ENVIRONMENTAL STUDY OF TRINGAS CANAL
AND ASSOCIATED WETLANDS
ENVIRONMENTAL PROTECTION AGENCY
SURVEILLANCE AND ANALYSIS DIVISION
ATHENS, GEORGIA
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ENVIRONMENTAL STUDY OF TRINGAS CANAL
AND ASSOCIATED WETLANDS
JUNE 22-27, 1981
Environmental Protection Agency
Surveillance and Analysis Division
Athens, Georgia 30613
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TABLE OF CONTENTS
Page No.
LIST OF TABLES ii
LIST OF FIGURES iii
PROJECT PERSONNBL iv
INTRODUCTION ... 1
SUMMARY AND CONCLUSIONS . 1
STUDY AREA 2
SITE DESCRIPTION 2
STATION DESCRIPTIONS 3
TASK AND METHODS . . 4
RESULTS 5
HYDROGRAPHIC STUDIES 5
Depth Measurements 5
Tidal Dynamics 5
Ground Water Levels ... 6
Ground Water Chemistry . • 6
WATER QUALITY STUDIES 7
Dissolved Oxygen, Salinity and Temperature ... 7
Surface Water Chemistry 8
Water Column Primary Production
and Respiration . 7~. I . . 9
Sediment Particle Size 10
Benthic Macrolnvertebrates 11
Phytoplankton - Chlorophyll a 12
Bacteriological 12
VEGETATIVE CHARACTERIZATION 13
DISCUSSION 14
REFERENCES 16
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LIST OF TABLES
Table No. Description Page No.
1 Ground surface and ground water elevations ... 26
2 Water chemistry data (mg/L), Auger holes .... 27
3 Dissolved oxygen, salinity and temperature
observations, June 1981 28
4 Summary of dissolved oxygen, salinity and
temperature observations 40
5 Water chemistry data, surface water 41
6 Visible light transmission 42
7 Water column primary production and
respiration rates 43
8 Particle size of sediments at selected
study stations 44
9 Numerical abundance of macroinvertebrates
from study stations 45
10 Checklist of macroinvertebrates collected
by qualitative sampling 46
11 Phytoplankton - chlorophyll a concentrations
from study stations 47
12 Coliform bacteria data (#/l00 ml) 48
13 Species composition of vegetation along
transects 49
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LIST OF FIGURES
Figure No. Description Page No.
1 Project Location 17
2 Project Map . 18
3 Water Quality and Biological Station
Locations 19
4 Fathometer Trace - Canal 20
5 Fathometer Trace - Tidal Creek 21
6 Fathometer Trace - East Bay River 22
7 Water Level Trace - East Bay River 23
8 Auger Hole Locations 24
9 Dissolved Oxygen Profiles - Tidal
Creek, East Bay River and Canal 25
ill
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PROJECT PERSONNEL
Tom Cavinder - Engineer
Del Hicks - Biologist
Hoke Howard - Biologist
Jim Kopotic - Environmental Scientist
Phil Murphy - Biologist
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INTRODUCTION
At the request of the Jacksonville District Corps of Engineers,
the Surveillance and Analysis Division of the U.S. Environmental
Protection Agency, conducted a chemical, biological and hydrographic
investigation of the Tringas, Riverview Estates project during the
period of June 22-27, 1981. Litigation toward settlement of the
unpermitted activity is presently in progress. Technical informa-
tion gathered during the above study will be used as support to
the government's jfosition and final disposition of the case.
SUMMARY AND CONCLUSIONS
1. From June 22 through June 27, 1981, personnel of EPA's Sur-
veillance and Analysis Division conducted sampling to assess
environmental impacts associated with construction and develop-
ment of the Tringas project.
2. The project canal" was dug in a forested wetland featuring such
species as cypress, swamp bay, sweetbay, black gum, red maple,
and an understory consisting principally of wax myrtle, ferns,
swamp lily, and lizards tail.
3. Construction of the canal resulted in the replacement of an
ecological asset, the functioning wetland, with a dead-end
canal which provides for numerous adverse impacts to the East
Bay River and associated estuary.
4. The adverse impacts include:
o Dissolved oxygen concentrations which were persistently
below values established in Florida State Standards.
o Anoxic benthic environment with associated levels of
hydrogen sulfide.
o A canal bottom devoid of a benthic macroinvertebrate
community.
o The canal trapped and accumulated excessive quantities
of organic matter (detritus) which would otherwise
normally be transported to the East Bay River and down-
stream estuary for maintenance of detrital based food
chains.
o Low primary productivity relative to the destroyed
wetlands.
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5. Direct communication between ground waters and East Bay River
was confirmed by similarities in chloride and water surface
elevations.
6. Ground water levels throughout the unfilled portions of the
project average 0.5 feet below the land surface, confirming
the saturated conditions of the preproject forest floor.
7. Total coliform bacteria counts for river and canal stations
exceeded standards established by the State of Florida for
Class III waters. Highest counts were associated with canal
stations. Septic tanks are the current treatment mode for
domestic waste's originating with residential units in the
project area.
STUDY AREA
The Tringas project is located near Navarre, Florida approxi-
mately midway between Pensacola and Fort Walton Beach, Florida
(Figure 1). The East Bay River bisects the project into a northern
and southern tract. State Route 87 delineates the western boundary
of the tracts (Figure"2). A single reversed "L" shaped canal
provides water access to the interior lots of the southern tract.
A small unnamed tidal creek exists immediately east of the northern
tract.
SITE DESCRIPTION
The Tringas Canal is approximately 900 feet long, 40 feet
wide and ranges in depths of 4 to 5 feet along its center line.
Land elevations on the project site are less than 2 feet (National
Seodetic Vertical Datum - NGVD). A limited number of the lots
have been filled to a finished elevation of 2.5-3.5 feet NGVD and
are occupied by mobile homes. Access is provided by unimproved
sarthen roads whose elevation is similar to the filled lots,
/egetation of the unfilled and adjacent lands is predominantly
wetland species.
The tidal creek adjacent to the northern tract is a meander-
Lng water course with a width of approximately 20 feet and a
lepth of 3-4 feet. The creek banks feature wetland vegetation
similar to the southern tract.
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Both the "L" canal and the tidal creek tidally exchanged
with the East Bay River. The river at the project site varied in
width from 150-300 feet and varied -in depth from 8 to 17 feet. A
diurnal tide with a range of 1.5 feet allowed for exchange of the
brackish, tannin and lignin stained river waters with East Bay
and hence to the Gulf of Mexico.
STATION DESCRIPTIONS
^Water Quality and Biological)
Station locations shown on Figure 3 featured the following
characteristics:
o Station R-2 was located in the unnamed tidal creek
approximately 500 feet from creek confluence with East
Bay River. The creek channel was heavily shaded by a
dense canopy of black gum (Nyssa sylvatica, sweetbay
(Magnolia virginiana and cypress (Taxodium distichium).
Average depths were 3-4 feet. Bottom substrate was
comprised of medium sand with overlying layer of
vegetative material (sticks, leaf fragments). Good
visibility to bottom.
o Station R-3 was located in East Bay River approximately
200 feet west of Highway 87 bridge. Bottom depth
averaged 12-14 feet. No particle size data from this
station; however, it was assumed to be similar to East
Bay River, Station R-4. Shoreline vegetation observed
was sawgrass (Cladium jaimaicensis), arrowhead (Sagittaria
latifolia) and pennywort (Hydrocotyle) along the southern
shore with a forested swamp flanking the northern bank.
o Station R-4 was located in East Bay River approximately
100 ft upstream of canal mouth. Bottom depth average
approximately 12-14 feet. Main component of bottom
substrate was coarse sand (83%) with a small amount of
organic material (<1%). Forested swamp flanked both
shorelines (i.e. black gum, cypress, bay).
o Station R-5 was located in Tringas Canal, approximately
100 feet from mouth. Bottom depth averaged approximately
3 feet. Bottom substrate of sand with overlying layer
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of silt and organic material. Canal bank lined with
wax myrtle (Myrica cerifera), arrowhead (Sagittaria
(latifolia), pickerelweed (Pontederia lanceolata),
black gum and bay.
o Station R-6 was located in Tringas Canal, approximately
450 feet from canal mouth. Bottom depth averaged
approximately 4 feet. Bottom substrate largely com-
posed of organically enriched silt overlying a layer
of medium sand. Vegetation along canal edge similar
to R-5.
o Station R-7 was located in Tringas Canal, approximately
350 feet from canal dead end. Bottom depth averaged
approximately 4 feet. No bottom characterization was
determined since this station was discontinued after
the initial diel (D.O., temperature, salinity) run.
o Station R-8 was located in Tringas Canal, approximately
50 feet from dead end of waterway. Bottom depth
averaged approximately 3-4 feet. Bottom substrate was
predominantly silt (46%) and organic material in form
of sticks, leaves and bark in various stages of decom-
position .
