have utilized the Class II: Shellfish Propagation and Harvesting

criteria and Class Ill Recreation, Propagation and Maintenance of a Healthy, Well Balanced

Population of Fish and Wildlife. Results are summarized in Appendix A, Tables A-1, A-4, A-5,

A-10, A-11, and A-12.

20
50J ,

 2o,

IA.

10,0

2.0 4.0 6.0

_\\\\\\\\\\\\\\\\_

8.0

Biochemical Oxygen Demand (mg/l)

Std. Dev = 1.48

Mean = 2.5

N = 64.00

0 I

0 I

10'

0

Std. Dev= 1403.85

Chemical Oxygen Demand (mg/I)

Figure 8. Water quality sample frequency distributions for biological oxygen demand

(BOD) and chemical oxygen demand (COD). The Florida Class II: Shellfish

Propagation or Harvesting Criteria for Surface Water Quality (62-302.530 F.A.C.) state

that BOD should not exceed values that depress dissolved oxygen below established

limits, or produce nuisance conditions. There is no criterion for COD.

21
2.3.2.1 Silver (Ag)

The Florida DEP criteria for Class II water used for shellfish propagation and harvest is

0.05 ug/l. Provancha et al. (1992) report that total Ag concentrations in excess of the 0.05 ug/l

criteria have been reported in all water bodies sampled at KSC and MINWR. Background values

for Ag in soils typically range between 0.03 and 3.2 mg/kg (Kabata-Pendias and Pendias 1984).

In addition, seawater is reported to contain Ag concentrations between 0.055 and 1.5 ug/l

(Friberg et al. 1986). The minimum observed value of 0.15 ug/1 was reported from Station I on

September 22, 1992, and the maximum observed value of 2.20 ug/l occurred on July 23, 1991 at

Station 4 (Table A-5). The average of observed values was 1.07 ug/l. Eighteen of the 71

possible samples were reported as below detection. The frequency distribution of reported

sample values is presented in Figure 9. Silver concentrations displayed significant positive

correlations with pH (r = 0.4277, p = 0.001), TDS (r = 0.3315, p = 0.015), and TOC (r = 0.3506,

p = 0.010). Negative bivariate correlations were observed with Al (r = -0.4028, p = 0.007), Fe (r

= -0.4090, p ---0.007), and NI-h-N (r = -0.3i48, p = 0.033). Silver concentrations in sediments

ranged between 0.05 mg/kg at Station 3 in 1993 and 10.13 mg/kg at Station 4 in 1992 with an

average across all station and sample periods of 1.78 mg/kg. Sediment concentrations of Ag

were negatively correlated with Pb (r = -.8108, p -- .027), and positively correlated with sediment

pH (r = .9355, p < .001). Long and Morgan (1990) report sediment concentrations below 1.0

mg/kg pose little risk to biota. Concentrations in excess of 2.2 mg/kg pose a greater risk.

2.3.2.2 Aluminum (Al)

Aluminum is a major constituent of the earth's crust and common to soils in coastal

Florida. Alumino-silicates are produced by weathering and are a major constituent of many

soils. The State criterion for Class H and HI water is 1.5 rag/1. Aluminum is an abundant

component of coastal soils in Florida and is frequently reported at concentrations near or above

the State criteria (Provancha et al. 1992). The toxicity of Al depends on a variety of factors

including form, complex, and pH. For example, organically bound forms of AI are generally less

toxic than inorganic forms. Aluminum is generally more toxic at low pH than high pH. Because

of the many species of Al found in water, the precise relationships of A1 concentrations to

toxicity are still not well understood (see Flora et al. 1984). Aluminum was reported as above

detection in 59 of 71 samples.

22
12

10,

,

4,

2,

0

[State criterionis_<2.3ug/l{

,",\\\\\",i

.25 .50 .75 1.OO 1.25 1.50 1.75 Z00 Z25

Silver (ug/l)

Std. Dev= .57

r

!Mean = 1.07

N= 53.OO

]stat_ C_te,i0_i_< 15_

30'

E,,\\\\"4

_,,,,_\\'q

_\\\\",]

2

1 !

IStd. Dev =.51

i

0.OO .25 .50 .75 1.00 1.25 1.50 t.75 2.OO 2.25 2.50 2.75

_un"inum (r_/I)

Figure 9. Water quality sample frequency distributions for Ag _nd AI compared to the

Florida Class II: Shellfish Propagation or Harvesting Criteria for Surface Water Quality

(62-302.530 F.A.C.). Criteria concentrations are depicted by a vertical line.

23
n w

The minimum reported value of0.11 mg/1 value occurred on March 2, 1992 at Station 5. The

maximum value of 2.64 rag/1 occurred on September 22, 1992 at Station 4. A value of 2.60 rag/!

was reported for Station 1 on May 5, 1992. The sample distribution and state criteria are shown

in Figure 9. Three of 71 samples were at or above the criteria of 1.5 rag/1. The overall average

reported concentration of A1 during this study was 0.54 rag/1 with a standard deviation of 0.51

mg/l. Aluminum was positively correlated with B (r = 0.2976, p = 0.022), Ca (r = 0.2826, p =

0.030), COL (r = 0.3531, p = 0.007), CPA (r = 0.5178, p = 0.001), Fe (r = 0.5249, p = 0.001),

SAL (r = 0.3549, p = 0.006), Si (r = 0.5906, p < 0.001), TB (r = 0.4469, p < 0.001), TKN (r =

0.2764, p = 0.037), and TSS (1"= 0.4882, p < 0.001). Aluminum was negatively correlated with

Ag (r = -0.4028, p = 0.007), pH (r = -0.3016, p = 0.020), and SO4 (r = -0.2745, p = 0.035).

Results of sediment analyses are presented in Tables A-l, A-4 and A-5. The average

value was 4528 mg/kg. The minimum AI concentration of 325 mg/kg was recorded at Station 5.

The maximum value of 21166 mg/kg was recorded at Station 2. Aluminum was highly

correlated with many parameters. Significant Spearman Rank Correlations were observed with

Be (r = 0.7218, p < 0.001), Cd (r = 0.4318, p = 0.002), Cr (r = 0.8093, p < 0.001), Cu (r =

0.4570, p = 0.006), Fe (r = 0.8440, p < .001), K (r = 0.6767, p < 0.001), Mg (r = 0.6227, p <

0.001), Mn (r = .8656, p < 0.001), Ni (r = 0.3221, p = 0.029), Pb (1"= 0.8812, p < 0.001), pH (r =

0.2525, p = 0.042), TKN (r = 0.3721, p = 0.002), TOC (r -- 0.4626, p < 0.001), TP (r = 0.3366, p

= 0.021), and Zn (r -- 0.4729, p < 0.001).

2.3.2.3 Beryllium (Be)

Beryllium is recognized as being widely distributed in low concentrations in soils and is

known to be toxic to plants (Kabata-Pendias and Pendias 1984). Sources of Be in the

environment include smelters and coal combustion. Soil Be samples at KSC are consistently

reported as below detection levels. Results for analyses of Be in water are presented in Figure 10

and Tables A-I, A-4 and A-5. Beryllium was reported in 30 of 71 possible samples. Forty-one

analyses were below detection. All reported values are above the Florida DEP criteria of 0.13

ug/l annual average. The minimum value of 0.20 ug/1 was reported for Station 5 on July 23,

1991 and September 22, 1992. The maximum value of 2.2 ug/l was reported for Station I on

February 3, 1992. Beryllium was positively correlated with CON (r = 0.4150, p = 0.023), Cr (r

= 0.3567, p = 0.053), and SO4 (r -- 0.3826, p = 0.037), and negatively correlated with grease and

oil (GO) (r = -0.5121, p = 0.015).

Analyses of Be concentrations in sediments are summarized in Table A-10. The

minimum value of 0.03 mg/kg was observed at Station 5 on September 18, 1991. The maximum

value of 2.04 occurred at Station 4 on March 31, 1993. The average value for all stations and

sample periods was 0.32 mg/kg. Total Be was significantly correlated with Al (r = .7218, p <

.001), Cd (r = .4894, p < .001), Cr (r "" .5787, p < .001), Fe (r = .7050, p < .001), K (r = .4781, p

< .001), Mg (r = .4058, p = .001), Mn (r = .6948, p < .001), Pb (r = .7228, p < .001), PO4 (r =

.6378, p -- .035), SOd (r = .3808, p = .008), TKN (r = .4271, p < .001), TP (r = -.3830, p = .008),

and Zn (r = .4898, p <0.001).

24
2.3.2.4Boron (B)

Figure 10 displays results for the chemical analysis of total B in Mosquito Lagoon

surface water samples. Concentrations of B in seawater typically average 4.6 ppm. (Gross

1972). There are no Florida DEP criteria for this element in Class II or Class HI waters. Boron

displayed significant but weak positive correlations with AI (r = 0.2976, p = 0.022), Ca (r =

0.6302,p < 0.001),CON (r= 0.3751,p - 0.001),Fe (r--0.3054,p --0.044),Mg (r= 0.3071,p =

0.009),Ni (r= 0.4367,p = 0.030),SAL (r= 0.6149,p < 0.001),and TDS (r= 0.4264, p < 0.001).

Boron displayedno negativebivariatecorrelations.The minimum value of 0.24 mg/1 occurred on

November 20, 1991 atStation2 (Table A-4). The maximum value of 5.98 mg/I occurred on

June 16, 1993 atStationI. The mean of reportedconcentrationswas 2.96 mg/l with a standard

deviationof 0.99 mg/1.

In sediments the minimum B valuereportedwas 6.15 mg/kg from Station1 on January

19, 1993. The maximum measured sediment concentrationwas 66.18 mg/kg forStation3 on

September 2, 1992. Sediment B concentrationswere significantlycorrelatedwith Cu (r= .6606,

p = .038),and K (r= .6393,p = .010).

2.3.2.5 Calcium (Ca)

The Florida DEP does not recommend criteria for Ca, a common and abundant

constituent of coastal soils and seawater. Results of Ca analyses for surface waters are presented

in Figure 11. The mean reported value was 297.7 rag/1 with a range of 80.0 to 453.0 mg/l. The

minimum value was reported fi'om Station 4 on March 13, 1993 and the maximum value was

recorded for Station 5 on May 5, 1992. Calcium was significantly positively correlated to A1 (r --

0.2826, p -- 0.030), B (r -- 0.6302, p < 0.001), Cd (r = 0.2977, p = 0.050), COD (r -- 0.3370, p =

0.004), CON (r -- 0.4399, p < 0.001), CPA (r = 0.4165, p = 0.003), Mg (r -- 0.6394, p < 0.001),

Ni (r = 0.4458, p -- 0.038), pH (r ---0.2409, p = 0.043), SAL (r -- 0.3908, p = 0.001), TDS (r =

0.4575, p < 0.001), and TSS (r = 0.2413, p = 0.043). Calcium was negatively correlated with Cu

(r = -0.6124, p = 0.020), and NI-h-N (r = -0.2743, p = 0.032). Total Ca concentrations in

sediments are directly related to the presence of shell materials and other Ca bearing particulates.

The minimum value reported was 1460 mg/kg from Station 6. The maximum value was 134,000

mg/kg from Station 1. The average concentration was 24,732 mg/kg. Sediment Ca was

significantly but weakly correlated with Cr (r = -.2516, p = .043).

25
2O

w m D

1._ _._ 1._ 1.7s z_ z_

State criterion is < O.13 ug/l[

.25 .50 .75

Beryllium (ug/I)

Std. Dev= .52

Mean= .54

N = 30.00

0 I

0 I

:32O

U10'

L_ ]Std. MeanDev= = 2.96.99

0 . . , . . _ = ._-_N=71.00

o.oo 1.oo _.oo 6.oo

.50 1.50 4.50 5.50

\\\\',

2.00 3.00 4.00

Z50 3.50

Boron (mg/I)

Figure 10. Water quality sample frequency distributions for be_llium and boron

compared to the Florida Class ll: Shellfish Propagation or Harvesting Criteria for

Surface Water Quality (62-302.530 F.A.C.). Criteria concentrations arc depicted by a

vertical line. There is no Class 11criterion for boron.

26
16,

12,

4

75.0 125.0 175.0 225.0 275.0 ,325.0 375.0 425.0

100.0 150.0 200.0 250.0 300.0 350.0 400.0 450.0

Std. Dev= 77.29

Mean = 297.7

N = 71.00

Calcium (rng/I)

16'

14

12

'10 _

2

0

0._ 1._ Z_ 3._ 4._ 5._ 6._ 7._

Std. Dev= 1.85

Mean= 1.28

N = 44.00

.50 1.50 Z50 3.50 ..... _i_ .... 5.50 6.50

Cadmium (ugTI)

Figure 11. Water quality sample frequency distributions for calcium and cadmium. The

Florida Class IT: Shellfish Propagation or Harvesting Criteria for Surface Water Quality

(62-302.530 F.A.C.) criterion for cadmium is _<9.3 ug/1. There is no criterion for

calcium.

27
2.3.2.6 Cadmium (Cd)

Cadmium is recognized as a highly toxic metal causing growth, behavioral and

physiological problems in fish and other aquatic organisms. It is known to bioaccumulate in fish

and invertebrates. Results of Cd analyses are presented in Figure 11 and Tables A-l, A-4 and

A-5, The Florida DEP criterion for Cd in Class II and Class HIwaters is 9.3 ug/l. All 44

reported values for this study were below the criterion. The average concentration was 1.28 ug/l

with a range of reported values between 0.01 and 7.10 ug/l. The minimum reported values were

from Stations 5 and 6 on November 20, 1991 and June 16, 1993 respectively. The maximum

value occurred on May 5, 1992 at Station 2 near Haulover Canal. Cd displayed positive

correlations with Ca (r = 0.2977, p = 0.050), COD (r = 0.572, p < 0.001), Cr (r = 0.6208, p <

0.001), Mg (r = 0.4888, p = 0.001), Ni (r = 0.571, p = 0.013), pH (r = 0.4352, p = 0.003), SO4 (r

= 0.3617, p = 0.016), TDS (r = 0.3592, p = 0.017), TOC (r = 0.6473, p < 0.0010). Negative

correlations were found between Cd and COL (r = -0.3996, p = 0.008), and GO (r = -0.3525, p =

0.052).

Cadmium is known to form complexes with S04, a common component ofesmarine

sediments, and it may become sequestered in the benthic environment. The minimum reported

sediment concentration was 0.01 mg/kg. The maximum concentration of total Cd in sediments

was 0.80 mg/kg. The average reported Cd concentration for sediments was 0.10 mg/kg. Cd was

significantly correlated with A1 (r = .4318, p = .002), Be (r = .4984, p < .001), Cr (r = .3044, p =

.030), Fe (r = .3447, p = .013), GO (r = -.3525, p = .019), Mn (r = .4293, p = .002), Pb (r = .3827,

p = .006), SO4 (r = .3960, p = .008), TKN (r = .3610, p = .009), TSS (r = -.6374, p < .001), and

Zn (r = .4830, p = .001).

2.3.2.7 Chromium (Cr)

Chromium behavior and potential toxicity in estuarine environments is a complex issue

because Cr may be present in a variety of forms (Manahan 1991). Depending on the chemical

state the same elemental concentration may have a wide range of mobility and reactivity. Most

Cr in surface waters is typically in a particulate trivalent form associated with suspended matter

and sediments. Ingestion of these particulates by organisms is a common form of exposure. The

hexavalent form of Cr is highly soluble and may enter organisms by sorption through the gills

and other membranes. The Florida DEP has set a Class II and Class Ill criterion of 50 ug/1 for

hexavalent Cr but provides no guidance for total Cr or trivalent Cr in Class II or Class RI waters.

Results of chemical analyses for total Cr are presented in Figure 12. Fifty-four of 71 samples

were reported to have total Cr levels above the detection limits oftbe laboratory procedure.

Minimum values of 0.002 mg/l (2 ug/l) occurred at Stations 5 and 6 on July 23, 1991 and

September 22, 1992. A maximum value of 0.258 mg/l (258 ug/l) occurred on March 31, 1993 at

Station 4. The mean value was 0.03 mg/l. Chromium was positively correlated with Be (r =

0.3567, p = 0.053), Cd (r = 0.6208, p < 0.001), COD (r = 0.3719, p = 0.006), pH (r = 0.2905, p =

0.033), PIlE (r = 0.2172, p -- 0.047), SO4 (r = 0.3992, p = 0.003), TDS (r = 0.3705, p = 0.006),

and TOC (r = 0.3158, p = 0,020). Chromium was negatively correlated with COL (r = -0.4411, p

= 0.001), and TB (r = -0.3373, p = 0.013).

The minimum total Cr sediment value was 0.17 mg/kg collected fi'om Station 5 on

September 18, 1991. The maximum was 251.00 mg/kg collected from Station 4. The average

28
sediment value was 18.53 mg/kg. Sediment Cr was significantly positively correlated with A1

(r = .8093, p < .001), Be (r = .5787, p < .001), Cd (1"= .3044, p = .030), Cu (r = .3709, p = .028),

Fe (r = .7418. p < .001). K (r = .7668, p < .001), Mg (r = .4284, p < .001), Mn (r - .8344, p <

.001), Pb (r = .7495, p < .001), PO4 (r = .7091, p = .015), SO4(r = .3328, p -- .022), TIGN (r =

.2705, p = .029), and Zn (r = .4629, p < .001). Negative correlations were found with Ca (r = -

.2516, p = .043), GO (r = -.4100, p = .004) and TP (r = -.4614, p = .001). Sources of potential Cr

contamination include industrial waste, mining and metal processing, wood preservatives and

sewage sludge (Kabata-Pendias and Pendias 1984).

2.3.2.8 Copper (Cu)

The Florida DEP has set a Class II and Class IT[criteria of 2.9 ug/l for Cu. Copper is an

essential element for life but in high concentrations it can become toxic. In water, Cu acts

synergistically with other contaminants such as Cd, Hg, and Zn to produce an increased toxic

effect on fish. Results of reported analyses are presented in Figure 12. Only 14 samples were

r_orted to contain concentrations in excess of laboratory detection limits for this compound.

Reported detection limits ranged from I ug/l to 30 mg/1 depending on method of analysis. This

inconsistency makes interpretation of these results problematic. The minimum reported value

was 0.02 mg/l from all stations on January 19, 1993. The maximum reported value was

collected at Station 2 on March 2, 1992. The average for the 14 reported values was 0.05 mg/l.

Even though the reported values were few in number Cu displayed a positive correlation with

NH4-N (r = 0.5774, p = 0.049), pH (r = 0.8815, p < 0.001), SO4 (1"= 0.5595, p = .037), TAK (r =

0.6956, p = 0.006), and TDS (r = 0.6014, p = .023). Copper was negatively Correlated with Ca (r

= -0.6124, p = 0.020), CON (r = -0.6232, p = 0.017), CPA (r = -0.6524, p = 0.021), SAL (r =

-0.8261, p < 0.001), and TOC (r = -0.6787, p -- 0.008).

Sediment Cu values were above the detection limits in 35 samples. Values ranged

between a low of 0.26 mg/kg at Station 5 and a high of 59.0 mg/kg at Station 3. The average

was 5.95 mg/kg. Sediment Cu was significantly correlated with AI (r = .4570, p = .006), B (r =

.6606, p = .038), Cr (r = .3709, p = .028), Fe (r = .3621, p = .033), K (r -- .5407, p = .001), Pb (r

-- .4383, p = .014), and TOC (r = .3743, p -- .027). Kabata-Pendias and Pendias (1984) report

that Cu concentration in soils typically range between 6-60 mg/kg and it is relatively immobile.

Agriculture chemicals such as fungicides and fertilizers may contribute to non-point source

discharges of Cu. Other possible sources include industrial processes, municipal waste, and coal

combustion.

29
State criterion is _<.05 mg/l I

4O

oooo _ ._ o_s 1_o 1_ .1_o .lzs _ z_ 2_o

Chromium (mg/I)

Std. Dev= .06

Meen = .028

N= 54.00

7_

1

1

o_

t- 4'

=E3,

LL

!

1

0

,_ Stat¢criterion is < .0029 mr,/1 j

x\\'_ .....

xxxxx

_xxxx

xxxxx _"

,xx'%..

.\\\N ....

.025 .050 .075 .100

Std. Dev= .04

Mean = .054

N = 14.00

Copper (mg/I)

Figure 12. Water quality sample fi'equency distributions for chromium and copper compared

to the Florida Class n: Shellfish Propagation or Harvesting Criteria for Surface Water Quality

(62-302.530 F.A.C.). Criteria concentrationsarc depicted by a vertical line.

30

i
2.3.2.9 Iron OFe)

Iron is the fourth most abundant element in the earth's crust making up about 4.7 % of

the total mass. It is present in hundreds of minerals including many silicates, sulfides and

carbonates where it exists mainly as insoluble ferric oxide. In reducing or anaerobic conditions

ferric iron is reduced to the much more soluble ferrous state. Iron in high concentrations

produces a distinct reddish color that can serve as a pollution indicator. In the presence of

oxygen Fe can form hydroxide or oxide precipitates that can flocculate and settle to the bottom.

This flocculent can be detrimental to benthic filter feeding organisms and eggs and larvae of fish

and shellfish. The Florida DEP criterion for Fe in Class II and Class Ill water is 0.3 and 1.0 mg/l

respectively. Results are presented in Figure 13. Iron was reported above detection limits in 44

of 71 possible samples. The minimum reported value was 0.05 mg/1 that occurred at Station I on

May 5, 1992 (Table A-I). The maximum reported value was 10.40 mg/l for Station 4 on March

3, 1993. The average concentration of Fe in seawater is reported by Gross (1972) as 0.01 rag/1.

The mean value across all stations and time periods was 0.50 mg/l (Table A-l), which is slightly

higher than the State criteria of 0.3 rag/1. Iron displayed significant positive correlations with AI

(r = .0.5249, p = 0.001), B (r = 0.3054, p = 0.044), K (r -- 0.3106, p -- 0.040), NI-h-N (r = 0.3500,

p = 0.027), TB (r = 0.3414, p = .023), and TSS (r = 0.3119, p = 0.039). Negative correlations

were found between Fe and Ag (r = -0.4090, p = 0.007).

In sediment samples the minimum value for total Fe was 349 mg/kg. This was observed

at Station 5 on September 18, 1991. The maximum value of 253401 mg/kg was collected at

Station 3 on May 5, 1992. Results ofbivariate correlations analyses are presented in Table A-16.

Total Fe was significantly correlated with A1 (r = .8440, p < .001), Be (r = .7050, p < .001), Cd (r

= .3447, p = .013), Cr (r = .7418, p < .001), Cu (r = .3621, p = .033), K (r = .5205, p < .001), Mg

(r = .5682, p < .001), Mn (r = .8184, p < .001), Pb (r = .7837, p < .001), pH (r = .1809, p =

.0149), PO4 (r = .6545, p = .029), SO4 (r = .5324, p < .001), TKN (r -- .4377, p < .001), TOC (r =

.2648, p = .033), TP (r = -.3681, p = .011), TSS (r = -.3600, p = .003), and Zn (r = .6023, p <

.OOl).

2.3.2.10 Magnesium (Mg)

Magnesium is a major constituent of seawater typically representing 3.7 % of the total

dissolved salts. In estuaries the concentration of Mg, like Na, CI, and Ca is greatly influenced by

the degree of mixing between seawater and flesh water inflows. There are no Florida DEP

criteria for Mg and it is generally of no toxicological concern. The average value for all sites and

sample periods was 972.94 mg/l. The minimum value recorded was 41.60 mg/l on March 13,

1993 and the maximum value was 1370.00 mg/l on May 5, 1992. Both:samples were collected

31
0 I

30'

20'

10'

0

0.0

//_ State criterion is < 0.3 mg/l ]

m

1.0 io 3"o ;o s:o 6"o

iron (rng/I)

7.'0 8"0 9.'0 10.0

Std. Dev= 1.54

Mean = .5

N = 44.O0

==

It.

0 I

0 _

1° 0 L. .

0.0

100.0

2o0.0",_.o _o

_\'_ Std. De,v= 214.46

X\\\

_,,'_ _\\'_\\\_'_\\\_ I Mean = 972.9

. = = .

800.0 1000.0 1200.0 1400.0

300.0 500.0 700.0 900.0 1100.0 1300.0

Magnesium (rng/I)

Figure 13. Water quality sample frequency distributions for iron and magnesium compared

to the Florida Class II: Shellfish Propagation or Harvesting Criteria for Surface Water Quality

(62-302.530 F.A.C.). Criteria concentrations are depicted by a vertical line. There is no criterion

for magnesium.

32
at Station 4. Gross (1972) reports an average concentration of Mg in seawater of 1350 mg/!

suggesting Station 4 was experiencing tidal influence from Ponce de Leon Irdet. Magnesium

was significantly positively correlated with B (r = 0.3071, p = 0.009), Ca (r = 0.6394, p < .001),

Cd (r = 0.4888, p = 0.001), COD (r = 0.2982, p = 0.012), CON (r = 0.6209, p < 0.001), K (r =

0.2698, p = 0.023), Ni (r = 0.5867, p = 0.004), pH (r -- 0.2805, p = 0.018), and TDS (r = 0.6011,

p < 0.001). Note that positive correlations existed with CON, TDS, and Ca, each of which are

related to the concentration of seawater in the lagoon. Magnesium was negatively correlated

with Zn (r = -0.3904, p = 0.040).

Sediment Mg levels ranged between a low of 245 mg/kg collected at Station 5 on January

19, 1993 and a high of 5838 mg/kg collected at Station 3 on July 27, 1992. Mg was significantly

correlated with A1 (r = .6227, p < .001), Be (r -- .4058, p = .001), Cr (r -= .4284, p < .001), Fe (1"=

.5682, p < .001), K (r = .3900, p = .002), Mn (r = .5553, p < .001), Pb (r = .5799, p < .001), SO4

(r -- .4702, p = .001), TKN (r = .4696, p < .001), TOC (r = .5773, p < .001), TSS (r = -.3908, p =

.001), and Zn (r = .4796, p < .001).

2.3.2.11 Manganese (Mn)

Manganese is an abundant trace element (Kabata-Pendias and Pendias 1984) with

generallylow concentrationsinsandy soils.All surfacewater samples forMn were reportedas

below detectionlimitwhich was 0.02 mg/l. Gross (I972) reportsaverage concentrationsin

seawater of 0.002 mg/l. The FloridaDEP criterionforClassIIwaters is0.I mg/l. Sediment

samples fortotalMn ranged from a low 4.17 mg/kg atStation5 on September 18, 1991 to a high

concentrationof 97.90 mg/kg atStation3 on July27, 1992. The average value was 21.78 mg/kg.

Sediment Mn was significantlycorrelatedwith othermetals such as Al (r= .8656, p < .001),Be

(r= .6948,p < .001),Mg (r= .5553,p < .001),Pb (r= .7806,p < .001)and Zn (r= .5831,p <

.001). Weaker correlationswere observed with SO4 (r= .4431,p = .002),TKN (r= .4402,p <

.001),TOC (r= .3106,p = .012),TP(r= -.2842,p = .053),and TSS (r= -.3105,p = .012).

Sources of Mn inthe environment includesewage sludge and fertilizersCgabata-Pendias and

Pendias 1984).

2.3.2.12 Nickel (Ni)

The Florida DEP criterion for Ni in Class H and Class HI marine water is 0.0083 mg/l. Nickel is

potentially toxic to marine organisms however its toxicity may be reduced in the presence of Mg

(Manahan 1991). Ni concentrations in seawater average about 0.0055 mg/l (Gross 1972).

Results of analyses are presented graphically in Figure 14. Twenty-two of 71 samples were

reported as having concentrations above the laboratory detection limits. The minimum

33
12

te criterion is __.0083 mg/l I

I

i'

0.00 .06 .13 .19 .25 .31 .38 .44 .50 .56

Nickel (rag/I)

Std. Dev= .15

Mean = .10

N = 22.00

2O

0.000

//_ State criterion is < .0056 rng/l j

_\\\\\\\\\\\\_'1_\\\\'% _\\\\_1 I_\\\\_ _\\\_

•013 .025 .038 .050

Std. Dev = .01

Mean= .008

N = 19,00

Lead (mg/i)

Figure 14. Water quality sample fi'equency distributions for nickel and lead compared to the

Florida Class II: Shellfish Propagation or Harvesting Criteria for SurfaceWater Quality (62-

302.530 F.A.C.). Criteria concentrations are depicted by a vertical line.

34
observed value of 0.004 rag/1 was reported for Stations 3 and 4 on September 18, 1991 and

November 16, 1992, respectively. The maximum value of 0.580 mg/1 was observed on May 5,

1992 at Station 6. The overall mean of reported values was 0.10 mg/l. Nickel was significantly

positively correlated with B (r = 0.4367, p = 0.030), Ca (r = 0.4458, p = 0.038), Cd (r = 0.571, p

= 0.013), CON (r = 0.5379, p = 0.010), K (r = 0.6167, p = 0002), Mg (r -- 0.5867, p = 0.004), pH

(r = 0.5330, p = 0.011), TDS (r = 0.6665, p = 0.001), and TOC (r = 04826, p = 0.023). Negative

correlations were observed between Ni and BOD (r = -0.5095, p = 0.022), COL (r = -0.4436, p

= 0.044), Si (r = -0.5449, p = 0.029), TB (r = -0.4662, p = 0029), and TP (r = -0.5665, p = 0.007).

Nickel is typically found at low concentrations in sandy coastal soils. Possible sources include

industrial activities such as metal plating operations, municipal sewage discharges, and fossil

fuel (coal) combustion (Manahan 1991).

Sediment concentrations of Ni were reported above detection in 46 of the possible 65

samples. The minimum value of 0.16 mg/kg and the maximum value of 12.26 mg/kg were

observed at Station 3 on June 16, 1993 and July 27, 1992 respectively. Sediment concentrations

were positively correlated with A1 (r = .3221, p = .029), SO4 (r ---.4013, p = .021), and TOC (r =

.4421, p -- .002).

2.3.2.13 Lead (Pb)

Results for the analysis of Pb in lagoon water are presented graphically in Figure 14.

Nineteen of 71 samples produced detectable results. The Florida DEP criterion for Pb is 0.0056

mg/1 in both Class H and Class HI waters. Lead is known to be toxic to fish and shellfish

impacting such traits as survival, growth, reproduction, learning, and metabolic processes. Lead

in estuarine environments may become tightly associated with sediment particulates with the

amount absorbed being dependent on the availability of ligands, pH, redox conditions, Fe

concentrations, salinity and other polar particulates (Manahan 1991). Cycling of Pb in estuaries

involves a complex interaction between dissolved and particulate phases. Lead is known to have

synergistic toxicity when present with Cd, Hg, Cu, and Zn. The average concentration of the

reported Pb values was 0.01 rag/1. The minimum value reported was 0.003 mg/l from Stations 2

and 5. The maximum observed value of 0.044 mg/1 was collected from Station 1 on July 27,

1992. Lead was significantly correlated with K (r = -0.6490, p ---0.003), pH (r = 0.4706, p =

0.042), and TAK (r -- 0.4646, p = 0.045).

