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TECHNICAL REPORT A-78-2
LARGE-SCALE OPERATIONS
MANAGEMENT TEST OF USE OF THE WHITE AMUR FOR CONTROL OF PROBLEM AQUATIC PLANTS
Report 1
BASELINE STUDIES
Volume V
The Herpetofauna of Lake Conway, Florida
By J. Steve God ley, Roy W. McDiarmid, and G. Thomas Bancroft
Department of Biology University of South Florida Tampa, Fla. 33620
June 1981
Report 1 of a Series
Approved For Public Release; Distribution Unlimited
Prepared for U. S. Army Engineer District, Jacksonville Jacksonville, Fla. 32201
and Office, Chief of Engineers, U. S. Army Washington, D. C. 20314
Under Contract No. DACW39-76-C-0047
Monitored by Environmental Laboratory U. S. Army Engineer Waterways Experiment Station P. O. Box 631, Vicksburg, Miss. 39180
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LARGE-SCALE OPERATIONS MANAGEMENT TEST OF USE OF THE WHITE AMUR FOR CONTROL OF
PROBLEM AQUATIC PLANTS
Report 1: Baseline Studies
Volume I: The Aquatic Macrophytes of Lake Conway, Florida
Volume II: The Fish, Mammals, and Waterfowl of Lake Conway, Florida
Volume III: The Plankton and Benthos of Lake Conway, Florida
Volume IV: Interim Report on the Nitrogen and Phosphorus Loading Characteristics
of the Lake Conway, Florida, Ecosystem
Volume V: The Herpetofouna of Lake Conway, Florida
Volume VI: The Water and Sediment Quality of Lake Conway, Florida
Volume VII: A Model for Evaluation of the Response of the Lake Conway, Florida,
Ecosystem to Introduction of the White Amur
Volume VIII: Summary of Baseline Studies and Data
Report 2: First Year Poststocking Results
Report 3: Second Year Poststocking Results
Destroy this report when no longer needed. Do not return
it to the originator.
The findings in this report are not to be construed as an official
Department of the Army position unless so designated
by other authorized documents.
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The contents of this report are not to be used for advertising, publication, or promotional purposes.
Citation of trade names does not constitute an
official endorsement or approval of the use of such commercial products.
Unclassified SECURITY CLASSIFICATION OF THIS PAGE (Whan Dala Entaraif)
REPORT DOCUMENTATION PAGE READ INSTRUCTIONS BEFORE COMPLETING FORM
1. REPORT NUMBER
Technical Report A-78-2 2. GOVT ACCESSION NO. 3. RECIPIENT'S CATALOG NUMBER
4. TITLE (and Submit) LARGE-SCALE OPERATIONS MANAGEMENT TEST OF USE OF THE WHITE AMUR FOR CONTROL OF PROBLEM AQUATIC PLANTS; Report 1, BASELINE STUDIES; Vol V: The Herpetofauna of Lake Conway, Florida
5. TYPE OF REPORT & PERIOD COVERED
Report 1 of a series (In 8 volumes)
8. PERFORMING ORG. REPORT NUMBER
7. AUTHORfaJ
J. Steve Godley Roy W. McDiarmid G. Thomas Ranrrnff
8. CONTRACT OR GRANT NUMBERfa)
Contract No. DACW39-76-C-0047
9. PERFORMING ORGANIZATION NAME AND APORESS
University of South Florida Department of Biology Tampa, Fla. 33620
10. PROGRAM ELEMENT, PROJECT, TASK AREA 4 WORK UNIT NUMBERS
Aquatic Plant Control Research Program
M. CONTROLLING OFFICE NAME AND ADDRESS U. S. Army Engineer District, Jacksonville Jacksonville, Fla. 32201 and Office, Chief of Engineers, U. S. Army, Washington, D. C. 20314
12. REPORT DATE
June 1981' 13. NUMBER OF PAGES
111 14. MONITORING AGENCY NAME 6) ADDRESSfff dittatant from Controlling Ollica)
U. S. Army Engineer Waterways Experiment Station Environmental Laboratory, P. 0. Box 631 Vicksburg, Miss. 39180
15. SECURITY CLASS, (ot thlm report)
Unclassified
15a. DECLASSIFICATION/DOWNGRADING SCHEDULE
IS. DISTRIBUTION STATEMENT foi thlm Rapott)
Approved for public release; distribution unlimited.
17. DISTRIBUTION STATEMENT (at tba abatract mtmd in Bloek 20, It dlttarmt from Rtport)
18. SUPPLEMENTARY NOTES
Available from National Technical Information Service, Springfield, Va, 22161
13. K EY WORDS (Contlnum on rmttt mldm If nacaaaaiy and IdMltlty by block numbtr)
Amphibia Lakes Aquatic plant control Reptiles Lake Conway White amur
20. ABSTRACT OCmrtfiju* an Itnru mtam H IWIUUJ mat Identity- by bloc* numbt)
This report summarizes the baseline conditions for the amphibian and rep- tile populations of Lake Conway, Florida, for the 15-month study period, June 1977-September 1978. These results will be used later to determine whether any changes in the herpetofauna result from the introduction of the white amur (Ctenopharynsodon idella) into the lake system to control aquatic vegetation. This baseline report includes detailed descriptions of the herpetofaunal study
(Continued)
DO , FORM JAM 73 1473 EDITION OF t KOV 6S IS OBSOLETE Unclassified
SECURITY CLASSIFICATION OF THIS PAGE flffean Date En farad)
W£&* !Sf!5tKIP?^WBIIIil
Unclassified JBCURITY CLASSIFICATION OF THIS PAOE(TWi«n Dmtm Entmd)
20. ABSTRACT (Continued).
sites and methods and community analyses of the temporal and spatial distribu- tions and densities of the species by pool.
A total of 5,836 individuals representing 11 amphibian species and 16 rep- tilian species were observed or captured on Lake Cbnway during the baseline study period. Approximately 93% of the total species pool was obtained within the first 3,000 specimens, and between 70% and 80% of the predicted herpeto- fauna inhabiting each pool has been recorded. Of the 27 species presently recorded from the Lake Conway complex, 11 occur in all pools and together account for 94.4% of the total sample. The mean relative densities of 11 spe- cies were found to vary significantly between pools. Development of the shore- line for housing during the baseline study period was shown to have a negative impact on some amphibian and reptile populations.
Unclassified
SECURITY CLASSIFICATION OF THIS PAGEfWIwn Oat* Bntmd)
PREFACE
The work described in this volume was performed under Contract No.