TASK AND METHODS
The Tringas tracts and associated waterways were characterized
chemically, hydrographically, and biologically. Accordingly, the
methodology associated with each specific task are presented
immediately preceding the results of each effort.
Biological assessments included water column metabolism as
well as qualitative and quantitative sampling of the benthic
macroinvertebrate community. Hydrographic investigations con-
sisted of determining depth profiles and centerline depth contours,
tidal dynamics, and ground water elevations.
Water quality sampling occurred over a 27-hour period with
primary focus on dissolved oxygen, temperature, and salinity
measurements as well as slack and mid-tide water sample col-
lections for analyses of nutrients, TOC, chlorides, hydrogen
sulfide, and chlorophyll a.
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RESULTS
HYDROGRAPHIC STUDIES
Hydrographic investigations were conducted at the Tringas
"L" Canal, at the tidal creek, and in East Bay River (Figure 2).
The studies included depth measurements and tidal dynamics.
Ground water elevations were measured throughout the two tranto
Depth Measurements
Centerline depths as well as selected cross sectional depths
were produced from recording fathometer traces and reported in
Figures 4, 5 and 6. The Tringas Canal featured a fairly uniform
bottom contour with depths to 4 feet (Figure 4). The tidal creek
featured depths of 3-4 feet and was partially blocked with fallen
trees (Figure 5). Both of the above water courses open into the
East Bay River which featured an irregular bottom with centerline
depths which varied from 8 to 17 feet. Near the State Highway 87
crossing of the river, the centerline depths remained quite
variable as shown in Figure 6.
In terms of cross sectional dimensions, the "L" canal featured
very steep banks. In contrast, the East Bay River featured much
gentler bank slopes. Along the south shoreline of the canal, an
irregular berm appeared to have been created from spoil obtained
from the dredging of the canal.
Tidal Dynamics
A recording water level instrument was positioned near the
North Bank of East Bay River at a point adjacent to lot 2C (Figure
3). Diurnal tides were recorded and featured a tidal range of
1.5 feet (Figure 7). The National Ocean Survey (NOS) tide tables
indicated a mean tidal range of 1.6 feet for East Bay.
The irregular trace of water level changes suggests effects
of both wind and upland drainage. East Bay, featuring a relative-
ly shallow depth, is susceptible to changes in water levels due
to wind. Consequently, wind effects in the Bay would be reflected
in the East Bay River. The River is also subject to water level
changes due to runoff from its associated water shed. Storm
events with accompanying wind and rainfall frequently occurred
during the survey period.
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The tidal record was referenced to National Geodetic Vertical
Datum (NGVD) for correlation to ground surface and ground water
elevations. Water levels in East Bay River ranged from 0.1 to
2.1 feet NGVD.
Ground Water Levels
To assess ground water levels on the project tracts, 16
auger holes were installed (Figure 8). A 4" hand auger was used
to penetrate the ground surface to a depth of 1-2 feet below the
ground water leve}. Standard engineering leveling techniques
provided ground surface elevation at each auger hole and then
served to provide a reference for measurement of ground water
elevation relative to NGVD.
Ground water elevations were measured on 3 consecutive
Says. The unfilled lots featured land surface elevations on the
order of 1.6 feet NGVD with the ground water table 0.5 feet below
the land surface, hence placing the elevation of ground water
table at 1.1 feet NGVD (Table 1). Auger hole A-6 placed in a
filled lot had a land surface elevation of 3.71 feet NGVD with a
tfater table elevation of 1.27 feet NGVD (ground water was 2.44
feet below land surface). Filled lots are referenced in Figure 8.
As discussed in the tidal dynamics section, the water level
Ln East Bay ranged from 0.1 to 2.1 feet NGVD. An average of
these two extremes is 1.1 feet NGVD which was the elevation of
the ground water table throughout the project tracts.
3round Water Chemistry
Grab samples of ground water were collected on June 25 and
26 from auger holes A-2, A-4, and A-5 (Figure 8) for chemical
inalyses. As indicated (Table 2), averages for TOC concentrations
ire not completed at this time. No attempt was made to determine
changes in ground water elevations relative to tides.
Elevated nutrient levels on the groundwater with respect to
mrface waters reflect the nutrient enriched forest floor.
Chloride levels in the groundwater were similar to those in the
!ast Bay River and the Tringas Canal thus indicating the communi-
:ation of groundwaters with the ambient surface waters.
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WATER QUALITY STUDIES
Water quality studies were conducted at stations shown on
Figure 3. The studies included (1) diel monitoring of dissolved
oxygen, salinity and temperature, (2) sampling and analysis to
characterize water chemistry and microbiology, (3) characteriza-
tion of sediment quality and particle size, (4) characterization
of the benthic macroinvertebrate community, (5) measurements of
chlorophyll a, and (6) measurements of water column primary
productivity.
Dissolved Oxygen, Salinity and Temperature
Measurements of dissolved oxygen, salinity and temperature
(DST) were conducted at 3-hour intervals over a 27-hour period.
The period commenced at 1210 hours on June 24, 1981 and terminated
at 1620 hours on June 25, 1981. Dissolved oxygen concentrations
were determined with a YSI model 57 probe which was calibrated
via the Winkler titration method at the beginning and end of each
3-hour sampling interval. Simultaneously with the D.O. measure-
ments, a Beckman model RS5-3 salinometer was employed to measure
temperature and salinity. Depending on water depth, vertical
profiles of DST measurements were made at 1 or 2 foot increments
from surface to bottom.
A relatively wide range in values occurred among the parameters
measured (Tables 3 and 4). In terms of low dissolved oxygen
concentrations, Stations R-6 and R-8 yielded dissolved oxygen
concentrations which averaged less than 4 mg/L. In the case of
Station 8, dead-end of canal, dissolved oxygen concentrations at
depths of 3 feet or greater never attained concentrations above 4
mg/L and at times approached an anoxic condition. Dissolved
oxygen concentrations below 4 mg/L fail to meet standards established
by the State of Florida. Figure 9 illustrates the strongly
stratified condition of the DO regimen at Station 8.
The severity of the DO depression appeared somewhat reduced
at Station 6, a mid-canal location; however, substandard IX)
concentrations were persistent features of the water near the
bottom (Table 3).
At the mouth of the canal, Station R-5, a marked improvement
in the DO regimen occurred. Although an occasional substandard
concentration was observed near the bottom, the water column
featured dissolved oxygen concentrations and saturation levels
similar to a nearby station (R-4) in the East River (Table 4).
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Dissolved oxygen concentrations observed in the tidal creek
(Station R-2) ranged from 5.1 to 7.6 mg/L and averaged 6.1 mg/L
during the diel study period. The DO regimen observed for the
stations on the East River averaged 5.4 and 6.1 mg/L (R-3 and R-
4, respectively). At Station R-3, which was the downstream
location nearest the estuary, dissolved oxygen concentrations as
low as 1.7 mg/L were recorded for waters exceeding depths of 8
feet. Although the concentrations were below State standards,
the low levels only persisted during a period of high tide on
June 25 from 1005,to 1620 hrs (Table 3 and Figure 7). During the
same time interval, the bottom water also increased in salinity
which suggests the intrusion of higher saline water from areas
downstream of the study area.
As indicated above, tidal penetration into the study area
was clearly evident. Salinity measurements at Station R-8 indi-
cated that tidal effects extended to the dead-end area of the
canal where saline water tended to be concentrated. As shown in
Table 3, bottom salinities of Station R-8 ranged from 1 to 5 ppt
and averaged 3.1 ppt. In contrast, the nearby river station (R-
4) featured bottom salinities which ranged from 0.0 to 4.3 but
averaged 0.7 ppt. The reading of 4.3 ppt appeared as an anomaly
in the data set because all other readings made over the 27-hour
period ranged from 0.0 to 0.5 ppt for Station R-4. Possibly, the
4.3 ppt observation reflects a pocket of higher saline water. As
3hown in Figure 6, the East River featured a very irregular
Dottorn contour in the area of study.