Sediment concentrations of Pb ranged from a minimum value of 0.11 mg/kg at Station 5

to a maximum value of 11.24 mg/kg at Station 3. The average reported value was 3.58 mg/kg.

Pb sediment concentrations were significantly correlated with Ag (r -- -.8108, p < .001), AI (r =

.8812, p < .001), Be (r _- .7228, p < .001), Cd (r = .3827, p = .006), Cr (r = .7495, p < .001), Cu (r

= .4383, p = .014), Fe (r = .7837, p < .001), K (r = .6190, p < .001), PO4 (r = .6455, p = .032),

SO4 (r ffi.4653, p = .001), TKN (r = .5515, p < .001), TOC (r = .4380, p < .001), TSS (r =-.3474,

p = .006), and Zn (r = .5956, p < .001). Sources of Pb in the environment include industrial

processes, municipal sewage, and burning of fossil fuels.

35
2.3.2.14 Silicon (Si)

Silicon, like AI, is a primary constituent of the sandy soils along the east Florida coast

and the Florida DEP does not provide a criterion. Silicon is basically an inert compound with

very low toxicity. The presence of Si in the water column is most often associated with

suspended sediments or other particulates such as diatoms. Results of silicon (Si) analyses are

presented in Figure 15. The average concentration across all stations and time periods was 2.57

mg/l. The minimum value was 0.80 mg/1 reported for Station 2 on February 3, 1992 and the

maximum value of 26.6 rag/1 was reported from Station 4 on March 3, 1993. Silicon was

positively correlated with AI (r = 0.5906, p < 0.001), BOD (r = 0.3384, p = 0.017), COL (r =

0.6314, p < 0.001), CPA (r = 0.6703, p < 0.001), TB (r= 0.7080, p < 0.001), and TKN (rffi

0.3656, p = 0.007). Negative bivariate associations were observed with Ni (r = -0.5449,

p--0.029), PHE (r = -0.2817, p = 0050), SO4 (r -- -0.2913, p = 0.031), and TOC (r = -0.3042, p =

0.024). Sediment samples were not analyzed for total Si because of the known high content

associated with local sandy soils.

2.3.2.15 Zinc (Zn)

Zinc is a trace metal that is considered an essential element at desired concentrations. At

high levels it is known to cause growth retardation, histopathological changes, physiological

stress, reduced fecundity, altered behavior and mortality in fishes (Fumess and Rainbow 1990).

Gross (1972) reports average concentrations in seawater of 0.01 mg/1. The Florida DEP has

established a Class H and Class Ill criteria of 0.086 mg/l for marine waters. Results of chemical

analyses are presented in Figure 15. For the 71 possible samples 43 were reported as below

detection and 28 were reported above detection. The minimum value recorded was 0.01 mg/l on

May 5, 1992, July 27, 1992, November 16, 1992, March 31, 1992, and June 16, 1993 at Stations

1,2,3,5,and 6, respectively. One sample was above the DEP criteria and this maximum value

came from Station 4 on March 31, 1993. Zinc displayed significant positive bivariate

correlations with COD (r = 0.4361, p = 0.020), COL (r = 0.5397, p = 0.003), NI-h-N (r = 0.4653,

p = 0.017), Si (r = 0.5122, p = 0.009), and TB (r = 0.4940, p = 0.008). Zinc was negatively

correlated with CON (r = -0.4855, p = 0.009), Mg (r -- -0.3904, p = 0.040), PHE (r = -0.4508, p =

0.021), and SAL (r = -0.3865, p = 0.042). The negative correlations with CON and other

indicators of seawater suggest Zn may be derived from freshwater inputs.

Sediment concentrations of Zn ranged between a minimum value of 2.15 mg/kg at

Station 6 and maximum value of 74.20 mg/kg from Station 4. The average Zn value for

sediments was 14.07 mg/kg. Zinc sediment concentrations were correlated with AI (r = .4729, p

< .001), Be (r = .4898, p < .001), Cd (r = .4830, p = .001), Cr (r = .4629, p < .001), Fe (r = .6023,

p < .001), GO (r= -.3362, p = .028), Mg(r= .4796, p < .001), Mn (r= .5831, p < .001), Pb (r=

.5956, p < .001), SO4 (r = .4573, p = .002), and TKN (r = .5341, p < .001). Possible sources of

Zn in the environment include industrial and municipal discharges, and corrosion control

coatings.

36
30,

10'

0.0

,\\\N

2.0

i w i

4.0 e'.o"d.o" 1_.o 2o.0

6.0 10.0 14.0 18.0 22.0

Silicon (rng/I)

._Std. l::)ev= 3.48

Mean = 2.6

N = 55.00

2,_.o

26.0

0

0

.0i3 .1125 .O38 .O50

State criterion is _<.086 mg/I

.o_ ._

I _ Std. Dev= .02 Mean = .025

. N = 28.00

,o_ .1_ 113

Zinc (rng/I)

Figure 15. Water quality sample fi'equency distributions for silicon and zinc compared to the

Florida Class 11: Shellfish Propagation or Harvesting Criteria for Surface Water Quality (62-

302.530 F.A.C.). Criteria concentrations are depicted by a vertical line'. There is no criterion for

silicon.

37
2.3.3 Inorganic Chemistry

2.3.3.1 Ammonia (NH3), Nitrite (NO2), and Nitrate (NO3)

The importance of nitrogen in Mosquito Lagoon rests upon its role in the synthesis and

maintenance of protein, a major component of all organisms. Derived originally from the

atmosphere, nitrogen is involved in a complex cycle that involves plants, animals and a variety

of chemical forms. Nitrogenous compounds in Mosquito Lagoon may be derived from external

(allochthonous) or internal (autochthonous) sources. External sources include precipitation and

atmospheric deposition, surface water runoff, tidal transport, and groundwater seepage.

Autochthonous sources include nitrogen fixing bacteria and algae. Once in the ecosystem a great

proportion is involved in a cycle of biological assimilation and decomposition along with other

inorganic processes (Reid 1960).

An important feature of shallow estuarine systems is the interaction or coupling between

benthic and pelagic communities. Pelagic primary production and sedimentation of detritus is

often a major source of organic material for benthic community metabolism. The rate of benthic

nutrient regeneration affects the nutrient availability in the overlying water column (Nowicki and

Nixon 1985). In Mosquito Lagoon, light reaches the bottom in sufficient quantity in many areas

to support the growth of seagrasses and benthic algae. In these communities the system supports

both heterotrophic remineralization as well as the production of organic forms of nitrogen.

Eventually, certain quantities are lost from the system through sedimentation and burial,

transport through Ponce de Leon Inlet and Haulover Canal, and biological harvesting and

migrations (Provancha et al. 1992).

The synthesis of inorganic nitrogen into plant and animal tissue produces various organic

nitrogen compounds such as proteins, and metabolic wastes such as urea or uric acid (Reid

1960). Blue-green algae and bacteria may secrete nitrogenous compounds such as polypeptides,

amides, and amino acids. The measure of organic nitrogen is a valuable indication of the

productivity of a body of water because most will ultimately be transformed into material that

can be used in the production of living matter.

In addition to its occurrence in the organic state, nitrogen is also present in inorganic

form such as ammonia (NH3), nitrite (NO3) and nitrate (h/Off In most natural systems

concentrations of these forms are low. These compounds are used by plants in photosynthesis.

Once locked up by the plant in organic compounds, nitrogen is returned to the environment by

decomposition. The first stage of oxidative degradation of animal and plant protein results

primarily in release of free NH3 with lesser amounts of ammonium hydroxide and ammonium

carbonate. Decomposition is the result of microbiologically mediated processes. In an

intermediate phase of the oxidation process, NH3 is attacked by nitrifying bacteria such as

Nitrosomonas that absorb NH3 and release NO2 ions. This process releases energy that is

utilized by the bacteria for growth. Nitrite nitrogen generally occurs in very small quantities, if

at all, in unpolluted waters. In the final phase of the de-nitrification process nitrites are oxidized

by bacteria (Nitrobacter) to (NO3) nitrate nitrogen. Nitrate nitrogen is an extremely important

inorganic nutrient. It is generally found in low concentrations because it is rapidly assimilated

by plants, including algae and submerged aquatic vegetation (SAV).

The average ammonia nitrogen (Nth-N) concentration across all stations and sample

periods was 0.12 mg/1 with a standard deviation of 0.09 mg/1 or about 75% of the mean (Tables

A-1, A-6 and A-7, and Figure 16). The minimum value was 0.02 mg/1, which was at the

detection limit of the analytical method. The maximum values recorded were 0.46 mg/l from

38
Station 4 on September 22, 1992 and 0.45 mg/l from Station 2 on March 2, 1992. A total of 61

samples had values above the detection limit. The Florida DEP does not set specific criteria for

ammonia. Ammonia nitrogen was only weakly correlated with COL (r= .318, p =- .013), K

• (r=.256, p=.046), PO4 (r=.489, p=.010), and TAK (r'=.369, p=.003). Results of analyses for

ammonia in sediments are presented in Tables A-10, A-I 1 and A-12. The minimum value was

0.73 mg/kg N observed on September 22, 1992 at Station 3. The maximum value of 47.79

mg/kg N was also collected at Station 3 on July 27, 1992. The average value for sediments was

11.03 mg/kg. Sediment ammonia concentrations were significantly correlated with NO3 (r =

.7143, p < .001), Pb (r -- .3335, p = .009), pH (r -- .3846, p = .002), PHE (r = .5597, p = .001),

and TSS (r = .2472, p = .047).

Results of NO2 and NO3 analyses are presented in Tables A-l, A-4 and A-5. There are

no Florida DEP criteria for NO2 and NO3. Samples for NO2 in Mosquito Lagoon were

consistently below the detection limit of 0.01 rag/l, consistent with areas having low organic

pollutant loading. Nitrite in natural situations is converted rapidly to nitrate by nitrifying

bacteria (Gross 1972). Nitrate samples for all stations across all sample periods averaged 0.06

mg/1 with a standard deviation of 0.08 mg/l or about 133% of the mean. Of the 71 samples, 45

were below the detection limit of 0.01 mg/1 and the maximum value recorded was 0.31 mgl.

Examination of averages by station indicated higher mean values at the shallow water Stations 1

and 2. Stations 3, 5, and 6, associated with the barge channel on the west side of the lagoon, had

the lowest average values. Spearman Rank Correlation analysis indicated NO3 values were

weakly positively correlated with TOC (r =.185, p -- .008).

In sediments, NO2 levels averaged 0.27 mg/kg and ranged between 0.33 and 9.29 mg/kg.

Nitrite was significantly correlated with NH4 (r = .7143, p < .001), NO3 (r = .6760, p = .016), pH

(r = -.3723, p = .043), PHE (r = .6902, p < .001), and TKN (r = .3935, p = .031). Sediment NO3

values ranged between 0.33 mg/kg and 9.29 mg/kg with an average of 3.78 mg/kg. The lowest

and highest values were collected from Station 2 during September and November of 1992.

2.3.3.2 Total Kjeldahi Nitrogen (TKN)

Measurement of organic and ammonia nitrogen at the six stations as estimated by the

TKN method averaged 0.84 mgq with a standard deviation of 0.49 mg/l (Tables A-I, A-6, and

A-7). The minimum value observed was 0.05 mg/1 and the maximum value was 3.04 mg/l. The

average from each station across all sample periods suggested no large north to south trend.

Stations 4 and 6 had average values of 0.84 mg/l and 0.89 mg/l respectively. The maximum

value was recorded at Station 6 on January 19, 1993. The Florida DEP has no specific criteria

for TKN in coastal water. Results of the Spearman Rank Correlation analysis indicated some

statistically significant but weak correlations between TKN and other parameters. Correlations

were observed with AI (r _- .2764, p = .037), BOD (r = .3747, p = .002), COL (r = .3297, p -_

.006), CPA (r = .5038, p < .001), pH (r = -.2579, p = .032), Si (r = .3656, p = .007), and TB (r =

.3391, p = .005)..

39
40_

0 I

_l-e.e.e.e.eq

20,

LL

10

0 L_._

_x_xx

_xxxx

o.oo .06 .la .1o ._ .51 ._ .44

Ammonia (mg/I as N)

Std. Dev = .09

Mean = .12

N = 61.00

0 I

10

0

[ Std. Dev = .49

0.00 2.50 " 3.00

.25 2.75

xxxxx

XXXX%

.75

o

1.00 1.50 ZOO

1.25 1.75 2.25

Total Kjeldahl Nitrogen (mg/I as N)

Figure 16. Water quality sample fi'equency distributions for ammonia and total Kjeldahl

nitrogen (TKN). There are no Class 11criteria for ammonia and TKN.

4O
a_

Results of sediment analyses for TKN are presented in Tables A-10, A-13, and A-14.

The minimum value was 6.46 mg/kg and the maximum value was 1522.14 mg/kg. TKN

averaged 506.01 mg/kg across all stations and sampling periods. Results of bivariate correlation

analyses for TKN are shown in Table A-15. TKN was weakly but significantly correlated with

A1 (r = .3721, p = .002), Be (r = .4271, p < .001), Cd (r = .3610, p -- .009), Cr (r ffi .2705, p =

.029), Fe (r = .4377, p < .001), K (r -- .3458, p = .006), Mg (r = .4696, p < .001), Mn (r = .4402, p

< .001), NO3 (r = .3935, p = .031), TKN (r = .5515, p < .001), PHE (r = .4393, p = .009), and

SO4 (r = .2839, p = .053).

2.3.3.3 Total Phosphorus (TP) and Orthophosphate (PO4)

From an ecologicalperspectivephosphorus (P)isoftenconsidered themost criticalsingle

factorinthemaintenance ofbiogeochemical cycles(Reid 1961). Phosphorus isnecessaryatthe

celllevelforenergy transfersystems and inthe naturalenvironment itisoftenfound in small

quantitieswhere itisa limitingfactorinsystem primary production. The concentrationof P in

theopen ocean isapproximately 0.7 mg/l (Gross 1972). In shallow estuarinesystems like

Mosquito Lagoon theconcentrationof phosphorus compounds inthe water column may be

directlyrelatedto assimilationby algae and submerged aquaticvegetation,storm-waterrunoff,

tidalmixing, groundwater seepage, and benthicremineralization.In surfacewaters,the

phosphate ion may enterinto combination with a number of otherions depending on pH and

relativeabundance. The two most common phases are calcium phosphate and ferricphosphate.

The interactionwith Fe isespeciallysignificantbecause under anaerobic conditions,as areoften

found inthebefRhicenvironment in summer months in Mosquito Lagoon, theP ion isreleased

from the ferric-phosphoruscomplex allowing ittorecycleintothe overlyingwater column

stimulatingprimary production ifothernutrientsarenot limiting(Reid 196 I).

Resultsof TP analysesare presentedin Tables A-I, A-6, A-7, and Figure 17. Total

phosphorous averaged 0.09 mg/l with a standarddeviationof 0.05 mg/l. The minimum value

reportedwas atthe detectionlimitof 0.02 mg/l. This was recorded on March 2, 1992 atStation

2. Average valuesforeach stationranged between 0.08 and 0.10 mg/l with no obvious spatialor

temporal trends.These data are v/rtuallyidenticaltoprevious samples collectedinMosquito

Lagoon between 1982 and 1991 (Woodward Clyde 1994). The maximum valueof 0.25 mg/l

was recorded atStation4 on 3une 16, 1993. Totalphosphorus was correlatedwith COL (r=

0.3747,p = 0.002),K (r= -0.2354, p = 0.052),Ni (r= -0.5665,p = 0.007),NO2 (r= 0.3800,p =

0.009),pH (r= -0.3749,p = 0.002, SAL (r= 0.4486,p < 0.001),TB (r= 0.3368,p = .005),TOC

(r= -0.5470,p < 0.001),and TSS (r= 0.4701,p < 0.001).

TotalPhosphorus in sediments ranged from a minimum of 0.61 mg/kg to a maximum

value of 1250.00 mg/kg (Table A-10). The overallmean concentrationwas 141.04 mg/kg. Total

phosphorous was significantlynegativelycorrelatedwith AI (r= -.3366,p = .02I),

Be (r= -.3830,p = .008),Cr (r= -.4614,p = .001),Fe (r= -.3681,p = .01l),and Mn (r= -.2842,

p = .053) (Table A-16).

Measurements of dissolved PO4 at all stations in Mosquito Lagoon consistently fell at or

below the detection limit. Data are presented in Figure 17 and Tables A-I, A-4, and A-5). The

minimum recorded value was 0.02 mg/1 and the maximum value was 0.05 mg/l. The average of

reported values was 0.03 mg/l. Orthophosphate was significantly correlated with BOD

(I" =-.4924, p -- .007), GO (r = .5045, p -- .012), NH4-N (r = .4890, p = .010), and NO2

(r = -.4601, p --.036).

41
In sediments, the minimum recorded value was 0.51 mg/kg and the maximum value was

4.57 mg/kg. The average sediment value was 1.99 mg/kg however, only 11 samples had

concentrations reported above the detection limit. For these few samples PO4 was significantly

correlated with A1 (r = .6000, p = .051), Be (r = .6378, p = .035), Cr (r = .7091, p = .015), Fe (r =

.6545, p = .029), K (r = .6818, p = .021), and Pb (r ffi .5455, p = .032). In general, phosphorous

levels in Mosquito Lagoon appear low with potential sources being fertilizer runoff, septic tank

seepage, and possible point source discharges.

2.3.3.4 Potassium OK)

The Florida DEP does not set criteria for K. Potassium is a common element in seawater.

Results of chemical analyses for K in Mosquito Lagoon surface waters are summarized in Figure

18 and Table A-1. Spatial and temporal data for K are presented in Tables A-6 and A-7.

Potassium was found in all 71 samples, ranging between 225 rag/1 and 998 mg/l. The average

value was 402 mg/l.

Results ofsediment analyses for K are presented in Tables A-10, A-12 and A-13. The

minimum value of 0.24 mg/kg was collected on November 16, 1992 from Station 6. The

maximum value of 5902 mg/kg was collected in May 1992 at Station 1. The average K value

was 991 mg/kg. Potassium in sediments was significantly correlated with AI (r = .6767, p <

.001), B (r = .6393, p -- .010), Be (r = .4781, p < .001), Cr (r = .7668, p < .001), Cu (r = .5407, p

= .001), Fe (r = .5205, p < .001), GO ( r= -.4284, p = .003), Mg (r = .3900, p = .002), Mn (r =

.6335, p < .001), NO2(r - .4077, p = .053), Pb ( r= .6190, p < .001), PO4 (r = .6818, p = .021),

and TKN (r = .3458, p = .006).

2.3.3.5 Sulfate (SO0

The Florida DEP does not provide criteria for SO4. The minimum value of 2000.0 mg/1

occurred on January 19, 1993 at Station 1. The maximum value of 7140 mg/l occurred on July

27, 1992 at Station 6. For all stations combined the average value was 2860.18 mg/l (Table A- 1,

Figure 18). Sulfate concentrations were significantly positively correlated with Be (r = .3826, p

= .037), Cd (r -- .3617, p = .016), CON (r = .3803, p = .001), Cr (r = .3992, p = .003), Cu (r =

.5595, p = .037), PHIl (r = .4511, p < .001), TDS (r = .3604, p = .002), and TSS (r = .2841, p =

.016). Sulfates in surface waters displayed a negative correlation with AI (r = -.2745, p = .035),

CPA (r = -.2940, p = .038), and Si (r = -.2913, p = .031).

The minimum sediment value was 96.70 mg/kg that was recorded at Station 5 on

September 18, 1991. The maximum value of 3510.49 mg/kg was recorded at Station 3 in July

1992. The average SO4 value across all sample periods and stations was 1284.55 mg/kg. Sulfate

concentrations were significantly correlated with A1 (r = .5459, p < .001), Be (r = .3808, p =

.008), Cd (r = .3960, p = .008), Cr (r = .3328, p = .022), Fe (r = .5324, p < .001), GO (r = -.2874,

p = .050), Mg (r = .4702, p = .001), Mn (r = .4431, p = .002), Ni (r= .4013, p = .021), Pb (r--

.4653, p = .001), TKN (r -- .2839, p = .053), TOC (r = .5737, p < .001), TSS (r = -.4792, p --

.001), and Zn (r = .4573, p = .002).

42
=- f

121 10

8 I

4_

.015

_xx_, "_-" .._._

,%,\\\-,,\\,q.........

N\\\\\\_\\\\\\-,_

.020 .t_ .030 .035 .0417 .045 ._

Phosphate (mg/I as P)

0 _

%\\\\_,v

20' _\\\\"_

"_ _ Std. Dev = .05

.025 .050 .075 ,100 ,125 .150 ,175 .200 .225 .250

Total Phosphorus (mg/I as P)

Figure l 7. Water quality sample frequency distributions for phosphate and total phosphorus.

Florida DEP criteria state that in no case shallnutrient levels be altered in a way that causes an

imbalance in natural populations of flora or fauna.

43
250.0 350.0 _.0 _.0 _.0 7_.0 _.0 _.0

_.0 _.0 _.0 _.0 _.0 _.0 _.0 1_.0

Std. Dev= 100.28

Mean = 4OZ0

N = 71.00

Potassium (rng/I)

10,

0

%,¢

• )

1

/

!L o IStd. E_ = 750.43

_J Mean = 2860.2

. _1N = 71.00

Sulfate (mg/I)

Figure 18. Water quality sample frequency distributions for potassium and sulfate. There are no

state criteria for potassium or sulfate.

44
2.3.4 Organic Chemistry

2.3.4.1 Grease and Oil (GO)

The Florida DEP criteria for GO is stated as" no undissolved oil, or visible oil as defined

as iridescence, shall be present so as to cause taste or odor or otherwise interfere with beneficial

use of waters". Sources of grease and oil include industrial and municipal discharges, boat

operations, and stormwater runoff. The minimum value reported was 0.52 mg/l from Station 6

on July 27, 1992. The maximum value recorded was 86.0 mg/l for Station 2 on September 18,

1991. Results are summarized in Figure 19. The average for all stations was 3.31 mg/l. Grease

and oil in the water cohmm displayed significant correlations with Be (r = -.5121, p = .015), Cd

(r = -.3525, p = .052), CPA (r -- -.3446, p = .037), PO4 (r = .5045, p = .012), and TSS (r = .3762,

p = .009).

The minimum sediment value of 1.86 mg/kg was observed at Station 2 on November 20,

1991. The maximum value of 1280.00 mg/kg was recorded at Station 4. The average

concentration for sediment GO was 243.92 mg/kg. Grease and oil was significantly correlated

with Cd (r = -.3525, p = .019), Cr (r = -.4100, p = .004), K (r = -.4284, p = .003), NOz (r = -

.5643, p = .005), PHE (r = .3549, p = .039), SO4 (r = -.2874, p = .050), and Zn (r = -.3362, p =

.028).

2.3.4.2 Phenols (PHE)

The Florida DEP provides a complex set of standards for phenolic compounds with

emphasis on man-made derivatives such as chlorophenois and nitrophenols. The Florida DEP

recognizes that naturally occurring PHE resulting from the decay of plant materials may be

present in relatively high quantities. Phenolic compounds are known to taint the flesh of fish and

shellfish and can produce objectionable odor and taste in water. At all stations for all sample

periods, measured values of total PHE in Mosquito Lagoon exceeded the Florida DEP criteria of

1.0 ug/1 (62-302.530, F.A.C). The overall average was 111.35 ug/1 with a standard deviation of

50.05 ug/l. The minimum value was 43.8 ug/1 and the maximum was 399.0 ug/l. There was no

obvious spatial trend in the data. The highest value of 399.0 ug/l was observed at Station 5 on

June 6, 1993. Phenol concentrations were significantly negatively correlated with CPA

(r = -0.3256, p = 0029), NH4-N (r = -0.2643, p = 0.047), NO3 (r = -0.3961, p = 0.050),

Si (r = -0.281, p = 0.050),) and Zn (r = -0.4508, p = 0.021). Phenols were positively correlated

with Cr (r = 0.2172, p = 0.047), and SO4 (r = 0.4511, p < 0.001).

The minimum value of PHE in sediments was 0.07 ug/kg. The maximum value of

4766.08 ug/kg was observed at Station 4. Sediment total PHE averaged 271.37 ug/kg. Total

phenols were significantly correlated with GO (r .3549, p = .039), NH4 (r = .5597, p = .001),

NO3 (r = .6902, p < .001), TKN (r = ,4393, p = .009), and TSS (r = -,3540, p = .041).

45
LI_

---.

10 "'" _"

0.0

_ State criterion is _<5.0 rag/1 [

,\N1

N

_d.o z_.o _.o 4_.o _.o _o _.o _.o 9o.0

Grease and Oil (rng/I)

Std. Dev= 12.34

Mean = 3.3

N = 47.00

LL

2O

10'

_ \\\MN'N

x\\\ xx\\ _ X\\N %

xx\x _ \\\N

_.o 1_.o 1_.o _.o'_.o " _/_.o" _.o

75.0 125.0 175.0 225.0 275.0 325.0

Std. Dev= 56.51

Mean = 111.4

N = 65.00

" 40_).0

375.0

Phenol (ug/i)

Figure 19. Water quality sample frequency distributions for grease and oil and phenol compared

to the Florida Class II: Shellfish Propagation or Harvesting Criteria for Surface Water Quality

(62-302.530 F.A.C.). Criteria concentrations are depicted by a vertical line. The state criteria

for phenolic compounds is < 1.0 ug/1 unless higher values are shown not to be chronically toxic.

m

46
2.3.4.3 Total Organic Carbon (TOC)

Total organic carbon in Mosquito Lagoon is composed of a variety compounds in various

oxidation states. These organic compounds contribute to BOD and COD and, depending on

structure, can serve as electron donors in the complexation process with metals and other cations.

The Florida DEP provides no criteria for TOC. Results of analyses are presented in Table A-1

and Figure 20. The maximum value of 20.80 mg/l as C was collected on January 19, 1993 at

Station 1. The minimum value of 0.24 mg/l as C occurred at Station 6 on July 16, 1993. The

overall average for the study was 2.63 mg/l as C. Total organic carbon was significantly

correlated with Ag (r -- 0.3506, p = 0.010), Cd (r = 0.6473, p < 0.001), COL (r = -0.4091, p <

0.001), Cr (r = 0.3158, p = 0.020), Cu (r = -0.6787, p = 0.008), Ni (r = 0.4826, p -- 0.023), NO2 (r

= -0.3351, p -- 0.023), pH (r = 0.4836, p < 0.001), SAL (r = -0.2585, p -- 0.029), Si (r = -0.3042,

p = 0.024), TB (r = -0.4179, p < 0.001), TKN (r -- -0.2433, p = 0.044), TP (r -- -0.5470, p <

0.001), and TSS (r = -0.2825, p = 0.017).

Results of sediment sampling for TOC are presented in Table A-10. The minimum value

was 189.00 mg/kg recorded from Station 4 and the maximum value of 53031 mg/kg was

collected from Station 5. The average sediment TOC value was 4354.45 mg/kg. Sediment TOC

concentrations were significantly correlated with AI (r = .4626, p < .001), Cu (r = .3743, p =

.027), Fe (r = .2648, p =- .033), Mg (r-- .5773, p < .001), Mn (r = .3106, p = .012), Ni (r = .4421,

p = .002), Pb (r = .4380, p < .001), SO4 (r -- .5737, p < .001), and Zn (r = -.464, p < .001).

3.0 Light Attenuation

3.1 Introduction

Water clarity is an important indicator of water quality (Kirk 1983). Suspended

Sediments and particulates can reduce light penetration through the water column (Duncan

1990). Reduced light availability potentially affects the existence of submerged aquatic

vegetation (SAV) that is considered the ecological foundation of the Indian River Lagoon system

(Kenworthy and Haunert 1991). The decline of SAV in various estuaries has been attributed to

increases in runoff and associated agricultural herbicides, suspended solids, nutrients, and toxic

discharges, many of which alter water clarity, color, and light transmission. Short (1991)

conducted a mesocosm study with the seagrass, Zostera marina, and determined that decreasing

light intensity (analogous to decreasing water clarity) caused a major effect on production,

biomass, and morphology. Effects included reduced growth rates, increased leaf

47
Ii

0

- m w .

0.0 4.0

2.0 6.0

£o " 1 ;.o " mo

10.0 14.0 18.0

Total Organic Carbon (rng/I as C)

Std. Dev= 3.62

Mean = 2.6

N = 71.00

Figure 20. Water quality sample frequency distributions for Total Organic Carbon. There is no

Class 1I criterion for total organic carbon.

size and decreased shoot densities. This project provides data on light attenuation in Mosquito

Lagoon using measures of photosynthetically active radiation (PAR). Attenuation is a measure

of the rate of loss of light energy along a path in the water column due to absorption and

scattering. A review 0f_e irieasurements and mbdelifi_ of light energy in the submarine

environment can be found in Duncan (1990) and Kirk (1983). _

3.2 Methods

Underwater irradiance (light) data were collected from July 1991 through May 1993 at

fifteen stations representing five transects (Figure 21). Three transects were oriented in a west to

east direction (Transects 1, 2 & 3) and two were oriented south to north (Transects 4 & 5). The

positioning ofthese stations is such that for Transects 1 and 2, the stations labeled A and C are

on the west and east edges of the lagoon, respectively, along the outer edge of the SAV in

shallow water (Figure 21). Stations labeled B are in the deeper central basin or trough of the

lagoon where no seagrasses were observed and the water depth often exceeds 2 meters. For

Transect 3, Station 3A is not vegetated with seagrass and is very close to the Intraeoastal

Waterway, while Station 3B is in the vicinity of a large seagrass meadow. Transects 4 and 5 are

shallow (maximum of 1.4 m) with extremely limited vegetative cover. These northern transects

are influenced by tidal fluctuations and associated currents.

Data were collected weekly between the hours of 1000 and 1400 during July through

September 1992, after which a biweekly schedule was implemented. Data were

48
t

Figure 21. Locations of underwater light attenuation sampling transects in Mosquito Lagoon.

Samples were collected on clear days between 10:00 am and 2:00 pm

49
collected only on days when weather met criteria of calm sea states and no excessive rain or

lightning. A Loran-C was used to locate stations. Some of the stations with no obvious

landmarks were additionally marked with buoys to alleviate problems associated with Loran-C

malfunctions.