DACW39-76-C-0047 between the U. S. Army Engineer Waterways Experiment
Station (WES), Vicksburg, Miss., and the University of South Florida,
Tampa. The work was sponsored by the U. S. Army Engineer District,
Jacksonville, and by the Office, Chief of Engineers, U. S. Army.
This is the fifth of eight volumes that constitute the first of a
series of reports documenting a large-scale operations management test
of use of the white amur for control of problem aquatic plants in Lake
Conway, Florida. Report 1 presents the results of the baseline studies
of Lake Conway; subsequent reports will present the annual poststocking
results.
This volume was written by Mr. J. Steve Godley, Mr. G. Thomas
Bancroft, and Dr. Roy W. McDiarmid of the Department of Biology of the
University of South Florida.
The authors wish to acknowledge Messrs. W. E. Ackerman and M. Lopez
and Mdms. D. T. Gross, N. N. Rojas, and D. A. Sutphen for their help
during the field operations.
The work was monitored at WES in the Environmental Laboratory (EL)
by Mr. R. F. Theriot under the general supervision of Dr. John Harrison,
Chief, EL, and Mr. B. 0. Benn, Chief, Environmental Systems Division (ESD),
and under the direct supervision of Mr. J. L. Decell, Manager, Aquatic
Plant Control Research Program.
Commanders and Directors of WES during the period of the contract
and preparation of the report were COL J. L. Cannon, CE, and COL Nelson P.
Conover, CE. Technical Director was Mr. F. R. Brown.
This report should be cited as follows:
Godley, J. S., McDiarmid, R. W., and Bancroft, G. T. 1981. "Large-Scale Operations Management Test of Use of White Amur for Control of Problem Aquatic Plants; Report 1, Baseline Studies; Vol- ume V: The Herpetofauna of Lake Conway, Florida," prepared by University of South Florida, Tampa, Fla., for the U. S. Army Engineer Waterways Experi- Station, CE, Vicksburg, Miss.
CONTENTS
Page
PREFACE 1
PART I: INTRODUCTION 3
PART II: METHODS AND MATERIALS 5
Sampling Equipment and Techniques 6 Marking and Measuring Procedures 10
PART III: THE LAKE CONWAY SYSTEM 13
South Pool 14 Middle Pool 15 East Pool 16 West Pool 17 Gatlin Canal 18
PART IV: THE HERPETOFAUNA OF LAKE CONWAY 19
Species Distribution and Abundance 20 Permanent Shoreline Sites 20 Deepwater Trapping Stations 33
PART V: DISCUSSION 34
REFERENCES 36
TABLES 1-5
FIGURES 1-42
APPENDIX A: SUMMARY OF PLANT SPECIES AND SUBSTRATUM TYPE FOR ALL PERMANENT SHORELINE HERPETOFAUNAL TRAPPING STATIONS ON LAKE CONWAY DURING THE BASELINE STUDY PERIOD Al
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LARGE-SCALE OPERATIONS MANAGEMENT TEST OF USE OF THE
WHITE AMUR FOR CONTROL OF PROBLEM AQUATIC PLANTS
BASELINE STUDIES
The Herpetofauna of Lake Conway, Florida
PART I: INTRODUCTION
1. The environment of central Florida with its extensive lake
habitats provides an ideal setting for intensive field studies of
subtropical aquatic ecosystems. With the exception of a few local
studies, no detailed, integrative investigations of aquatic .community
dynamics exist. Thus, the proposal by the U.S. Army Engineer Waterways
Experiment Station (Addor and Theriot 1977) to investigate the suita-
bility of the white amur (Ctenopharyngodon idella, herein referred to
as white amur) as a potential biological control agent of hydrilla
(Hydrilla verticillata), a recently introduced aquatic plant in the
Lake Conway System of central Florida, was particularly interesting and
timely. Not only did the proposed study include an evaluation of the
effectiveness of the white amur as a weed control agent and its impact,
direct or indirect, on the associated biota of the system, but also it
provided an opportunity to do the first detailed study of a community
of amphibians and reptiles in a large aquatic environment.
2. In June of 1977 a study of the herpetofauna of Lake Conway was
initiated with the following objectives: (a) to determine the species
of amphibians and reptiles inhabiting the lake system; (b) to ascertain
the habitat requirements, distribution, ecology, and seasonal activity
of these species in the system; (c) to establish quantitative baseline
population data for the more common or otherwise important species in
each pool in the system including density by habitat, relative age (size)
structure, movements, growth, reproduction, food habits, and related
parameters as deemed feasible; (d) to quantitatively monitor changes in
the species composition or their population parameters during post-
stocking periods; and (e) to determine whether any changes are the result,
directly or indirectly, of the white amur weed control program.
3. This report summarizes the findings of the amphibian and reptile
study on Lake Conway for the 15-month period from June 1977 through
September 1978. Although the white amur was introduced into Lake
Conway in September 1977, only three months after the herpetofaunal
project began, the data presented herein necessarily are considered
"baseline" to which subsequent poststocking periods will be compared.
Included are detailed descriptions of the herpetofaunal study sites,
sampling methods and techniques, and data collection procedures. In
addition, this report provides for the baseline study period a list of
the amphibian and reptile species encountered on Lake Conway, an
analysis of their temporal and spatial densities and distributions, and
a composite of those parameters deemed important to understanding
community dynamics within the system. Future poststocking reports
also will include detailed accounts of the individual species, emphasizing
temporal changes in the herpetofauna of Lake Conway,
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PART II: METHODS AND MATERIALS
4. The first month of fieldwork was spent surveying the total
Lake Conway system and associated waterways for habitat types. Based
on this reconnaissance, one section of shoreline and one deepwater transect
in each pool of the Lake Conway complex were selected for future
censusing and permanent trapping stations (Figure 1). These sites
contained all the major vegetation types with their associated water
depths and substratum and were representative of the habitats available
to the herpetofauna within the Lake Conway system. Each permanent shore-
line site is described in detail in Part III, "The Lake Conway System."
5. Along the entire length of each permanent shoreline site
numbered stakes were placed 10 m. apart in 30 to 60 cm. of water. The
stakes facilitated location of capture points and subsequent movement of
all marked amphibians and reptiles and served as permanent trapping
stations. At each trapping station estimates of the percent plant
species cover within a 2-sq.-m. area of the trap, water depth, and
substratum were recorded quarterly from October 1977 through September
1978, and biannually thereafter.