Surface Water Chemistry
At periods of slack high and low water, water samples for
:hemical analysis were obtained with a horizontal Van Dorn sampler,
tn cases where the water column was fully mixed in terms of
iissolved oxygen concentrations and salinity, samples were taken
it mid-depth. When the water column was subject to marked strati-
fication, as the case with Station R-8, samples of each strata
fere obtained. All samples received appropriate preservation and
'ere returned to the Athens Laboratory for analyses which included
leterminations for TKN, NH3, NO2-NO3, total phosphorus (T-P),
:hlorides (CI), and hydrogen sulfide (H2S). The latter parameter
H2S) required a special sampling and preservation procedure. For
his purpose, a 6 mm ID piece of tygon tubing leading from an
svacuation flask was connected to the Van Dorn sampler. With
ach sample, the evacuation flask first received 2 ml of zinc
cetate preservative. Next, the flask and tubing were purged
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with nitrogen gas. With the Van Dorn sampler deployed to the
desired depth, a vacuum was placed on the flask system and a
discrete water sample obtained and preserved under an oxygen-
free atmosphere.
As expected, the chloride values correlate with the salinity
determinations made with the salinometer (Table 5). The chloride
values for the stations positioned along the Tringas Canal support
the previous discussions that the waterway tends to trap saline
water.
The listed concentrations for hydrogen sulfide reveal that
the only discernible level occurred near the bottom at the dead-
end station on the canal. The presence of H2S is only possible
in an anaerobic environment. Anaerobic conditions could be
anticipated on the basis of the low D.O. readings reported for
Station R-8. For example, D.O. values near the bottom of Station
8 attained a low of 0.2 mg/L in the late morning hours (Table 3).
The concentrations reported for total phosphorus appeared similar
and normal for all stations sampled. Ammonia levels at Station
R-8 (dead-end area of canal) appeared slightly elevated compared
to other locations but similar to ground water concentrations
(Table 2). Like hydrogen sulfide, ammonia is produced by bacterial
action under anaerobic conditions.
Water Column Primary Production and Respiration
Light-dark bottle techniques were used to measure primary
production and respiration of the water column in the canal,
river, and tidal creek (Stations R-2, R-4, R-5, R-6 and R-8).
Techniques followed were those generally outlined in Standard
Methods, 14th Edition. Three sets, composed of two light and two
dark bottles per set, were placed at variable depths at the above
stations and incubated between 5 and 7 hours. All bottles for
each specific depth were filled with water collected from that
depth with a horizontal van Dorn water sampler. The same water
from each respective depth was used for replicate determination
of initial D.O. concentration at that depth. Prior to initiation
of each experiment, light extinction through the water column was
determined with a submarine photometer. Percent transmission of
light values were used as a basis for bottle depth placement.
The percent transmission data shows that relative to depth
the extent of visible light penetration is about equal for all
stations except for the tidal creek (Table 6). Light penetra-
tion was significantly better in the creek with nearly 50 percent
of the available light reaching the bottom.
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As shown in Table 7, no net production occurred at any
station. Net primary production only results when the value for
gross primary productivity exceeds the rate of respiration. In
all cases, respiration exceeded gross production thus indicating
the heterotrophic nature of the aquatic system. Under these
circumstances, allochthonous inputs of organic carbon originate
from other sources than the primary productivity of the water
column. Such sources could be assigned to the wetlands associated
with the project and riverine system.
Sediment Particle Size
Bottom sediment cores (top 10 cm) were taken at all stations,
except R-3, with a 2-inch coring tube by SCUBA divers. Sediment
analysis was by the modified Wentworth method (EPA, 1973).
Results of sediment sizing analyses show a progressive in-
crease in a finer bottom composition toward the canal head (Table
8). For example, canal stations R-6 and R-8 are characterized by
an inorganic bottom substrate composed predominantly of particle
sizes representative of silt, clay and medium sand. The organic
fractions at stations R-6 and R-8 were also similar with the
medium sand and silt size classes carrying the greatest organic
content. Divers noted the unconsolidated nature of the sediments
and observed that the finely divided benthic substrate measured
approximately 3 feet in depth.
In contrast to canal stations R-6 and R-8, the river station
(R-4), unnamed tidal creek station (R-2), and canal station R-5
featured coarser sized substrate material, similar to dimensions
associated with medium sand particles (Table 8). At stations R-2
and R-5, the layer of loosely consolidated material measured about
I inches and 2 feet, respectively. The river station, R-4, featured
a firm bottom composed mostly of coarse sand. Another striking
difference between R-4 and the other study stations was the low
organic fraction observed. Station R-4 had a total organic fraction
3f only 0.8%, while all other study stations ranged from 23.2 to
30.6%. The river channel at station R-4 appeared well-scoured
-hus allowing little accumulation of finer sediments.
Similarities observed between stations R-2 and R-5 can best
3e explained by their locations. Canal station R-5 is approxi-
nately 100 feet (Fig. 3) from the river thus receiving some
benefits of flushing and allowing less settlement of finer sedi-
nents. Station R-2, located in the unnamed tidal creek, was a
latural artery for wetland drainage and was strongly affected by
-he rise and fall of the tide.
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Benthic Macroinvertebrates
Benthic macroinvertebrates were collected by qualitative
sampling utilizing SCUBA divers, hand-sorting from submerged
vegetation and logs and collection with biological dip nets. In
addition, quantitative samples (6 replicates) were collected with
4 inch PVC coring tubes by divers.
Quantitative macroinvertebrate data revealed the most diverse
station to be R-2/ the tidal creek (Table 9). The river station,
R-4, was represented by only 3 taxa. The paucity of taxa at
station R-4 can probably be attributed to substrate character-
istics of the river channel. A review of substrate particle size
data (Table 8) reveals the presence of a much coarser substrate
(coarse sand) at R-4 than other study stations. A shifting sand
bottom is known to be a poor habitat for macroinvertebrates
(Hynes, 1970). Quantitative macroinvertebrate samples from the
canal stations (R-5 and R-8) were devoid of macroinvertebrate
organisms. Past studies in dead-end tidal canal systems (Hicks,
et al., 1975; EPA, 1975; and Yokel, 1979) have revealed the
paucity of benthic organisms in the study canals to be related to
the organic, finely divided sediments that accumulate in poorly
flushed canals. The Tringas Canal, though only 3-4 feet in water
depth, was characterized by an extensive layer of finely divided
organic material. Dissolved oxygen and salinity stratification
in the canal indicate poor vertical mixing, particularly at the
dead-end area. As a result, the bottom sediments at the head of
the canal (Station R-8 have become depleted of dissolved oxygen
and contaminated with an elevated concentration of hydrogen
sulfide, a by-product of anaerobic respiration and toxic to
aquatic life.
Qualitative macroinvertebrate collections, which entailed
mainly shoreline searches, revealed diverse communities at stations
R-2 and R-4. Seventeen taxa were present at both R-2 and R-4
(Table 10) while stations R-5 and R-8 were represented by 6 and 0
taxa, respectively. The shoreline of the river and tidal creek
provided a shallow and varied habitat for benthic macroinvertebrates.
Rooted, emergent vegetation, tree roots and submerged logs and
the shore edge provided ample habitats as can be seen in the
liverse assemblage of organisms (Table 10? Stations R—2 and R—4).
Hie close proximity of the river to canal station R—5 to the
"iver probably explains the improved diversity of species collected
Hong the shore relative to the dead-end area (Station R-8).
Adequate mixing and exchange with the river system aid in the
establishment of a benthic invertebrate community along the shore
>f R-5; however, the bottom habitat remained devoid of macroinverte-
>rates. Water quality perturbations and the extensive accumulation
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of finely divided sediments precluded the establishment of a
benthic community at the canal deadend (R-8) where no benthic
organisms were found in either qualitative or quantitative samples.
Phytoplankton - Chlorophyll a
Phytoplankton-chlorophyll a sampling coincided with collection
of samples for water chemistry. Samples were collected at a depth
of one foot and then filtered, frozen and returned to the EPA lab
in Athens for analyses.
Phytoplankton-chlorophyll a concentrations followed a pro-
gressive increase along the length of the Tringas Canal (Table
11) wi t.h peak levels of chlorophyll found at the canal's dead-end
station (R-8T.—Rt~SnEaTiOn K-ar7~€fie~average concentration for the
two sampling periods was 10.65 mg/m^ whereas river stations R-3
and R-4 yielded a mean chlorophyll a^ concentrations of 0.47 and
0.45 mg/m^ respectively.