Two Licor LI-192SA (4pi) underwater quantum radiation sensors were employed to

collect the PAR data. The scalar (spherical) sensors were calibrated on 22 April 1992 and again

on 28 October 1992. A Licor LI-1000 data logger recorded each light measurement sensor,

simultaneously logging time, date, and energy. The overall sampling protocol Was a

modification ofKenworthy et al. (1993). The 400-700 nm response sensors were mounted in

PVC poles (painted flat black to minimize reflection) that held the sensors approximately 50 cm

away from the boat to minimize shadowing effects on the underwater light field. Measurements

were made by two methods. Data collected by a fixed depth (15 em below the surface) sensor

was used to account for cloud cover and light reflection caused by waves on the water surface.

Some researchers use a fixed sensor mounted above the water on the boat and refer to it as the

deck cell. Our modification was assumed to yield a more accurate estimate of the scalar

irradiance intensity at the top of the water column. The second sensor measured light energy at

different depths with sample depth defined by the maximum depth at the site. Tables 3a and 3b

provide details of the depth intervals used. Data were collected at each depth using a three

second averaging time.

Table 3a. Depth profile schedule used at each PAR Station in Mosquito Lagoon prior to January

1993.

Station Depth (cm)

70

80

90

100

110

120

130

140

150

160

170

180

190

200

210

220

230

240

250

260

270

280

iii i i

Profile SchedulesIntervals for Variable Depth Cell

10 20 30 40 N/A

10 30 40 50 N/A

20 30 45 60 N/A

20 40 50 70 N/A

20 30 50 60 80

20 40 50 70 90

20 40 60 80 100

20 40 70 90 110

20 50 70 100 120

30 50 80 100 130

30 60 80 110 140

30 60 90 120 150

31 60 100 130 160

30 70 100 130 170

40 70 110 140 180

40 80 110 150 190

40 80 120 160 200

40 80 130 170 210

40 90 130 180 220

50 90 140 180 230

50 100 140 190 240

50 100 150 200 250

I|

5O
Table 3b.

Janua.n/1993.

Station Depth (cm)

flo

9O

100

110

120

130

140

150

160

170

180

Any depth >180

Depth profile schedule used at each PAR Station in Mosquito Lagoon beginning

Profile Schedules/Intervals for f'ariable Depth Cell

15 20 40 60 N/A N/A N/A N/A N/A

15 20 40 60 N/A N/A N/A N/A N/A

20 40 60 80 N/A N/A NIA N/A N/A

20 40 60 80 N/A NIA N/A N/A N/A

20 40 60 80 100 N/A N/A N/A N/A

20 40 60 80 100 N/A N/A N/A N/A

20 40 60 80 100 120 N/A N/A N/A

20 40 60 80 100 120 N/A N/A N/A

20 40 60 80 100 120 140 N/A N/A

20 40 60 80 100 120 140 N/A N/A

20 40 60 80 100 120 140 160 N/A

20 40 60 80 100 120 140 160 Bottom

On January 13, 1993 the original sampling profile described above was slightly altered

based on agreements with the St. Johns River Water Management District PAR network. These

changes were to make the data more consistent among all participants of the network sampling

throughout the Indian River Lagoon system. Changes included a ten second averaging time,

collecting samples in triplicate, and using a slightly altered depth schedule (Table 3b). The

schedule changed so that the variable depth PAR sensor was positioned at 20 em increments up

to 160 cm. The constant depth cell remained at 15 em below the surface.

Other parameters measured during the light attenuation study were TSS, COL, CPA,

wind speed, and cloud cover. The first three parameters were collected monthly and analyzed in

the laboratory. Cloud cover was determined subjectively by the biologist at each station using

relative percent cloud cover in increments of 10. Other physical water parameters collected at

each station during each sample period included CON, SAL, DO, pH, temperature, and ORP.

Data were downloaded to a spreadsheet for storage and manipulation that included basic

statistics and simple regression analyses. In computing a scalar attenuation coefficient K m "_(Kvalue), the values collected from the variable depths were divided by values from the constant

depth (15 cm) to yield percent light at each depth. The percent light was convened to the natural

log and a regression was performed using these values and their corresponding depths to estimate

K.

Data were analyzed for seasonal variation in K m 1 at each station as well as among

stations. For the periods when triplicate samples were collected, the data were averaged. Annual

mean K-values were calculated along with the 95% confidence intervals for each station. A

graphical comparison was generated for mean K-values and percent scalar irradiance collected at

depths ranging from 1.4-1.9 m (the typical edge zone ofseagrass growth). To assess

relationships between mean K-values and the maximum depth of seag/'ass growth scalar

irradiance was measured for each station located neara seagrass meadow edge using the depths

collected at the deep edge of the bed (Kenworthy 1993), The SAV section of this report

describes the collection ofseagrass positions, density and depth of growth. This calculation of

percent scalar irradianee resulted from the equation: depth = InX/K where depth was the

maximum depth of local seagrass growth (based on 1-3 edge measurements); K was the average

51
w, T

annual K value for the given PAR station and X was percent light. The Spearman Rank

Correlation procedure was used to evaluate relationships between attenuation), TSS, CPA and

COL.

3.3 Results and Discussion

Photosynthetically active radiation (PAR) measures were collected on 68 days of the twoyear period. The number of sample periods for each season is listed in Table 4. The average

attenuation K m "_ for all stations combined was 0.92. Figures B-1 through B-5 display average

values for each transect by season and year. Transects 3, 4 and 5 displayed a general increase in

water clarity in the winter months with means for K m "_ranging from 0.3 to 0.7. The overall

range (all seasons) for these station averages was 0.3 (Station 3A) to 1.69 (Station 4A).

Transects 1 and 2 tended to have a narrower range of values with reduced water clarity in the fall

and spring of each year and the best water clarity in winter and summer. The trend for summer

was somewhat surprising based on general observations of reduced water transparency in

summer. Seasonal mean K m "] along Transect 2 ranged from 0.59 to 1.23. Station IA showed

the least variation with a range of 0.64 to 0.84. Rainfall data show lowest recorded volumes

since 1984 for the October-December 1991 timeframe (Table D- 10). Our seasonal K estimates

for that period show a corresponding increase in water clarity at the majority of stations. A

period of high rain volume occurred in June 1992 but the data for Transects 1 and 2 do not show

a relationship with this potential effect. Annual total rainfall volumes for 1991 and 1992 were

the highest since 1984, except for 1987 (Table D-10). If a relationship between estuarine water

clarity and rainfall inputs exists for Mosquito Lagoon, it is possible that our sample period

occurred during a cycle of higher than usual turbidity due to increased rainfall.

In contrast to Mosquito Lagoon, Kenworthy et al. (199 I) reported a recurring seasonal

cycle at Hobe Sound for the amount of light transmitted to the 2.0 m depth where the minimum

values (5-20% transmittance) occurred between September and April and the maximum values

(40-50% transmittance) occurred in summer between May and August. Their seasonal trends

were attributed primarily to increased boat traffic in the winter months.

Highest wind periods during the Mosquito Lagoon study occurred during October 1991,

and January through March 1992. March 13, 1993 was the day the storm of the century passed

through east central Florida, with many sites around the state recording winds in excess of 70

mph. PAR data were not collected in association with this storm event. The K values increased

(water clarity was reduced) substantially between March 2 and March 29 at all stations on these

transects, with the largest change recorded at Station 2A where attenuation increased from 0.6 to

1.5. The relationship between wind mixing, TB and increased light attenuation deserves

additional investigation.

Percent PAR data at various depths below the surface for each station are plotted in

Figures D-6 to D-10. These data are based on averages calculated for each depth class.

Available PAR near the bottom never dropped below 10% (with the exception of Station IB at

1.5 m) and yet seagrasses did not grow in those 10% zones. Recall that these zones are the

deeper trough stations labeled B for transects 1 and 2 and station 3A. The variability at transects

4 and 5 (indicated in Figures B-9 and B-10, respectively) is probably explained by tidal effects.

Grizzle (1988) documented a decrease in tidal range from north to south for the northern

Mosquito Lagoon portion of CNS. The northern boundary is approximately 15 km south of

52
Poncede Leon Inlet with a tidal range of 50 cm and the southern zone, near PAR station 3A,

contrasts with a tidal range of 2 era. Tidal change at PAR Station 4C was estimated to be about

25 cm (Van Cott, personal communication). Grizzle noted that water currents (both wind and

tide driven) were strongest along the navigable channels (Transect 4) and along the intracoastal

waterway (Transect 5). Currents associated with these sites may reduce the ability of seagrasses

to stabilize and survive.

Table 4. Number of collection periods for PAR measurements at u I null I_ u

Station Summer Fall Winter Spring Summer Fall

Number

1A

1B

1C

2A

2B

2C

3A

3B

3C

4A

4B

4C

5A

5B

5C

each station 1991-1993.

i i i

Winter Spring

1991 1991 1992 1992 1992 1992 I993 1993

6 11 8 11 12 5 3 5

6 11 9 10 11 6 5 6

7 12 10 10 13 5 3 5

6 11 8 10 12 3 2 5

8 11 8 10 12 5 2 5

7 10 9 10 10 5 2 5

7 10 10 12 13 6 3 5

7 11 10 11 13 6 3 5

6 9 10 11 13 6 3 4

7 10 8 12 12 4 4 4

5 10 10 11 13 5 4 4

7 12 9 12 15 4 4 4

7 11 9 10 13 6 4 5

7 10 10 11 13 6 4 5

7 11 10 11 13 5 4 5

Transects 1, 2 and 3 represent the most static environments relative to tidal fluxes and are

in a region of the lagoon where seagrass abundance is high. These stations typically had 30% of

available light measured near the bottom. The trends in percent available light from the six PAR

stations that had seagrass were analyzed in relation to the seagrass ground truth data collected

across many areas of the lagoon (N = >160). (See ground truth discussion within the Seagrass

Section of this report). Frequency of occurrence dropped markedly for Halodule wrightii and

Syringodiumfiliforme for depths greater than 1.4 m. In addition, percent cover of these species

declined at depths greater than 1.0 m (Figures C-7 and C-8). Figures B-6 to B-10 indicate that at

1.4 m depths, the light availability was reduced to a range of 10-38%. Depth ranges of 2.0 to 3.3

m did not support seagrass beds although occasional shoots were observed. At PAR Station 1B,

light availability in the deeper waters ranged between 10-15% of incident light (Figure B-6).

Each station, with its annual mean K value and 95% confidence limit is displayed in

Figure B-11. Figure B-12 indicates the average depth measured at each station plotted with the

annual mean K. Kenworthy (1993) assessed the relationships between mean K, the maximum

depth of seagrass growth, and percent light for Hobe Sound. Similar calculations are reported

here for Mosquito Lagoon and as indicated in Figure B-13 no trends are evident. As described in

the Methods section, the depths used in the percent light calculations came from locations of

deepest seagrass growth relatively near the PAR stations. Figure B-14 is a simple plot of the

actual data for K and percent light measured at stations with maximum depths in the 1.4 m to 1.9

m range typical of the seagrass meadow edge. Onuf (1991) studying seagrass meadows in

Laguna Madre, Texas, found the outer boundary of the meadows to be in the 5-20% light at the

53
bottom zone. Based on long-term mean values of percent surface PAR reaching the bottom, the

level at which light became limiting to meadow development was 12 to 21% with a convergence

at 15%. Onuf(1991) concluded that at least a 15% transmission of PAR is required to sustain

grass bed development. Kenworthy et al. (1991) also suggested that the ecological light

compensation point for Halodule wrightii and Syringodiumfiliforme are in excess of l 0-15% of

incident light and that previously reported values 0-5%) are unsuitable for use as standards by

agencies interested in protecting the seagrass resource.

Kenworthy et al. (1991) found Halodule wrightii and Syringodium filiforme grew to

maximum depths of 1.7 to 2.0 m respectively, in Hobe Sound. Onuf(1991) found only minor

differences in the depth limits ofthe three seagrass species in Texas. Mosquito Lagoon shows

the same general trend relative to Syringodium sp. and Halodule sp. Table 5 indicates values for

COL, TSS, and CPA from samples taken at the various PAR stations. Color shows a relatively

strong relationship with K. Results of Spearman Rank Correlation analyses between K and COL

displayed a positive correlation (r = 0.632, p < .001). TSS and COL also showed a weak

significant positive correlation (r = 0.481, p < 0.001).

4.0 Biota

4.1 Seagrass and Other Submerged Aquatic Vegetation (SAV)

4.1.1 Introduction

Much public and scientific attention has been focused on seagrasses due to the

documentation of man's direct and indirect influence on the decline of these habitats worldwide

and the increased awareness of the importance of such. The seagrass meadows have been

referred to as the ecological foundation of the lagoon system (Kenworthy et al. 1991). Two

approaches were taken for the seagrass database in Mosquito Lagoon. One was to map the

distribution and relative abundance of the SAV through aerial image interpretation and the other

was to establish new fixed and permanent transects that could be sampled each year (minimally).

A review of SAV mapping and distribution methods can be found in Kirkman (1990). In

addition, a historical perspective could be gained from data collected at existing long-term

transects located at the southern end of the lagoon. These sites have been sampled annually

since 1983 as part of the KSC Ecological Program.

4.1.2 Methods

A total of thirteen seagrass transects were monitored during the summer of the two year

project for species composition, percent cover, water depth and basic water quality parameters.

Six transects, all located at the extreme southern end of the lagoon, were sampled on an annual

basis since 1983 as part of the KSC Ecological Program. Nine more transects were added for the

CNS project but two were lost to vandalism prior to the second year. The seven

54
Table 5. Total Suspended Solids (TSS), Chlorophyll-A (CPA), and Color (COL)

results from samples collected monthly, at _r_domly selected PAR stations.

Date Sla_on _S (_) CO_(prcoHit) CPAf_/,,_)

07/24/91

08/08/91

09/05/91

10/03/91

! 1/08/91

12/06/91

01/08/92

02/10/92

03/02/92

O4/O6/92

05105/92

O6/02/92

07/01/92

08/18/92

09/01/92

10/13/92

11/23/92

12/17/92

01/06/93

03/02/93

04/23/93

05/05/93

07/24/91

08/08/91

09/05/91

10/03/9 I

11/07/91

!2/06/91

01/08/92

02/10/92

03/02/92

04/06/92

05/05/92

06/02/92

07/01/92

08118/92

09/01/92

10/13/92

11/23/92

12/17/92

01/06/93

03/02/93

O4/23/93

05/05/93

07/24191

08/08/91

09/05/91

10/03/9!

! 1/07/91

12/06/91

0 i/08/92

02/10/92

03/02/92

04/O6/92

O5/05/92

06/02/92

07/01/92

09/01/92

10/13/92

11/23/92

12/17/92

01/06/93

03/O2/93

04/23/93

1B 24.0

IC 49.0

IC 40.0

IB 50.0

1C 52.0

IC 22.0

IA 36.0

IA 43.0

1C 37.0

IC 57.0

IC 39.0

IC 48.0

1B 20.0

IB 39.0

1B 24.5

IC 26.0

IB 33.0

IC 19.0

1A 38.0

IA 13.0

IB 58.0

IC 28.0

• 2C 33.0

2B 44.0

2A 49.0

2C 42.0

2B 51.0

2C 32.0

2B 1.0

2C 53.0

2C 38,0

2A 129.0

2B 54.0

2C 48.0

2A 28.0

2B 21.5

2B 19.0

2A 29.0

2A 23.0

2B 20.0

2B 27.0

2B 15.0

2C 33.0

2A 24.0

3A 40.0

3A 42.0

3B 43.0

3A 37.0

3A 62.0

3C 14.0

3C 41.0

3C 42.0

3A 32.0

3B 50.0

3C 54.0

3A 47.0

3B 32.0

3A 27.0

3B 36.0

3B 39.0

3A 3! .0

3B 24.0

3A 23.0

3A 39.0

20.0 3.3

10.0 <4.0

15.0 5.3

20.0 ! 1.0

40.0 4.0

20.0 3.7

20.0 <4.0

20.0 4.0

i0.0 2.7

20.0 6.7

5.0 20.0

40.0 5.3

5.0 9.3

20.0 29.4

I0.0 14,7

5.0 .5

15.0 33.4

5.0 6.7

5.0 <4.0

<5.0 9.3

20.0 4.0

<5.0 10.7

40.0 10.0

20.0 6.7

40.0 5.0

20.0 4.0

20.0 10.7

30.0 2.0

15.0 <4.0

15.0 4.0

5.0 <2.0

20.0 <I .5

I0.0 <4.0

20,0 <1.5

5.0 13,3

20.0 <4.0

15.0 5.3

5.0 8.0

20.0 14.7

10.0 4.0

10.0 <4.0

<5.0 9.3

15.0 10.7

<5.0 9.3

20.0 2.0

15.0 8.0

40.0 18.0

20.0 2.7

40.0 6.0

20.0 <2.0

I 0.0 <4.0

5.0 3.3

5.0 <2.0

20.0 <1.5

I0.0 12_0

10.0 17.4

5.0 8.0

15.0 ' 9.3

15.0 20.0

15.0 20.0

5.0 <4.0

I0.0 <4.0

<5.0 10.7

I0.0 6.7

i

55
Table 5 (continued).

Color _COL) results

05/05/93

07/24/91

08/08/91

09105/91

10/03/91

11/07/91

12/06/91

01/08/92

02/10/92

03/02/92

04/06/92

05/05/92

06/02/92

07/01/92

08/I 8/92

10/13/92

11/23192

12/17/92

01/06/93

03/02/93

04/23/93

05/05/93

07/24/91

08/08/91

09/05/91

10/03/91

11/07/91

12/06/91

01/08/92

02/10/92

03/02/92

04/06/92

05/05/92

06/02/92

07/01/92

O8/18/92

09/01/92

10/13/92

11/23/92

12/17/92

01/06/93

03/02/93

04/23/93

05/05/93

Total Suspended Solids (TSS), Chlorophyll-A (CPA), and

from samples collected monthly, at randomly selected PArR stations.

3C 30.0 <5.0 41.4

4A 92.0 40.0 14.0

4C 92.0 20.0 16.0

4C 56.0 40.0 I 1.3

4A 40.0 20.0 5.3

4A 55.0 30.0 8.0

4B 42.0 30.0 2.0

4C 47.0 I0.0 <4.0

4B 20.0 15.0 <2.0

4A 48.0 5.0 4.7

4C 46.0 10.0 <1.5

4B 53.0 5.0 16.0

4C 34.0 20.0 <4.0

4A 32.0 5.0 18.7

4B 64.0 40.0 22.7

4C 34.0 15.0 17.4

4A 39.0 20.0 16.0

4A 19.0 5.0 <4.0

4C 33.0 20.0 <4.0

4C 21.0 <5.0 16.0

4C 34.0 10.0 <4.0

N/A N/A N/A N/A

5(2 II0.0 30.0 7.3

5B 65.0 20.0 8.0

5C 49.0 40.0 14,7

5B 32.0 30.0 6.7

5C 68.0 30,0 <2.0

5B 34.0 30.0 <2.0

5B 46.0 I0.0 <4.0

5C 30.0 5.0 <0.8

5A 49.0 5.0 4.7

5A 51.0 I0.0 <1.5

5C 59.0 i 5.0 6.7

5C 42.0 I0.0 <4.0

5B 27.0 5.0 9.3

5B 37.0 30.0 16.0

5B 29.0 15.0 24.0

5A 30.0 15.0 12.0

513 28.6 15.0 6.7

5B 25.0 <5.0 <4.0

5C 35.0 I0.0 <4.0

5B 23.0 <5.0 8.0

5C 44.0 15.0 <1.5

5B 28.0 <5.0 <4.0

remaining CNS seagrass baseline transects are shown in Figures 22 and 23. The light blue-green

regions in the maps are generally SAV and the darker regions are areas with little or no SAV.

Three transects are in the south and central regions of the lagoon and four new transects were

positioned in the northern reaches of CNS where the lagoon contours become complicated with

islands and oyster beds. The seagrass beds are considerably restricted in size at this northern

end. Signs were placed at each transect in the northern reaches of the park in late 1992 to aid

Park rangers in locating transects and to educate the public. Global Positioning System (GPS)

positions for the remaining un-vandalized transects were collected in 1993 (Table 6). The data

collection methods for this part of the SAV program were designed, as per request, to allow two

rangers or staff members of varying experience to accomplish annual (or seasonal, if desired)

sampling with limited assistance.

56
Table6.

transects

Global Positioning System (GPS) coordinates for submerged aquatic vegetation

sampled in Mosquito _oon. Ends of transects are desi_:nated A and B.

Station X Y

1590442.99145

1590513.58688

1605279.91408

1605562.41921

1605695.63014

1605926.18417

1662198.78600

1662054.20300

1662065.03496

1670220.07962

1668782.93256

1668618.42485

SGSCNS1A

SGSCNS1B

SGSCNS2A

SGSCNS2B

SGSCNS3A

SGSCNS3B

SGSCNS6A

SGSCNS6B

SGSCNS7A

SGSCNS8B

SGSCNS9A

SGSCNS9B

598969.19746

598822.81000

583120.36038

583297.88951

582749.20235

582999.49455

557122.64600

557170.69200

557223.89710

555751.03809

554830.52108

554874.59085

Transect (50 m in length) locations were selected and the origin and terminal poles

determined. A nylon cord was marked off in 5 m increments and was temporarily connected

between the two PVC poles to delineate the line against which all subsequent measures were

made. Transects that followed a general north/south orientation were measured on the east side

of the line, while those running in a east/west fashion were measured on the north side.

Measurements were recorded at each 5 m mark and based on the position from the origin (i.e.,

meter 0 is the origin, meter 5 is 5 m from the origin, etc.). A meter square plot flame with 16

(25x25 cm) sub-quads was laid along the transect cord with the bottom comer touching the line

at each of these loci (i.e., 0, 5, 10). KSC long-term station sampling methods involved collecting

percent cover and species composition at 5 m intervals along transects (similar to those described

above) but using a canopy coverage technique of vegetation analysis originally developed for

terrestrial systems (Daubenmire 1968). This method employs the use of a frame with inside

dimensions of20x50 em marked offso that coverage estimates can be quickly made using a

series of six unequal coverage classes. These classes yield the following density categories

2.5%, 15%, 37.5%, 62.5%, 85% and 97.5%.

57
Figure 22. Locations of submerged aquatic vegetation sampling transects in southern Mosquito

Lagoon.

58
Figure 23. Locations of submerged aquatic vegetation sampling transects in the Canaveral

National Seashore and Mosquito Lagoon.

59
q v

4.1.3 Results and Discussion

Data collected at the new permanent transects are graphically displayed in Figures C-I

and C-2. The only seagrass species observed were shoal grass (Halodule wrightii) and manatee

grass (Syringodiumfiliforme). Seagrass beds are less dense and reduced in distribution at the

northern end of the Park where tidal fluctuations and high turbidity are evident.

Temporal trends (1983-1993) in the percent cover of seagrass species on the six longterm KSC transects are displayed in Figures C-3 to C-5. These graphs depict the average percent

cover along the entire transect for each species. Figure C-6 employs the same data means from

the above figures but indicates the general trends using a linear fit for five of these transects.

Transect 12 was not displayed in this manner due to data gaps (Figure C-3). The data displayed

in Figure C-6 indicates a slight downward trend in percent cover as shown for Transect 22.

Transect 22 is located on the southeast side of Pelican Island, west of Eddy Creek in extreme

shallows (0.5 m) and therefore protected from north and easterly winds. Note that the vegetation

is still quite lush, but the downward trend will be investigated further.

4.2 Submerged Aquatic Vegetation Mapping

4.2.1 Introduction

Various agencies throughout the State of Florida recently began routine mapping of SAV

as part of water quality monitoring protocol. Mapping involves documenting the distribution and

to some extent the density of the submerged aquatic vegetation. These maps provide a

description of large-scale patterns for a big picture approach to looking at trends within a lagoon

system.

4.2.2 Methods

Seagrass beds were mapped using 1:12000 aerial imagery obtained by KSC contract with

Aeromap, Inc. The images were collected on 9 April 1992. Base maps, were supplied by

SJR MD and their contractor Natural Systems Analysts, Inc. (NSAI) in mid August !992.

Most of the interpretation was done directly on the base maps that were printed on translucent

mylar. Interpretations were shipped to NSAI for computer entry and final map production.

Ground truth operations began in late May 1992. The objective was to get a more accurate

assessment of the location of the edge of the beds and obtain ground truth sample data from the

center of the water body where it is often assumed that seagrasses do not occur. These midwater regions are often turbid and no data, based on systematic surveys across these zones, are

available.

GPS and Loran C receivers were calibrated using known locations at the outset of each

trip. Data were collected along eleven east/west transects in Mosquito Lagoon. Each transect

generally began in shallow waters where the bottom visibility became reduced enough to

question its signature on the aerial imagery. A diver/observer was pulled behind the boat, and

60
instructed to dive to the bottom every 0.1 minutes of longitude to determine SAV composition

and coverage. The diver used five coverage categories (0, <10%, 10-40%, 40-70% and 70-

100%). Composition categories totaled seven and included the four local seagrasses, drift algae,

Caulerpa prolifera and Penicillus capitatus. The diver then surfaced and relayed (using hand

signals) the results, which included the position data (GPS/LORAN), SAV data, and water depth,

to a recorder. Depth was collected with a lub line off the bow as soon as the signal was made for

the diver to submerge. This allowed the data derived from the diver's scan to be located within a

few meters of the determined depth. The overall location data associated with the attribute data

are believed to be good within about 10 m (due to boat speed and distance between the diver and

the GPS or LORAN). Add to this the accuracy of the GPS/LORAN (up to 30 m). Data were

entered in a database spreadsheet for management and analyses. Location coordinates were

converted to units used by the Geographical Information System (GIS) for development of an

ARC/INFO coverage.

4.2.3 Results and Discussion

One hundred sixty-one positions were sampled in the turbid zones of Mosquito Lagoon

along the eleven transects (Figure 24). Halophila engelmannii and widgeon grass (Ruppia

maritime) were not observed during any of the surveys. Widgeon grass is generally considered

to be a more flesh water species and so it's absence in this often hypersaline lagoon was not

surprising. Halophila engelmannii, however, is often found in deeper waters where other

seagrasses do not persist. Its absence was a surprise. The marine alga Caulerpa sp. and

Penicillus sp., fairly common in the nearby Banana River and Indian River, were not observed.

Manatee grass was observed in i7 of the 16i samples. Shoal grass was seen in 38 samples and

drift algae species were observed in 61 samples. Seventy-two percent of the samples provided

zero cover or bare bottom.

Data were stratified by depth into four categories to look for patterns in seagrass species

and drift algae zonation (Figures C-7 to C-11). As apparent l_om these figures, manatee grass

generally does not occur at depths greater than 1.5 m. While the occurrence of shoal grass was

low but more persistent than manatee grass in the 1.5 to 1.9 m range, it was rarely found at

greater depths. The average percent cover for both shoal grass and manatee grass was greatest in

the depth range of 0.5 to i.0 m, Figure C-7. Algae tended to be most abundant in two of the four

depth zones, the shallowest zone of study (0.5 to 1.0 m) and the deepest (2.0 to 3.3 m).

4.3 Shellfish

4.3.1 Introduction

A screening for metals in clams inhabiting the seashore was conducted to provide

baseline data on potential food chain contamination. A lagoon wide project conducted in 1992

(Trocine and Trefry 1993) did not include sampling clams in Mosquito Lagoon. Clams are

recognized as good indicator species for potential bioaccumulation of metals in the environment.

61
Figure 24. Locations of transects utilized to ground truth maps of the distribution of submerged

aquatic vegetation. Transects were located in deeper regions to sample areas not readily

observable on aerial photography.

62
4.3.2 Methods

Clams (Mercenaria mercenaria) were collected by hand at five sites in the study area

near existing water quality Stations 1, 2, 4, 5 and 6 (see Figure 3). No clams were found at

Station 3. Samples were collected at the end of the baseline survey period in July 1993. Clams

were gathered randomly at each of the five sites. They were then stored in plastic bags and

placed on ice for transport to the laboratory. A wet weight was determined for each clam and the

shell width was measured. The clams were then freeze dried using liquid nitrogen, placed in a

drying oven for approximately 24 hours, crushed, and microwave digested with nitric acid. They

were then analyzed by heated graphite analysis for the following heavy metals: AI, Cd, Cr, Cu,

Fe, Pb, Mg, Ni, Ag and Zn. All metals data were recorded in ug/g.

4.3.3 Results and Discussion

The shell widths of the clams yielded a range of 2.5-10.1 cm. The results of chemical

analyses are shown in Table 7. Means for the analyses are found in Figures F-1 through F-5.

Trocine and Trefry (1993) collected clams from the Indian River Lagoon System, except

Mosquito Lagoon, and analyzed them for Cd, Cr, Cu, Fe, Pb, Hg and Zn. Differences in

collection and laboratory procedures used by Trocine and Trefry (1993) included: analyses on

clams of uniform size, the use ofperchloric acid (HCIO4) with the graphite furnace analysis, and

a depuration of gut contents. Based on these differences our data are not comparable to theirs.

The clams examined in this study often showed elevated levels for metals tested but those values

may be inflated through the method used. The only other data relative to bioaccumulation of

metals in animal tissues were collected by Morrison (unpublished data) for Hg in muscle tissue

in seatrout. His values are reported for Banana River and Mosquito Lagoon in Table 8.

An overview of information regarding shellfish in Mosquito Lagoon is found in

Provancha et al. 199Z In a 1993 Florida DEP appraisal, 14464 acres of the shellfish area had

been changed from approved for harvest to conditionally approved for harvest due to the

correlation between fecal coliform levels and three day rainfall volumes. Results of sampling are

presented in Table 9. Harvesting was prohibited in the remaining 4910 acres. Between January

1990 and December 1992 the conditionally approved area was closed 33 times for a total of 248

days (Browning and Beadle 1993). The harvesting area has not been closed due to red tide

Gymnodinium breve (concentrations exceeded 5000 cells per liter) since 1980.

The two municipal domestic wastewater treatment plants in the CNS study area

(Edgewater and New Smyrna) have surface water discharge and are predominantly domestic

with a small amount of industrial waste. The Edgewater plant pre-treats waste prior to discharge

and a recent resolution has been passed to require the same from New Smyrna (Browning and

Beadle 1993). The Edgewater plant is undergoing construction to expand the

capacity from 1.0 million gallons per day (mgd) to 2.25 mgd. In addition, eleven marinas are

located in the area. All of these marinas are located in the zone prohibiting shellfishing.

Three canals in the study area act as the primary source of stormwater drainage and

mosquito control. Wildlife is a significant contributor to fecal coliform levels in the area.