6. At the permanent shoreline sites, mark and recapture
population studies were conducted twice a month; destructive samples
for stomach and reproductive analyses of selected species were taken
monthly, or as time permitted, from distant areas of similar habitat
within the lake system. Destructive samples were placed on ice at
capture and frozen for future analysis. Animals that accidentally
drowned in traps or were killed inadvertently during processing also
were frozen*and, when possible, saved for analysis. Later, all samples
were preserved in 10 percent formalin and dissected at the University of
South Florida, For food habit studies, the preserved stomach sample was
blotted dry, then weighed. The number of individuals of a prey taxa and
their estimated percent of total weight were recorded. If a prey taxa made
up more than 50 percent of a stomach sample, its individual weight also was
taken. Reproductive analysis included weighing the testes and epididymes
of males, the ovaries and oviducts of females, and counting, weighing, and
m
measuring the ovarian follicles, oviductal eggs (or embryos), and corpora
lutea of females.
7. The deepwater sites duplicated vegetation transects of the
Florida Department of Natural Resources (Nail and Schardt 1978). Traps
were set for one day 100 m. apart at FDNR sampling points on a
quarterly basis. Only destructive samples were taken in deepwater
benthic traps because it was impossible to prevent drowning of specimens,
Trap success of amphibians and reptiles at deepwater sites during the
first year was extremely low compared to shoreline trapping. These low
densities made it impossible to detect statistical differences in
population parameters as a result of the white amur introduction without
a substantial increase in effort. As a result, deepwater funnel trapping
was discontinued after one year of sampling, and the time was devoted to
more profitable research.
8. Thus, the herpetofaunal sampling program involved spending
3 days and 2 nights every other week on the lake so that each permanent
shoreline site was censused and sampled by traps twice a month, Alternate
weeks were spent in the laboratory processing data and destructive
samples. Deepwater sampling required an additional day and night per
quarter.
Sampling Equipment and Techniques
9. Because of the ecological and behavioral differences that
characterize the amphibian and reptile species of Lake Conway, several
different kinds of collecting equipment and techniques were used, A
5.33-m. (16-ft.) John boat with a 25-h.p. (18.6-kw.) outboard motor was
used in placing and monitoring funnel traps, in conducting alligator
counts, and in censusing shoreline sites. Brief descriptions of these
and other maj or sampling methods are given in the following paragraphs.
Funnel trapping
10. Funnel traps, 60x30x30 cm., were designed specifically
to sample aquatic salamanders, tadpoles, small carnivorous turtles, and
several species of water snakes. Most funnel traps were constructed of
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3-nnn. black plastic Vexar netting (Du Pont De Nemours & Co., Model No.
5-59-V-360-BABK) stretched over welded metal frames with funnel entrances
at each end. Some wire mesh funnel traps of the same dimensions were
used in dense stands of cattails (Typha latifolia) at the Middle and
East Pool sites. Wire traps were used at these sites because rice
rats, Oryzomys palustris, were common and gnawed numerous holes in
Vexar traps.
11. All traps were baited with fresh, cut fish and set for a 24-
hr. period. To determine general diel activity patterns for the more
common species, all shoreline traps were checked at dawn and dusk
during the baseline study period. Shoreline, littoral zone traps
were placed on the substratum with the top above water to prevent
drowning of animals; deepwater traps were submerged on the bottom.
12. The number of traps set at permanent shoreline sites was
increased gradually during the first year as newly constructed traps
became available and as the sizes of the permanent sites were expanded
(see Part III, "The Lake Conway System"). By July 1978, the total number
of shoreline trapping stations was stabilized at 77 and traps were set
twice a month at each station. A total of 61 traps was used for quarterly,
deepwater trapping samples (October and December 1977, April and July
1978). Within- and between-site comparisons of the first years' trapping
data are based on seasonal trap success per total number of trap days
per season. The standard notation of trap days (sum of all traps set/
24 hrs.) was used throughout the study.
Herp-patrol
13. In addition to funnel trapping, all permanent shoreline sites
were censused twice a month at night from a boat. Preliminary work
showed that most species of amphibians and reptiles were more active and
much easier to catch at night than during the day. This censusing
technique, termed "herp-patrol," involved use of an electric motor and
two 12-volt, 120,000-candlepower spotlights. During herp-patrols the
permanent shoreline sites were sampled by motoring slowly along the edge
of the littoral zone. One spotlight in the rear was directed towards
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the emergent vegetation while the other in the front was shlned in
adjacent, open water. A third individual collected animals with a
dipnet or by hand. The species, time, location, water depth, vegetation
type, substratum, activity, and behavior for all specimens observed or
heard calling were recorded on standardized data sheets. All captured
individuals were sexed, measured, weighed, marked, and released at the
capture point the following day.
14. Herp-patrol sampling effort was standardized for each perma-
nent shoreline site but varied between sites because of differences in
the lengths of shoreline sampled. Between-site comparisons were based on
the number of animals collected per unit total search time. Beginning
in November 19 77, herp-patrols on permanent sites were replicated each
sampling night and assigned a run number of I or II to provide an estimate
of within-site variance. The same collecting path was used on each run.
Alligator census
15. The alligator population of the entire Lake Conway complex
was estimated using nocturnal censusing techniques. In the first year
the entire shoreline of the lake system was scanned monthly using a
12-volt, 120,000-candlepower spotlight to search for the characteristic
red-orange glow of the alligators' eyes. When an animal was located,
it was approached quietly until the size of the alligator could be
estimated. The number, locations, and approximate sizes of all sighted
individuals were recorded. Because the Lake Conway alligator population
was found to be small, easily monitored, and unlikely to have a signifi-
cant impact on the white amur population, nocturnal censusing of
alligators was reduced to a bimonthly schedule in June 1978.
16. In addition, during the summer nesting season all stretches
of suitable shoreline habitat were searched for nesting females. All
located nests were monitored until the young hatched in the fall.
Juvenile alligator production was estimated by counting the number of
hatched eggs and by counting the number of juveniles seen at the nest
site. Incubating eggs were not counted because nest disturbance
significantly increases predation (T.C. Hines, personal communication).
?^«^^^^
Gill netting
17. All animals collected in gill nets operated by the Florida
Game and Fresh Water Fish Commission (FGFWFC) were taken and used for kill
samples. Two gill nets of various mesh sizes were set monthly in South,
Middle, and West Pool during the baseline study period (Guillory 1979).
18. In addition, several other methods were used as time and
man-power permitted, Although quantifiable, these methods either were
selective in the species taken or were done on an irregular basis in
order to increase the sample for a particular species,
Shoreline census
19. All animals collected or observed while checking or setting
funnel traps, or while walking along the shore at other times, were assigned
to the sampling technique of shoreline census. The data collected and the
procedures used during shoreline censuses were similar to those used
during herp-patrols.