Chlorophyll a concentrations provide a relative measure of
phytoplankton biomass and bloom conditions# Although the chloro-
phyll a values reported do not indicate bloom conditions, the
apparent growth of phytoplankton in the canal system possibly re-
flected associated increases in nutrient concentrations as suggested
in Table 5. For example# increases in total inorganic nitrogen
(NH3 plus NO0-NO3) correlated with chlorophyll a values for the
canal stations. Such a relationship would be possible ®*nc®
septic tank drainage to the canal is expected to occur based on
other studies involving the placement of septic tanks in shallow
ground water areas (Hicks, et al., 1975 and EPA and N.C. Dept. of
Natural and Economic Resources, 1975). With further development
of the property adjacent to the canal and installation of septic
tanks, future blooms of algae of nuisance proportion would appear
possible for the dead-end waterway.
Bacteriological
Grab samples were collected at stations R-2 through R-8 and
analyzed for ?otal and fecal coliform baeter:la. ,
obtained from the one foot depth on 6/24 and and were trans-
ported to the State of Florida J"'*™"Shi?IT
Utlon (PL-DER) laboratory in pensacola for analyses.
presents the results of these efforts.
Florida Class III waters, suitable for ^creation and propaga-
tion and management of fish and wildlJfe' 5able 12 stations
=oliform limit of 2,400 per 100 ml. As seen from Table 12,
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R-3, R-4, R-6, R-7 and R-8 exceeded this standard during the
sampling period. Stations R-6, R-7 and R-8 located on the long
arm of the reverse "L" canal exhibited the highest coliform bacteria
levels. In contrast, station R-2 located in the unnamed tidal
creek did not exceed standards. Stations R—3 and R—4 located in
East Bay River exceeded standards.
Coliform bacteria sources to the canal waters can be identi-
fied with the septic tank/drainfields employed on the developed
lots (Figure 8). The relatively low bacterial counts associated
with the tidal crefek suggest that runoff from the forested swamp
is not the prime source of coliform bacteria. High ground water
levels as previously demonstrated preclude effective bacteria
removal of septic tank effluent by percolation via the draintiles.
VEGETATIVE CHARACTERIZATION
The Tringas property (Riverview Estates) was characterized
in terms of vegetational types by listing plant species observed
along 7 selected survey lines on the subject property (Fig. 3). A
key to wetland types," found in the Preliminary Guide to Wetlands
of the Gulf Coastal Plain (USCOE Tech. Rept. Y-78-5), was utilized,
and as a result the Tringas property falls into the category of
"freshwater swamp."
The definition of a freshwater swamp, according to technical
report Y-78-5, is wetlands that have more than 40 percent cover
by woody plants and are occasionally or regularly flooded by fresh
water. The predominant species present on the Tringas property
were wetland species which included red maple (Acer rubrum),
buttonbush (Cephalanthus occidentalis), holly (Ilex sp.), sweetbay
(Maqnolia virginiana), black gum (t£££sa sylvatica), cypress
(Taxodium distichium), wax myrtle (Myricacerifera) and swamp bay
(Persea p'alustris). Common understory species present were the
cinnamon fern (Osmunda cinnamonea), royal fern (Osmunda regalis),
swamp lily (Crinum americanum), sea lavender (Limonium carolinianum),
lizard's tail (Saururus cernuus), saw palmetto (Serenoa repens)"
false nettle (Bnehemeria cylindrical, and goldenrod (Solidago).
Many of these species appear in technical report Y-78-5 as dominant
and associated species of a freshwater swamp.
A complete listing of plant species observed along each
survey line is given in Table 13.
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DISCUSSION
As shown by the vegetational survey, the Tringas Canal was
escavated in a forested wetland. Furthermore, results of this
study demonstrate the environmental consequences of such an action.
Environmental impacts associated with the dredging of the canal
and related filling of wetlands can be examined and assessed in a
variety of environmental terms.
To date, the Tringas project has resulted in the direct
destruction of approximately 4.2 acres of wetlands. Such losses
also effect a proportional reduction in the special benefits
traditionally derived from wetlands. For example, forested wet-
lands provide habitat and food for a diverse community of terrestrial
and aquatic life. Via net primary production, the wetland forest
and associated herbaceous plants also maintain a continual source
of plant matter, which is exported from the swamp as detritus and
delivered to the estuary. There, the material serves as the
energy basis for numerous detrital based food webs that sustain
the growth and development of valuable sport and commercial species
of fish and shellfish". The canal failed to mitigate the loss in
net primary production and estuarine support. As shown by the
results of the light-dark bottle work, the canal waters yielded no
net primary production. Instead, the canal consumed via respira-
tion more organic matter than it produced.
The reduction in detrital export to the estuary, however, is
greater than can be directly attributed to just the loss of 4.2
acres of forested wetlands. As shown by sediment data (Table 8)
and diver observations, the Tringas Canal effectively traps organic
matter. Furthermore, via groundwater sampling and the measurement
• 4-uj. wuv*mv* vr - — — ~ _ - - ,
o-f l^nri surface elevations, surface and subsurface drainage pro-
river rather than providing for the excessive accumulation of organic
Thus, detritus originating with the
matter as sediments.
-14-
-------
The trapping effects of dead-end tidal canal systems are well
known and have been demonstrated by the results of several other
studies (Hicks, et al., 1975; EPA, 1975? and Hicks, 1979). Further-
more, these same studies have also demonstrated that the trapping
effects are related to poor flushing dynamics, relative to natural
tidal waterways.
The excessive accumulation of finely divided matter as sedi-
ments also had an adverse impact of the quality of benthic life
associated with the bottom of the canal. For example, no benthic
macroinvertebrates/ were found living in the bottom sediments of
the canal. In contrast, the unnamed tidal creek provided a benthic
habitat suitable for a wide variety ofbenthic macroinvertebrates,
many of which are viewed as valuable fish food items. The only
benthic macroinvertebrates observed in the canal were associated
with underwater debris such as dead limbs and the root systems of
emergent macrophytes along the shoreline (Table 10).
inflow of organic matter to the canal from adjacent
wetlands and its accumulation as sediment also imposed a bio-
chemical demand on the dissolved oxygen resources of the system.
The demand was created and sustained by the microbial decomposition
of the organic matter as discussed below.
Detritus can be defined as dead plant matter in various
stages of fractionation and decomposition. During the decomposition
process, aerobic bacteria and other microscopic animals colonize
the surface of the plant particles. As the organic carbon of the
material is assimilated, the microbes "spirecarbondioxide
consume dissolved oxvgen, and accumulate protein as body matter.
s e dissolve yg matter into smaller particles with
This process reduces the m*^®itional quality of the material,
a corresponding increase in t*®gnlg the intr}nsic value of detritus
is nutrient enrichme;ne animals. Under anaerobic conditions,
as a food source for ef^i^3simiiar except that specialized
e decomposition proc oxvqen such as combined in nitrogen
an ST,1; USe ^rS^rSlSSnsST- nitrite-nitrate
-------
As discussed earlier, an extensive build-up of organic matter
occurred on the bottom of the canal, with the greatest accumulation
found at the dead-end region. The decomposition processes associated
with the organically enriched bottom sustained a dissolved oxygen
demand which exceeded the DO resources of the canal. Inadequate
exchange between the canal and the river coupled with vertical
stratification of the water column restricted the replenishment of
dissolved oxygen which was used in the decomposition process.
Incomplete mixing of the water column precluded the full benefit
of atmospheric reaeration. Poor water exchange between the canal
and river limited the recruitment of oxygenated water from the
riverine system. Thus, substandard D.O. concentration characterized
much of the canal system. In contrast, the tidal creek and river
successfully coped with the oxygen demands of the organic load
from the swamp drainage and subsequently provide an aquatic system
with few environmental liabilities.
REFERENCES
Hicks, Delbert B. 1979. Appendix D - Water quality. Naples Bay
Study. The Collier County Conservancy.
Hicks, Delbert B., T. R. Cavinder, B. J. Carroll, R. L. Raschke
and P. J. Murphy. 1975. Finger-fill canal studies. Florida
and North Carolina. U. S. Environmental Protection Agency,
Region IV, Athens, Georgia (EPA-904/9-76-017).