Twenty-three bacteriological stations are located throughout this portion of the lagoon,

63
w

Table 7.

quality stations in Mosquito Lagoon in 1993.

Station

CNSI

CNSI

CNS1

Mean

Std. Dcv.

CNS2

CNS2

CNS2

CNS2

CNS2

CNS2

Mean

Std. Dcv.

CNS4

CNS4

CNS4

CNS4

CNS4

CNS4

Mean

Std. Dov.

C'NS5

C'NS5

CNS5

CNS5

CNS5

CNS5

Mean

Std. Dec.

C'NS6

CNS6

Mean

Std. Dev.

Heavy metal concentrations (ug/g dry weight) in clams collected at the six water

AI Cd Cr Cu Fe Pb Mn Ni dg Zn

236.04 2.28 2.28 18.92 290.19 2.04 8.32 1.60 0.92 19.44

323.87 0.72 2.48 12.56 285.29 1.84 18.00 1.44 0.36 22.52

157.61 1.04 1.41 12.65 209.09 1.69 9.78 2.69 0.69 18.85

239.17 1.35 2.06 14.71 261.52 1.86 12.03 1.91 0.66 20.27

67.91 0.67 0.46 2.98 37.13 0.14 4.26 0.56 0.23 1.61

204.8 0.68 4.08 11.32 623.87 8.16 156.96 5.92 0.72 34.92

56.01 1.01 2.32 6.80 245.00 2.24 12.36 3.48 0.56 42.64

222.29 0.40 1.84 9.44 264.82 1.72 8.04 1.64 0.92 32A0

25.98 0.32 1.36 6.68 156.80 1.52 87.36 1.80 0.12 36.96

63.50 0.39 1.83 5.72 142.22 1.18 10.42 1.99 0.70 32.93

60.58 0.40 1.80 11.08 121.21 0.84 3.72 1.92 0.72 32.92

105.53 0.53 2.21 8.51 258.99 2.61 46.48 2.79 0.62 35.46

77.52 0.24 0.88 2.21 171.48 2.52 57.22 1.53 0.25 3.57

271.64 2.g4 7.36 531.24 7.28 35.60 3.48 0.04 54.24

645.85 0.68 2.60 15.16 658.48 3.04 105.88 6.16 0.56 65.04

865.08 0.52 2.96 16.96 755.40 1.52 12.52 3.08 0.64 50.00

460.48 0.15 2.77 13.17 582.22 4.53 34.76 2.89 1.08 32.37

443.20 3.08 16.52 592.13 4.64 38.88 3.36 2.12 43.80

525.70 0.48 2.92 14.72 782.37 11.16 97.64 2.68 1.32 76.88

530.33 0.46 2.86 13.98 650.31 5.36 54.21 3.61 0.96 53.72

187.04 0.19 0.15 3.21 91.97 3.13 34.77 1.17 0.66 14.33

9.04 294.80 4.56 99.12 5.96 77.20

10.48 321.31 3.00 25.04 2.16 2.32 42.64

395.67 13.88 69.64 1.96 2.92 118.12

449.02 6.80 54.76 3.32 2.08 ..... 44._,52

-4_1_. i9 43_,'"" 4,.36 : _0.3i 0.16 _36.33

330.62 4.48 12.36 0.52 41.04

368.77 6.21 44.21 2.37 1.87 59.98

56.41 3.61 33.52 1.90 1.03 29.25

152.19 0.72 4.20

224.86 0.48 3.28

55.77 0.76 2.64 10.16

23_98.--21 0.92 2.40 9.88

• 260.40 .... -0719....1787 " i0._

40.88 0.96 2.96 7.88

232.05 0.67 2.89 9.71

108.93 0.27 0.73 0.99

127.91 1.04 1.60 12.60 168.71 5.84 46.12 0.32 3.40 61.80

45.60 0.96 1.84 10.12 75.03 3.68 20.32 4.88 0.20 70.20

86.76 1.00 1.72 11.36 121.87 4.76 33.22 2.60 1.80 66.00

41.46 0.04 0.12 1.24 46.84 1.08 12.90 2.28 1.60 4.20

64
Table 8.

Refuge.

Sample Id

SBR-1

SBR-2

SBR-3

SBR-4

SBR-5

SBR-6

SBR-7

SBR-8

SBR-9

SBR- 10

Mean

Std. Dev.

ML-1

ML-2

ML-3

ML-4

ML-5

ML-6

ML-7

ML-8

ML-9

ML-IO

Mean

Std. Dev.

Mercury concentrations in seatrout collected in Merritt Island National Wildlife _

Date Collected Fish Length (mm) Fish Wt.(g/wet) Sample Wt.(g/wet)

South Banana River

Mercu,-y (ppm)

08/10/92 405 511 121.8 0.4

08/10/92 460 795 86.4 0.362

08/10/92 370 341 93.5 0.248

08/10/92 370 426 85.3 0.247

08/10/92 380 426 82.5 0.301

08/10/92 350 369 85.8 0.256

08/10/92 375 454 80.2 0.268

08/10/92 330 284 80.6 0.244

08/10/92 350 341 94.1 0.296

08/10/92 345 284 63.3 0.587

373.5 423.2 0.321

37.05 149.95 0.107

Mosquito Lagoon

08/12/92 400 483 98.5 0.66 l

08/12/92 375 426 93 0.597

08/12/92 320 284 46.8 0.371

08/12/92 375 454 82.6 0.429

08/12/92 350 369 62.9 0.376

08/12/92 356 341 88 0.154

08/12/92 305 256 58.6 0.161

08/12/92 310 227 60.1 0.223

08/12/92 318 227 69.8 0.103

08/12/92 310 227 68.7 0.094

341.9 329.4 0.317

33.79 99.51 0.203

eighteen of which are located in the conditionally approved area. Five monitor potential

pollution sources from septic systems, nine monitor wildlife waste and nine look at shoreline

sources (Browning and Beadle 1993). National Shellfish Sanitation Program (NSSP) standards

have been exceeded at two of eighteen stations in the conditionally approved area. Four stations

of the eighteen exceeded the NSSP standards when the harvesting area was open. Oyster tissue

was collected at one station at the north end of Government Cut. Background levels for fecal

coliforms were 75 mpn(100g when the area was open and 78 mpn/100g when it was closed.

These numbers were not significantly different, thereby indicating no aceurnulation of fecal

coliforms by the oysters (Browning and Beadle 1993). It was determined that the current

designation of conditionally approved is not valid and a comprehensive shellfish harvesting area

survey was ordered for April 1993. Since this survey, the new standards have not been

65
Table 9. Results of

1

Star/on

CNSI

CNS2

CNS3

CNS4

CNS5

total and f_al coliform monitorin_ in Mosquito Lagoon.

Date Total coliform(mpn/lOOmO Fecal coliform (cfu/lOOml)

09/18/91 92 <10

11/20/91 <11 <100

02/04192 < 11 < 1O0

03/03/92 < 11 < 10

05/05/92 11 10

07/27/92 11 10

09/22/92 11 <10

11/16/92 N/A N/A

01/19/93 <11 <10

06/16/93 >160 <10

09/18/91 5.1 <10

11/20/91 36 <100

02/04/92 <11 <100

03/03/92 <11 <10

05/05/92 <11 <10

07/27/92 <11 <10

09122/92 51 <10

11/16/92 11 <10

01119/93 11 <10

06/16/93 >160 <10

09/18/91 >16 10

11/20/91 120 <100

02/04/92 11 <1 O0

03/03/92 >230 <10

05/05/92 22 <10

07/27/92 <11 <10

09/22/92 22 < 10

11/16/92 92 10

01/19/93 11 <10

06/16/93 160 <10

09/18/91 2.2 <10

11/20/91 >230 <100

02/04/92 I 1 <100

03/03192 <1 ! <10

05/05/92 >230 <10

07/27/92 51 20

09/22/92 22 <10

11/16/92 92 <I0

01/19/93 36 <10

06/i6/93 -_'1_- <10

09/18/91 5.1 <10

11120191 22 ; <100

02/04/92 <11 <100

03/03/92 <11 40

05105/92 <11 <10

07/27192 <11 <10

09/22/92 <11 <10

11/16/92 22 10

66
Table 9 (continued

CNS6

_. Results of total and fecal coliform monitoring in Mosquito Lagoon.'

01/19/93 <11 10

06/16/93 >160 <I0

09/18/91 16 <10

11/20/91 <11 <100

02/04/92 11 <100

03/03/92 < 11 10

05/05/92 22 <10

07/27/92 11 <10

09/22/92 < 11 < 10

11/16/92 160 70

01/19/93 36 <10

06/16/93 >160 <10

implemented but will be as follows: classification will remain conditionally approved but when

rainfall reaches or exceeds 0.3 inches per 24 hour period, area closure will result (The standard

was previously 1.5 inches per 72 hour period (H. Beadle, personal communication)).

Body A, the Florida DEP designation for Northern Brevard County including Mosquito

Lagoon, has four bacteriological stations in Mosquito Lagoon. The area is classified as approved

for harvest with the exception of all man-made canals and marinas, where the classification

remains prohibited. The area was reevaluated in 1990 (Royal and Pierce 1991) with all point and

non-point pollution sources located and water quality determined. No discharge of industrial

waste into the harvesting area was observed. The approved shellfish harvesting area in Mosquito

Lagoon is approximately 12 miles long. The soil along the west coast of Mosquito Lagoon was

considered to be of the tidal marsh-tidal swamp association and therefore had severe restrictions

for housing, septic systems, and roads due to the continual flooding. Fecal coliforms from

wildlife do not appear to have significant impacts on the water quality in the area. All

bacteriological stations within the lagoon met the Interstate Shellfish Sanitation Program (ISSP)

standards and a shellfish tissue station was established at Station 73 (northeast of Haulover

Canal). This station was chosen due to its proximity to the conditionally approved area and

potential coliform sources and due to the north and south tidal flow transporting pollutants to

shellfish in this area (Royal and Pierce 1991). During the period of April 1982 through May

1990 the approved area of Body A was never closed.

4.4 Demersal Fish Community

A monitoring program to evaluate the demersal fish community was conducted by Dr.

F.F. Snelson, University of Central Florida, during the summers of 1991 and 1992. Details of

the study are reported in Snelson (1993). Five fixed stations were sampled yielding 26,000 fish

of 49 species. The fish fauna consisted of few specimens that numerically dominate and a larger

number of increasingly rare species. The bay anchovy often composed over 90% of the catch.

Although a small species, the bay anchovy often predominates in biomass because of sheer

abundance. Other numerically common species are silver perch, pinfish, pigfish, spot, croaker,

Gulf pipefish, silver jenny, and code goby.

67
Some species that reach a large size are relatively rare in trawl collections. When they

are caught, however, they may dominate in biomass due to their large size. Typical examples are

the butterfly ray, bluntnose stingray, and hardhead catfish. Importance value (IV), an index that

incorporates relative abundance, relative biomass, and frequency of capture, is a measure of

overall importance of a species. The bay anchovy usually had the highest IV ranking. Other

high ranked species were pinfish, spot, silver perch, pigfish, croaker, code goby, silver jenny,

and hardhead catfish. Species diversity, evenness, and richness followed patterns predicted

largely by the number of species, the size of the sample, and the degree to which the samples

were dominated by one species, usually the bay anchovy.

Community composition varied from station to station and between sampling periods.

Although this variation was often of large magnitude, most of it proved to be statistically random

and insignificant. The patterns of variation that appeared to be consistent and statistically

significant over the two year period were: 1) Stations I and 2 were highly correlated and were

very similar in community composition. (2) Station 4 was consistently uncorrelated with any

other station and had a different community composition. (3) The silver jenny was more

abundant in 1991 than in 1992. (4) The spot was more abundant in 1992 than 1991. (5) Rare

species were encountered more often at the northern stations than at the southern stations.

Important environmental considerations that appear to influence community composition are

habitat diversity and proximity to ocean access (Stations 1 and 2) and drift algae density (Station

4).

In comparing the historical data from 1979-80 to the recent data from 1991-92, there

were few indications of major community change over time at either Station 3 or 5. Although

many of the numbers and indices showed differences, most of these were not statistically

significant. The differences that proved to be statistically reliable were as follows: (1) There

were more silver jenny at both Stations 3 and 5 in 1991-92 than in 1979-80. (2) There were

more code goby and Gulfpipefish at Station 3 in 1979-80 than in 1991-1992. There was no

clear environmental explanation for the increased abundance of the silver jenny in 1991. The

explanation for the increased abundance of the code goby and Gulfpipefish in 1979-80 is that

benthic drift algae concentrations were heavier at that time. Both species are known to be

positively associated with drift algae cover.

5.0 Meteorology

5.1 Rain Volume and pH

5.1.1 Introduction

Development of a comprehensive understanding of water resources associated with CNS

and east central Florida requires quantification of atmospheric inputs to the watersheds and

lagoon surfaces of the region. At the southern end of Mosquito Lagoon, in the industrial

operations area of KSC, NASA operates a National Atmospheric DepoSition Program (NADP)

monitoring station. This station was established at KSC in 1982 to expand an acid rain

monitoring program being conducted by Dr. Brooks Madsen (1979) of the University of Central

Florida in the late 1970s (Dreschel 1984). This station is still in operation.

68
5.1.2 Methods

Rainfall amounts for the study period (July 1991-March 1993), were recorded at the

NADP site (Drese 1991a and b, 1992a, b, c, and d 1993). The rain collecting stations consist of a

Belfort Dual Traverse Universal Recording Rain Gage and one or two Aerochem Metrics

Automatic Sensing Wet/Dry Precipitation Collectors. The rain gage records rainfall on a weekly

basis, in inches, on a chart and the collector collects "wet-only" and "dry-only" samples with a

cover which is moved mechanically from the "wet side" collection vessel to the "dry side"

collection vessel when water is present on the sensor (Dreschel 1984). During dry periods, the

cover remains over the "wet side" collection vessel. These instruments are wired together so that

when the collector opens, the event is recorded at the top of the rain gage chart (Dreschel 1984).

The recording charts are changed weekly and the samples are collected in a 13 liter

polyethylene bucket. When a sample is collected, the amount of sample is determined (from the

rain chart and/or by weight) and a suitable aliquot is removed for analysis ofpH and conductivity

(Dreschel 1984). The pH and conductivity values are determined from a cumulative weekly

sample and not for specific rainfall events. The remaining sample is then sent to the NADP

Calibration Laboratory for chemical analysis (Dreschel 1984).

5.1.3 Results and Discussion

Rainfall volumes for the study period July 1991through March 1993 are shown in Figures

D-1 to D-7. Tables D-1 to D-7 display conductivity and pH values of rain during the study

period. The daily rainfall amounts ranged from 0 to 2.95 in. with recorded precipitation

occurring on 207 of the 640 days. The 2.95 inches of rain was recorded on September 29, 1991.

The mean volume from the 207 rain days was 0.44 +__0.55 in. The pH ranged from 3.85 to 7.06

pH units (Figures D-8 to D-14) with a quarterly volume-weighted mean and standard deviation

of 4.67+_1.09 pH units (n = 207). The conductivity values ranged from 0.04 to 72.5 ttmho/cm

(Figures D-8 to D-14) with a quarterly volume-weighted mean and standard deviation of 9.59 +_.

11.43 gmho/cm (n = 207).

Rainfall totals for the quarters (October 1983-March 1993) and annual totals from 1984

through 1992 at the NADP rain site, the 86-yr Titusville record, and the 75-yr Merritt Island

record are presented in Tables D-8 to D-10. The period July-September of 1991 yielded the

highest total rainfall amount of the seven quarters and had the second highest total amount

recorded for the period 1984-1992 (Table D-8). In contrast, the fourth quarter (OctoberDecember) 1991 had the lowest rainfall during our study and was the second lowest over the

period 1984-1992. The 1991 and 1992 total annual rainfall amounts at KSC were higher than all

years except 1987 (Table D-10).

The maximum daily rainfall amount for 1992 was 2.29 in and occurred on March 6,

1992. June of 1992 had the highest total rainfall of the seven quarters (21 months) and had the

second highest total rainfall for the period 1984-1992. However, there were only 1.83 inches of

rain in July that may have contributed to the large number of wildfires that occurred during early

July. The water quality data collected for this time period showed no noticeable increase in

nitrites, nitrates, phosphorous or other parameters that would be expected to increase after such a

heavy rainfall event. The TitusviUe 86-yr record was exceeded during three out of the seven

quarters (Tables D-8 to D-9) and the Merritt Island 75-yr record was exceeded four out of the

69
seven quarters. The 1991 and 1992 annual totals also exceeded the KSC mean and the Merritt

Island 75-yr record (Table D-10).

The maximum daily rainfall amount for the period January-March of 1993 was 2A0 in

and occurred on March 13, 1993. This rainfall event coincided with a storm front that produced

winds ranging from 11-26 miles/hour (mph) and averaged 18 mph over a 24 hour period (Drese

1993). In addition to producing the maximum daily rainfall for this quarter, winds in excess of

67 mph (gusts ofTl mph) were recorded on February i 1, 1993 from the wind tower located at

the Haulover Canal bridge. That period represented the highest first quarter total amount of rain

recorded in the last 10 years. Finally, pH values for the third and fourth quarters of 1991, and the

first quarter of 1992 and 1993 were higher than the ten year mean (4.58 pH units). The second,

third and fourth quarters of 1992 were lower for the period of October 1977 through December

1987 (Tables D-1 to D-7).

5.2 Wind

5.2.1 Introduction

The northern Indian River Lagoon complex, of which Mosquito Lagoon is a part, is

predominantly a wind driven (aeolian) system with regard to circulation processes. Tidal

influences in northern Mosquito Lagoon are evident in response to Ponce de Leon Inlet, but wind

is the primary force in water movement for the remainder of this lagoon.

5.2.2 Methods

Wind rose plots were developed for each month fi'om May 1991 through May 1993 from

data collected at the U.S. Air Force Tower 419 located at the top of the Haulover Canal bridge.

Hourly averages were used to generate monthly wind roses. Wind roses provide information on

the direction and intensity of local low altitude wind fields.

5.2.3 Results and Discussion

Results are summarized in Appendix E, Figures E-1 to E-25. Winds in spring (MarchMay) had an eastern and western component to their direction and were predominantly in the 6-

15 mph range. In fact, all the seasons yielded wind speeds that were predominantly in this range

except summer (June-August) that showed some variability with light winds (mainly westerly) of

2-5 mph in July and August. The fall (September-November) winds were predominantly from

the east. As expected, winter (December-February) winds were from the north. Most winds for

this period were between 0-30 mph, although four strong wind events (31-70 mph) did occur in

the months of October 1992, and January through March of 1993 (Figures E-18 and E-21 to E23). The maximum winds in october were out of the SSW at 60 mph.: January and February

produced 43 mph winds out of the SSW and 67 mph (gusts to 71 mph) out of the NNE,

respectively. The storm of the century took place in March of 1993 but the data from the

Haulover Site indicated WSW winds at only 35 mph, several other stations on KSC recorded

winds in excess of 70 mph.

70
5.3 Solar Insolation

5.3.1 Introduction

Solar radiation is one of the single most important parameters influencing the estuarine

ecosysterns associated with Mosquito Lagoon. Sunlight, in combination with chemical nutrients,

in the presence of plants creates the basis of the food chain through primary production. Daily

cycles in light and heat drive both photosynthesis and respiration rates. In addition, solar

radiation directly influences all photochemical processes and micro-scale mixing rates in the

water column. Heating of the surface layer may induce density stratifications that in turn can

lead to the development of anoxic conditions in bottom waters and sediments. This may alter

oxidation-reduction potentials at the sediment Water interface leading to dramatic changes in

chemical partitioning coefficients and concentrations. In extreme cases these anoxic conditions

may prove lethal to benthic organisms and fishes resulting in fish kills.

5.3.2 Methods

Solar radiation data were collected by the Florida Solar Energy Center at Port Canaveral,

Florida. The collection station is one of twenty located on the Florida Solar Energy Center

property, approximately 29 km south of Mosquito Lagoon. A Licor pyranometer (model

#PYI8239) was used to record the radiation in watts m "2. The data were stored on a Campbell

Scientific digital data logger, which takes an integrated average at 15 minute intervals to produce

mean hourly averages. The solar radiation data were then reduced into monthly averages for the

period January 1990-June 1993.

5.3.3 Results and Discussion

Monthly mean solar insolation data are presented in Figure 25. In general, solar radiation

levels follow the annual seasonal pattern with maximum values during May, June, and July and

minimum values during November, December, and January. Levels increase between the

months of January through May, peaked in late June around the summer solstice and decreased

from July through December and the time of the winter solstice. The year 1990 had highest

average solar radiation levels during the months ofl/anuary through June, and October through

December suggesting somewhat lower cloud cover. September yielded the highest levels in

1991, while the highest levels in 1992 were in May and 3uly. June 1992 displayed low

insolation for a summer time period, most probably as a result of cloud cover.

71
v

SOLAR ENERGY, MONTHLY MEANS, 1990-1992

7O0O.00

6000.00-

5000.00-

4000.00-

3000.00-

1o0o.00-

0.00

JAN FEB MAR APR MAY JUN JUL AUC SEPT OCT NOV DEC

MONTH

Ig9O_ Ig91ES_1992

Figure 25. Monthly mean solar insolation values for the east central Florida coastal region. Data

were collected by the Florida Solar Energy Center at Port Canaveral Florida.

72
V 4r

6.0 Impoundments and Culverts

6.1 Introduction

Mosquito control impoundments were constructed in the late 1950s in Brevard County

and the 1960s in Volusia County (Provancha et al. 1992). Other methods of source reduction

such as hand ditching (1930's) and grid ditching with draglines (1950s and 1960s) were used in

Mosquito Lagoon. These early methods brought environmental changes to the region. Drastic

shifts in plant and animal communities, the changing of the food web dynamics, and the loss of

biological diversity by preventing exchange between the estuary and the impoundment were only

a few of those effects. Impoundment techniques have improved over the years and the negative

impacts have been lessened but management remains cumbersome and costly. Brevard County

Mosquito Control is not actively managing any impoundment in Mosquito Lagoon at this time.

Volusia County and the U.S. Fish and Wildlife Service are actively managing mosquito control

impoundments with renewed emphasis on multi-objective management strategies that include

mosquito reduction, enhancement of waterfowl and wading bird habitats, and enhanced fisheries

productivity.

6.2 Methods

Water quality data were collected monthly by Merritt Island National Wildlife Refuge

staff at each impoundment. Collections were made in close proximity to the water level gauge at

each site. The parameters included SAL, DO, temperature and water level. Data for 18

impoundments were reviewed, three of which were selected for analyses based on their relative

locations within the lagoon. One was located at the northern end of the impoundment system

(V-1), one near the central region of the lagoon (T-O) and one at the southern end of the lagoon

(T-38) (Figure 26). In the vicinity of the T-44 gauge is another station located just outside of the

impoundment referred to as County Line. Data for this site were also plotted.

6.3 Results and Discussion

Figures G- 1 through G-8 display the data collected at the impoundment sites. Salinity

fluxes showed the greatest variability at the northern impoundment (V-l) and the lowest

variability at the southern impoundment (T-38). As expected, SAL was generally inversely

related to water level. Data for V-1 and T-38 show large increases in water levels relative to two

previous years. Open Marsh Water Management (OMWM) is a progressive mosquito source

reduction technique that is currently being used by Volusia County. The main objectives of

OMWM are to control saltmarsh mosquitoes, reduce pesticide use, and enhance the tidal food

chain (Duhring 1989). OMWM is actually thought to stimulate saltmarsh plant productivity and

increase biotic diversity (Duhring 1989). Twelve previously hand-ditched marsh island

73
!

,D

Figure 26. Locations of Mosquito Control Impoundment sampling areas along the

eastern shoreline of Mosquito Lagoon.

74
sites and one impoundment C-8 are slated for OMWM. The impoundment dikes on C-8 and D12 south, both of which had been impounded prior to 1972, were breached in 1986 as part oft.he

OMWM program (East Volusia Mosquito Control District 1993). Impoundment C-8 (90 acres)

had 22 primary areas of mosquito habitat made up of potholes and low vegetated areas

dominated by Salicornia virginica and Distichlis spicata. These potholes and low areas were

interconnected by a ditching network which was then connected to the perimeter ditch which

surrounds the impoundment and finally to the lagoon itself.

Prior to OMWM, mosquito production occurred in 5 acres of potholes and 85 acres of

vegetated land and the area had to be larvicided 8 times a year over a total of 720 acres. Since

OMWM, mosquito production has occurred in 0.2 acres of potholes and 6 acres of vegetated

land and the area has been larvicided 1.5 times a year over a total of 9.3 acres. This represents a

95% reduction in mosquito production and a 99% decrease in larvicid application (Duhring

1989). Salinities and DO fluctuations decreased after OMWM. Prior to OMWM SAL ranged

from 3-55 ppt, after OMWM the range was 27-41 ppt Before OMWM DO ranged from 0.2-12

rag/1 and after OMWM it was between 3-10 mg/l. Overall fish diversity increased but the three

larvivorous species remained dominant Species of shrimp and crab increased. Numerous

wading bird species were observed feeding and Salicornia virginica and Distichlis spicata still

dominated with Borrichiafrutescens and Ivafrutescens expanding their ranges after OMWM.

Two control stations in the marsh, two in the estuary and three stations in impoundment D-12

south (248 acres) were established to collect water depth, surface water chemistry, field SAL and

DO. No significant difference between impoundment sites and controls were found (Gamble et

al. 1990).

7.0 Summary and Recommendations

7.1 Water and Sediment Quality

Water and sediment quality in Mosquito Lagoon is generally good, meeting the Florida

DEP criteria for Class II and Class HI waters in most cases. Exceptions include 1) the frequent

occurrence of low DO conditions in early morning hours during warm summer months resulting

from high system respiration and BOD and 2) the frequent and unexplained elevated levels of

metals and GO in surface waters. Pesticide and herbicide sampling consistently produced results

that were below detection limits indicating no concern exists for these parameters. The

following recommendations are provided for consideration:

.

.

Continue to develop information necessary to quantify the water budget for Mosquito

Lagoon. This should be accomplished at a level of detail that will allow for creation of a

simple mass balance model that can be used to support management decisions. One area

needing immediate attention is the rate and quality of groundwater leakage into and/or

out of Mosquito lagoon.

Develop information on the relationship between sediment chemistry and the chemistry

of the overlying water column with emphasis on the possible exchange rates for metals

and other ions. Define sources of metals in the environment.

75
. Work closely with the St. Johns River Water Management District and Volusia County

staff to develop and participate in a joint interagency monitoring program that includes

Canaveral National Seashore. Participate in the St. Johns River Water Management

District Pollution Load Reduction Program.

4. Develop a working adaptive water resources management strategy that defines the goals

of the CNS with regard to water quality issues. Set specific objectives and priorities.

By addressing the above concerns, efforts can be directed more efficiently and effectively by

eliminating duplicate efforts and standardizing data collection and format. This will also enable

the Park Service to integrate data collected from other areas of the Indian River Lagoon complex

with CNS data to provide an overview of water quality in this Estuary of National Significance.

7.2 Seagrass Transects

Seagrass transects located at the southem end of Mosquito Lagoon that are part of the

KSC long-term system will continue to be monitored annually through the KSC Ecological

Program. There are six stations and these data will be made available upon request to NASA.

The new CNS sites however, should continue to be monitored by park rangers following the

methods described in the seagrass section above. The stations should be sampled annually at a

minimum but could be sampled as often as quarterly. In addition to the basic composition and

cover data it would be recommended that shoot counting be added at specific locations along the

transects for a measure of productivity (density) that can be repeated over time at the same

location. The aerial view of the CNS seagrass resources is also an important one. Therefore,

mapping of SAV on a regular basis (at least every 3 years) is recommended.

7.3 Fisheries

Several important issues were brought forward as recommendations for future monitoring

of the fish community inhabiting Mosquito Lagoon. The key, as with all monitoring programs,

is being realistic about the long-term commitment required to evaluate any ecological system.

The fish data (comparing 1979-80 to 1991-1992) indicate that there has not been any significant

deterioration in this community over the decade. Continuation of periodic fish sampling with a

commitment to the long-term (i.e., 20yrs +) is appropriate. We are unsure at this time if fish data

currently collected by the state (R. Peperno, FMPd, peas comm.) is sufficient for CNS to look to

as a no-cost source of continuation of the fish community monitoring. It is currently unclear as

to the future commitment of the state to Mosquito Lagoon fish community monitoring. There is

a need to better understand their long-term goals of comparability and statistical reliability. The

current recommendation is to consult withthe state, MINWR, and UCF to determine future

direction.

A relatively expensive but probably more sensitive approach would be to look at the

larval fish population dynamics. This would afford an understanding of recruitment and

spawning and how environmental factors influence relative abundance of the larval fish in the

lagoon. Adult populations are often months or years removed from the recruitment event.

Environmental factors have a larger influence on the larval life history stages than the adult

76
i

stage. Again, this method of monitoring requires more extensive sampling periods and longer

identification time and is therefore, considerably more expensive.

Red fish are abundant in Mosquito Lagoon and have become a large draw for recreational

fishermen. Appropriate questions to be answered are:

1. What are fishing pressure effects.'?

2. What effect does an increase in predators have on various prey species?

7.4 Sea Turtles

A cooperative study of the juvenile population of sea turtles that reside in Mosquito

Lagoon is recommended. Both species, Caretta caretta and Chelonia mydas, are federally listed

by the USFWS. These animals have obvious importance to the faunal and floral structure of

Mosquito Lagoon, consuming seagrasses, algae, invertebrates, and fish. A netting and tagging

survey conducted in cooperation with NASA, FMRI, NPS, and MINWR would enable the

following objectives to be met: 1) compare current population structure and distribution to the

baseline data collected between 1976 and 1979. 2) evaluate current seasonal distribution and

occurrence of sea turtles through analysis of catch per unit effort (CPUE). 3) provide updated

statistical summaries of CPUE to determine the regional importance of this lagoon relative to

other studied juvenile habitats on the Florida east coast.

77
8.0Acknowledgments

Many individuals,organizations,and agencies assisted with various phases of this

project. A special thanks is extended to Patrice Hall for her assistance in data analyses and

document preparation. John Stiner, Doug Morrison, Harvey Hill, Opal Tilley, Julio Harvey,

Melissa Durette, Candy McMillan, Desiree Villare.al, Steph_ Gaugerin, Judd Kenworthy, Bob

Virnst¢in, Ross Hinkle, and William Knott, lII provided valuable input and review. Supporting

information was provided by the St. Johns River Water Management District, Volusia County,

Brevard County, U.S. Air Force at Cape Canaveral Air Force Station, the U. S Fish and Wildlife

Service at Merritt Island National Wildlife Refuge, and the National Aeronautics and Space

Administration, Kennedy Space Center Biomedical Operations Office.