Hyacinth sieving
20. At some sites, dense stands of the introduced waterhyacinth,
Eichhornia crassipes, were sampled with a 0.5635-sq.-m. boxlike hyacinth
sieve. The sampling procedure and device are described in Godley
(1979).
Drift fence
21. At several sites, permanent drift fences (5 m. long, 0.8 m.
high) were set with pairs of unbaited funnel traps at each end. In
South Pool, two drift fences, one upland (20 m. from water) and one
aquatic (perpendicular to shore), were set in November 1977 at markers
160 and 130, respectively. Another aquatic fence was set perpendicular
to shore at marker 1135 in Middle Pool in April 1977. Within a month, the
drift fences at both sites were vandalized or stolen and the sampling
method was discontinued.
Electrofishing
22. Specimens of amphibians and reptiles selectively obtained by
FGFWFC personnel while electrofishing on Lake Conway (Guillory 1979)
generally were used for stomach and reproductive analyses.
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Marking and Measuring Procedures
23. The Lake Conway herpetofaunal sampling program involved long-
term mark and recapture studies of certain species and incidental and/
or short-term studies of the remaining species. Because of the varied
ecologies and life histories of the species, several different measuring
and marking procedures were required.
Aquatic salamanders
24. Early in the study no permanent marking technique was
available for salamanders of the families Amphiumidae and Sirenidae, and
species either were released unmarked or taken for destructive samples.
From September 1977 through July 1978, adults of these salamanders
were experimentally tagged with plastic numbered Floy fish tags (Model
No. FD-68) similar to those described by Pough (1970). The tags,
measuring 4.8 cm. in total length and weighing 2.0 g., were inserted
through the base of the salamander's tail with the T-portion protruding
through the opposite side (salamanders lack the pterygial bones of
fishes preventing internal anchorage of the T). Specimens were weighed
(to 0.1 g,); then the snout-vent length (SVL = tip of snout to posterior
margin of vent) and total length (TL = tip of snout to end of tail) were
measured by placing the salamander in a V-shaped, clear plexiglas measuring
device. As a secondary means of identification, all bite marks, scars,
and deformities of salamanders were recorded beginning in March 1978.
After processing, all salamanders were released at the capture site,
25. Many salamanders that were Floy-tagged, released in the field,
and subsequently recaptured had lost the tag. Although these
animals could be distinguished as a recapture, positive identification
of individuals often was not possible and Floy-tagging of salamanders
was discontinued. Beginning in August 1978, all Siren and Amphiuma were
cold-branded for 8 to 10 sec. on the abdomen with copper wire numbers
dipped in liquid nitrogen. These brands were recognizable for at least
one year in the field and this method was used for salamanders for the
remainder of the study.
10
Aquatic turtles
26. All species of aquatic turtles in the lake system were
monitored. Standard measurements taken were weight (to nearest 0,1 g.
for turtles < 1000 g.; to nearest 10 g. for turtles > 1000 g.), carapace
length (CL = straight mid-line distance with calipers from anterior-
most to posterior-most point of carapace), and plastron length (PL =
anterior-most to posterior-most point of plastron) to the nearest
millimeter. Throughout the study emydid turtles (Chrysemys floridana,
C. nelsoni, Deirochelys reticularia) were marked by drilling holes in
(adults) or notching (juveniles) the marginal scutes using a numbering
system similar to Cagle's (1939). Other species were toe-clipped from
July 1977 through December 1977 but marked with numbered Floy fish tags
(4.8 cm. total length, 2.0 g.) beginning in January 1978, The Floy tags
were inserted through a hole drilled in a posterior marginal scute of
the turtle.
Alligators
27. American alligators (Alligator mississippiensis) were not
marked for recapture on Lake Conway because (1) the animals are difficult
and dangerous to capture and process, (2) Federal and State permits are
required for these procedures, and (3) the alligator population on Lake
Conway was found to be small and easily monitored by nocturnal censuses
and nest counts.
Larval amphibians
28. The composition, distribution, and relative density of the
tadpole fauna of Lake Conway were estimated for each permanent trapping
station at the five littoral zone sites. Initially, five standard sweeps
of a dipnet were taken before the funnel traps were set at a station. In
addition, the number and identity of all tadpoles collected at littoral
zone and deepwater trapping sites were recorded. Because dipnetting
disturbed the vegetation at trapping stations and was less successful
at collecting tadpoles than funnel traps, dipnetting was discontinued.
Beginning in April 1978, all tadpoles collected in traps were staged
(Gosner 1960) to obtain populational estimates of developmental rates
and larval lifespan.
11
Adult frogs
29. Frog species were monitored by shoreline censuses, herp-patrols,
and funnel traps. Because of their cryptic nature and difficulties in
capturing adequate numbers of most species, adult frogs in general were
not marked for recapture. Instead, the most effective method of monitorin;
the frog populations proved to be recording on data sheets the calling
activities of males during herp-patrols. This sampling technique was
expanded in December 1977 to Include actual counts of calling males per
10-m. increments on all permanent shoreline sites.
Snakes
30. All species of aquatic and semiaquatic snakes on Lake Conway
were monitored by diurnal shoreline censuses, herp-patrols, and funnel
traps. All collected snakes were identified, sexed (adults only),
weighed and measured, individually marked by clipping the ventral scales
(Brown and Parker 1976), and released at the capture site.
12
PART III: THE LAKE CONWAY SYSTEM
31. Lake Conway is a 737.1-ha. urban lake (Figure 1) located in
South Orlando, Orange County, Florida. The lake consists of five inter-
connecting pools, which include Lake Gatlin, Little Lake Conway (East
and West Pool), and Lake Conway (Middle and South Pool), The lake system
is mesotrophic with gradually increasing eutrophic conditions as one
proceeds north through the various pools. The substratum is primarily
sand, except in areas of thick vegetation near shore or in dredged
canals where organic detritus or silt has accumulated. The bottom
contours are rather steep when compared with most central Florida lakes
and greater than 30% of the total lake bottom is deeper than 6.0 tn.
(Nail and Schardt 1978).