Hynes, H. B. N. 1970. The Ecology of Running Waters. Liverpool
University Press. 555 pp.
U. S. Environmental Protection Agency. 1975. An evaluation of
physical, chemical and biological aspects of canals and
associated waterways at Marco Island, Florida. Surveillance
and Analysis Division, Region IV, Athens, Georgia.
U. S. Environment^") Protection Agency and N. C. Department of
Natural and Economic Resources. 1975. Waste source and
water quality studies. Surf City, North Carolina and vicinity.
Yokel, Bernard J. 1975. Appendix E - Biology. Naples Bay Study.
The Collier County Conservancy.
-16-
-------
FIGURE ±
/>Ao7£cr LOCAt'OAS
17-
-------
f/GURE 2
AiveR\/i£w £$mres
-18-
-------
F/GURE 3
AlveRV/EW ssmres
SAMPLING LOCATIONS
JUNE 1981
{—
H
3A
- « ! 5/1
__
I
® ^ Sfq-f)0ns
-19-
-------
Z**K
I
to
o
(Sari 0
R-6
canal
R'S Srib
J/ 1
TT-rrrr; n > r > iT~r-rr-r-i
/s/otZ-fH ~?t> 5 e> vjt H 'i&c+ior* //V £~A*>t R i v£ £.
THC
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O too zoo 3oo
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C>IS>/AMC£ - ^e«.T (AfffoK)
-------
FIGURE 7
WATER LEVEL TRACE
EAST BAY RIVER @ HWY. 87
JUNE 1981
Q
>
i
O
K
u
12 IB
*-23-8)
DFtTG " r,W 2
-23-
-------
f/QURE s
/Zt\J£R\l/EW ESTATES
AUGER HOLE LOCATIONS
JUNE 1981
u
2A
3A
. ti
5A
6A
. M
// Filled or partially filled
lots
• A-1 Auger holes - ground
water samples
-24-
-------
Figure 9
Dissolved Oxygen
Profile
June 1981
i s >
— fKl
USls
rTTi
«ii
r it r
'111 X *Vl'
• • • • I
QC
vs
-------
TABLE 1
AUGER HOLES
LAND SURFACE AND GROUND WATER ELEVATIONS (NGVD)
JUNE 1981
Avg. DIs-
Land
Ground
Ground
Ground
Avg. Ground
tance Below
Surface
Water
Water
Water
Water
Land
Station
Elev.
Date
Time
Elev.
Date
Time
Elev.
Date
Time
Elev.
Elevation
Surface
A-l
1.63
6/24
0845
1.15
6/25
1120
1.11
6/26
0815
1.07
1.11
0.52
A-2
1.77
6/24
0850
1.25
6/25
1328
1.17
6/26
0822
1,06
1.16
0.61
A-3
1.54
6/24
0855
1.21
6/25
1325
1.14
6/26
0830
1.04
1.13
0.41
A-4
1.50
6/24
0907
1.12
6/25
1345
1.04
6/26
0845
0.98
1.05
0.45
A-5
1.49
6/24
0910
1.20
6/25
1355
1.14
6/26
0855
1.03
1.12
0.37
A-6
3.71
6/24
0913
1.29
6/25
1402
1.23
6/26
0910
1.29
1.27
2.44
A-7
1.52
6/24
0915
1.14
6/25
1405
1.06
6/26
0920
0.94
1.05
0.47
A-8
1.53
6/24
0918
1.26
6/25
4107
1.20
6/26
0925
1.11
1.19
0.34
A-9
1.42
6/24
0922
1.40
6/25
1409
1.38
6/26
0927
1.29
1.36
0.06
A-10
1.51
6/24
0927
1.18
6/25
1423
1.05
6/26
1012
0.95
1.06
0.45
A-ll
1.73
6/25
1412
0.98
6/26
1045
0.98
0.98
0.75
A-12
1.62
6/25
1414
0.93
6/26
1035
0.97
0.95
0.67
A-13
1.57
6/25
1418
0.84
6/26
1025
0.84
0.84
0.73
A-14
1.69
6/25
1421
1.20
6/26
1015
1.18
1.19
0.45
A-15
1.79
6/25
1320
1.46
6/26
0835
1.37
1.42
0.37
A-16
1.97
6/25
1323
1.66
6/28
0840
1.59
1.63
0.34
-------
TABLE 2. WATER CHEMISTRY DATA (mg/L), AUGER HOLES, JUNE 1981.
S&A
Date
Time
CL
h2s
TKN
nh3
NO2-NO3
T-P
TOC
\-2
6/25
6/26
1330
0825
553
776
<0.2
<0.2
0.75
0.80
0.15
0.10
<0.05
<0.05
0.46
0.35
\-4
6/25
6/26
1345
0845
744
749
<0.2
8.0
1.55
2.40
0.55
1.50
<0.05
<0.05
0.60
0.39
K-5
6/25
6/26
1400
0900
1329
1542
<0.2
<0.2
0.96
0.88
0.15
0.15
<0.05
<0.05
0.33
0.27
-27-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981 R-2
FEET
oC
o/oo
mg/1
STATION
DATE
TIME
DEPTH
TEMP.
SALINITY
DO
R-2
6/24/81
1210
Surf.
21.5
-
5.6
3
5.6
5 (bott)
21.5
5.6
R-2
6/24/81
1620
Surf.
25.5
0.1
6.1
1
25.5
0.1
6.1
2
25.5
0.1
6.1
3
25.4
0.1
6.1
3.5 (bott)
25.4
0.1
6.2
R-2
6/24/81
1907
S
23.2
0.0
6.5
1
22.9
0.0
6.6
2
22.7
0.0
6.7
2.5
22.7
0.0
6.7
R-2
6/24/81
2154
S
22.1
0.1
5.8
1
22.1
0.1
5.9
2
22.1
0.1
5.9
2.5
22.0
0.1
5.9
R-2
6/25/81
0030
S
21.8
0.1
5.8
1
21.8
0.1
5.8
2
21.8
0.1
5.8
2.5
21.8
0.1
5.8
R-2
6/25/81
0322
S
21.3
0.1
5.5
1
21.2
0.1
5.4
2
21.2
0.1
5.4
R-2
6/25/81
0655
S
21.4
0.15
5.4
1
21.4
0.15
5.2
2
21.5
0.15
5.2
2.5
21.4
0.15
5.2
1-2
6/25/81
0945
S
21.8
0.13
5.3
1
22.1
0.1
5.2
2
21.7
0.1
5.1
2.5
21.9
0.1
5.1
-2
6/25/81
1330
S
23.7
0.0
7.0
1
23.7
0.0
7.1
2
23.4
0.0
7.1
3
23.4
0.1
7.1
-2
6/25/81
1610
S
24.6
0.08
7.5
1
24.4
0.08
7.6
2
24.3
0.08
7.6
3
24.5
0.1
7.5
-28-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-3
STATION
DATE
TIME
FEET
DEPTH
oC
TEMP.
o/oo
SALINITY
mg/1
DO
R-3
6/24/81 1250
R-3
6/24/81 1630
R-3
6/24/81 1915
6/24/81 2142
6/25/81 0020
(bott)
(bott)
5
2
4
6
8
10
12
14
5
2
4
6
8
10
12
14
16
5
2
4
6
8
10
12 (bott)
5
2
4
6
8
10
11 (bott)
5
2
4
6
8
10
11 (bott)
26.2
26.0
25.1
25.0
25.0
25.0
25.0
25.0
26.8
26.8
26.0
25.7
25.7
25.7
25.7
26.0
26.0
25.8
25.7
25.5
25.5
25.5
25.5
25.5
25.3
25.3
25.3
25.3
25.3
25.3
25.2
24.8
25.0
25.0
25.0
25.0
25.0
24.8
0.20
0.20
0.20
0.30
0.40
0.40
0.40
0.90
1.00
0.10
0.10
0.10
0.00
0.00
0.10
0.10
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
6.0
6.0
6.0
5.9
5.9
5.9
5.8
5.6
5.9
5.9
5.9
5.8
5.7
5.7
5.6
5.3
5.0
5.9
5.9
6.0
6.0
6.0
6.0
6.0
6.0
6.1
6.1
6.1
6.1
6.1
6.1
6.3
6.3
6.3
6.3
6.3
6.3
6.3
-29-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-3
STATION DATE TIME
R-3 6/25/81 0312
R-3 6/25/81 '0705
R-3 6/25/81 1005
R-3 6/25/81 1335
R-3 6/25/81 1620
FEET
oC
o/oo
mg/1
DEPTH
TEMP.