78
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Dreschel, T.W. 1984. A preliminary status report, rainfall monitoring at the Kennedy Space

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Drese, J.H• 1991a. Air quality summary and monitoring status at John F• Kennedy Space Center

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• 1992a. Air quality summary and monitoring status at John F• Kennedy Space

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• 1993• Air quality summary and monitoring status at John F. Kennedy Space

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Duncan, M.J. 1990• Measurement of light energy. Pages 147-151. In: R.C. Phillips and C.P.

McRoy. (eds.), Seagrass Research Methods. France, UNESCO 210 pp.

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79
Flint, R.W. 1985. Long-term estuarine variability and associated biological response. Estuaries

8(2A): 138-159.

rFlora, M.D., T.E. Ricketts, J. Wilson, and S. Kunkle. 1984. Water quality criteria: an overview

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Friberg, L. Nordberg, G.F., Kessler, E. and V.B. Vouk, (eds). 1986. Handbook of the

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Gamble, LC., J.P. Stewart, and W.R. Ehrhardt. 1990. Water quality changes associated with

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Grizzle, R.E. 1988. Distribution and abundance of commercially important Molluscan Shellfish

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Kenworthy, W.J., M.S. Fonseca, and S.J. DiPiero. 1991. Defining the ecological light

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_ 8o
Kirk, J.T. 1983. Light and photosynthesis in aquatic ecosystems. Cambridge University Press.,

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programs to protect seagrasses from deteriorating water transparency. Report to NOAA's

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Royal, J., and B. Pierce. 1991. Reevaluation of the Northern Brevard County Body A shellfish

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Short, F.T. 1991. Light limitation on seagrass growth. Pages 37-40. In: W.J. Kenworthy and

D. Haunert (eds.), Results and recommendations of a workshop convened to examine the

capability of water quality criteria, standards and monitoring programs to protect seagrasses from

deteriorating water transparency. Report to NOAA's Coastal Ocean Program, Estuarine Habitat

Studies.

Snelson, F.F. 1993. A trawl monitoring program to evaluate the epibenthic fish community in

Mosquito Lagoon: Summer 1992 results and study summary. Annual Contract Report, No. 837-

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Trocine, R.P. and J.H. Trefry. 1993. Toxic substances survey for the Indian River Lagoon

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92F274C.

81
Appendix A: Water and Sediment Chemistry

82
TableA-1. Summary statistics for water quality samples collected for Mosquito Lagoon: All

samples and stations combined. Samples are included only if values are above the method

detection limits.

Parameter

AG ug/I

_me, n

8mgn

BE ug/l

BOD mg/l

CA men

CD ug/l

COD m_

COL ptco units

CON umhos/cm

CPA mg/m3

CRm_

cumg_

FE mg/l

c-o mgn

Kn_

MG ms/]

NH4N rag/1 as N

NO2 mg/l as N

NO3 mg/l as N

PB men

PH pH units

pI_ ug/l

PO4 mg/lasP

SAL ppt

sI mg/1

so4 men

TAK rag/1 as

CaCo3

TBn_

TDS men

TKN mg/l as N

TOC mg/1 as C

TP mg/las P

TSS mg/l

ZNn_

Statistics for Water

N of cases Minimum Maximum Mean Standard Dev

53 .15 2.20 1.07 .57

59 .11 2.64 .54 .51

71 .24 5.98 2.96 .99

30 .20 2.20 .54 .52

64 1.00 7.00 2.48 1.48

71 80.00 453.00 297.69 77.29

44 .I0 7.10 1.28 1.85

71 355 9300 1142 1404

69 5.00 50.00 21.59 11.26

71 39900 59900 47077 4484

50 2.7 53.4 10.3 7.8

54 .002 .258 .03 .06

14 .02 .15 .05 .04

44 .05 10.40 .53 1.54

47 .52 86.00 3.31 12.34

71 225 998 402 100

71 41.60 1370.00 972.94 214.46

61 .02 .46 .12 .09

22 .004 .580 .I0 .15

46 .01 .02 .01 .00

26 .01 .31 .06 .08

19 .003 .044 .01 .01

71 7.98 9.04 8.41 .28

65 43.80 399.00 111.35 56.51

33 .02 .05 .03 .01

71 4.5 37.2 26.7 6.8

55 .80 26.60 2.57 3.48

71 2000.00 7140.00 2860.18 750.43

71 111.00 622.00 139.38 60.30

71 .93 22.60 6.15 4.34

71 25960 40500 32612 2966

69 .05 3.04 .84 .49

71 .24 20.80 2.63 3.62

69 .02 .25 .09 .05

71 16.00 350.00 61.49 67.02

28 .01 .12 .02 .02

83
Table A-2. Descriptive statistics for physical/chemical parameters measured at all Mosquito

Lagoon water quafit7 stations sorted by s_ple,¢olloction date.

statistic

N of ca._ys

Minimmn

Maximum

Mean

Standard Dev

N of cases

Minimum

Maxiraum

Mean

• Standard Dev

N of cases

Minimum

Maximum

Mean

Standard Dev

N of cues

Min_um

Maximum

Mean

Standard Dev

N of cases

Minimum

Maxinmm

Mean

Standard Dev

N of cases

Min_am

Maximum

Mean

Standard Dev

Date COL CON plt SAL TAK 7B TD5 TS$

910723 6 6 6 6 6 6 6 6

20 41400 8.59 16.00 111.00 2.03 30100 33.00

40 46400 8.82 33.50 131.80 12.22 35100 47.00

30 43350 8.72 28.00 123.47 8.99 31800 38.83

1921 0.08 7.25 8.70 3.72 1809 5.08

910918 6 6 6 6 6 6 6 6

20 45800 8.02 28.00 139.00 4.90 30700 40.00

50 49000 8.31 32.00 146.00 17.80 34300 58.00

35 47967 8.19 30.00 142.57 11.03 33067 51.50

I 1 1211 O.12 1.67 2.67 4.47 1422 7.15

911120 6 6 6 6 6 6 6 6

15 40230 8.14 16.00 126.70 3.11 25960 22.00

40 57770 8.31 19.00 174.20 8.08 32240 58.00

29 47143 8.23 18.33 145.40 5.47 29730 36.33

12 5772 0.07 1.17 18.63 1.69 2307 12.21

920203 6 6 6 6 6 6 6 6

5 45000 8.32 20.00 124.00 1.87 29700 28.00

20 47800 8.42 29.00 158.00 6.54 34700 53.00

12 46567 8.39 26.42 134.67 3.26 32950 42.33

5 948 0.04 3.23 13.38 1.78 1776 8.91

920302 6 6 6 6 6 6 6 6

5 42300 8.78 16.00 141.40 1.33 31900 30.00

15 45600 9.00 18.00 165.20 8.28 33300 51.00

10 43717 8.86 16.83 147.23 3.70 32783 39.83

3 1094 0.08 0.75 9.05 2.56 500 7.78

920505 6 6 6 6 6 6 6 6

10 47800 8.78 31.00 120.00 1.79 33700 35.00

30 52900 9.04 33.00 166.00 3.18 37100 114.00

15 51483 8.87 32.50 132.83 2.35 35733 68.67

8 1871 0.11 0.84 17.57 0.51 1232 26.91

84
Table A-2 (continued).

at all Mosqu to Lagoon water qualiv stations sorted by sample

Sm_c

N of cases

Mininmm

Maxinalm

Mean

Standard Dev

N of cases

Mininmm

Maximum

Mean

Standard Dev

N of cases

Mininmm

Maximum

Mean

StandardDev

N of cases

Minimum

Maximum

Mean

Standard Dev

N of cases

Minilratm

Maximum

Mean

Standard Dev

N of cases

Minimum

Maximum

Mean

Standard Dev

Descriptive statistics for physical/chemical parameters measured

collection date.

I

Date COL CON pH SAL 7AK TB TDS TSS

920727 6 6 6 6 6 6 6 6

20 41000 8.34 4.5 120.00 4.59 31400 34.00

40 49600 8.83 25.0 622.00 14.20 34500 52.00

27 46917 8.51 15.7 222.67 8.86 33000 43.75

8 3131 0.18 6.6 198.28 3.34 986 7.37

920922 5 5 6 6 6 6 6 6

20 45300 8.04 29.0 119.00 2.89 27000 24.00

40 47800 8.34 31.0 129.00 22.60 36400 98.00

28 46640 8.20 30.0 123.50 11.28 31067 58.17

8 913 0.11 0.6 3.83 7.01 3227 26.28

921116 5 5 5 5 5 5 5 5

20 45300 8.03 30.5 121.00 4.72 30600 210.00

30 47800 8.16 32.2 124.00 10.90 32000 350.00

26 46640 8.08 31.6 121.80 7.88 31140 290.00

6 913 0.05 0.7 1.30 2.70 573 62.05

930119 6 6 6 6 6 6 6 6

5 43700 7.98 27.5 II1.00 0.93 30700 22.00

20 46700 8.32 29.4 143.00 5.69 32400 42.00

9 45733 8.13 28.7 117.33 2.31 31417 30.00

6 1093 0.12 0.6 12.60 1.90 682 7.12

930331 5 6 6 6 6 6 6 6

5 42100 8.27 26.1 116.00 1.64 27700 16.00

20 46000 8.49 29.4 143.00 5.68 31200 42.00

! 2 44350 8.35 28.1 127.17 4.31 29483 31.67

6 1401 0.08 1.1 9.50 1.51 1251 9.14

930616 6 6 6 6 6 6 6 6

20 52400 8.18 31.6 127.00 2.07 34800 33.00

30 59900 8.55 37.2 142.00 8.14 40500 53.00

27 57483 8.29 35.4 131.00 4.71 38933 44.83

5 2822 0.13 2.1 5.51 2.20 2108 8.59

85
Table A-3. Descriptive statistics for physical/chemical parameters measured at each

Mosquito Lal oon water _Lualit _ station for all sample collection dates.

Statistic Station COL CON pH SAL TAK TB TDS TSS

N ofcases

Minimum

Maximum

Mean

Standard Dev.

N of cases

Minimum

Maximum

Mean

Standard Dev.

N of cases

Minimum

Maxinnun

Mean

Standard Dev.

N of cases

Min_aum

Maximum

Mean

Standard Dev.

N of cases

Minimum

Maximum

Mean

Standard Dev.

N of cases

Mininmm

Max/lralm

Mean

Standard Dev.

CNSI 9 II II II II II II II

5 40230 8.22 16.0 I!I I.14 25960 16.00

20 52400 9.04 31.6 165 6.54 35 I00 53.00

16 45439 8,55 25.1 141 3.15 31087 32.86

5 3497 0.27 5.9 16 1.84 3250 9.17

CNS2 12 12 12 12 12 12 12 12

5 44400 8.03 4.5 111 1.87 29500 22.00

40 59900 9.00 37.2 207 14.20 39300 310.00

22 48137 8.40 25.3 138 6.72 33115 63.50

12 4341 0.31 9.2 25 3.80 2665 78.32

CNS3 12 12 12 12 12 12 12 12

5 41400 8.10 16.0 113 1.32 29300 28.00

30 57100 8.88 34.9 166 12.10 39900 350.00

20 46788 8.41 26.9 131 6.91 32398 70.42

11 4178 0.27 6.3 15 3.94 2956 89.13

CNS4 12 12 12 12 12 12 12 12

10 42300 7.98 17.0 113 3.02 31200 22.00

50 59300 8.78 37.2 174 22.60 40500 240.00

29 47688 8.29 27.7 132 8.79 33660 71.58

13 4364 0.29 6.6 17 5.63 2920 58.81

CNS5 12 12 12 12 12 12 12 12

5 39900 8.16 14.5 112 0.93 28100 31.00

40 56700 8.97 35.6 622 8.65 40200 210.00

19 45993 8.46 27.4 168 4.30 32417 53.83

I0 4661 0.28 7.0 143 2.72 3223 49.962

CNS6 12 12 12 12 12 12 12 12

5 41800 8.06 17.0 112 1.29 28900 28.00

40 59500 8.81 35.9 147 17.80 38900 340.00

22 48280 8.35 27.8 128 6.81 32870 74.33

12 5702 0.28 6.6 II 5.I1 2768 84.89

86
o

C_00

0

i "d_ "_o " " "_ o .... _o ._ " "

000_ _

[ "°

. _ ...........

i

87
88
•

__ .....

89
Table A-6. Descriptive statistics for inorganics measured at all water quality stations

sorted b_ sar_

Sta_ac

N of cases

Mininenn

Maxinmm

Mean

StandardDev.

N of cases

Mininmm

Maximmn

Mean

Slandard Dev.

N of cases

Mininmm

Maximum

Mean

Standard Dev.

N of cases

Mininmm

Maxilmnn

Mean

StandardDev.

N of cases

Mininmm

Maxhnmn

Mean

StandardDev.

N of cases

Mininmm

Maxinmm

Mean

Standard Dev.

ale collection date:

Date Ntt4.N NO2 NO3 P04 K S04 TKN 17"

910723 6 6 3 2 6 6 6 6

0.06 0.010 0.01 0.026 370 2110.00 0.54 0.05

0.27 0.020 0.05 0.038 416 2620.00 0.97 0.08

0.12 0.012 0.03 0.032 386 2418.33 0.70 0.06

0.08 0.004 0.02 0.008 16.6 189.89 0.15 0.01

910918 6 6 1 3 6 6 6 6

0.12 0.010 0.03 0.026 462 2093.00 0.85 0.04

0.20 0.010 0.03 0.034 515 2780.00 1.29 0.09

0.16 0.010 0.03 0.031 497 2532.17 0.94 0.07

0.03 0.0 0.004 18.8 252.44 0.17 0.02

911120 6 6 6 3 6 6 6 6

0.13 0.010 0.03 0.026 346 2595.00 0.57 0.04

0.23 0.010 0.20 0.036 429 3415.00 1.27 0.08

0.17 0.010 0.07 0.031 398 3030.00 0.75 0.06

0.03 0.0 0.07 0.005 32.6 322.08 0.27 0.02

920203 6 1 0 2 6 6 6 6

0.06 0.020 0.027 357 2640.00 0.55 0.03

0.26 0.020 0.040 413 3160.00 1.03 0.21

0.11 0.020 0.034 393 2920.00 0.74 0.10

0.07 0.009 21.4 187.51 O.18 0.06

920302 6 0 2 6 6 6 6 4

0.05 0.02 0.016 371 2430.00 0.31 0.02

0.45 0.03 0.041 400 5640.00 0.72 0.07

0. i9 0.03 0.027 389 3703.33 0.47 0.04

0.15 0.01 0.009 12.8 1058.52 0.17 0.02

920505 6 4 1 0 6 6 6 6

0.04 0.010 0.02 . 394 2690.00 0.37 0.04

0.09 0,0i0 0.02 700 3100.00 1.20 0.08

0.08 0.010 0.02 461 2911.67 0.65 0.06

0.02 0.0 118 132.88 0.32 0.02

||m r i i

9O
TableA-6 (continued).Descriptivestatisticsfor inorganicsmeasured at all

stations sorted b_, sample collection date.

Statistic

N of cases

Mh_m

Maximum

Mean

Standard Dev.

N of cases

Mininmm

Maximum

Mean

Standard Dev.

N of cases

Minimum

Maximum

Mean

Standard Dev.

N of cases

Minimum

Maxinmm

Mean

Standard Dev.

N of cases

Mininalm

Maximum

Mean

Standard Dev.

N of cases

Mininmm

Maxina.n

Mean

Standard Dev.

Date NH4-N NO2 NO3 P04 .K S04

water quality

7KN 7/'

920727 6 0 6 2 6 6 6 6

0.03 0.02 0.020 225 2120.00 0.87 0.03

0.13 0.31 0.020 998 7140.00 1.93 0.07

0.08 0.12 0.020 426 3233.33 1.33 0.06

0.04 0.15 0.0 285 1934.79 0.37 0.02

920922 2 6 1 6 6 6 6 6

0.26 0.010 0.17 0.030 330 2230.00 1.12 0.08

0.46 0.020 0.17 0.040 442 2490.00 1.61 0.21

0.36 0.012 0.17 0.032 367 2355.00 1.36 0.16

0.14 0.004 0.004 42.5 103.68 0.21 0.05

921116 2 5 5 4 5 5 5 5

0.03 0.010 0.03 0.020 361 3060.00 0.88 0.11

0.06 0.020 0.05 0.020 369 3282.00 1.60 0.18

0.05 0.018 0.04 0.020 365 3193.40 1.22 0.14

0.02 0.004 0.01 0.0 3.21 82.50 0.26 0.03

930119 4 6 1 0 6 6 6 6

0.02 0.010 0.02 . 348 2000.00 0.18 0.03

0.07 0.010 0.02 414 2970.00 3.04 0.I0

0.05 0.010 0.02 369 2651.67 0.73 0.05

0.02 0.0 22.91 360.97 1.14 0.03

930331 6 0 0 3 6 6 4 6

0.03 0.020 354 2222.00 0.05 0.06

0.14 0.030 680 2426.00 0.64 0.10

0.06 0.023 422 2298.83 0.24 0.08

0.04 0.006 128 75.90 0_27 0.02

930616 5 6 0 2 6 6 6 6

0.06 0.010 0.030 334 2570.00 0.60 0.11

0.15 0.010 0.050 358 4070.00 1.12 0.25

0.11 0.010 0.040 346 3130.00 0.86 0.18

0.04 0.0 0.014 10.9 501.00 0.18 0.05

91
Table A-7. Descriptive statistics for inorganics

stationforall s ,pl¢ collectiondates,,

Statistic Station NHd-N NO2 NO3

N ofcases

Mininmm

Max/mum

Mean

Standard Dev

N ofcases

Minimum

Maxinaun

Mean

Standard Dev

N of cases

Minimum

Maximum

Mean

Standard Dev

N of cases

Minimum

Maxilmm

Mean

Standard Dev

N of cases

Mininmm

Maximum

Mean

Standard Dev

N of cases

Mini.nmm

Maxinaun

Mean

Standard Dev

iiiii "r

measured at each Mosquito Lagoon water quality

CNS1 10 8 4

0.05 0.010 0.03

0.27 0.020 0.31

0.16 0.011 0.14

0.O9 0.0O4 0.14

CNS2 11 8 4

0.04 0.010 0.03

0.45 0.020 0.31

0.13 0.011 0.11

0.12 0.004 0.13

CNS3 9 7 3

0.03 0.010 0.03

0.15 0.020 0.04

0.09 0.011 0.03

0.05 0.004 0.01

CNS4 12 8 7

0.03 0.010 0.01

0.46 0.020 0.17

0.14 0.014 0.05

0.11 0.005 0.06

CNS5 9 8 3

0.04 0.010 0.02

0.16 0.010 0.04

0.08 0.010 0.03

0.04 0.0 0.01

CNS6 10 7 5

0.02 0.010 0.02

0.26 0.020 0.04

0.11 0.011 0.03

0.08 0.004 0.01

all i if

P04 K S04 TKN TP

4 11 11 11 11

0.03,0 225 2000.00 0.05 0.03

0.041 462 2940.00 1.40 0.21

0.037 361 2443.27 0.89 0.08

0.005 58.5 277.24 0.44 0.06

8 12 12 12 12

0.020 355 2420.00 0.20 0.02

0.040 700 4070.00 1.19 0.20

0.028 418 2892.25 0.77 0.09

0.006 97.0 507.65 0.29 0.05

5 12 12 12 11

0.019 287 2210.00 0.13 0.03

0.030 505 3300.00 1.28 0.20

0.023 395 2741.75 0.67 0.09

0.005 54.3 379.04 0.37 0.06

8 12 12 11 12

0.020 326 2120.00 0.19 0.04

0.050 680 3610.00 1.60 0.25

0.030 412 2776.58 0.84 0.10

0.010 98.3 441.12 0.45 0.06

2 12 12 12 II

0.016 336 2260.00 0.12 0.04

0.030 998 3770.00 1.93 O. 18

0.023 435 2872.67 0.89 0.09

0.010 182 450.63 0.57 0.05

6 12 12 11 12

0.020 334 2110.00 0.48 0.03

0.033 507 7140.00 3.04 O. 17

0.027 388 3399.83 1.04 0.08

0.006 46.0 1482.92 0.72 0.04

92
Table A-8. Descriptive statistics for organics measured at all Mosquito

Lagoon water quality stations sorted by ,s_ple collection date.

Stat/st/c

N ofcases

Minimum

M_

Mean

StandardDev

N ofcases

Minimum

Maximum

Mean

StandardDev

N ofcases

Minimum

Maxinmm

Mean

StandardDev

N of cases

Minimum

Maximum

Mean

StandardDcv

N ofcases

Minimum

Maximum

Mean

StandardDev

N ofcases

Minimum

Maxinmm

Mean

StandardDev

N ofcases

Minimum

Maximum

Mean

StandardDev

N ofcases

Minimum

Maximmn

Mean

Standard Dcv

Date BOD COD CPd G&O PHE TOC

910723 6 6 6 4 6 6

1 493 4.7 0.86 59.80 1.87

2 1330 16.0 2.71 114.00 2.54

1.8 671 10.5 2.07 87.95 2.09

0.4 326 4.0 0.87 20.03 0.24

910918 6 6 4 6 6 6

2 355 10.7 0.71 66.00 0.93

3 740 13.4 86.00 92.50 2.47

2.5 617 12.4 15.22 75.75 1.28

0.6 137 1.3 34.68 9.23 0.60

911120 6 6 4 5 6 6

1 441 4.0 0.71 62.00 0.71

2 834 8.0 1.71 104.00 2.22

1.5 620 6.4 1.43 89.98 0.98

0.6 142 1.7 0.44 14.67 0.61

920203 6 6 3 3 6 6

1 510 3.3 0.71 98.70 1.24

3 870 6.7 1.86 138.00 2.16

2 690 4.4 1.19 117.95 1.45

0.6 127 2.0 0.60 13.17 0.36

920302 6 6 5 5 6 6

1 541 2.7 1.14 91.40 2.57

2 823 4.7 1.57 166.00 3.26

1.5 639 3.7 1.34 125.90 2.82

0.6 109 0.8 0.19 25.44 0.29

920505 6 6 1 0 6 6

1 1350 12.0 46.70 2.40

2 3510 12.0 158.00 4.98

1.3 2340 12.0 102.23 3.66

0.5 795 45.39 1.03

920727 6 6 6 2 6 6

4 860 9.3 0.52 74.30 2.29

5 9300 53.4 0.71 399.00 2.95

4.8 2647 21.1 0.62 137.37 2.58

0.4 3273 16.3 0.13 128.37 0.29

920922 5 6 4 6 6 6

2 400 10.7 0.83 58.90 0.63

2 1540 22.7 2.93 113.00 1.53

2.0 837 14.7 1.92 76.82 0.90

0.0 478 5.7 0.92 19.36 0.33

93
Table A-8 (continued.).

water qualit_ stations sorted bY sample collection date.

Star, tic

N of cues

Mininmm

Maximum

Mean

Standard Dev

N of cases

Minimum

Maxinalm

Mean

Standard Dev

N of cames

Minimum

Maxinaun

Mean

Standard Dev

N of cases

Min_num

Mean

Standard Dev

Descriptive statistics for organics measured at all Mosquito Lagoon

Date BOD COD CPA G&O PIIE TOC

921116 5 5 5 2 5 5

5 690 8.0 0.74 143.00 0.40

7 830 18.7 1.03 160.00 0.58

5.8 764 I 1.7 0.89 156.60 0.47

1.1 56 4.4 0.21 7.60 0.07

930119 6 6 5 6 0 6

I 660 5.3 0.81 11.10

4 830 10.7 3.00 20.80

2.3 747 7.5 1.97 13.48

1.0 58 2.4 0.77 . 3.63

930331 0 6 4 3 6 6

550 6.7 0.75 43.80 0.33

7700 10.7 1.21 160.00 1.50

2253 9.0 0.96 89.90 0.62

2803 2.0 0.23 42.36 0.44

93O616 6 6 3 5 6 6

1 540 5.3 1.26 65.80 0.24

4 950 6.7 2.30 250.00 1.70

2.2 817 5.8 1.89 171.98 0.83

1.0 145 0.8 0.38 78.82 0.54

_ 94
Table A-9. Descriptive statistics for organics mcasm'ed at each Mosquito

Lagoon water qualit_stationforallsample collectiondates.

Statistic Station BOD COD CPA G&O PHE TOC

N of cases

Minimum

Maximum

Mean

StandardDev

N of cases

Mininmm

Maximum

Mean

StandardDev

N ofcases

Mininmm

Maximlun

Mean

StandardDev

N of cases

Mininmm

Maxinmm

Mean

StandardDcv

N of cases

Minimum

Maximum

Mean

StandardDev

N ofcases

Minimum

Maximum

Mean

StandardDev

CNS1 10 1! 7 6 10 1 !

1 355 3.3 1.29 46.70 1.50

5 9300 9.3 2.73 127.00 20.80

2.2 1697 6.1 1.97 79.61 4.19

1.5 2620 2.2 0.56 21.99 5.60

CNS2 10 12 7 7 11 12

1 493 4.7 0.75 54.10 0.58

5 7700 22.7 86.00 224.00 12.80

2.6 1483 12.8 13.62 110.76 2.62

1.4 2000 6.1 31.93 51.51 3.40

CNS3 11 12 11 10 11 12

1 493 3.3 0.71 72.00 0.41

5 1560 18.7 2.20 161.00 11.90

2.6 829 10.0 1.21 114.22 2.40

1.4 338 6.1 0.49 31.65 3.22

CNS4 11 12 7 8 11 12

1 400 2.7 0.93 58.80 0.33

7 3510 12.4 3.00 160.00 12.30

2.6 1054 10.2 1.78 98.28 2.32

1.6 840 3.4 0.78 30.82 3.28

CNS5 11 12 8 8 11 12

I 480 5.3 0.71 58.90 0.41

7 2850 53.4 2.71 399.00 12.00

2.5 1038 13.2 1.72 152.72 2.23

1.9 770 16.4 0.69 98.25 3.19

CNS6 11 12 I0 8 II 12

I 400 4.0 0.52 43.80 0.24

5 1890 16.0 2.00 239.00 II.I0

2.5 796 9.9 1.05 109.65 2.15

1.3 444 3.9 0.49 51.53 2.97

ill

95
Table A-10. Summary statistics for sediment quality samples collected for Mosquito

Lagoon. All samples and stations combined. Samples are included only if values are

above the method detection IL,nits__ ,........

Parameter N of cases Minimum Maximum Mean Standard Dev

AGmg_

AL m_g

amg_

BE mg/kg

CA mg/kg

CDmg/kg

CRmg_

CUn_/_

FEmg/kg

C-OmgAg

gmg_

MG mg/kg

MN m_g

NH4N mg/kg N

_mg_

_o2 m_g

NO3 mg/kg

PBm_g

PH pH um_

PHE u_/i_

Po4 _,_g

so4 _/kg

TI_ m_g

TOC

ZNm_g

10 .05 10. I3 1.78 2.99

65 325 21166 4258 4267

16 6.15 66.18 27.04 15.52

64 .03 2.04 .32 .36

65 1460 134000 24732 27619

51 .01 .80 .10 .12

65 .17 251.00 18.53 39.59

35 .26 59.00 5.95 10.98

65 349 253401 9039 31919

47 1.86 1280 243.9 312.1

63 .24 5901.84 857.13 990.70

65 245 5828 1976 1240

65 4.17 97.90 21.78 15.31

65 .73 47.79 11.03 11.92

46 .16 12.26 3.02 2.84

23 .01 1.76 .27 .38

30 .33 9.29 3.78 2.71

61 .11 11.24 3.58 2.66

65 6.82 8.58 7.75 .38

34 .07 4766 271.4 819.7

11 .51 4.57 1.99 1.25

47 97 3511 1285 711

65 6.46 1522.14 506.01 369.36

65 189 53031 4355 8324

47 .61 1250 141 204

61 2.15 74.20 14.07 12.66

96
__ __ __ o _

_0

O0

• °o °_ •

97
_ __

__- -_

98
v

99
v

i

L_.

C_ W

_c_

loo
.i!

"i

101
j_

i

i

ii

•-q ,_ll"0

0 .... _ .... 0

0 .... 0 ....

I

102
Table A-14. Descriptive statistics for inorganic and organic parameters

each sam plin

Statistic

N of cases

Minimum

Maxinmm

Mean

StandardDev

N ofcases

Mininann

Maxinalm

Mean

StandardDev

N ofcases

Minimmn

Maxinmm

Mean

StandardDcv

N of cases

Miniraum

Maxina_

Mean

StandardDev

N of cases

Mininmm

Maxinatm

Mean

Standard Dev

N of cases

Minimum

Maxinaim

Mean

Standard Dev

Station G&O NH4-N

stationfor allsample collection dates.

NO2 NO3

CNSI 7 10

7.94 2.24

779.2 39.60

223.6 14.78

319.0 14.32

CNS2 8 11

1.86 1.06

875.0 35.50

289A 8.94

347.1 10.25

C'NS3 8 I I

13.61 0.73

801.0 47.79

253.4 12.28

306.6 13.41

CNS4 8 II

11.41 1.17

1280 47.10

308.6 16.03

451.8 14.47

CNS5 8 I1

5.41 1.19

798.7 32.20

225.9 6.90

286.1 9.01

CNS6 8 11

21.60 1.67

59O.O 23.90

160.1 7.60

190.3 8.38

measured in sediment at

r/ 1,1-ierie eo# so4 . roc rp

3 5 10 6 2 7 10 I0 7

0.17 0.57 6.82 0.08 0.99 762 150 721 16.4

0.48 7.69 8.16 909.1 3.00 1950 1040 11544 1250

0.28 3.88 7.56 284.2 ZOO 1447 631 4339 281

0.18 3.13 0.34 390.5 1.42 412. 286 4134 437

3 5 11 7 2 8 11 11 8

0.01 0.33 7.28 0.13 0.72 116 _41.9 343 33.8

0.46 9.29 8.44 515.0 2.26 3280 666 53031 328

0.17 3.93 7.91 171.7 1.49 1133 349 6354 109

0.25 3.70 0.35 183.6 1.09 989 247 15704 95.8

5 5 I1 5 1 8 11 II 8

0.05 0.85 6.92 0.07 2.09 114 71.2 230 5.78

0.77 6.62 8.35 334.0 2.09 3510 1522 29604 264

0.29 3.83 7.78 118.6 2.09 1625 781 7226 57.6

0.29 2.74 0.44 149.7 1081 462 10351 85.6

4 6 11 6 2 8 11 11 8

0.03 0.38 7.08 0.15 2.07 1006 20.5 189 1.57

0.27 7.50 8.58 4766 4.57 1930 1140 15059 237

0.13 3.71 7.84 890.5 3.32 1469 728 4800 78.0

0.11 3.24 0.52 1901 1.77 368 398 5475 78.3

4 4 11 5 2 8 11 11 8

0.01 1.01 7.14 0.08 0.63 96.7 116 448 76.9

1.76 4.89 8.10 85.00 3.08 1648 463 2635 655

0.54 3.63 7.67 42.51 1.86 906 284 965 217

0.82 1.82 0.30 42.31 1.73 472 143 669 190

4 5 11 5 2 8 11 11 8

O.O1 0.76 7.24 0.08 0.51 534 6.46 270 0.605

0.64 5_64 8.06 85:52 1.98 1870 635 11321 336

0.21 3.68 7.71 34.18 1.25 1147 275 2441 121

0.29 2.57 0.26 38.08 1.04 513 231 3680 105

II

- 103
v

Table A-15. Results ofbivmiate Spearman Rank Correlation analyses between water quality sample vluiables for

all stations and san__ le I_"r/ods combined.