32. Illinois pondweed (Potomogeton illinoensis) and eelgrass
(Vallisneria americana) are the dominant shallow-water (<2,0 m.) aquatic
macrophytes in most pools; stonewart (Nitella megacarpa) and hydrilla
(Hydrilla verticillata) predominate in deeper water but do not grow
below 6.0 m. (Nail and Schardt 1978). As is typical of many urban
Florida lakes, most of the emergent vegetation on Lake Conway has been
removed for beach development. However, in some areas a narrow fringe
of maidencane (Panicum hemitomon), lake rush (Fuirena sclrpoides),
pickerelweed (Pontederia lanceolata), or cattail (Typha latifolia)
remains intact.
33. Given below are brief descriptions of each permanent shoreline
herpetofaunal sampling site and a chronology of important events.
Appendix A summarizes the vegetation and substratum characteristics of
each permanent trapping station for all sites during the baseline study
period (June 1977-September 1978). Because deepwater trapping stations
duplicated the vegetation transects of the Florida Department of Natural
Resources (Nail and Schardt 1978) in South (Transect A.-A2), Middle
(Cj-C2) , East (I-j-ip, and West Pool (K^-K^) and Lake Gatlin (N -N„),
these data are not duplicated herein.
13
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South. Fool
34. The South Pool permanent shoreline site was 530 m. in length and
included the only major section of undeveloped shoreline in the pool
(Figure 1). Other small, scattered patches of Panicum or Typha occurred
along the eastern and northeastern shores of South Pool, However,
these patches of emergent vegetation had houses on the upland. The South
Pool site underwent rapid development for housing during the baseline
study period (see below) and was studied intensively during this period to
determine the effects of shoreline development on the herpetofauna.
35. Initially, the site consisted of 460 m. of emergent vegetation
stretching from an offshoot canal (marker 0) to the Perkins Street boat
ramp (460), and 70 m. of urban beach habitat (460-530) to the northwest
of the boat ramp. In order of decreasing abundance, the more common
emergent species were Fuirena scirpoides, Panicum hemitomon, Pontederia
lanceolata, Typha latifolia, and Eichhornia crassipes (see Appendix A).
Undisturbed pine-flatwoods or evergreen bayhead associations occurred
upland from the vegetated shoreline. Potomogeton illinoensis was the
dominant nearshore submergent aquatic plant. The substratum at the
trapping stations was mostly sand except for a buildup of mucky detritus
at markers 0-30 and 450-460 where waterhyacinths occurred. A thin (3-5
cm.) layer of silt usually was present at stations dominated by stands
of P_. lanceolata. Offshore, the water dropped off rapidly to 2.0 m.
in depth except at marker 0 (and offsite eastward from there) and
between markers 320-530 (and northward), where broad shelves of shallow
water (less than 1.5 m.) extended 30 to 60 m. out from shore.
36. As mentioned, development of the South Pool shoreline site
for housing occurred during the baseline study period. Habitat modifica-
tion began in August 1977 and involved the clearing of access roads
through the upland pine-palmetto flatwoods arid abandoned orange groves
west of the site, an area of approximately 20 ha. In late September
1977, construction of two houses began immediately upland between markers
345-460, and another house was started along the shore in mid-October
between markers 240 and 300. In both cases construction activity was
14
limited to the housing sites. The littoral zone and first 30 to 50 m. of
transitional uplands were left undisturbed temporarily. In mid-December
all remaining vegetation in these two areas (240-300, 345-460) from the
houses to within a meter of the waterline was cleared with bulldozers.
This left only a small piece of undisturbed transition zone between
300 and 345, and a larger section from 0 to 230.
37. In late November and December 1977, most of the housing lots
in the pine flatwoods and abandoned orange groves greater than 100 m.
from shore between markers 200-460 were cleared of understory vegetation.
By mid-April 1978, almost all remaining upland habitat (0-200) along the
South Pool site had been cleared to within 30 m. of the shoreline. In
late April, the remaining vegetation from markers 30 to 120 was removed
with bulldozers to the waterline. Small sections of the littoral zone
also were cleared from 240 to 250, 345 to 355, and 390 to 400 by June 1978.
38. In summary, within 10 months of the start of herpetofaunal
sampling of Lake Conway, approximately 78% of upland and transitional
zone habitats bordering the South Pool site was cleared of natural
vegetation. Although most of the emergent littoral zone vegetation was
left intact, most site preparation occurred in winter and early spring.
Middle Pool
39. The Middle Pool permanent shoreline site (Figure 1) was
located at the northern end of a large cattail marsh that extended along
much of the southeastern shore of Middle Pool. Emergent vegetation at
this site was zoned with a broad, 20- to 40-m. outer fringe of cattails
(Typha latifolia) and a narrower, denser inner zone of herbaceous aquatics.
Near the trapping stations, Fuirena scirpoides and Panicum hemitomon
dominated at markers 1000 to 1030, T\ latifolia and Pontederia lanceolata
from markers 1040 to 1170, and Eichhornia crassipes at markers 1180 to 1200.
Upland, the site was bordered by an orange grove. In the cattail zone and
immediately offshore, Potomogeton illinoensis was the only submergent
macrophyte. At this site, P. illinoensis was sparsely distributed, and
percent cover generally was less than 20%. The substratum was coarse
15
^IKW-WJ^VK :*y•«S-fW5f^
sand except in thick vegetation nearshore where a layer of organic
detritus had been deposited. In general, this muck overburden increased
in thickness from markers 1000 to 1200.
40. The band of emergent vegetation at the Middle Pool site was
much broader than at other sites. To more accurately determine habitat
preferences and to monitor the movements of marked animals, three parallel
transects were established along the 200-m, length of this site, A
nearshore transect, where trapping was conducted, was designated the
1000 series. To monitor amphibian and reptile activity within the
cattails and to provide boat access (2000 series) during herp-patrols,
a 2.0-m.-wide swath was removed from the center of the cattail marsh in
October 1977. In addition, the outer edge of the cattails (3000 series)
was herp-patrolled.
41. In April 1978 after nine months of study, all shoreline and
upland vegetation between markers 1000 and 1120 was cleared with bull-
dozers and draglines. This resulted in the removal of all vegetation
from trapping stations 1000 to 1120 and the 2000 series of cattails from
markers 2000 to 2120. A lO-m.-wide outer fringe of cattails and the
3000 series were left intact. To document changes in amphibian and
reptile distribution and abundance at this site as a result of habitat
modification, normal sampling procedures were continued.