SALINITY
DO
S
24.7
0.1
6.1
2
24.7
0.1
6.1
4
24.7
0.1
6.1
6
24.8
0.1
6.1
8
24.8
0.1
6.1
10 (bott)
24.8
0.1
6.0
S
24.5
0.0
6.0
2
24.6
0.0
6.1
4
24.6
0.1
6.1
6
24.5
0.1
6.0
8
24.6
0.1
6.0
10
25.0
0.9
5.4
12 (bott)
25.9
3.6
3.4
S
26.2
0.1
6.2
2
25.8
0.1
6.0
4
24.8
0.1
6.0
6
25.0
0.2
5.7
8
27.0
3.6
3.4
10
27.5
4.8
2.4
12
27.8
5.2
2.1
14
27.8
5.1
2.1
S
28.2
0.1
6.1
2
25.7
0.1
6.0
4
25.2
0.1
6.0
6
25.1
0.2
5.8
8
27.6
5.0
2.5
10
28.4
6.0
2.0
12 (bott)
28.5
6.1
2.0
S
28.9
0.0
6.2
2
26.4
0.0
6.3
4
25.3
0.1
6.2
6
25.6
1.5
5.7
8
28.4
5.5
2.1
10
28.6
6.4
J.8
12 (bott)
28.6
6.4
1./
-30-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-4
STATION DATE TIME
R-4 6/24/81 1225
R-4 6/24/8i 1602
R-4 6/24/81 1858
R-4 6/24/81 2130
R-4 6/25/81 0012
oC o/oo mg/1
TEMP. SALINITY DO
26.0 6.2
25.5 6.2
25.0 6.2
25.0 6.2
25.0 6.2
25.0 6.1
25.0 6.0
25.0 6.0
26.1 0.2 6.3
25.8 0.2 6.2
25.7 0.2 6.2
25.7 0.2 6.2
25.5 0.2 6.2
25.5 0.2 6.2
25.4 0.2 6.1
25.3 0.2 5.9
25.8 0.1 6.0
25.8 0.1 6.0
25.8 0.1 6.0
25.9 0.1 6.1
25.7 0.1 6.1
25.6 0.2 6.0
25.7 0.2 5.9
25.6 0.5 5.5
25.2 -0- 6.4
25.2 -0- 6.2
25.2 -0- 6.2
25.2 -0- 6.2
25.2 0.1 6.1
25.2 0.1 6.1
25.3 0.1 6.1
24.9 -0- 6.3
24.9 -0- 6.3
24.9 -0- 6.3
24.9 -0- 6.3
25.0 0.1 6.3
25.0 0.1 6.3
25.0 0.1 6.3
FEET
DEPTH
S
2
4
6
8
10
12
14 (bott)
S
2
4
6
8
10
12
14
S
2
4
6
8
10
12
14 (bott)
S
2
4
6
8
10
12 (bott)
S
2
4
6
8
10
II (bott)
-31-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-A
STATION DATE TIME
R-4 6/25/81 0302
R-4 6/25/81 0640
R-4 6/25/81 093G
R-4 6/25/81 1320
R-4 6/25/81 1600
oC
o/oo
mg/1
TEMP.
SALINITY
DO
24.4
0.1
6.3
24.6
0.1
6.2
24.7
0.1
6.2
24.7
0.1
6.2
24.7
0.1
6.2
24.7
0.1
6.1
24.5
0.0
6.1
24.5
0.0
6.1
24.5
0.0
6.1
24.5
0.0
6.1
24.5
0.0
6.1
24.5
0.0
6.1
24.5
0.0
6.1
24.5
0.0
6.1
26.4
0.12
6.0
25.4
0.2
6.0
25.0
0.2
6.1
25.1
0.2
6.1
25.0
0.2
6.1
25.0
0.2
6.1
25.1
0.2
6.1
24.9
0.2
6.1
24.8
0.2
6.1
27.8
0.1
6.2
25.9
0.1
6.3
25.4
0.1
6.2
24 .'9
0.1
6.2
25.0
0.1
6.2
24.9
0.1
6.2
25.0
0.1
6.1
24.8
0.3
5.8
24.8
0.5
5.6
28.2
-0-
6.5
26.2
-0-
6.4
25.3
-0-
6.3
24.7
0.1
6.2
24.9
0.6
5.7
25.5
1.3
5.0
26.0
2.6
3.9
26.8
4.3
4.4
FEET
DEPTH
S
2
4
6
8
9 (bott)
S
2
4
6
8
10
12 ,
14 (bott)
S
2
4
6
8
10
12
14
16
S
2
4
6
8
10
12
14
15 (bott)
S
2
4
6
8
10
12
14 (bott)
-32-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-5
STATION DATE TIME
R-5 6/24/81 1235
R-5 6/24/81 1554
R-5 6/24/81 1853
R-5 6/24/81 2123
R-5 6/25/81 0007
R-5 6/25/81 0255
R-5 6/25/81 0628
r-5 6/25/81 0920
FEET
oC
o/oo
mg/1
DEPTH
TEMP.
SALINITY
DO
S
27.0
5.9
1
26.0
5.6
2
26.0
4.4
3 (bott)
26.5
3.4
S
26.2
0.1
6.1
1
26.2
0.1
6.2
2
26.2
0.1
6.2
3
26.2
0.1
6.2
3.5 (bott)
26.2
0.2
6.2
S
26.6
0.3
5.3
1
26.5
0.3
5.3
2
26.3
0.2
5.7
3 (bott)
26.3
0.2
5.7
S
26.3
0.4
5.8
1
26.3
0.3
5.1
2
26.4
0.3
5.0
3 (bott)
26.4
0.3
5.1
S
26.4
0.5
4.7
1
26.4
0.4
4.7
2
25.8
0.4
5.1
S
25.7
0.4
4.7
1
25.8
0.4
4.8
2
25.8
0.4
4.8
2.5
25.6
0.4
4.8
S
25.0
0.2
5.4
1
25.0
0.2
5.4
2
25.0
0.2
5.4
3
25.0
0.2
5.4
S
25.8
0.2
5.8
1
26.0
0.3
5.7
2
25.7
0.2
5.6
3
25.5
0.1
5.8
-33-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-5
STATION DATE TIME
R-5 6/25/81 1315
r-5 6/25/81 1550
FEET
oC
o/oo
mg/1
DEPTH
TEMP.
SALINITY
DO
S
27.4
0.2
6.0
1
27.0
0.2
5.8
2
26.6
0.1
5.8
3
25.7
0.1
5.9
S
30.1
0.4
5.7
1
28.4
0.1
6-2
2
26.8
0.1
6.2
3
25.6
0.1
6.2
-34-
-------
STATION
R-6
R-6
R-6
R-6
R-6
R-6
R-6
DATE
6/24/81
TIME
1543
6/24/81
1846
6/24/81
6/25/81
6/25/81
6/25/81
2115
0003
0248
0625
6/25/81
0855
TABLE 3
[ITY AND TEMPERATURE
OBSERVATIONS
JUNE, 1981
R'
FEET
oC
o/oo
mg/1
DEPTH
TEMP.
SALINITY
DO
S
27.2
0.5
5.1
1
27.0
0.5
5.0
2
26.9
0.6
4.4
3
27.0
0.7
3.9
4
26.9
0.8
3.5
4.5
27.0
0.9
3.1
S
27.7
0.6
4.7
1
27.6
0.6
4.6
2
27.5
0.6
4.3
3
27.4
0.8
3.4
4
27.4
0.9
1.4
S
27.1
0.7
4.0
V
27.1
0.6
4.0
2
27.3
0.7
3.9
3
27.3
0.7
2.7
S
26.8
0.7
4.0
1
26.8
0.7
3.8
2
26.9
0.7
3.7
3
26.9
0.7
3.4
S
26.4
0.7
3.6
1
26.6
0.7
3.6
2
26.6
0.7
3.5
3
26.6
0.8
3.5
S
26.0
0.5
4^2
1
26.0
0.5
3.9
2
26,1
0.5
3.9
3
26.2
0.6
3.8
4
26.2
0.6
3.6
S
26.5
0.6
4.3
1
26.5
0.6
4.4
2
26.5
0.5
4.3
3
26.2
0.6
4.5
4
26.0
0.4
4.5
-35-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-6
FEET
oC
o/oo
mg/1
STATION
DATE
TIME
DEPTH
TEMP.