Para_ter

AG coeff

AG si 8

AL co¢ff

AL si8

BE coeff

BE si8

B coefl"

B siB

BOD coeff

BOD sig

CA c_eff

CA sig

CD ¢ceff

CD sis

COD coeff

COD sig

COL coeff

COL sig

CON coeff

CON si8

CPA coeff

CPA sig

CR coeff

CR si8

CU coeff

CU si[F

AG AL BE B BOD CA CD COD COL CON CPA CR CU FE GO K MG NH4-N

-.4028

,007

,3012 -.2527

,106 .233

1976 .2976 -.0640

156 .022 .737

0058 .1779 .2081 -.0543

967 .203 .270 .670

2052 .2826 .0726 .6302 .1322

.141 .030 .703 .000 .298

.0810 .1712 .2807 -.1405 .0118 .2977

.624 .333 ,194 .363 .941 .050

.0730 .0999 .0930 .1770 .0446 .3370 .572

.604 .452 .625 .140 .726 ,004 0

-.1452 .3531 -.2001 .1569 .3033 .2060 -.3996 .1929

.304 .007 ,298 .198 .016 .090 .008 .112

.1128 .1307 .4150 .3751 .0483 .4399 .2728 .2887 .2445

,421 .324 .023 .001 .704 .000 .073 .015 ,043

-.0501.5178 -,1344.1358 .4577 .4165 .125 .2327 .5384 .0568

•765 .00| ,583 .347 .002 ,003 .488 .104 .000 .695

,0854 .0260 .3567 .1331 -.0636 -.0724 .6208 .3719 -.4411 .1930 -.2551

_,._43 .867 .053 .337 .654 .603 0 .006 .001 .162 .i17

1449 -.4250 .4201 -.2889 .4807 -.6124 .3735 -.4068 .1440 -.6232 -.6524 -.4144

784 .168 ,407 .316 .114 .020 .362 .149 .623 .017 .021 .355

104
TableA-15(continued).ResultsofbivariateSpearmanRankCorrelationanalysesbetweenwaterqualitysample

variables for all s_tlons an,l samnle periods combined.

........ li i

ParamGf_"

FE coeff

FE si 8

GO coeff

GO sig

K coeff

K sig

MG coeff

MG si 8

NH4-N coeff

NH4-N sis

NI coeff

NI si8

NO2 coeff

NO2 sig

NO3 coeff

NO3 _ig

PB coeff

PB sig

PH coeff

PH sig

PILEcoeff

PHE sig

I'O4 ¢oeff

i_4 sig

SAL ¢oeff

SAL s_s

AG AL BE

r

B BOD CA CD COD COL CON CP,4 CR CU FE GO K MG NH4-N

-.4090 .5249 -.0930 .3054 .0414 .0007 -.1471 .1148 .2342 -.0662 .1047 .1798 .1437

.007 .001 .651 .044 .794 .996 .438 .458 .126 .669 .575 .249 .734

•.2678 -.1419 -.5121 .1847 -.2340 .0793 -.3525 .0417 -.0620 -.1720 ..3446 -.2855 -.4447 .0936

132 .395 .015 .214 .131 .596 .052 .781 .683 ,248 .037 .102 .147 .636

0119 .1297 .2730 .0995 -.2588 .1988 .1481 .0789 -.0266 .0553 -.0043 .0895 .4632 .3106 -.2312

933 .328 .144 .409 .039 .097 .337 .513 .828 .647 .976 .520 .095 .040 .118

2198 -.0532 .3366 .3071 -.0536 .6394 ,4888 .2982 .0387 .6209 -.0646.!934 .4724 -.0938 .1140 .2698

114 .689 .069 .009 .674 .000 .001 .012 .752 .000 .656 ,161 .088 .545 .445 .023

..3148 .0293 .0489 -.1965 -.1356 -.2743 -.2657 .4948 .3184 .0094 -.2004 -.1059 .5774 3500 -.0458 .2561 -.0962

033 .840 .805 .129 .323 .032 .098 .000 .013 .943 .198 .479 .049 .027 .779 .046 .461

,3542 -.0801 -.2048 .4367 -.5095 .4458 .571 .3275 -.4436 .5379 -,4378 .1729 -.6088 -.1053 -.1372 .6167 .5867 .{}{)37

,115 .752 .546 .030 .022 .038 .013 .137 .044 .010 .103 .442 .200 .658 .705 .002 .004 .989

,0779 .0859 .1152 -.1049 ,4562 -.1163 .0542 .0046 ,1981 -.0661 .1683 .2191 -.0857 -.1211 -.2531 -.2827 -.0194

,662 .613 .649 .488 .002 .441 .78 .976 .192 .662 .357 .213 .671 ,495 .090 .057 ,911

-.3062 -.0748 .3087 -.1364 .0690 -.1268 -.1486 .2715 .2375 .0480 -.1227 -.0475 .0000 -.2145 .0427 -,2205 -.0063".2935

,137 .747 .457 .507 .738 .537 .569 .180 .243 .816 .577 .822 1.000 .378 .885 .272 .976 .174

.3933 -.1691 .1773 .1387 -.0912 -.1256 .!194 .3484 -.2765 . -.0868 .2980 1.000 -.4185 .2267 -.6490 -.0290 -,3371

,106 .516 .704 .571 .728 .609 .672 .144 .252 .778 .215 i.000 .136 .456 ,003 ,906 .171

.4277 -.3016 -.0707 .1665 -.3170 .2409 .4352 .1533 -.3406 .1605 -.2737 .2905 .8815 -.1092 -.0202 .1431 .2805 -.0758

.001 .020 .710 .165 .011 .043 .003 .202 .004 .181 .054 .033 .000 .481 .893 .234 .018 .561

.0148 -.2066 .3288 -.0496 .1895 -.0730 .2104 .1442 -.1842 .1357 -.3256 .2172 .2169 -.0812 .1395 .0287 .1625 -.2643

•916 .134 .076 .695 .154 .564 .176 .252 .148 .281 .029 .047 .606 .605 .384 .821 .196 .047

-.2018 .1593 .1020 -.0911 -.4924 .1077 -.3744 -.1286 .1925 -.0404 -.1374 -.2302 .0360 .1771 .5045 .1287 .2045 .4890

•303 ,418 .718 .614 .007 .551 .078 .476 .291 .823 .512 .230 .939 .408 ,012 .475 .254 .010

-.2387 .3549 -.2290 .6149 -.0045 .3908 -.1712 .1616 .2053 .3808 .1512 -.2215 -.8261 .1791 .2205 -,0317 .1283 -.2143

•085 .006 ,224 .000 .972 .001 .266 .178 .091 ,001 .295 .107 .000 .245 .136 .793 .286 .097

105
Table A-15 (continued). Results ofbivariate Spearman Rank Correlation analyses between water quality sample

variables for all stafiom and sample periods combined.

Parameter AG AL BE B BOD CA CD COD COL CON CPA CR CU FE GO K

SI coeff

SI si8

SO4 c_ff

SO4 sig

TAK coeff

TAK si8

TB coeff

l"B sig

TDS coeff

TDS si 8

1"KNcoeff

TKN si 8

TOC ¢oeff

sig

TP coeff

TP sig

TSS coeff

TSS sig

ZN coeff

ZH sis

MG NH4-N

-. 1493 .5906 -.2400 -.0349 .3384 •1045 .0187 .I 890 .6314 -.0304 .6703 -. 1269 .2286 .3544 .2417 -.0198 -.0973 •1887

371 .000 .322 .800 .017 .448 .914 .167 .O00 .826 .000 .441 .499 .055 .162 .886 .480 .209

0831 -.2745 .3826 -.0606 -.0615 -.2122 .3617 .0033 -.0806 .3803 -.2940 .3992 .5595 -.1562 -.2380 .1107 .i 938 .1285

554 .035 .037 .616 .629 .076 .016 ,978 .510 .001 .038 .003 .037 .311 .107 .358 .105 .324

0525 -.i 315 .2664 -.1347 -.0568 -.0678 .1802 •1428 .0888 -.0569 -.0912 .1193 .6956 .0088 -.0446 .2220 .2195 .3689

709 .321 .155 .263 .656 .574 .242 .235 .468 .637 .529 .390 .006 .955 .766 .063 .066 .003

..1841 .4469 -.1750 .0265 .4605 .1028 -.2497 .2324 .7757 -.0322 .6598 -.3373 .3646 .3414 -.2496 .0056 -.IO99 .2336

.187 .000 .355 .827 .000 .393 .102 .051 .000 .79_) .000 .013 .200 .023 .091 .963 .362 .070

•3315 .1091 .2568 .4264 -.1001 .4575 .3592 .2019 .0988 .7228 -.0343 .3705 .6014 .1736 -.0917 .0810 .6011 .0818

•015 .411 .171 .O00 .206 .000 .017 .091 .419 .O00 .813 .006 .023 .264} .540 .502 .OO0 .531

-,2590 .2764 -.1287 -.0555 .3747 .1088 -.! 791 .0286 .3297 .0653 .5038 -.2561 .2783 .0606 -.0172 -.2243 -.1403 .1797

.061 .037 .498 .651 .002 .373 .251 .816 .006 .594 .000 .064 .357 .700 .910 .064 .250 .173

•3506 -.0012 -.0200 .0223 -.2263 .1447 .6473 .1689 -.4091 -.0794 -.1708 .3158 -.6787 -.0588 .229! .0557 1.000 -.0764

•010 .993 .916 .853 .072 .228 0 .159 .000 .510 .236 .020 .008 .705 .121 .644 .407 .558

-.2679 .2031 .1642 .1377 .2322 -.0671 .2723 .0723 .3747 .2052 .2446 -.0791 -.2307 .2218 -.0942 -.2354 -.1077 .0145

.057 .130 .404 .259 .069 .584 .081 .555 .002 .091 .090 .577 .471 .158 .538 .052 .379 .913

-.2085 .4882 .1375 .1872 .3361 .2413 .2628 .0064 .4626 .3990 .4391 .0350 .4860 .3119 .3762 .1550 .1510 .1235

.134 .0O0 .469 .118 .007 .043 .085 .958 .000 .001 .001 .802 .078 .039 .009 .197 .209 .343

•3306 .0027 -.3964 .0788 .1053 -.1285-.3883 .4361 .5397 -.4855 .3795 -.2341 1.0000 .1408 .0465 .2879 -.3904 .4653

•143 .991 .379 .690 .616 .515 .091 .020 .003 .009 .082 .294 .000 .603 .850 .137 .040 .017

- 106
Table A-15 (continued). Results ofbivariate Spearman Rank Correlation analyses between water quality sample

variables for all stations and sample periods combined.

Parameter

NO2 coeff

NO2 sis

NO3 coeff

NO3 sig

PB coeff

PB sig

PH coeff

PH sig

PHE coeff

PHE sig

PO4 coeff

PO4 sig

SAL cocff

SAL sig

SI coeff

$1 sig

S04 coeff

SO4 sig

TAK coeff

TAK sig

TB cocff

TB sig

TDS coeff

TDS sig

TKN coeff

NI NO2 NO3 PB PH PHE P04 SAL

-.0892

.772

-.4978 -.0648

.143 .805

-.6156. .2338

.269 . .516

.5330 *.2783 -.1477 .4706

.011 .061 .471 .042

*.0816.2937 *.3961 .1566 ,0422

.718 .066 .050 .522 .739

0451 -.4601.1227 .2958 -.0887-.3115

878 .036 .663 .477 .623 .078

SI S04 TAK TB 7DS 7KN TOC TP

3584 .1119 -.1378 .0645 -.2266.1281 .1459

101 .459 .502 .793 .057 .309 .418

•.5449.0340 .1128 .2430 -.2139-.2817.0691 -.0069

029 .839 .656 .447 .I 17 .050 .737 .960

•.1207.1687 -.1230 .1909 -.0178.4511 -.1864 .0021 -.2913

593 .262 .549 .434 .883 .000 .299 .986 .031

•.0982-.2190.1463 .4646 .2952 -,0260.2658 -.3754.0337 .0694

664 .144 .476 .045 .012 .837 .135 .001 .807 .565

-.4662.3351 .1830 .4367 -.3256-.1351 -.0215 .0646 .7080 -.1908 .0766

029 .023 .371 .062 .006 .283 .906 .593 .000 .i I 1 .525

6665 -.1026-.1664 .1143 .2072 .1767 .0478 .2935 -.0165.3604 .0447 -.0586

001 .497 .417 .641 .083 .159 .792 .013 .905 .002 .711 .627

-.4088.1391 .2542 .I 301 -.2579-.|650-.0164 .0574 .3656 -.I 307 -.0280.3351 .0096

IIIII

107
Table A-15 (continued). Results ofbivariate Spearman Rank Correlation analyses between water quality sample

variables for all stations and sample periods co.n_ ,ined. , ,,

Parameter

TKN sig

TOC_-ff

TOC sis

TP coeff

TP sig

TSS coe/T

TSS sig

ZN coeff

ZN si§

NI NO2 NO3 PB PH PHE P04 SAL 51 S04 TAX TB

t

77)5 TY.V TOC TP

,066 .357 .210 .607 .032 ,196 .929 .640 ,007 .284 .819 .005 .938

,4826 -.3351 -.2683 ,3862 .4836 -.1412 .1445 -.2585 -.3042 -.0028 .1017 -.4179 .1795 -.2433

023 .023 .185 .102 .000 .262 .422 .029 .024 .982 .399 .000 .134 .044

r

TSS

•.5665 .3800 .0086 .2716 -.3749 .1976 .0221 .4486 .2463 .1179 -.0629 .3368 ,1300 .2326 .5470

007 .009 .967 .276 .002 .121 ,906 .000 .073 .335 ,608 .005 ,287 .058 .000

,.0034 .4952 -.1160 .0963 -.1977 .1785 .1638 .3843 .2813 .2841 -.0434 .4536 .3260 .3290 .2825 A701

988 .000 .573 .695 .098 .155 .362 .001 .037 .016 .720 .000 .006 .006 _17 .000

..3719 -.1227 -.2539 .3146 -.0328 -.4508 _159-,3865 .5122 -.3670 -.0175 .4940 -.2433 .0436 .0899-_187 .!192

.468 .606 .479 .346 .868 .021 .957 .042 ,009 _55 .930 .008 .212 .829 .649 .264 .546

108
7

Table A-16. Results ofbivariate Spearman Rank Correlation analyses between sediment sample

variables for all stations and sample periods combined..

Parameter

AG coeff

AG sig

AL coeff

AL sig

B coeff

B sig

BE coeff

BE si8

CA coeff

CA sig

CD coeff

CD si8

CR ¢o¢ff

CR si8

CU co¢ff

CU $ig

FE coeff

FE sig

GO coeff

GO sig

K coeff

K sig

MG coeff

MG sig

MN coeff

MN si8

NH4 co¢ff

N_A4 $i8

NI coeff

NI sig

NO3 coeff

NO3 sig

PB coeff

PB si8

PH coeff

PH sis

4G AL B BE CA CD CR CU FE GO K MG MN

..2523

482

..5000 .2353

667 .380

•.6234 ,7218 .2474

073 .000 .356

2462 -.1645 -.2029 -.0757

493 .190 .451 .552

5000 .4318 -.5385 .4984 .0693

667 .002 .071 .000 .629

•.0862 .8093 .3088 .5787 -.2516 .3044

813 .00¢ .244 .000 .043 .030

•,5727 .4570 .6606 .3166 -.0228 .1176 .3709

,107 .006 .038 .068 ,896 .593 .028

-.3631 .8440 .2471 .7050 -.1877 .3447 .7418 .3621

,302 .000 .356 .000 .134 ,013 .000 .033

-.2454 -.1273 -.!106 .0489 -.3525 -AI00 -.4657 -.1968

.096 .709 .459 .744 .019 .004 .060 .185

.1846 .6767 .6393 .4781 -.1806 .2372 ,7668 .5407 .5205 -.4284

,610 .000 .010 .000 .157 .097 .000 .00I .000 .003

-.0677 .6227 .1735 .4058 .0296 .2229 .4284 .3004 .5682 .1038 ,3900

.853 .O00 .520 .001 .815 .116 .000 .079 .000 .487 .002

-.0369 .8656 .4176 .6948 -.0796 .4293 .8344 .3142 .8184 -.2195 .6335 .5553

.919 .000 .107 .000 .528 .002 .000 .066 .000 .138 .000 .000

-.3385 .2030 .3194 .0663 -.0634 -.1075 .1354 -.1395 .1014 .2177 .1848 .1855 .2064

.339 .105 .228 .603 .616 .453 .282 .424 .421 .141 .147 .139 .099

.2530 .3221 .1473 .1350 .1629 .1405 .2466 .2636 .2307 .0428 .0128 .2316 .2276

•545 .029 .615 .371 .279 .414 .098 .203 .123 .813 .933 .121 .128

-.1546 .6786 .0863 .2392 .0285 -.0839 1.0000 -.0483 .1671 .1497 -.0176 .0590

•415 .094 .650 .203 .886 .659 1.000 .800 .378 A30 .927 357

.8108 .8812 .0607 .7228 -.1773 .3827 .7495 .4383 .7837 -.1967 ,6190 .5799 .7806

.027 .000 .830 .000 .172 .006 .000 ,014 .000 .185 .000 .000 .000

.9355 ,2525 ,0927 -.0902 -.1158 -.0220 .1939 -.2409 .1809 .0231 .0400 .0672 .2023

.000 .042 333 .479 .359 .878 .122 ,163 .0149 .878 .756 .595 .106

PHE coeff

PHE sig

PO4 coeff

PO4 $i8

SO4 coeff

SO4 sig

TKN coeff

TKN si_

•1413 .4524 .2297 .1939 .1534 -.1740 .8000 .1126 .3549 .1257 .3262 .0863

•425 .260 .191 .272 .410 .325 .200 .526 .039 A79 .060 .627

.6000 !.000 .6378 .2091 .3333 .7091 .6545 -.4273 .6818 -.0364 .5818

_51 .000 .035 .537 .381 .015 .029 .190 _21 _.915 .060

5459 .1364 .3808 -.0194 .3960 .3328 .2206 .5324 -.2874 .2473 .4702 .4431

.000 .689 .008 .897 .008 .022 .395 .000 .050 .094 .001 .002

..3877 .3721 -.0382 .4271 .1606 .3610 .2705 .1226 .4377 ,-.0791 .3458 .4696 .4402

1.268 .002 .888 .000 .201 .009 .029 .483 .000 .597 .006 .000 .000

109
Table A-16 (continued). Results ofbivariate Spearman Rank Correlation analyses between

sedimem sample variables for _stations and sample peri'_ combined.

Parameter

TOC coeff

TOC sig

TP coeff

TP sig

TSS coeff

TSS sig

ZN ¢oeff

ZN sig

4G AL B BE CA CD CR CU IrE GO K MG M']V

2462 .4626 .3355 .1223 .1428 .2042 .2128 .3743 .2648 -.2334 .1957 .5773 .3106

493 .000 .204 .336 .256 .151 .089 .027 .033 .! 14 .124 .000 .012

-.3366 .1091 -.3830 .2815 -.1983 -,4614 .1005 -.3681 .1131 -.2596 .1076 -.2842

.021 .750 .008 .055 .197 .001 .701 .011 .449 .078 .472 .053

.1600 -.2242 .[ 853 -°5507 -.05 [3 -.6374 -.1450 .1465 -.3600 -.I 277 -.0910 -.3908 -.3105

,659 .073 .492 .000 .685 .000 .249 .401 .003 .392 .478 .001 .012

.3570 .4729 .2000 .4898 -.0547 .4830 .4629 .1637 .6023 -.3362 .2414 .4796 .5831

_311 .000 .458 .000 .676 .001 .000 .347 .000 .028 .065 .000 .000

llO
Table A-16 (continued). Results ofbivariate Spearman Rank Correlation analyses between sediment

sample variables for all stations and sample periods combined.

Param_er

NI coeff

NI sig

NO3 coeff

NO3 sig

PB coeff

PB sig

PH coeff

PH sig

PHE coeff

PHE sig

PO4 coeff

sig

SO4 coeff

SO4 stg

TI_I cocff

TKH sig

TOC coeff

si S

TP cocfT

"IT sig

TSS coeff

TSS sis

ZN coeff

ZN sig

NH4 NI NO2 NO3 PB PH PHE P04 S04 INN TOC TP FSS

.1677

,265

.7143 .1325 .6760

.000 .567 .016

.3335 .2794 .1471 .1760

.009 .070 .503 .352

.3846 .1510 -.2685 -.3723 .2002

.002 .317 .215 .043 .122

.5597 .3277 -.0724 .6902 .3070 -0.1096

.001 .110 .782 .000 .077

.3273 .3333 .2364 .6455

.326 .38! .484 .032

.1643 .4013 .0986 -.0514 .4653

.270 .021 .654 .787 .001

0.537

0.3273.0273

0,326.937

0.1596-.0915 .2818

0,284.607 .401

.0917 -.0426 .2794 .3935 .5515 -0.1653.4393 .4455 .2839

.468 .779 .197 .031 .000 0.188.009 .170 .053

.1678 ,4421 .2170 -.0171 .4380 0.1638.1488 .4328 .5737 .1696

.182 .002 .320 .928 .000 0,192.401 .184 .000 .177

.0210 -.2473 .0699 .1776 -.2650 -0.0497.1653 -.5604 -.0725 .0518 .1779

,888 .165 .751 .348 .072 0.74.350 .073 .628 .729 .232

.2472 .1198 -.0391 -.2067 -.3474 0.4065-.3530 .2636 -.4792 -.5855 .0935 .0956

.047 .428 .859 .273 ,006 0.001.041 .433 .001 .000 .459 ,523

-.0598 .0973 .1713 .1172 .5956 -0.0021.3113 .4603 .4573 .5341 -.4645 -.1599 -.4645

.647 .525 .458 .560 .000 0.987.094 .213 .002 .000 .000 .306 .000

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LL

%

Std. Dev= 4267,21

Mean = 4258.2

.L_ ._ _'N = 65.00

%%%%%%° • , , , . •

Aluminum (mg/kg dry wt.)

5

4

i3

2

I

0

I0.0 20.0 30.0 40.0 ,_.0

Boron (mg/kg dry wt.)

60.0 70.0

Std. Dev= 15.52

Mean = 27.0

N = 16.00

Figure A-72. Mean, standard deviation, and sample frequency distributions for aluminum

and boron in Mosquito Lagoon sediment samples.

180
_t

LL

10'

i m m w • w m _ i iI

L00 .25 .50 .75

.13 .38 .63

1.oo 1.zs" 1._ " l._s" z_o

.88 1.13 t.38 1.63 1.88

Beryllium (mg/kg dry wt.)

iStd, Oev==.36

Mean = .32

N = 64.00

2O

Std. Dev= 27618.90

Mean = 24732.0

-O.o-_ .....

• • ° . • .

Calcium (mg/kg dry wt.)

Figure A-73. Mean, standard deviations, and sample frequency distributions for beryllium

and calcium in Mosquito Lagoon sediment samples.

181
0 I

3O

10,

0 I I I i i

0.00 .06 .13 ,19 .25 .31 .38 .,_ .,_0 .,_ ._3 .69 .75 .81

Cadmium (mg/kg dry wt.)

Std. Dev= .12

Mean = .10

N = 51.00

0 I

40

0>'3O

10,

I I ! i I I !

0.0 40.0 " 8().0 " 120.0 160.0 200.0 240.0

20.0 60.0 100.0 140.0 180.0 220.0 260.0

Chromium (rng/kg dry wt.)

Std. Dev= 39.59

Mean = 18.5

N = 65.00

Figure A-74.. Mean, standard deviations, and sample frequency distributions for

cadmium and chromium in Mosquito Lagoon sediment samples.

182
W

v

20

10,

0

o.o io.o _.o

5.0 15.0

- _.o- 46.0" s6.o " eo.o

_.o 35.o _.o ss.o

Copper (mg/kg dry wt.)

Std. Dev= 10.98

Mean = 6.0

N = 35.00

70

60

5O

20

10

.............. -- N = 65.00

.... __%- - - _"

Std. Dev= 31919.43

Mean = 9039.2

Iron (rng/kg dry wt.)

Figure A-75. Mean, standard deviation, and sample frequency distributions for copper

and iron in Mosquito Lagoon sediment samples.

183
IJ.

0 I

0 I

10

m u m w l= u

0.0 1000.0 2000.0 3000.0

500.0 1500.0 2500.0

Std. Dev= 990.70

Mean = 857.1

.L_ _ N = 63.00 " ,_o.o _o.o " 8000.0

3500.0 4500.0 5500.0

Potassium (rng/kg dry wt.)

12,

10,

8

i w i

%%

i t I i i !

%%%%%%%%%%

Std. Dev= 1239.95

Mean = 1976.3

N = 65.00

Magnesium (mg/kg dry wt.)

Figure A-76. Mean, standard deviation, and sample frequency distributions for potassium

and magnesium in Mosquito Lagoon sediment samples.

184
,l

14

12

10

i 6

4,

2'

0

5.0

10.0

15.0 25.0 35.0 45.0 55.0 65.0 75.0 85.0 95.0

20.0

Std. Dev= 15.31

Mean = 21.8

N = 65.00

30.0 40.0 50.0 60.0 70.0 80.0 90.0 100.0

Manganese (mg/kg dry _.)

c

0 I

10'

0

0.0

1.0

, w w w

2.0 4.0 6.0

3.0 5.0

w n ! m m

8.0 10.0 12.0

7.0 9.0 11.0

Nickel (mg/kg dry wt.)

Std. Dev= 2.84

Mean = 3,0

N = 46.00

Figure A-77. Mean, standard deviation, and sample frequency distributions for manganese

and nickel in Mosquito Lagoon sediment samples.

185
16,

14,

12

10

8

IJ.. 6

1

J

0 w

0.0 1.0 2.0 3.0 4.0 5.0 6.0 7.0 8.0 9.0 10.0 11.0

Lead (mg/kg dry wt.)

Std. Dev= 2.66

Metal= 3.6

N = 61.00

,

LL

2'

1

0

0.0 2.0 4:0 6:o 8:o

Silver (mg/kg dry wt.)

10.0

Std. Dev= 2.99

Mean = 1.8

N = 10.00

Figure A-78. Mean, standard deviation, and sample frequency distributions for lead and

silver in Mosquito lagoon sediment samples.

186
V

U..

2O

10

0 W u w w m m m w Io

0.0 10.0 20.0 30.0 40.0

5.0 15.0 25.0 35.0

w i

500 do 7H.o

45.0 55.0 65.0 75.0

Zinc (mg/kg dry wt.)

Std. Dev= 12.66

Mean = 14.1

N = 61.00

12,

10,

, 8

4

2

0 ! w J i w

6.88 7.13 7.38 7.63 7.88 8.13 8.38 8.63

7.00 7.25 7.50 7.75 8.00 8.25 8.50

pH (pH units)

Std. Dev= .38

Mean = 7.75

N = 65.00

Figure A-79. Mean, standard deviation, and sample frequency distributions for zinc and

pH in Mosquito lagoon sediment samples.

187
2O

10

0

Std.De/= 11.92

Mean- 11.0 N- 65,00

i i m u w m w i _ _ w

0.0 5.0 10.0 15.0 20.0 25.0 30.0 35.0 40.0 45.0

2.5 7.5 12.5 17.5 22.5 27.5 32.5 37.5 42.5 47.5

Ammonia (mg/kg N dry wt.)

12

6'

4,

2'

0

0.0 200.0 400.0 600.0 800.0 1000.0 12()0.0 1400.0

100.0

Std. Dev= 369.36

Mean = 506.0

N = 65.00

300.0 500.0 700.0 900.0 1100.0 1300.0 1500.0

Total Kjeldahl Nitrogen (mg/kg dry wt.)

i

Figure A-80. Mean, standard deviation, and sample fi'equency distributions for ammonia

and total kjeldahl nitrogen in Mosquito Lagoon sediment samples.

188
I

_e

10,

1

2,

0

0.00

w w _ i w

.25 .50 .75 1.00 1.25

Nitrite (mg/kg dry wt.)

1.50 1.75

Std. Dev= .38

Mean = .27

N= 23.00

12'

10

LL

4

0

D

0.0 1.0 2.0 3"0

Nitrate (mg/kg dry wt.)

Std. Dev = 2.71

Mean =3.8

N = 30.00

Figure A-81. Mean, standard deviation, and sample frequency distributions for nitrite and

nitrate in Mosquito Lagoon sediment samples.

189
3.5

3.0 =

2.5'

_' 2.0,

_" 1.5,

LL.

1"01

.5

0.0

®

w

.50 1.00 1._o 3._o4.Go m t

2.00 2.50 3.00

Phosphate (mg/kg dry wt.)

i

4.50

Std. Dev= 1.25

Mean = 1.99

N= 11.00

0 i

10

0

. t _ w

0.0 200.0 40_.0

._

" 6o_).o8oo.o"lO(_O.O"12_.o

100.0 300.0 500.0 700.0 900.0 1100.0 1300.0

Std. Dev= 204.14

Mean = 141.0

N = 47.00

Total Phosphorus (mg/kg dry wt.)

Figure A-82. Mean, standard deviation, and sample frequency distributions for phosphate

and total phosphorus in Mosquito Lagoon sediment samples.

190
10

8

4'

2,

0

0o0 500.0 1000.0 1500.0 2000.0 2500.0 3000.0 35(X).0

250.0 750.0 1250.0 1750.0 2250.0 2750.0 3250.0

Std. Dev= 710.98

Mean = 1284.6

N = 47.00

Sulfate (mg/kg dry wt.)