East Pool
42. The permanent sampling site in East Pool was located at the
northwest end of an uninhabited island (Figure 1). This site was 200 m,
in total length and consisted of a 10- to 15-m. outer fringe of cattails
(Typha latifolia) and an inner zone of waterhyacinths (EichhornJa crassipt
along most of the distance. A 20-m. stretch of Panicum hemitomon and
Pontederia lanceolata occurred from markers 1025 to 1045, Funnel trapping
was conducted along the inner zone (1000 series) and herp-patrols (2000
series) were run along the outer edge of the emergent vegetation, A 10-
to 25-cm. layer of mucky detritus was present in all areas with water-
hyacinths. Immediately offshore the bottom dropped sharply to over 2,0 m
16
1!" "I:
^4 ••W^/l^n^tn^f~<fX r,-!,^,-,!'—-H--.-.;-ri..,^tr?-rt,rr r-.-M—,- -^, - -.-.. ... T—• -. -• - --" r • rf- >r^r--t -r^W•^7I"^[gp«p»JBf^B?R "^pwMwr#mm^#gp^gp*^
in depth. The submergent aquatic vegetation was primarily Vallisneria
americana with scattered patches of Potomogeton illinoensis on a sand
bottom. No development occurred at this site during the baseline
study period.
West Pool
43. The West Pool permanent shoreline site was 370 m. in total
length. It encompassed the only large, continuous section of emergent
vegetation in the pool and was bordered by beach habitat at both ends.
The site included a 70-m. stretch of beach (markers 0-70) and a larger
section of undisturbed littoral zone (markers 80-370) dominated by
Panicum hemitomon-Pontederia lanceolata or P_. hemitomon-Eichhornia
crassipes with scattered patches of Typha latifolia. An orange grove
which was regularly disked occurred 10 to 15 m. upland of the vegetated
shoreline. The dominant submergent plants at the edge of the emergent
vegetation were Potomogeton illinoensis and Vallisneria americana. The
substratum at the trapping stations consisted of sand along the beach
and a variable (5- to 20-cm.) layer of silt and organic debris in the
vegetated section. The bottom contours along most of the West Pool
site were gradual but several deep holes (to 2.0 m.) occurred immediately
offshore.
44. During the baseline study period, no development occurred on
the West Pool site. To serve as a control for the effects of housing
development in South Pool and to more clearly determine the home ranges
of individuals along a continuous section of habitat, the West Pool site
was gradually enlarged from an original 200 m. (markers 0-200) to 370 m.
(0-370) by July 1978. West Pool was chosen because this site was most
similar to South Pool in terms of size, vegetation, and topography,
and because it was deemed unlikely that it would be developed in the
next five years.
17
II MWIL-rmt ""' "•&*^5}"""j-^*HA'&^^ia^fTfyqF^TLfr^.?•f-r^-^M^ ^vni^^asivTC "^y^w^^^f^^Tt^V^J^IJWVy' -rynML',!',* #*,.,,",,, .^^H^H^|Hji|
Gatlin Canal
45. The permanent shoreline site chosen for Lake Gatlin was the
entire length of the canal from Lake Gatlin to West Pool (470 ra.).
This site represented the most eutrophic site sampled in Lake Conway and
was typical of the many shallow, dredged canals in the system. Most of
the shoreline bordering Gatlin Canal consisted of yards mowed almost to
the waterline. Emergent vegetation along the yards included Panicum
repens, Nymphaea odorata, Nuphar luteum, and Typha latifolia, in order of
decreasing abundance. Away from shore, most of the dredged bottom was
less than 1.0 m. in depth, bare, and with a 0.1- to 1.0-m. layer of
unconsolidated silts and muds. Large mats of floating filamentous algae
were common in summer. Initially the only submergent aquatics included
a small patch of Vallisneria americana on the east side of the canal
between markers 1130 and 1150, Cabomba caroliniana in the west offshoot
canal at marker 150, and some Eleocharis sp. near the bridge (markers 230-
By the end of the baseline study period (September 1978), the (X
caroliniana mat had spread and occurred from markers 1120 to 1150.
46. Unlike all other sites, only one herp-patrol run was done in
Gatlin Canal. However, this run often required 1.5 hrs. and included a
census of both the east and the west sides of the canal. To distinguish
movements of marked animals across the canal, the west side of Gatlin
Canal was designated the 100 series and the east side the 1000 series.
A total of 20 funnel traps were set in Gatlin Canal from markers 0 to 40
and 1050 and 1190 so that all major habitats would be sampled.
47. No major development occurred in Gatlin Canal during the
baseline study period other than normal mowing and yard upkeep.
13
«u
PART IV: THE HERPETOFAUNA OF LAKE CONWAY
48. A total of 5,836 individuals representing 11 species of
amphibians and 16 species of reptiles were observed or captured on Lake
Conway during the 15-month baseline study period (June 1977-September
1978). Only species dependent on Lake Conway proper for some portion of
their life cycle and therefore potentially affected by the introduction
of white amur were considered. Figure 2 shows the cumulative number of
species as a function of the cumulative number of individuals recorded
on Lake Conway. Approximately 96.3% of the sampled herpetofaunal species
was obtained within the first 3,000 specimens and one species thereafter.
Based on this sample, there are three species of salamanders, eight
anurans, one crocodilian, eight turtles, and seven snakes inhabiting the
Lake Conway complex (Table 1). Several other rare species may be present.
49. Table 2 gives the frequency distribution of species by
sampling method. On all subsequent tables, information for the different
life stages (egg, larva, adult) of each species is tabulated separately.
Herp-patrol and funnel traps accounted for 86.54% and 8.10%, respectively,
of all animals observed or captured on Lake Conway. These two methods
also produced the greatest number of captures (of 2,281 individuals,
71.2% and 20.7%, respectively).
50. The probability of capturing or observing a species also
varied by sampling method. Of the 27 amphibian and reptile species
known from Lake Conway, 23 species were identified on herp-patrols and
three (Deirochelys reticularia, Hyla femoralis, H_. squirella) were known
only from herp-patrol activities. No species were taken only in funnel
traps during the baseline study period, but this method did account for
a sizeable portion (>30%) of the observations for Amphiuma means (93.5%),
Siren lacertina (57.8%), Kinosternon subrubrum (49.1%), Nerodia eyelopion
(31.1%), and most anuran larvae. Three species were known only from
shoreline censuses, including a salamander (Eurycea quadridigitata) and
two snakes (Regina alleni, Thamnophia sirtalis). All other species were
taken by at least two sampling methods.
19
^i•"!•*• f.TTj^
Species Distribution and Abundance
51. Table 3 summarizes the distribution of all amphibian and
reptile species recorded from the five pools of the Lake Conway complex.
These figures include the total number of specimens observed or collected
by all sampling methods on and off the permanent stapling sites in each
pool. Because sampling effort and catch varied between pools, these
data provide only a preliminary estimate of the relative species
density and abundance between pools.