SALINITY
DO
R-6
6/25/81
1310
S
29.3
0.6
4.4
1
28.4
0.7
3.8
2
28.1
0.8
3.5
3
27.5
0.8
3.3
4
27.6
0.8
3.3
R-6
6/25/81
1540
S
31.6
0.7
4.6
1
30.6
0.4
4.2
2
27.9
0.3
4.7
3
27.0
0.4
4.7
-36-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981 r-7
FEET
oC
o/oo
mg/1
STATION
DATE
TIME
DEPTH
TEMP.
SALINITY
DO
R-7
6/24/81
1240
S
26.8
4.6
1
26.6
4.0
2
26.5
3.7
3
26.8
2.7
4
27.0
2.5
Temp, Salinity, DO data for station R-7 was discontinued after initial run.
-37-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-8
STATION DATE
R-8 6/24/81
R-8
6/24/81
R-8
6/24/81
R-8
6/24/81
R-8
6/24/81
R-8
R-8
6/25/81
6/25/81
FEET
oC
o/oo
mg/1
TIME
DEPTH
TEMP.
SALINITY
DO
1245
S
27.0
5.4
1
27.0
5.6
2
27.0
4.4
3
26.8
3.6
4
26.8
0.5
1525
S
28.3
0.5
6.5
1
28.3
0.6
5.8
2
27.7
0.9
4.7
3
27.5
1.1
3.7
4
27.8
4.0
0.4
1840
S
28.3
0.7
5.3
1
28.1
0.7
5.0
2
27.8
0.8
4.6
3
27.7
1.0
3.3
4
27.6
2.2
0.3
2100
S
27.5
0.7
4.6
1
27.5
0.7
4.4
2
27.5
0.9
4.1
3
27.5
1.0
2.5
4
27.4
3.1
0.4
2353
S
27.0
0.9
4.5
1
27.0
0.8
4.4
2
27.0
0.8
4.3
3
27.1
2.4
1.7
3.5
27.2
5.0
0.9
0240
S
26.7
0.8
3.9
1
26.7
1.0
3.5
2
26.8
1.0
3.7
3
26.9
1.0
0.7
0608
S
26.4
0.8
3.5
1
26.3
0.9
3.5
2
26.3
0.9
3.4
3
26.6
0.8
3.3
4
26.8
5.0
0.4
-38-
-------
TABLE 3
DISSOLVED OXYGEN, SALINITY AND TEMPERATURE OBSERVATIONS
JUNE, 1981
R-8
STATION DATE TIME
R-8 6/25/81 0905
R-8 6/25/81 1300
R-8 6/25/81 1535
oC o/oo mg/1
TEMP. SALINITY DO
28.0 0.9 3.4
27.2 0.9 3.2
27.0 0.9 3.1
26.9 0.9 3.0
27.5 4.3 0.2
29.3 0.8 4.0
29.2 0.8 3.5
28.3 0.8 3.2
27.4 0.9 2.5
27.4 1.5 0.4
30.6 0.8 4.5
29.8 0.8 4.4
28.8 0.8 3.7
27.9 0.8 3.2
27.8 1.5 1.0
FEET
DEPTH
S
1
2
3
4
S
1
2
3
4
S
1
2
3
4
-39-
-------
TABLE 4. SUMMARY OF DISSOLVED OXYGEN, SALINITY, AND TEMPERATURE CONCENTRATIONS
GATHERED IN DIEL SAMPLING, JUNE 24-25, 1981
Temperature °F
Salinity
Dissolved Oxyge
Station
Mean
Range
Mean
Range
Mean
Range
R-2
22.8
21.2-25.5
0.1
0.0-0.2
6.1
5.1-6.2
R-3
25.8
24.5-28.9
1.0
0.0-6.4
5.4
1.7-6.3
R-4
25.3
24.4-28.2
0.2
0.0-4.3
6.1
3.9-6.2
R-5
26.2
25.0-30.1
0.2
0.1-0.5
5.5
3.4-6.1
R-6
27.1
26.0-31.6
0.6
0.3-0.9
3.9
1.4-4.3
R-8
27.5
26.3-30.6
1.3
0.5-5.0
3.3
0.2-4.6
Percent
Dissolved Oxygen
Saturation
71
67
74
68
49
42
-------
TABLE 5. WATER CHEMISTRY DATA (mg/L), STATIONS R-2 THRU R-8,
JUNE 1981.
S&A
R-2
R-3
R-4
R-5
R-6
R-8
Date
6/24
6/25
6/25
6/25
6/26
6/26
6/24
6/24
6/25
6/25
6/25
6/26
6/26
6/24
6/24
6/25
6/25
6/25
6/26
6/26
6/24
6/24
6/25
6/25
6/25
6/26
6/26
6/24
6/24
6/25
6/25
6/25
6/26
6/26
6/24
6/24
6/24
6/24
6/25
6/25
6/25
6/25
6/26
6/26
Time
Depth
CL
h2s
TKN
nh3
NO2-NO3
T-P
1624
2 ft
0.30
0.10
0.07
0.03
0324
1
0.12
0.06
0.07
0.03
0950
2
0.40
0.15
0.13
0.09
02 50
2.5
8.5
1746
3
<0.2
1747
3
<0.2
1637
8
0.25
<0.05
0.05
0.05
2145
6
0.25
0.06
0.07
0.04
0317
5
0.20
0.05
0.07
0.04
1013
8
0.25
<0.05
0.07
0.04
1019
14
1700
1535
14
<0.2
1540
14.
<0.2
1612
8
0.10
0.07
0.03
0.05
2136
6
0.45
0.07
0.05
0.04
0307
4.5
0.15
<0.05
0.07
0.14
0935
8
0.15
0.07
0.10
0.14
0935
16
18.1
1525
16
<0.2
1530
16
<0.2
1558
2
0.25
0.07
0.07
0.06
2127
1.5
0.15
0.07
0.10
0.04
0258
1
0.15
0.13
0.07
0.06
0925
2
0.20
<0.05
0.07
0.05
0925
3
37.2
1515
3
<0.2
1520
3
<0.2
1549
2
0.30
0.13
0.05
0.06
2120
2
0.20
0.09
0.07
0.08
0251
1.5
0.30
0.09
0.05
0.04
0900
2
0.30
0.09
0.05
0.06
0900
4
186
1505
4
<0.2
1510
4
<0.2
1525
2
0.25
0.20
0.07
0.05
1526
4
0.20
0.20
0.07
0.05
2100
2
0.20
0.09
0.07
0.05
2100
3
0.25
0.09
0.07
0.05
0242
1
0.25
0.13
0.07
0.12
0243
3
0.12
0.15
0.06
0.08
0910
2
0.25
0.13
0.08
0.07
0910
4
660
0.36
0.28
0.05
0.10
1715
4
<0.2
1715
4
5.0
-41-
TOC
-------
TABLE 6. VISIBLE LIGHT TRANSMISSION.
Station Date Depth % Transmission
R-2 6/25 Surface 100
1 69
2 57
3 (bot) 40.3
R-3 6/25 Surface 100
2 16
4 2.8
6 0.6
8 0.002
10 0.001
11 (bot) —
R—4 6/25 Surface 100
2 17.7
4 3.5
6 0.8
8 0.003
10 0.001
12
12.5 (bot)
R-5 6/25 Surface 100
1 39.1
2 13.8
3 (bot) 3.4
R-6 6/25 Surface 100
1 40.6
2 15.8
3 (bot) 6.8
R-8 6/25 Surface 100
1 44.3
2 16.2
3 5.8
4 (bot) 2.0
-42
-------
TABLE 7.
WATER COLUMN
PRIMARY PRODUCTION
AND RESPIRATION RATES.
Prim^ Prod.
g 02/m2/day*
Station
Net
Gros s
Respiration g 02/m2/day*
R-2
-1.32
0.12
1.44
R-4
-2.28
0.12
2.40
R-5
-0.60
0.12
0.72
R-6
-1.08
0.12
1.20
R—8
-0.84
0.60
1.44
*Gross Primary Production based on 12-hour photoperiod.
Respiration based on 24-hour period.