0 I

0 I

o>,

10,

0 m m _ w _

%

Std. Dev= 8323.92

Mean = 4354.5

. _ N = 65.00

w m

%0 _ _ " . .

Total Organic Carbon (mg/kg dry wt.)

Figure A-83. Mean, standard deviation, and sample frequency distributions for sulfate and

total organic carbon in Mosquito Lagoon sediment samples.

191
p

20

10

m

0.0 200.0"_.o" _.o" _.o " 1_.o" 1_,o"

100.0 300.0 500.0 700.0 900.0 1100.0 1300.0

Std. Dev= 312.05

Mean = 243.9

N = 47.00

Grease and Oil (mg/kg dry wt.)

0 I

0 I

:3

LJ.

10'

@o @

0.'0 " 1000.0 " 2000.0 " 3000.0

500.0 1500.0 2500.0

" 40_.0 5000.0

3500.0 4500.0

Phenol (ug/kg dry wt.)

Std. Dev= 819.72

Mean = 271.4

N = 34.00

Figure A-84. Mean, standard deviation, and sample frequency distributions for grease and

oil, and phenols in Mosquito Lagoon sediment samples.

192
Appendix B: Light Attenuation

193
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207
Appendix C: Submerged Aquatic Vegetation

208
l

FREQUENCY OF OCCURRENCE

100-

7oJ

_ so.

10-

OHALODULE

i

i

1 _ 3 4 5 6 7 8 9

STATION

1991 _ 1992

Figure C-1. Percent coverage of shoal grass, Halodule wrightii, along 9 transects in

Mosquito Lagoon. Percent cover was estimated at 5 m intervals along a 50 m transect

utilizing a 1 m 2 plot frame.

209
FREQUENCY OF OCCURRENCE

t--

Z

W

0

pr

I

70-_1

I

40-- "_

30-.t

I

1o- .t

O

)____

1

SYRINGODIUM

. "

N_ .it

_ 3

STATION

_'_ 1991 _ 1992

Figure C-2. Percent coverage of manatee grass, Syringodiumfiliforme, along 3 transects

in Mosquito Lagoon. Percent cover was estimated at 5 m intervals along a 50 m transect

utilizing a 1 m 2 plot frame.

210
TL_"_,,IPOF::":,!_. I.'1_ r,_j:_ _i .-(; ',.].;- PE_',-'Et._7 L-"O'v_'_

FOR H. V,RIGF-I]ii .±,LONG TRANSECT 12

gO

80

70

60

I 50

20"-- - ' F

'°L L

83 84 85 86 87 BB 8g gO 91 g2 g3

TEMPORAL DISTRIBUTION OF PERCENT COVER

FOR SEAGRASS ALONG TRANSECT 2 0

lOO

90 _m

70 _ .

so _--I [--i

8_ so _ _ , I _---- __ l-- i J ! !

-- '-- _-- ,-- ;-- . F-- -- _° i

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hiD i I' I1! | _ LI

8.3 84 85 86 87 88 89 g0 gl g2

YEAR

10

g

8

7

8

5

4

--'3

'2

-1

!o

g3

I_ II. V,t':IGHTll _ S. MUFC'_ME

ud

¢._)

Figure C-3. Historic data on percent cover of submerged aquatic vegetation at Transects

I2 and 20, monitored by the NASA Biomedical Office, in south Mosquito Lagoon

between 1983 and 1993. Shoal grass, Halodule wrightii, is the dominate species in this

region..

211
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go

80

70-

60-

,50"i

40-

30"

20"

10

0

83 84 85 88 87 88 89 90 91 92 93

_E.,N'R

TEMPORAL DISTRIBUTION OF" PERCENT COVER

FOR SEAGRASS ALONG TRANSECT I 4

83 84 R5 86 87 88 89 90 91 9_2 93

YE/_R

i H _,P4OFITlt _ S. RLIFC_,t.tE

Figure C-4. Historic data on percent cover of submerged aquatic vegetation at Transects

13 and 14, monitored by the NASA Biomedical Office, in south Mosquito Lagoon

between 1983 and 1993. Shoal grass, Halodule wrightii, is the dominate species in this

region.

212
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83 8_ 85 86 87 88 89 90 91 92 g3

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TEMPORAL DISTRIBUTION OF PERCENT COVER

FOR SEAGRASS ALONG TRANSECT 2 2

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84 93

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-- "10

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83 8 L, 86 87 88 89 90 91 92

'FEt,R,

-o

o_

Figure C-5. Historic data on percent cover of submerged aquatic vdgetation at Transects

21 and 22, monitored by the NASA Biomedical Office, in south Mosquito Lagoon

between 1983 and 1993. Shoal grass, Halodule wrightii, is the dominate species in this

region.

213
f_3

9O

80

70-

60'

50

40"

30

20

10-

0

UNEAR FIT: PERCENT COVER OVER NINE

YEARS FOR 5 TRANSECTS IN SOUTH MOSQUITO

z _ : :_: -

! ! i I / F 1 I f '

B5 86 87 88 89 90 91 92 93

TR13

TR,14

TR20

___o.

TR2 1

-o4-°_

TR2 2

Figure C-6. Estimated trend lines for percent cover of submerged fiquatic vegetation on 5

transects in south Mosquito Lagoon Transects monitored by the NASA Biomedical

Office, in south Mosquito Lagoon between 1983 and 1993. Shoal grass, Halodule

wrightii, is the dominate species in this region.

214
Variation in Percent Cover of Species

Along Depth Ranges in Mosquito Lagoon

V

>

0

U

krY

35

SO

25-

20-

15-

10-

0.5-1.0 1.1 --1.4 1.5 -1.9 2.0--3.3

DEPTH

S. flliforrne

H. wrightii

r-q

_Algal sp. j

Figure C-7. Plot of relationship between percent cover of different types of submerged

aquatic vegetation and depth in Mosquito Lagoon. Note the decrease in seagrass and

increase in algae with depth.

215
Variation in Species Occurring

Along Depth Ranges in Mosquito Lagoon

80-

70-

V

60-

E

©

50-

u

0 4oo

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12

C

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/.,

//

//

/ /

/ t

/ t

/ /

1.1-1

42

.4 1.5--1 .g 2.0-3.3

DEPTH

I"

Figure C-8. Plot of relationship between frequency of encounter of different species

types of submerged aquatic vegetation and depth in Mosquito Lagoon.

216
w

FREQUENCY OF DENSITY CATEGORIES BY

DEPTH FOR SYRINGODIUM IN MOSQUITO-1 9 9 2

,,--,, 100

I;,o

"'J ¢J0

Ld

('-) 80

Z

IM

0d 70

Od

(_ 60

£3

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SYRINGODIUM

't

5-10_ 10--40_ 40--70_. 70--100_

COVER CATEGORY

0.5-1.0 m _ 1.1--1.4 m _ 1.5-1.9 m L'___/_2.0-2.2 m

Figure C-9. Frequency of occurrence of different density categories by depth for manatee

grass, Syringodiumfiliforme, collected at the Mosquito Lagoon transects in 1992.

217
FREQUENCY OF DENSITY CATEGORIES BY

DEPTH FOR HALODUI F IN MOSQUITO- 1 9 9 2

100

"J 90

W

ro 8o

Z

W

Pc" 70

(..) 60

U

O 50

I,

O 40

>- 30

Z

W 2o.

53

O _ow

I'Y

i, o

i:i.i

i::::

/.:.

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1_,,

_,,_/

_,PI /

5-10, _. 10--40_ 40--70_ 70--100_

COVER CATEGORY

0.5--1.0 m _ 1.1--1.4 m _ t.5--1.9 m _ 2.0--2.2 m

Figure C-10. Frequency of occurrence of different density categories by depth for shoale

grass, Halodule wrightii, collected at the Mosquito Lagoon transects in 1992.

218
FREQUENCY OF DENSITY CATEGORIES BY

DEPTH FOR ALGAL SPP. IN MOSQUITO- 1 9 9 2

100-

I;,1

v 90-

l,J

80-

Z

ILl

70-

r2Z

_-3

U 60-

U

O 5oh._

0 40-

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(..9 30-

Z

Ld 20-

?.3

O lOw

tY

LL 0-

ALGAE

4±

B.a,k-"E 5-10_ 10--40, _. 40-70_ 70-100_

COVER CATEGORY

0,5--1.0 m _ 1.1 --1.4. m _ 1.5--1.9 m _, 2.0--2,2 m

Figure C-11. Frequency of occurrence of different density categories by depth for all

algae species combined collected at the Mosquito Lagoon transects in 1992.

219
Appendix D: Atmospheric Deposition

220
Table D-1. John F. Kennedy SpaceCenter Rainfall Totals, pH, and Conductivity

1991 Third Quarter

Date Amount Field pH Field Conductivity(umho/cm)

(inches) Weekly Sample Weekly Sample Volume Weighted

7/01/91 0.24/.60 4.56 16.5 6.60

7/04/9 1 0.20 4.56 17.6 6.52

7/05/91 0.20 6.52

7/06/91 0.11 3.59

7/07/91 0.03 0.98

7/10/91 0.20 4.60 14.9 0.87

7/12/91 2.69 11.75

7/13/91 0.20 0.87

7/14/91 0.20 0.87

7/15/9 1 0.12 0.52

7/20/91 0.53 4.89 11.0 11.00

7/26/91 1.98 4.40 20.9 9.24

7/27/91 2.10 9.80

7/29/91 0.40 1.87

7/30/91 0.20 4.29 26.8 2.16

7/3 1/91 0.03 0.32

8/01/91 0.55 5.94

8/05/91 1.70 18.37

8/09/91 0.65 4.00 49.2 30.75

8/10/91 0.35 16.56

8/11/9I 0.04 1.89

8/15/91 0.15 4.37 24.2 3.70

8/18/91 0.13 3.21

8/19/91 0.70 17.29

8/2 4/91 0.44 4.73 13.2 13.20

8/3 0/91 0.05 4.98 18.7 18.70

9/03/91 0.30 4.85 25.3 8.93

9/08/91 0.25 4.85 25.3 7.44

9/09/91 0.15 4.46

9/10/91 0.50 21.72

9/11/91 0.04/.39 4.70 24.2 2.48

9/20/91 1.45 4.45 20.9 13.78

9/2 1/91 0.14 1.33

9/22/91 0.58 5.51

9/23/91 0.03 0.29

9/28/91 0.10 6.03 16.5 0.50

9/29/91 2.95 14.66

9/30/91 0.27 1.34

Total 20.95

Me an 0.55 (N=38) 4.65 7.51

Standard

Deviation 0.75 1.10 7.28

221
Table D-2. John F. Kennedy Space Center Rainfall Totals, pH, and Conductivity

1991 Fourth Quarter

Date Amount Field pH

(inches) Weekly Sample

Field Conductivity(umho/cm)

Weekly Sample Volume Weighted

10/01/91 1.15 5.20 9.9 3.6

10/02/91 0.35 1.1

10/03/91 0.04 0.1

10/05/91 0.05 0.1

10/06/91 1.55 4.9

10/10/91 0.08 5.08 20.9 20.9

10/15/91 0.25 5.05 11.0 11.0

10/23/91 0.04 5.02 75.2 21.5

10/24/91 0.10 53.7

11/09/91 0.08 4.55 13.7 13.7

11/18/91 0.24 6.19 47.9 39.6

11/19/91 0.05 8.3

11/20/91 0.10 7.06 39.9 30.7

11/23/91 0.03 9.2

11/29/91 0.03

12/04/91 0.30 4.91 7.7 7.7

12/10/91 0.05 5.40 14.8 4.1

12/12/91 0.13 10.7

Total 4.62

Mean 0.26 (N=18) 5.34 15.06

Standard

Deviation 0.42 1.14 14.96

222
Table D-3. John F. Kennedy Space Center Rainfall Totals, pH, and Conductivity

1992 First Quarter

Date Amount Field pH Field Conductivity(umho/cm)

(inches) Weekly Samole Weekly Sample Volume Weighted

1/01/92 1.02 4.72 19.4 11.05

1/02/92 0.77 8.35

1/14/92 0.14 4.94 16.8 16.80

1/17/92 0.04 4.77 9.7 3.23

1/18/92 0.08 6.47

1/23/92 0.08 5.66 23.9 23.90

2/05/92 0.90 4.81 11.6 9.24

2/07/92 0.04 0.41

2/09/92 0.15 1.54

2/10/92 0.04 0.41

2/23/92 0.30 4.30 43.9 29.27

2/24/92 0.15 14.63

2/25/92 0.44 4.72 13.8 13.80

3/05/92 0.10 4.69 16.3 0.60

3/06/92 2.29 13.72

3/07/92 0.33 4.76

3/11/92 0.25 4.90 9.0 7.50

3/12/92 0.05 1.50

3/19/92 0.03 4.43 38.7 6.45

3/22/92 0.15 32.25

3/25/92 2.10 4.70 16.3 16.30

Total

Mean

Standard

Deviation

9.45

0.45 4.77 10.58

0.65 1.07 9.26

223
Table D-4. John F. Kennedy Space Center Rainfall Totals, pH, and Conductivity

1992 Second Quarter

Date Amount Field pH Field

(inches) Weekly Sample Weekly Sample

Conductivity(umho/cm)

Volume Weighted

4/11/92 0.03 5.00 15.7 0.22

4/12/92 1.40 5.00 15.7 10.08

4/13/92 0.75 5.00 15.7 5.40

4/17/92 0.05 4.71 34.8 34.8

4/2 1/92 1.70 4.77 12.9 11.36

4/23/92 0.23 4.77 12.9 1.54

5/14/92 0.38 4.18 50.2 38.15

5/18/92 0.12 4.18 50.2 12.05

5/26/92 0.15 4.35 38.7 2.90

5/29/92 0.30 4.35 38.7 5.81

5/30/92 0.05 4.35 38,7 0.97

6/2/92 0.15 4.50 21,9 2.67

6/3/92 0.35 4.50 21.9 6.23

6/4/92 0.40 4.50 21.9 7.12

6/6/92 0.30 4.50 21.9 5.34

6/8/92 0.03 4.50 21.9 0.53

6/10/92 0.69 4.20 33.0 4.62

6/11/92 0.82 4.20 33.0 5.49

6/12/92 0.53 4.20 33.0 3.55

6/13/92 1.09 4.20 33.0 7.30

6/15/92 1.80 4.20 33.0 12.05

6/20/92 0.70 4.01 55.0 35.65

6/21/92 0.38 19.35

6/23/92 0.20 4.82 5.1 0.33

6/25/92 0.05 4.82 5.1 0.08

6/26/92 1,00 4.82 5.1 1.65

6/27/92 1,30 4.82 5.1 2.14

6/28/92 0.50 4.82 5.1 0.82

6/29/92 0.05 4.82 5.1 0.08

6/30/92 0.20 4.42 21.3 21.3

Total 15.70

Mean 0.52

Standard

Deviation 0.51

4.49 8.65

1.07 10.77

224
Table D-5. John F. KennedySpaceCenter Rainfall Totals, pH, and Conductivity

1992 Third Quarter

Date Amount Field pH Field

(inches) Weekly Sample Weekly Sample

Conductivity(umho/cm)

Volume Weighted

7/13/92 0.35 4.34 27.1 27.1

7/14/92 0.44 4.51 21.9 14.2

7/17/92 0.06 1.9

7/19/92 0.03 1.0

7/20/92 0.15 4.8

7/21/92 0.18 4.76 11.0 7.3

7/23/92 0.09 3.6

7/30/92 0.53 3.85 72.5 72.5

8/04/92 0.90 4.25 27.9 23.9

8/08/92 0.15 4.0

8/12/92 0.60 4.80 10.2 2.2

8/14/92 1.40 5.1

8/15/92 0.23 0.8

8/16/92 0.14 0.5

8/17/92 0.45 1.6

8/18/92 0.07 4.42 19.1 0.4

8/19/92 0.11 0.7

8/20/92 1.54 9.9

8/22/92 0.62 4.0

8/23/92 0.55 3.5

8/24/92 0.07 0.4

8/29/92 0.70 4.26 28.8 28.8

9/02/92 0.20 4.66 15.0 9.7

9/03/92 0.03 1.5

9/04/92 0.05 2.3

9/07/92 0.03 1.5

9/10/92 0.95 4.42 21.3 7.7

9/13/92 1.35 10.9

9/14/92 0.34 2.7

9/16/92 0.01

9/18/92 0.01

9/24/92 0.08 4.98 12.7 0.7

9/27/92 0.20 1.6

9/28/92 1.28 10.4

9/29/92 2.10 4.93 14.0 8.6

9/30/92 0.09 0.4

Total 16.08

M e a n 0.45 4.50 8.1

0.51 1.07 13.4

Standard

Deviation

225
Table D-6. John F. Kennedy Space Center Rainfall Totals, pH, and Conductivity

1992 Fourth Quarter

Date Amount Field pH

(inches) Weekly Sam ole

Field Conductivity(umho/cm)

Weekly SamDle Volume Weighted

10/02/92 0.14 4.93 17,8 2.0

10/03/92 0.65 9.6

10/04/92 0.42 6.2

10/06/92 0.85 4.83 37.4 14.5

10/07/92 0.65 11.1

10/09/92 0.02 0.3.

10/11/92 0.68 11.6

10/23/92 0.19 4.06 80.0 42.2

10/24/92 0.17 37.8

10/31/92 0.07 4.40 27.1 27.1

11/08/92 0.25 4.23 80.0 57.1

11/09/92 0.10 22.9

11/12/92 0.40 4.62 36.3 29.6

11/16/92 0.06 4.4

11/17/92 0.03 2.3

11/18/92 0.11 4.76 20.3 0.9

11/20/92 0.02 0.2

11/21/92 0.12 1.0

11/22/92 1.67 14.0

11/23/92 0.50 4.2

11/28/92 0.09 4.33 25.8 25.8

12/10/92 0.60 4.81 7.7 7.7

12/16/92 0.02 4.58 50.3 25.2

12/20/92 0.02 25.1

12/27/92 0.05 4.44 47.7 47.7

12/29/92 0.40 4.72 19.4 3.5

12/30/92 1.02 9.0

12/31/92 0.77 6.8

Total (N=28) 10.07

Mean 0.36 4.27 16.06

0.39 1.27 15.67

Standard

Deviation

226
w

Table D-7. John F. Kennedy Space Center Rainfall Totals, pH, and Conductivity

1993 First Quarter

Date Amount

(inches)

1/02/93 0.23

1/03/93 0.25

1/04/93 0.53

1/08/93 0.54

1/09/93 0.07

1/11/93 0.12

1/13/93 0.03

1/14/93 0.90

1/15/93 0.60

1/16/93 0.45

1/20/93 0.23

1/23/93 0.03

1/25/93 1.10

1/26/93 0.93

1/26/93 0.20

1/27/93 0.30

2/09/93 0.55

2/10/93 0.05

2/11/93 0.50

2/17/93 0.09

2/21/93 0.03

2/22/93 0.95

2/26/93 0.40

3/03/93 0.05

3/04/93 0.20

3/07/93 O.05

3/13/93 2.10

3/16/93 0.09

3/17/93 0.15

3/18/93 0.18

3/20/93 0.05

3/21/93 0.68

3/23/93 0.10

3/24/93 0.14

3/26/93 0.03

3/31/93 0.85

Total 13.75

Mean (N=36) 0.38

Standard

Deviation (N=I) 0.43

Field pH

Weekly Sample

4.93

4.88

4.30

5.06

4.45

5.0O

4.67

4.70

5.02

5.02

4.93

4.38

4.90

4.78

1.06

Field Conductivity(umho/cm)

Weekly Sam.Die Volume

27.1

9.0

10.3

9.0

39.9

7.7

15.5

20.6

20.6

6.5

36.1

30.9

9.0

Weighted

6.2

6.7

14.2

6.7

0.9

1.5

0.4

4.7

3.1

2.3

0.9

0.1

4.3

3.7

16.0

23.9

3.9

0.3

3.5

1.3

0.4

13.8

20.6

3.4

13.7

3.4

6.5

2.8

4.7

5.7

1.6

21.3

11.4

16.0

3.5

7.3

6.41

6.32

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Appendix E: Wind Tower Data Summaries

245
24 hour Wind Rose

Direct ion & Speed

may i991

0-t 2-5' 6-I5

!

t5-30 3J-75 >75HPH

±J

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

Pange9

O-J

16-30

Zof

total

Z of each dJrect.|on for- IlouP]y averages X of

N NNE NE ENE E ESE SE 5SE 5 5SH 5H HSH H WNH NW NNH total

55.6 J2.5 0,0 10.0 4.9 2.3 .5 0.0 8.5 0.0 2.6 ]l.J 12.5 50.0 37.5 25.0 J0.8

5,7 50.0 20.0 35.0 46.3 26.7 g.6 50.6 7t.8 68.E 52.6 ll.! 25.0 25.0 37.5 50.0 31.4

25.7 37,5 50.0 55,0 48.8 70,g 86,9 4g.4 1g.7 31.8 44.7 77.8 62.5 25.0 12.5 25.0 56.8

0.0 0.0 0.0 0.0 0.0 0.0 3,0 0.0 0.0 O.O 0,0 0.0 0.0 0.0 12.5 0.0 1.0

excluding calm wlncls

3,5 l,l 1.6 2.g 6.3 t3.5 31.7 13.3 t0.5 3.5 5.9 2.6:1.t .6 .5 |.0

Figure E-I. Wind direction and speed measured at Haulover Canal bridge during May

1991.

246
24 hour Wind Rose

Direction 8 Speed

jun 1991

0-! 2-5 6-15 |6-30 3|-75 >7514PH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ran_jes

O-t

P.-5

6-15

16-30

5 of

Lotal

5 of esch direction for hourly IlVer'llgmS 5 of

N _ HE ENE E ESE SE SgE S SSM S_ WSM _( _N_ N_ NHW _otlt

74.0 IR.2 22.a t.6 ,9 3.6 9.5 |4.3 t5.4 J,I.3 7.7 12,8 7.0 6.8 0.0 8.0 12.1

24.0 63.5 22.2 _3.0 t7.9 26.8 36.t 66.7 76.9 71.4 38.5 27.7 2t.t 50.0 68.2 64.0 34.9

2.0 18.2 5fl.6 ,_0.8 72.6 67.9 5a.4 |9.0 7.7 14.3 53.8 59.6 71.9 43.2 31.8 8.0 49.7

0.0 0.0 0.0 24.6 8.5 t.8 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 4.3

exc|udtng calm winds

_.4 t.7 2.6 tt.2 21.6 t0.] 3.5 3.4 2.t 3.4 4.5 7.6 g.9 7.6 4,t 4.3

Figure E-2. Wind direction and speed measured at Haulover Canal bridge during June

1991.

247
24 hour Wind Rose

Direction _ Speed

jul _99_

0-1 2-5 6-15 t6-30 3|-75 >75NPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ranges

O-t

2-5

6-t5

i6-30

ZOf

tota]

of each direction for hourly averages g of

N NNE NE ENE E ESE SE SSE S S$_ SW NSW W WNW NH HNN total

6t.3 40.0 16.7 26.7 23.8 3.1 0.0 g.8 3.g 7.5 3.3 3.0 4.4 9.1 21.4 8.3 8.t

6.3 60.0 83.3 33.3 42.9 59.4 32.7 62.3 71.t 65.0 34.2 35.6 33.8 75.8 50.0 66.7 48.i

12,fi 0.0 0.0 40.0 33.3 37.5 67.3 27.g 25.0 27.5 62.5 59.4 58.6 15.2 28.6 25.0 43.2

0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 2.0 2.9 0.0 0.0 0.0 .6

excluding calm winds

,5 .5 .8 t.7 2.4 4.7 8.4 8.4 tt.l 1t.3 17.7 14.g g.g 4.6 t.7 t.7

Figure E-3. Wind direction and speed measured at Haulover Canal bridge during July

1991.

248
24 hour Wind Rose

Direction @ Speed

aug 199_

0-i 2-5 6-15 t6-30 31-75 >75MPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rmnges

0-!

2-5

8-t5

16-30

Z of

total

_l of esch direction for hQurly iverages _ of

N NNE HE ENE E EgE 56 SSE S SS_ SW MSw W HNW NW NNN total

60.0 5.6 t0.0 g.1 6.5 0.0 1.7 6.8 7.g 3.0 5.g g.| 12.5 3.1 0.0 13.3 7.5

20.0 33.3 50.0 31.6 34.8 41.3 28.8 67.8 66,7 66.7 44.t 27.3 50.0 59.4 45.5 53.3 45.7

20.0 Et.t 40.0 59.| 58.7 58.7 63.5 25.4 25.4 30.3 50.0 83.8 37.5 34.4 54.5 33.3 46.8

0.0 0.0 0.0 O.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 3.i 0.0 0.0 .2

excluding ca]m winds

1.0 2.g 3.1 3.5 7.5 6.0 10.1 9.5 t0.1 6.5 lJ.| J2.1 "6.1 5.4 1.9 2.3

Figure E-4. Wind direction and speed measured at Haulover Canal bridge during August

1991.

249
24 hour Wind Rose

Direction _ Speed

sep 1991

0-1 2-5 8-i5 18-30 3i-75 >75NPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ranges

o-t

16-30

Z of

total

X of each direction for hourly averages X of

N NNE NE ENE E ESE SE SSE S SSW SH WSM N HNW NH HNW tote]

84.8 10,0 7.0 3.0 t.9 4.5 0.0 0.0 15.6 li.8 ll.t 0.0 0.0 26.3 4.8 8.3 t0.8

2_.0 45.0 22.8 1_,8 28.6 40.9 50.0 90.5 84.4 58.8 0.0 50.0 69.2 53.2 85.7 7g.2 40.8

10,4 45.0 63.2 74.3 88.6 54,5 50.0 g.5 0.0 2g.4 88.9 50.0 30.8 i0.5 g.5 t_.5 48.7

0.0 0.0 7.0 6.g t.O 0.0 0.0 0.0 0.0 0.0 0.0 0.0 O.g 0.0 0.0 0.0 2.i

excluding calm winds

3.4 3.8 t0.5 lg.3 20.3 8.3 5.5 4,t 5.3 3.0 1.6 1.6 2.5 2.8 3.g 4.3

Figure E-5. Wind direction and speed measured at Haulover Canal bridge during

September 199 I.

250
=

24 hour Wind Rose

Direction _ Speed

oct _99I

0-1 2-5 6-15 iB-30 3|-75 >75NPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

ranges

O-t

2-5

6-t5

16-30

Z of

total

SSW SSE

S

Z of each direction for hourly averages Z of

N NNE HE ENE E ESE 8E SSE 8 6St/ gW MSi4 M NNN NW NHN total

27.3 2.2 1.3 4.8 .8 2.9 i0,S 0.0 13.3 8.3 0.0 25.0 20.0 15.4 12.9 4.8 5.8

45._ 37.0 22.| t9.3 8.g |9. i 36_.8 85.7 86.7 75.0 80.0 50.0 60.0 50.0 58.i 31.0 29.0

27.3 52.2 70.1 54.8 78.0 76.5 52.6 t4.3 0.0 t6.7 40.0 25.0 20.0 34.6 29.0 64.3 57.8

0.0 8.7 8.5 22.| tl.5 1.5 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0,0 0.0 7,6

excluding calm winds

3.5 8.8 |i.2 14.6 27.g 9.7 2.5 2.1 1.8 i.6 2.2 i.3 1.8 3.2 4.0 5.9

Figure E-6. Wind direction and speed measured at Haulover Canal bridge during October

1991.

251
24 hour Wind Rose

Direction & Speed

nov 199_

0-! 2-5 6-15 18-30 31-75 >7514PH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ranges

0-!

2-5

6-15

of

tote1

Z of each direction for hourly averages Z of

N NNE NE ENE E ESE SE SSE S SSH SH #SH H HN# NW NNW total

21.4 2.2 3,i 5,0 5.3 i.5 7.7 3.3 7.9 i3.0 i4.8 0.0 ii.i 0.0 0.0 1.0 5.4

_3._ 2_.8 53.i 60.0 2t.i 23.9 29.2 46.7 63.2 56.5 48.i 44.4 88.g 35.3 32.3 24.0 33.4

55.4 75,0 43.8 35.0 73.7 74.8 64.i 50,0 28.9 30.4 37.0 55.6 0.0 64.7 67.7 75.0 6i.2

axcluding calm winds

7.0 21.0 4.g 3.0 S.7 I0.4 5.7 4,6 5.5 3.2 3.6 1.4 1.3 _'7 _.g i5,0

Figure E-7. Wind direction and speed measured at Haulover Canal bridge during

November 1991.

252
24 hour Wind Rose

Direction & Speed

dec t99t

0-! 2-5 6-t5 16-30 3t-75 >75t4PH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rsngss

O-J

2-5

6-t5

16-30

Z of

tots1

Z of esch direction for hourly svsrages _ of

H HI_ HE EHE E ESE SE 5$E S SSN SN NSH N N_ NN _ total

t4.! t.7 7.3 4.3 3.6 5.8 5.8 3.0 9.7 0.0 0.0 2.G i4.B 3.4 5.9 5.0 5.!

_7.8 26.3 30.9 37.0 33.g 38.5 52.8 89.7 4t.g 50.0 51.g 47.4 44.4 55.2 5g.g 33.3 39.9

6t.I 65.3 58.2 28.3 5t.8 50.0 4|.7 27.3 48.4 50.0 44.4 50.0 40.7 41.4 37.3 6L.7 50.3

0.0 6.8 3.6 30.4 t0.7 5.8 0.0 0.0 0.0 0.0 3.7 0.0 0.0 0.0 0.0 0.0 4.7

exc]udJng cslm winds

8.g t6.7 7.3 8.3 7.8 7.! a.9 4.6 4.0 2.6 3.9 5.3 3!3 4.0 5.9 8.a

Figure E-8. Wind direction and speed measured at Haulover Canal bridge during

December 1991.

253
24 hour Wind Rose

Direction & Speed

jan t992

0-t 2-D 6-t5 t8-30 3t-75 >76HPH

N

NNW NNE

NW NE

WNW ENE

W E

WSW ESE

SW SE

SSW SSE

S

rsnoes

0-t

6-t5

1_-30

I of

tots]

_IIof esch direction for hourly sversges II of

N NHE 1_ _ E ESE 5E SSE S SSH SH _SH W _t_ NW NNH torn1

J6.0 3.1 _.3 6.5 3.8 t6.7 6,7 8.7 0.0 0.0 7.0 0.0 3.2 0.0 4.6 t.g 5.0

23,3 tg.4 3Cl.5 4t,9 38,5 60.0 60.0 34.8 26.3 45.6 25,6 5t.9 3;_.3 37.5 23.6 32.0 32.0

5l_.0 flt._ 5._.3 6t.6 57.7 33.3 33.3 66.3 73.7 64.6 53.6 44.4 3|.6 80.4 70.6 ES.0 58.7

2.7 ]6.3 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 |4.0 3.7 12.g 2.1 |.l l.O 4.3

excluding cslm *]nds

9.0 13.6 10.3 4.1 3.6 t,4 _.0 3.0 2.7 3.1 _.7 3.g 4.3 6.8 ]:J.| 14.4

Figure E-9. Wind direction and speed measured at Haulover Canal bridge during January

1992.