52. Judging from the total cumulative species-number curve for Lai
Conway shown in Figure 2 and the total number of observations recorded fc
each pool (Table 3), between 70% and 80% of the total herpetofaunal
species inhabiting each pool has been recorded. South Pool had the
greatest total number of observations (N=1,429) and the highest number oi
recorded species (N=22); West Pool had the lowest total number of obser-
vations (888) and recorded species (14). Other pools had intermediate
values but the species rank order was not in agreement, perhaps indicatii
differences in habitat availability, species evenness, and/or sampling ei
53. The known distribution of herpetofaunal species varied by
pool (Table 3). Of the 27 species presently recorded from the Lake
Conway system, 11 occur in all pools. These 11 species account for
94.44% of the total observations; none represent less than 1.71% of
the species total. Among the 16 species not known from all pools, no
single species contributes more than 1.35% to the species total,
Additional observations in poststocking years should more clearly
define the distribution of rarer amphibians and reptiles within the
Lake Conway system.
Permanent Shoreline Sites
54. Table 4 presents the distribution of the total number of
individuals of all species encountered on permanent shoreline sites in
each pool. These five sites accounted for 71.85% of the 5,836
20
"^T-M ^^^^^^^^^^ mWMMUWM
herpetofaunal observations made during the baseline study period and were
the major locations for funnel trapping and herp-patrolling activities.
Of the 27 species presently known from Lake Conway, 26 were observed on
permanent shoreline sites. One salamander (Eurycea quadridigitata), a
frog (Hyla squirella), three turtles (Chelydra serpentina, Deirochelys
reticularia, Kinosternon bauri), and four snakes (Coluber constrictor,
Regina alleni, Thamnophis sauritus, T. sirtalis) were recorded only on
these permanent sites. The treefrog Hyla femoralis is the only species
on Lake Conway not known from a permanent shoreline site.
55. Table 4 also gives the mean relative density of each species
on the five permanent shoreline sites as determined by the two major
sampling methods: herp-patrol (mean number/hr.) and funnel traps
(mean number/100 trap days) . Between-pool differences in relative
abundance of a species were determined by using the chi-square approxi-
mation of the nonparametric Kruskal-Wallis extension of the Mann-
Whitney U-test (Barr et al. 1979) for herp-patrol trips, and the
difference among proportions chi-square test (Freund 1973) for funnel
trapping. The mean tested on herp-patrols was the mean number of
individuals of a species observed per hour for all trips with run numbers
on a permanent site (i.e., after October 1977). The proportion tested
was the total number of a species captured at a site divided by the total
number of trap days set at that site during the baseline study period,
If significant (P<.05) between-pool differences were found, pair-wise
comparisons of pools were made using the Mann-Whitney U-test (herp-patrols)
or the difference among proportions test (funnel traps). Because the
same data were analyzed for this second test, the alpha level of signi-
ficance was increased to P<.025.
56. The mean relative densities of 11 species were found to vary
significantly between the five permanent shoreline sites during the
baseline study period (Table 3). Funnel trapping showed significant
between-site differences in the relative densities of two salamanders
(Amphiuma means, Siren lacertina), three frogs (Hyla cinerea larvae,
Rana grylio adults and larvae, R. utrlcularia larvae), two turtles
(Kinosternon subrubrum, Sternotherus odoratus), and a snake (Nerodia
21
'•a. • '^^^^)WI^^'!^T'^^^^*^7'^%^r^^^f 7^?"^?^ "*Ti-f— «-npr*rrv 'THpyng? jr-Ty-.?•?•" ?f-r vye? p^ryp* t- ry-wr«nggy^B •jf^r^rt^r^p^ paprgy^? wm Mfflmpi ffiWflSNiWj
cyclopion). The mean number of individuals observed or collected per
hour on herp-patrols varied significantly in four species including one
frog (Acris gryllus) and three turtles (Chrysetnys floridana, CL nelsoni,
J3. odoratus) .
57. Four species of frogs (Hyla cinerea, Gastrophryne carolinensi;
R. grylio, R. utricularia) recorded on herp-patrols differed in the mean
densities of calling males, but the site means were not significantly
different if the entire baseline study period was considered (Table 4).
When only the breeding seasons of these species were analyzed, signifi-
cant between-site differences in mean densities were obtained for
A. gryllus, H. cinerea, R. grylio, and R. utricularia (Table 5).
Apparently, the large number of tied scores introduced by including the
many nights during the nonbreeding season, when no frogs were calling,
biased the rank sums tests and significantly reduced the differences
between sites.
58. Included below are detailed community analyses of the five
permanent shoreline sites on Lake Conway. For each site a "point analys:
and a "trip analysis" are presented. Point analyses show the numerical
distributions of amphibians and reptiles observed or captured along 10-m
increments of the shoreline sites. Trip analyses show the numerical
distributions of species through time on the bimonthly sampling trips
to Lake Conway. Table 1 provides the species codes used in all point
and trip analyses figures cited.
59. For both the point and the trip analyses of each site at
least three figures are given, one for funnel trapping (total captures)
and two for herp-patrols (anurans only, and salamanders and reptiles
only). Each figure provides the total number of funnel traps set at a si
(per trip or per trap station) and for herp-patrols, the total time
(minutes) spent on each herp-patrol trip at a site • Thus, each figure
is scaled by sampling effort. In some cases the total number of indivi-
duals recorded on the point analysis for a site will be less than the
number of individuals recorded on the trip analysis for that site; this
means that some individuals on a trip were not given a sample point
and thus do not appear on the point analysis.
22
X *M
•• r-,- ^nM^K-a^,^ K%^ ?YF^P?7*" *w •"* ^"Wffi-'w^wflWiS^JW'.!'! !>'* 'W-iWPipl
South Fool
60. The South Pool permanent shoreline site had the most diverse
herpetofauna of any site (20 species), but also received the most
sampling effort (Table 4). The relative density of one species
(Kinosternon subrubrum) was significantly greater on South Pool than on
all other sites (Table 4). The highest total number of observations for
11 other species also was recorded from the South Pool site including
two frogs (Acris gryllus, Hyla squirella), four turtles (Chrysemys
floridana, Kinosternon bauri, K. subrubrum, Sternotherus odoratus), and
five snakes (Coluber constrictor, Farancia abacura, Nerodia cyclopion,
Regina alleni, Thamnophis sirtalis). Four of these species (H, squirella,
C^. constrictor, R. alleni, ^T. sirtalis) were encountered only on the
South Pool site during the baseline study period. Thus, many elements of
the Lake Conway herpetofauna are best known from South Pool,
61. During the baseline study the shoreline of the South Pool
site was developed gradually for a housing subdivision (Table Al),
Because shoreline development was gradual, changes in herpetofaunal
populations are expected to be subtle,
62. Point analysis. The distribution of all amphibians and
reptiles captured in funnel traps along the South Pool permanent shore-
line site is presented in Figure 3. Most (91.7%) of the 84 total captures
in South Pool were concentrated between markers 0 and 100 and between mark-
ers 360 and 460, where 48.0% of the total traps was set during the baseline
study period (Figure 3). In general, these more productive trapping areas at
the ends of the transect were characterized by a diverse emergent flora and
a mud substratum; the central, animal-poor region was dominated by
Fanicum hemitomon-Fuirena scirpoides and a sand substratum (see Table
Al). In addition, much of this central region underwent extensive
development near shore during the baseline study period (Table Al).