-------
TABLE 8. PARTICLE SIZE OF SEDIMENTS AT SELECTED STUDY STATIONS,
TRINGAS PROJECT, NAVARRE, FLORIDA, JUNE 22-27, 1981
Location
Station
Inorganic Component Subtended by On
(all as % total dry weig
ganic Fraction
tit)
Medium*
Gravel
Bine*
Gravel
Coarse*
Sand
Mediun*
Sand
Pine*
Sand
Silt
Clay
Totals
Unnamed
tided, creek
R-2
2.8
3.8
1.4
3.0
14.6
5.1
38.8
6.8
5.3
1.2
11.4
1.9
2.3
1.4
76.6
23.2
East Bay
River
R-4
0.01
0.1
0.1
0.1
82.9
0.1
15.0
0.1
0.3
0.1
0.6
0.2
0.3
0.1
99.2
0.8
Tringas
Canal
R-5
1.3
2.6 '
.8
2.4
14.3
4.8
33.3
8.9
8.3
3.1
12.3
3.7
3.2
0.1
73.5
25.6
Tringas
Canal
R-6
0.4
1.2
0.9
1.8
3.6
3.6
23.0
10.2
4.5
3.1
31.6
9.6
5.3
1.1
69.3
30.6
Tringas
Canal
R-8
0.04
0.1
0.4
0.9
2.4
2.9
8.9
5.2
5.1
3.1
45.6
14.0
9.1
2.3
71.5
28.5
These designations arc for representation of particle size and
are not Indicative of the nature of the material retained in
sieving. For examplef materiel reported under the medium gravel
heading may actually be comprised mainly of woody particles
rather than gravel*
-44-
-------
TABLE 9. NUMERICAL ABUNDANCE OF MACROINVERTEBRATES FROM
STUDY STATIONS, TRINGAS PROJECT, NAVARRE, FLORIDA,
JUNE 22-17, 1981
Organisms
Annelida
Lumbriculidae
Tubificidae
Polychaeta
Arthopoda
Crustacea
Asellus sp.
Gammarus sp. A
Penaeidae
Mysidacea
Insecta
Trichoptera
Polycentropus sp.
Neuroptera
Sialis sp.
Diptera
Cryptotendipes sp.
Bezzia-Probezzia
Tanytarsus nr. querlus
Coleoptera
Dubiraphia sp.
# m
R-2 R—4 R-5 R-8
82
2163
41
20
20
41
20
20
143
41
20
20
Total #/m
Total taxa
2550
9
81
3
0
0
0
0
*Based on six replicate quantitative core samples.
-45-
-------
TABLE 10. CHECKLIST OF MACROINVERTEBRATES COLLECTED BY
QUALITATIVE SAMPLING. TRINGAS PROJECT, NAVARRE, FLORIDA
JUNE 22-23, 1981
Organisms
Stations
R-2
R-4
R-5
R-8
Arthropoda
Crustacea
Asellus sp.
Gammarus sp. A
G. mucronatus
Grandiderella sp.
Palaemonetes kadiakensis
Mysidacea
Xanthidae
Astacidae
Insecta
Odonata
Argia sp.
Enallagma sp.
Amphiagron sp.
Trichoptera
Polycentropus sp.
Hydroptila sp.
Neuroptera
Sialis sp.
Diptera
Ablabesmyia hauberi
A. tare1la-ma1lochi
Parachaetocladius sp.
Parametriocnemus lundbecki
Dicrotendipe poss. lobus
D. neomodestus
Pseudochironomus nr. prasinatus
Tanytarsus (glabrescens) gp.
Dolichopodidae - Hydrophorus sp,
Tribelos fusccicornis
Polypedilum illinoense
Chironomus attenuatas
Coleoptera
Dubiraphia sp.
Dytiscidae
Berosus
lollusca
Pelecypoda
Congeria leucophaeta
Gastropodae
Amnicola sp.
'otal species collected
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
17
17
X
X
6
+j
c
0>
to
-------
^ ij jruiiuriiAiNiMvju-cnjjUKUfniLij A .CONCENTRATIONS FROM STUDY STATIONS,
TRINGAS PROJECT, NAVARRE, FLORIDA, JUNE 22-21, 1981
Station Date Time Depth Chlorophyll a (mq/m^)
R-2 6/24/81 1620 1' 0.70
R-3 " 1630 1' 0.45
R-4 " 1602 1' 0.55
R-5 " 1554 1' 1.20
R-6 " 1543 1' 1.30
R-8 " 1525 1' 11.48
R-2 6/25/81 0945 1» 1.25
R-3 " 1005 1' 0.50
R-4 " 0930 1' 0.35
R-5 " -0920 1' 1.50
R-6 " 0855 1' 4.16
R-8 " 0905 1* 9.82
-47-
-------
TABLE 12
COLIFORM BACTERIA DATA (#/100 ML)
JUNE 1981
Geometric
Mean
Station
Date
Total
Fecal
Date
Total
Fecal
Total
Fecal
R-2
6/24
1,000
80
6/25
100
30
316
49
R-3
6/24
3,000
300
6/25
10,000
460
5,477
371
R-4
6/24
2,000
360
6/25
10,000
630
4,472
476
R-5
6/24
500
320
6/25
1,000
<10
707
57
R-6
6/24
14,000
1,000
6/25
10,000
540
11,832
735
R-7
6/24
18,000
1,000
6/25
3,000
1,160
7,348
1,077
R-8
6/24
10,000
3,100
6/25
11,000
750
10,488
1,525
48
-------
TABLE 13. SPECIES COMPOSITION OF VEGETATION ALONG TRANSECTS.
TRINGAS STUDY, JUNE 22-27, 1981.
Location Plant Species
to A-3 Myrica cerifera, Gramineae, Limonium
carolxnianum, Boehemeria cylindrica,
Serenoa repens, Crinum americanum,
Saururus cernuus, Ce pha1anthus occidentalis,
Acer rubrum, Nyssa sylvatica, Osmunda
regalis, Ilex
A-3 to A-5 (canal) Nyssa sylvatica, Myrica cerifera, Pinus
taeda, Acer rubrum, Rhus~r"ad jeans, Ilex,
Osmunda regalis, Osmunda cinnamonea,
Serenoa reyens, Vitis sp., Cephalanthus
occidentalis, Saururus cernuus, Sagittaria
latifolia, Typha sp., Pontederia lanceolata
B-l Magnolia virginiana, Nyssa sylvatica,
Persea palustrxs, Myrica cerifera,
Saururus cernuus, Serenoa repens, Osmunda
regalisT Osmunda cinnamonea, Vitis sp.
B-2 Crinum americanum, Serenoa repens,
Osmunda regalis,Osmunda cinnamonea,
Myrica"cerifera, Rhus radicans, Vitis
sp., Ilex sp., Cephalanthus occidentalis,
Magnolia virginiana
C-i to C-3 Magnolia virginiana, Persea palustris,
Nyssa sylvatica, Myrica cerifera, Saururus
cernuus, Serenoa repens, Osmunda regalis,
Osmunda cinnamonea, vTtis sp.
C_3 Magnolia virginiana, Persea palustris,
Nyssa sylvatica, Myrica cerifera, Taxodium
distichlum, Acer rubrum, Crinunfamericanum,
Serenoa repens, Osmunda regalis, Saururus
cernuus
E-i Acer rubrum, Pinus taeda, Nyssa sylvatica.
Magnolia virginiana, Persea palustris
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TABLE 13 (continued)
Location
Plant Species
E-2
F-l to F-4
F-4 through F-6
H
Persea palustris, Nyssa sylvatica,
Taxodium distichium, Acer rubrum, Osmunda
regalisT Osmunda cinnamonea, Serenoa
repens
Acer rubrum, Persea palustris, Magnolia
virginiana,. Tax-odium distichium, Nyssa
sylvatica, Myrica ceripera
Persea palustris, Magnolia virginiana,
Taxodium distichium, Nyssa sylvatica,
Crinum americanum,Gramineae, Serenoa
repens, Osmunda regalis, Saururus cernuus,
Limonium carolinianum
Ilex sp., Persea palustris, Nyssa sylvatica,
Taxodium distichium, Serenoa repens,
Osmunda regalis, Crinum americanum,
Limonium carolinianum, Acer rubrum
Nyssa sylvatica, Persea palustris,
Magnolia virginiana, Pinus taeda, Centella
asiatica, Eriocaulon sp., Rhus radicans,
Eleocharis parvula, Myrica cerifera,
Osmunda regalis, Osmunda cinnamonea
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