254 ' i
9

24 hour Wind Rose

Direction _ Speed

feb 1992

0-1 a-5 8-1_ 16-30 31-75 >7m4PH

!

N

NNW NNE

NW NE

WNW

W E

WSW ESE

SW SE

SSW SSE

S

ranges

O-I

2-5

8-_5

16-30

Iof

total

_IIof each dtr'aC_lon for holJr]y averages II of

N NHE HE ENE E ESE SE SSE $ aSH SN NSW N NNN FiN HNH tOtS1

9,5 t.2 3.8 9.7 2.8 0.0 8.8 2.g 0.0 0.0 5.8 3.6 •0.0 1.5 4.5 4.9 3.2

4.8 8.4 8.5 BS.t 30.6 44.4 58.1 47.1 34.3 51.5 40.7 17.9 a4.5 20.9 t6.4 18.5 27.4

85.7 8.q.2 86._ 32.3 66.7 55.6 35.5 50.0 65,7 48.5 83.7 75.0 59.2 71,8 77.5 75.6 67.2

0.0 t.2 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 3.5 16.3 6.0 t.5 0.0 2.2

excluding calm x/nds

_.8 12.3 7.5 4.2 5.2 4.0 4.3 4.8 5.2 4.g 7.8 4.0 7.3 9.g 9.6 5.8

Figure E-10. Wind direction and speed measured at Haulover Canal bridge during

February 1992.

255
24 hour Wind Rose

Direction _ Speed

mar 1992

0-1 2-5 6-15 16-30 3t-75 >75MPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rgngs8

9-S

_-5

6-15

16-30

oe

tote]

% of each direction for hourly evsPages g of

N WE NE ENE E EgE SE $SE S SSH SH MSM H HNW NH NNW tote1

2t.4 B.3 1.7 0.0 3.6 0.0 ].B 6.5 2,5 4,0 4.0 5.0 0,0 2.3 0.0 5.6 2.9

PR.6 _0.8 _0.3 40,B 3a.| 44.a _E.B J9.4 40.0 3a.O _fl.O J_.O t7.0 _3.3 a9.7 38.Q a8,8

_0.0 B8.3 78.0 57.8 64.3 _3._ 69.8 B7.7 _7.5 6A.O 68,0 80.0 81.S 73.3 88.8 55.8 87.0

0.0 S_.5 0,0 1.6 0.0 2.3 t.8 8.5 0.0 0.0 0.0 0.0 t.9 t.a 1.6 0.0 S.5

e_cludtng calm xtnds

J._ 3.t 8.a 9.0 3.8 6.J 7.7 4.J B._ 3.4 6.8 5.4 7.5 Ji.B g.O 7.2

Figure E-11. Wind direction and speed measured at Haulover Canalbfidge duringMarch

1992.

256
24 hour Wind Rose

Direct. ion & Speed

apr _992

0-| e-5 6-t5 /8-30 3t-75 >75MPH

N

NNW NNE

NW NE

20%

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rsnQes

0-!

2-5

6-1._

t8-30

Z of

total

% of asch direction for hourly averages % of

N NNE NE ENE E ESE SE SSE S SSW SW NSW W WNff NW N_ total

9.t 0.0 5.6 t.7 6.9 0.0 3,2 2.4 4.0 33.3 9.| 0.0 0.0 4.0 0.0 |.6 3.7

9.t t8.0 2i.3 27.1 27.8 37.5 12.9 38.| aO.O t6.7 36.4 t4.3 20.0 12.0 26.5 14.5 22.!

7t.4 80.9 72.2 7t.2 62.t 62.5 83.9 59.5 58.0 50.0 54.5 85.7 80.0 82.0 73.5 80.8 72.2

t0.4 t.t .g 0.0 3.4 0.0 0.0 0.0 0,0 0.0 0.0 0.0 0.0 0.0 0.0 3.2 2.0

excluding calm wlndS

iO._ t3.| i5.0 8._ 7.g 5.9 4.4 6.0 3.5 .6 t.5 2.1 3.7 3.5 5.O 9.0

Figure E-12. Wind direction and speed measured atHaulover Canalbfidge during April

1992.

257
24 hour Wind Rose

Direction @ Speed

may 1992

O-t 2-5 6-t5 t6-30 3i-75 >75HPH

I _

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ranges

0-1

2-5

15-30

Xof

totsl

X of each direction for hourly averages X of

N NNE HE ENE E ESE SE SSE S 55W SW WSW W WNW NW NNW total

33,3 t0.5 0.0 2.9 1.3 2.4 2,2 2.8 3.0 O.O 0.0 5,5 5.9 1.7 8.3 3.5 3.9

29,2 21.t 8.2 22.g t0,3 9.5 t3.3 47.2 57.6 52.5 33.3 22.2 25.5 33.3 33.3 B7.g 25.7

37,.5 57.9 9_.e 7|±4 8B.5 88,t 84.4 50.0 39.4 47.4 6(3.7 72.2 68.6 65.0 60.4 25.0 6g.7

0.0 10.5 0.0 2.9 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 O.0 0.0 3.6 ,7

excluding calm winds

2.3 2.5 8.9 9.9 li.2 t2.0 6.4 5.t 4.7 2.8 3.1 5.0 _.0 8.6 6.6 3.9

Figure E-13. Wind direction and speed measured at Haulover Canal bridge during May

1992.

258
w

24 hour Wind Rose

Direction _ Speed

jun 1992

0-! 2-5 6-t5 18-30 31-75 >75NPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

ranges

0-!

2-5

6-t5

t8-30

_l of

total

SSW SSE

S

I of aach direction for hour|y averages Z of

H NHE HE ENE E ESE SE SSE S Sgtf SM HSH N NHH NH HNH total

53.3 33.3 0.0 0.0 2.6 0.0 3.3 0.0 3.B 3.2 .7 4.4 2.4 9.[ 0.0 0.0 3.7

33.3 50.0 77.8 _7.3 El.5 5t.2 36.7 EJ.7 39.8 39.1 17.8 |4.1 43.9 58.2 58.3 75.0 35.0

13.3 16.7 2_.2 72.7 35.g 48.B 60.0 38.3 _2.8 55.8 BO.| 80.7 53.7 _2.7 4t.7 J2.5 EO.t

0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 3.8 3.2 !.4 .7 0.0 0.0 0.0 t2.5 l.l

excluding calm winds

i.O .6 t.3 4.9 5.8 8.t 4.3 7.0 7.6 9.! 21.5 i9.! 5.9 3.0 i.8 1.2

Figure E-14. Wind direction and speed measured at Haulover Canal bridge during June

1992.

259
24 hour Wind Rose

Direction _ Speed

jul 1992

0-! 2-5 6-|5 |6-30 31-75 >75MPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rongos

O-I

2-5

S--t_

Zof

total

Z of wsch diroctto_ for houP]y ovsroge8 X of

N N_ HE E_ E ESE SE SSE S SSM SH HSH M NNW _ NNH total

88.0 28.e 7.| 9.! g.| 2.4 1.7 3.4 3.3 g.4 4.5 3.8 _.l it.6 7°| 28.6 9.0

12.0 42.9 _7.t 90.9 63.6 40,5 t9°0 52.5 76.7 65.8 _.8 50.0 7|.2 Bg.8 64.3 57.t 53.0

0.0 28.6 33.7 0.0 27.3 57.i 7g.3 44.t 20.0 25.0 56.7 45.3 23.7 |8.8 28.6 t4.3 38.t

oxc]uding coin Ntndo

,5 .9 2.3 1.8 5.3 7.2 |0.0 |0.0 |0.2 5.1 1|.2 t3.5 _.8 6.7 4.6 .g

Figure E-15. Wind direction and speed measured atHaulover Canalbfidge during July

1992.

260
.r

24 hour Wind Rose

Direction 6 Speed

aug _992

O-I 2-5 6-i5 |5-30 31-75 >75MPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rengeg

O-i

2-5

8-t5

15-30

Z of

total

K of emch direction for hourly averages Z of

N NNE NE ENE E ESE SE $SE S SS_ $N WBW H NN_ NW NHW tote1

69.6 7.4 it.! t7.8 8.7 1.3 3.7 t5.0 t3.0 5.6 3.4 5.7 14.7 28.6 t8.2 50.0 ti.7

30.4 48.t 49.1 5|.1 52.2 24.0 29.6 50.0 73.9 66.7 4t,4 35.8 58.8 47.6 63.6 50.0 45.8

0.0 44.4 38.0 28.7 3g.l 74.7 68.7 35.0 13.0 27.8 55.2 58.5 2(;.5 tg.O t8.2 0.0 4j.8

0.0 0.0 1.9 4.4 0.0 0.0 O.O 0.0 0.0 0,0 0,0 0.0 0.0 4.8 0.0 0.0 .7

excluding calm winds

t.l 24.2 t5.5 6.0 6.8 it.9 4.2 2.7 3.2 2.7 4.5 8.t 4.7 2.4 t.4 .6

Figure E-16. Wind direction and speed measured at Haulover Canal bridge during

August 1992.

261
24 hour Wind Rose

Direction & Speed

sep _992

0-i 2-5 6-15 |6-30 3|-75 >75MPH

= i I

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ranges

0-t

2-5

6-15

16-30

I Of

total

I of each direction for hourly averages I of

N NNE NE EHE E ESE SE SSE S SSM SH MSN N WHt¢ HI4 NNM tote|

35.7 |1.8 6.5 2.5 3.E og |.0 7.1 3.4 3t.6 |0.0 18.8 23.| 29.4 lO.0 0.0 7.0

30.0 4t.2 9.7 12.3 22.7 31.9 33.3 7|.4 93,1 52.6 60.0 82.5 6t,5 4i.2 15.0 23.8 35.8

30.0 23.5 61.3 79.0 70.0 87.2 65.6 2t.4 3.4 25.8 30.0 18.8 15.4 29.4 75.0 76.2 54.2

3.3 23.5 22.E 6.2 3.6 0.0 0.0 0.0 0,0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 3.0

oxc)uding celm winds

2.9 2.3 4.5 t2.2 16.4 t7.8 t4.7 10.0 4.3 2.0 |.4 2.0 1.5 t.9 2.8 3.2

Figure E-i7_Wind direction and speed measured at Haulover Canal bridge during

September 1992.

262
v

24 hour Wind Rose

Direction & Speed

oct 1992

0-i 2-5 6-115 16-30 31-75 >75HPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

ranges N

0-t 15.4

2-5 35.9 5.7 23.g t4.2 ii.6 t9.2 32.1 32.1 56.7

6-i5 48.7 75.5 69.0 62.3 77.9 60.6 60.7 67.9 36.7

t6-30 0.0 /8.9 7,0 23.6 |0.5 0.0 3.6 0.0 3.3

3t-75 0.0 0.0 O.0 0.0 0.0 0.0 0.0 0.0 0.0

of excluding calm

tots1 4.8 7.8 10.4 |5.5 |2.6 7.6 4.0 4.t 4.2

SSW SSE

S

Z of each direction for hourly averages ]; of

NNE HE ENE E ESE SE SSE 6 SgW SW HSM M HNM NW NNW total

0.0 0.0 0.0 0.0 0.0 3.6 0.0 3.3 0.0 0.O 0.0 12.| O.O /0.3 6.0 2.8

50.0 20.0 44.0 45.5 53.t 58.8 30.0 28.0

4|.7 80.0 48.0 42.4 46.g 3t.0 64.0 61.8

0.0 0,0 8.0 0.0 0.0 O.0 0.0 7.6

8.3 0.0 0.0 0.0 0.0 0.0 0.0 .!

wlnda

|,8 1.5 3.7 4!2 7.2 3.8 6.9

Figure E-18. Wind direction and speed measured at Haulover Canal bridge during

October 1992.

263
24 hour Wind Rose

Direction _ Speed

nov _992

0-1 2-0 6-15 i6-30 31-75 >75HIPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

rBnooa

O-t

6-1U

16_30

I1 of

total

J; of each d|r_ctton for hoorly averages I of

H H_ H_ E_£ ! ESE SE 99! 6 SSW SW ,8, , WNW NW N_ totl!

13.3 0.0 0_0 0.0 0.0 t.4 O.0 t.7 0.0 0.0 3.6 0.0 12.5 0.0 0.0 0.0 |.2

20.0 1.t 3.9 6.0 8.3 20.3 17.8 35.6 34.0 25.0 21.4 6.7 12.5 12.5 3|.5 16.5 t5.8

66.7 60.0 64.5 66.0 72.9 76.6 78.t 62.7 66.0 75.0 75.0 93.3 75.0 87.5 60.4 8t.5 73.0

0.0 |_.g _|.0 _.0 |0.0 1.4 _.| 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 |0.0

_:excludlngcelm .ln_e

3.9 /3.4 tt._ 7.4 7.1 t0.1 t0.O 0.6 7.0 t.2 4.0 2.2 1.0 1.2 2.9 6.0

Figure E-19. Wind direction and speed measured at Haulover Canal bridge during

November 1992.

264
v

24 hour Wind Rose

Direction @ Speed

dec 1992

0-! 2-5 8-i5 t6-30 3t-75 >75_PH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

SSW SSE

S

ranges

0-!

2-5

i8-30

Z of

total

Z of each direction for hourly averages Z of

N NNE NE ENE E ESE 8E SSE 8 8St_ 8W WSW t( MHH NW FINN total

8t.7 7.9 ||.8 42.9 3.3 0.0 0.0 8.7 0.0 |7.4 8.9 0.0 0.0 8.3 0.0 0.0 t0.8

t2.8 20.7 29.2 9.5 20,0 30.8 40.7 80.g 47.6 34.8 37.9 46.2 53.! 36.! t9.4 87.3 28.4

23.4 65._ 80.0 47.6 70.0 8g.2 59.3 30.4 52.4 47.8 55.2 53.8 40.6 50.0 75.0 72.7 57.8

2.i 8.2 0,0 0.0 5.7 0.0 0.0 0.0 0.0 0.0 0.0 0.0 6.3 5.8 5.6 0.0 3.!

excluding calm winds '

2.7 3J.8 i|.4 1.8 4.4 5.9 4.1 3.2 3.2 2.g 4.i 4.0 4.9 5.0 5.5 5,0

Figure E-20. Wind direction and speed measured at Haulover Canal bridge during

December 1992.

265
24 hour Wind Rose

Direction 6 Speed

jan 1993

0-! 2-5 6-15 t8-30 31-75 >75NPH

'1

N

NNW NNE

NW NE

WNW ENE

WSW ESE

sw S'E

266
w

24 hour Wind Rose

Direction _ Speed

feb 1993

O-I 2-5 6-55 t8-30 3|-7D >75MPH

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

Figure E-22. Wind direction and speed measured at Haulover Canal bridge during

February 1993.

267
2A hour Wind Rose

Direct ion & Speed

mar 1993

O-I 2-B 5-15 |8-30 3L-75 >7HHPH

, _

N

NNW NNE

NW NE

WNW ENE

WSW ESE

SW SE

Figure E-23. Wind direction and speed measured at Haulover Canal bridge during March

1993.

268
tit

24 hour Wind Rose

Direction & Speed

apr 1993

0-! 2-5 6-t5 t6-30 3t-75 >75NPH

N

NNW NNE

NW NE

I01

WNW ENE

W E

WSW ESE

SW SE

SSW SSE

S

I of each direction for hourly averages II of

ranges H NNE HE ENE [ ESE $E SgE 9 BSW SN IVSW M MNH NM Nl_l_ total

0-1 3.4 0.0 t.9 e.9 0.0 t.O 0.0 4,D ta.O 11,5 L4 0.0 0,0 I.I 0.0 0,0 i.8

a-5 3.4 |0._ 35.0 36,a 50,0 _t.4 3e.5 45._ Ot.? a_.O |I.9 1_.8 t3,| 28.l 30.5 88.7 _8.1

8-1._ E9.O 85.7 43.4 58.5 50.0 78.8 8t.B 4E.4 34.5 54.2 73.8 87.5 83.6 71.7 5@.7 33.3 84,6

J6-30 24.| 4,4 t8.9 4.3 0.0 0.0 t.9 |.8 0.0 8.3 lt.g 0.0 3.3 0.0 0.0 0.0 4.8

_IIof excluding calm winds ',

total 4.t 7.;_ 7,7 9.9 6._ 8.t 7.7 8.7 3.7 3.t 6,1 5.9 9.0 5.7 4.9 .9

Figure E-24. Wind direction and speed measured at Haulover Canal bridge during April

1993.

269
24 hour Wind Rose

Direction _ Speed

may 1993

0-! 2-5 6-t5 18-30 3|-75 >75/4PH

N

NNW NNE

NW NE

WNW ENE

W cd)mm 2..Z E

WSW ESE

SW SE

SSW SSE

S

roflgll!

O-I

8-t5

16-30

S of

tote1

Z of eech direction for hour']y overages X of

N NNE NE ENE E ESE SE SSE 9 SSW SH MSH H _NW NW NNM total

42.9 4.3 0.0 0.0 .O 1.2 2.0 11.ff 0.0 4.0 0.0 5.3 0.0 0.0 0,0 33.3 2.0

0.0 |7.4 2=J.9 |3.7 |3,3 |2oB 33.3 60.7 72.7 38.0 26.7 36.8 38.t 80.0 66.7 |8.7 28.8

57.! 70.3 70.4 86.3 83.9 88,0 64.7 27.g 27.3 60.0 73.3 57.9 63.9 50.0 33.3 80.0 70.2

0.0 0.0 3.7 0.0 0.0 0,0 0,0 0.0 0,0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 .|

excluding calm xtndo

.6 3.2 3.9 7.4 dT.0 23.5 14,5 7.8 1.8 3°8 4.4 2.6 8.2 2.3 to7 .6

Figure E-25. Wind direction and speed measured at Hauiover Canal bridge during May

1993.

270
Appendix F: Total Metals in Clams from Mosquito Lagoon

271
6OO

5OO

4OO

E 3OO

!

i i////j/.

fl/g//_,

_z?//..

_///..4

Y/2,;7._

Station

f1_Jl_#

/ff/[fl

F11_##I

/ff###/

ffffJff

_5

1.6

1.4

1.2

1

0.8

U 0.6

0.4

0.2

0

y/, # #jj_

Y//'JffJ/I

v Q,'//.4/__

/Ft..l/.

/..///,|

l- -f #/f #,,,'I

V. "I/JJ/_l

VJ/X/'//_I

vf/IL,_.4

Station

>'//7"//,

_//'//_

_////,b.

"_/_AY,4;:

_'///_

P///J/J

I//////,

Figure F-1. Concentrations of aluminum and cadmium in whole clams collected at the Mosquito

Lagoon surface water and sediment chemistry stations.

- 272
3.S I

I

2,5 t

°]1.5

,1= i

0

0.5

01

_/If/I/#

_1//ili

:::t/f_

lJJJfJJ

rfJf/_/

ffffff_

/jfjfjl

_JffJf_

4:11t/J

VIII/J/

FJfJl:ll

f J /Jf /Jl

:Jf]fiJt

1

*////2

/Jill/,

• :11_s,

v/Z///,

"/////_

//////,.,,;

ril///f /

i_r

2

::///,(/'/_

_//)'J/j/

VII/Ill.

///J]_ f,

3

Station

:_..-.,:...

• ,'L//:///

_'/'////-/

_,://///:

4 5

_'//////,

///I/I/_

.111111_

_///,_

VII/Ill

viii/I/,

I

16

14

12

10

i'

o

i

, f///J/_

V /./2"//I

/,,".,"/:'I"/

:,:/2"///:

///i'/I_

.wl,.'/IJl

"/////_

_'I :J:x,,

f/'L.,:li/

_d/zZZ

_//////

:J._l///

i i

2 4 :

i

:>'/////_

,f_/fl/, I

/Z/IJ/:

/ .,.:.if j:

#_ 111"

3

Station

;v'/////.

:////-///

./:/

ii:_ • , /_:.if11

_,_.//;I :-'_:;_

_;,_'//x'..4 ".........

"L :/.:I/..I

.-_9"///:_1

_,,y,._//:j ........

_?...I "Zl-"//_

<,:/:.,:.-n :,::/,/::/-/.

_//.,::1

•//,_//J.l

,:III/./:IA

..... _, ar

FigureF-2.Concentrationsofchromium and copperinwhole clamscollectedattheMosquito

Lagoon surfacewaterand sedimentchemistrystations.

273
700

6OO

5OO

400

_ 300

2OO

100

s';;,Z2

_"."/I//_

V//////

_//_

/l/Ill×

I/////_

"l#Ji[¢l

1 2

¢illlit

#¢#¢¢¢e

Viii.

:¢]1¢]_

rl/¢/1_

:¢#i##i

s_#¢mm.

V/I/I/.

ililiis

4 5

4

t3

0

#lilll

I¢:lt/t##l if

,,..,,.......... $(/) ///A

_///'.dXt ":)'32):)_4

.......... il, - i

r::i¢/.,i

;.*.,7"4_

_:!4z//2 $,)2 .....

i%.'//_

t

k'tl/,'A

#: ¢..'liJ/

z

./

/ : sl.

"..','.1tlit

3

_latlon

$'/7///1

_/./:,1

,'2;,/////,t

;;itlk';iA

/tlilil.4

i .s _!11.1

. iil:'/i

_./I.'/I1:1

;r,Y/._:_I

r., _::,,#A

,",:i,;'.,v"

:yl.._l :x'/:'<'l

"i "i:;,</lll

l,%.</:li, t

¢ls ,7/'.!

1 2 4

:ii/i/la

_///_

9$////1_:

v//J////,

N

,'#_%<,3 ,_

5

Figure F-3. Concentrations of iron and lead in whole clams collected at the Mosquito Lagoon

surface water and sediment chemistry stations.

274
|

B

6O

5O

4O

3O

2O

10

r====.=

i -1

i !

I

1

i

I

2 3 4

$tatton

m m

3.5

2.5

Z

1.5

0.5

J.-:_72'_

t k

1 2 3 4 5

Station

Figure F-4. Concentrations of manganese and nickel in whole clams collected at the Mosquito

Lagoon surface water and sediment chemistry stations.

275
1.8

1.6

1.4

1.2

v 1

0.8

0.6

0.4

0.2

0

1 2 3 4 5

Station

i

7O

60

50

10

0

1

40

i_ 30

. __:_

2 3 4 5

Station

Figure F-5. Concentrations of silver and zinc in whole clams collected at the Mosquito Lagoon

surface water and sediment chemistry stations.

276
w

Appendix G: Results From Impoundment Monitoring

277
_o

4-; 4D,

D.

Z

-i

10-

D

, /

" / i,..' ,,

',,i

so

# !

,, ---, jm°lt _ _,. W sm !

i.Ir

I # !

P I I

} I "

!

iI

i!

q P t!

I

i_i _ N _ill _ i .i. i i

I I I I I I I I I I I I I I"I I I I I I I I I I I I I I I I I I I I I I I I I

3 5 8 7 g O 1041121 2 3 4 5 0 7 e giDttl21 2 3 4 5 6 7 9 IIDIli2 t 2 3 4 5 8 11

MONTH

-I- WATER LEVEL -®- SALINITY

10

-8

-7 I-

.w

._1

-e LLI

I--

-2

-1

Figure G-1. Monthly water level and salinity measurements for Impoundment V-1 on the

east side of Mosquito Lagoon. Data were collected between 1990 and 1993.

278
45

36-

W

15"

lff

SO

45

-4O

MONTH

_ DI880LVED OXYGEN --+-- TEMPERATURE

Figure G-2. Monthly dissolved oxygen and temperature measurements for Impoundment

V-1 on the east side of Mosquito Lagoon. Data were collected between 1990 and 1993.

279
i

u

Z

-7

10-

O"

MONTH

-l- WATER LEVEL -®- SALINITY I

Figure G-3. Monthly water level and salinity measurements for Impoundment County

Lineon theeastsideofMosquitoLagoon.Datawerecollectedbetween1990and1993.

280
45

40-

,z

_! 15-

10"

5-

G

i g# u

t s _, ! i j

• • • " i g

_l t g

I T T • I ] J I I • 1 1 I I ! I I I I I T !

1 2 3 4 6 6 ? g 9 10 1t t_ 1 2 3 4 5 8 7 0 g 10

MONTH

--m- D.O. -._- TEMPERATURE I

45

-40

-35

-15

"10

"5

0

Figure G-4. Monthly dissolved oxygen and temperature measurements for Impoundment

County Line on the east side of Mosquito Lagoon. Data were collected between 1990

and 1993.

281
¢,m

LIJ

I3fl

t0-

s

&

5 _

_ DISSOLVED OXYGEN --+--TEMPERATURE

45

E

a

LLI

-15 _I

0

-10

m

O

-5

Figure G-5. Monthly water level and salinity measurements for Impoundment T-44 on

the east side of Mosquito Lagoon. Data were collected between 1990 and 1993.

282
4C

4O"

9GZ 2O"

"-i

1o,

5-

ii

/

if

a _

, ",, /, _

',t; i

IJ

I

# /

2

I_ I I I I I I I 1 I I I I ! .... _ I I t I I L I I t_ ,1I

MONTH

--_--- WATER LEVEL --+-- SALINITY I

4_

-4O

I::

d

I-.

-16 ,_

-10

-S

Figure G-6. Monthl3_ dissolved oxygen and temperature measurements for Impoundment

T-44 on the east side of Mosquito Lagoon. Data were collected between 1990 and 1993.

283
45

6"

4O35-

v

I.U

rr

2gt.U

1J.!

b--

1o45

:t ....... t:

MONTH

t "-_- DISSOLVED OXYGEN "-I-" TEMPERATURE I

_= "_

E

-3o Z

LU

0

ILl

O

O)

-10

m

Figure G-7. Monthly water level and salinity measurements for Impoundment T-38 on

the east side of Mosquito Lagoon, D at_awcr_c_llected between 1990 _d 1993.

284
45

4O35-

2Sin

t5-

10-

5-

0

!

; 4t

' I

I I •

I ! !

I ! !

I I !

j

! I

' I I

0 !

•" 0 I

t t

It !

SJ !

I! 1

I ! I

I I I

! I I

i I I!

g, • ! • t_ ; "!

-_ O-O-q d I I ! t _ l' I¢

t 1 / • i S I I ! I .. I t;

I I • L a _ 4 _ I •

I S I t f t I I I

I

I I I I I I I I I I I I I I I I

MONTH

I --!_- WATER LEVEL ---I-- SALINITY I

45

-4O

Z

-10

-S

0

Figure_G-8. Monthly dissolved oxygen and temperature measurements for Impoundment

T-38 on the east side of Mosquito Lagoon. Data were collected between 1990 and 1993.

285
Form Approved

REPORT DOCUMENTATION PAGE OMa 0 04-o18s

ill

Public reporting burden for this collection of information is estimated to average 1 hour per response, including the time for reviewing instruCtions, searching existing data sources,

gathering and maintaining the data needed, and completing and reviewmg the collection of information. Send comments recjardlng this burden estimate or any other aspect of this

collection of information, including suggestions for reducing this burden, to Washington Headquarters Services, Directorate tor Information Operations and Reports, 1215 Jefferson

Davis Highway, Suite !204, Arlington, VA 22202-4302, and to the Office of Management and Budget, Paperwork Reduction Pro eCt (0704°0188), Washington, OC 20503.

1. AGENCY USE ONLY (Leave blank) 2. REPORT DATE 3. REPORT TYPE

July 2001

4. TITLE AND SUBTITLE

Camaveral National Seashore Water Quality and Aquatic Resource Inventory

6. AUTHOR(S)

C.R. Hall, J.A. Provancha, D.M. Oddy, R.L. Lowers, and J.D. Drese

7. PERFORMING ORGANIZATION NAME(S)AND ADDRESS(ES)

Dynamac Corporation

Mail Code DYN-2

Kennedy Space Center, Florida 32899 "

9. SPONSORING/MONITORING AGENCY NAME(S) AND ADDRESS(ES)

NASA

Mail Code YA-D3

Kennedy Space Center, Florida 32899

AND DATES COVERED

5, FUNDING NUMBERS

8. PERFORMING ORGANIZATION

REPORT NUMBER

10. SPON SORING / MONITORING

AGENCY REPORT NUMBER

NASAfrM

11. SUPPLEMENTARY NOTES

Water quality, sediment chemistry, underwater irradiance measurements, submerged aquatic vegetation

distributions, meteorology, and fisheries

12a. DISTRIBUTION / AVAILABILITY STATEMENT 12b. DISTRIBUTION CODE

13. ABSTRACT (Maximum 200 words)

Mosquito Lagoon is a shallow, bar-built estuary located on the east central Florida Coast, primarily within 2

the KSC boundary. The lagoon and watershed cover approximately 327 km (79422 acres). The lagoon

occupies 159 km"(37853 acres). Water depths average approximately 1 m. The lagoon volume is

approximately 1.6x108m 3. Water quality in Mosquito Lagoon is good. Salinity data typically range

between 20 ppt and 35 ppt. The lowest value recorded was 4.5 ppt and the highest value was 37 ppt.

Water temperatures fluctuate 2-3°C over a 24 h period. Cold front passage can rapidly alter water

temperatures by 5-10°C or more in a short period 0ftime. The highest temperature was 33.4°C and the

lowest temperature was 8,8°C after a winter storm. Dissolved oxygen concentrations ranged from a low of

0.4 mg/l to a high of 15.3 mg/l. Extended periods of measurements below the Florida Department of

Environmental Protection criteria of 4.0 mg/l were observed in fall and spring months suggesting high

system respiration and oxygen demand. Metals such as antimony, arsenic, molybdenum and mercury were

report as below detection limits for all samples. Cadmium, copper, chromium, silver, and zinc were found

to be periodically above the Florida Department of Environmental Protection criteria for Class II and Class

III surface waters.

14. SUBJECT TERMS

17. SECURITY CLASSIFICATION 18. _;ECURITY CLASSIFICATION 19.

OF REPORT OF THIS PAGE

Unclassified Unclassified

NSN 7540-01-280-5500

SECURITY CLASSIFICATION

OF ABSTRACT

Unclassified

15. NUMBER OF PAGES

285

16. PRICE CODE

20. LIMITATION OF ABSTRACT

Standard Form 298 (Rev, 2-89)

Prescriio;_:l by ANSI Std Z3g-IR -

298-102