63. The spatial distribution of reptiles observed or collected on
herp-patrols (Figure 4) was similar to the pattern observed for funnel-
trapped animals (Figure 3) along the same section of shoreline (i.e., mark-
ers 0 to 460; traps were not set between 470 and 530 and thus data from
this section are not comparable). Most observations (67.1%) of reptiles
23
on herp-patrols between markers 0 and 460 were located between 0 and 100
and 360 and 460. However, in this case the concentration of reptiles (es
pecially Sternotherus odoratus and Chrysemys floridana) at the ends of tr
transect may be correlated with offshore habitat preferences rather
than with their preference for emergent vegetation in the littoral zone.
Both turtle species were active in shallow-water regions at night.
On the South Pool site, deep water occurred immediately offshore from
the emergent vegetation except at the ends of the transect (see South
Pool site description, paragraph 36), At the transect ends broad
shelves of shallow (<1.5 m.) water extended out from shore and most
turtles were captured in these areas (Figure 4), It is perhaps signifi-
cant that the greatest concentration of turtles occurred between markers
470 and 530, a section of developed shoreline with extensive shallows
but no emergent vegetation.
64. The distribution of calling frogs on the South Pool site is
given in Figure 5. The cricket frog, Acris gryllus, was the most common
frog on this site (Table 4, Figure 5) and was recorded calling along mosJ
of its length. Other species appeared to have a more patchy distribution
during the baseline study period, but the total number of observations
was small.
65. Trip analysis. Figure 6 shows the temporal distribution of
amphibians and reptiles collected in funnel traps on the South Pool
permanent shoreline site. In general, trap success decreased with time
on the site even though the number of traps set per trip increased. The
highest success rates occurred early in the study, between 21 July-24
September 1977. In this time period the few funnel traps available for
sampling (N=13) were set between markers 0 and 120. These traps account'
for 34 (66.6%) of the 51 total animals taken along this section of shore-
line during the baseline study period (Figure 3). When the trapline was
expanded to include the entire piece of vegetated shoreline (21 March 19'
most subsequent specimens were taken between markers 0 and 120 and betwe*
markers 360 and 460, although rates of capture for 0 to 120 were lower.
66. The relatively low trapping success for any one species makes
seasonal activity patterns difficult to evaluate for this site alone
24
"•AC i ifjE»i|ljj3l|jl^g||qjj|M^
(Figure 6). The only conspicuous change was the absence of the green
water snake (Nerodia cyclopion) from traps between October and February,
During this time N. cyclopion were observed leaving the water and entering
upland overwintering sites.
67. The temporal distributions of all species other than frogs,
and calling frogs, on South Pool herp-patrol trips are given in Figures
7 and 8, respectively. Most individuals of salamanders and reptiles
(Figure 7) generally were observed early in the study (July^November
1977) and decreased thereafter. A secondary peak in total*abundance
occurred in the summer of 1978, The highest peak on 17 November 1977 was
associated with the greatest amount of time spent on the site during a
single trip (187 min.). However, the mean total number of individuals
observed per hour on this trip (23.74/hr.) was 2.48 times the mean for
all trips (9.59/hr.) and truly reflects a high, local density of animals.
68. The stinkpot, Sternotherus odoratus, accounted for a majority
of the reptilian observations on nearly all herp-patrols (Figure 7).
Most apparent seasonal patterns in Figure 7 can be attributed to this
species, but Chrysemys floridana also followed the same trends (i.e.,
the relative densities of both species were high in fall and summer but
low in winter arid spring). Nerodia cyclopion was encountered on herp-
patrols from July to November 1977, but disappeared until 27 March 1978
when a single individual was observed. No other specimens of this snake
species were seen on South Pool herp-patrols throughout the remainder
of the baseline study period.
69. Frog calling activity on the South Pool site varied by
species and by season (Figure 8). Rana utricularia was the only species
heard calling in the late fall and winter months. All other species
called during spring and summer with some activity in early fall.
Middle Pool
70. The Middle Pool site had the second highest number of recorded
species (18), but the mean relative density of any one species was not
significantly higher or lower than other permanent shoreline sites
(Table 4). Middle Pool was the only site where the salamanders
Amphiuma means and Siren lacertina were equally common (A. means was
25
fr^^r^n^KTO^p^^ff^
4.27 times more abundant than _S, lacertina averaged over all sites,
4). Pig frogs (Rana grylio) and ribbon snakes (Thamnophis sauritus)
more common at the Middle Pool site than at any other site. Of the
female alligators (Alligator mississippiensis) known to nest on Lake
during the baseline study period, one nested in the marshes of the &
site and successfully hatched 12 to 16 young in August 1977. The ne
of this female (marker 1110) was destroyed in April 1978 (see below)
the best of the authors' knowledge, she did not nest on Lake Conway
summer of 1978.
71. The Middle Pool site underwent significant changes during
baseline study period (Table A2). On 26 April 1978 all upland and
shoreline vegetation between markers 1000 and 1120 and between 2000
2120 was cleared with bulldozers and draglines for a housing develo]
but markers 1121 to 1200 and 2121 to 2200 were left intact (see par.
To better elucidate changes in the distribution and abundance of tin
fauna as a result of this perturbation, the analyses that follow we:
into several subsets. All transects (1000, 2000, and 3000 series) i
divided into "disturbed" (meters 0 to 120) and "undisturbed" (meter
to 200) sections. In addition, all point and trip analyses were fu
subdivided into before and after disturbance categories.
72. Point analysis. Figures 9 and 10, respectively, show the
spatial distribution of funnel-trapped animals before and after the
Middle Pool site was cleared. Before development (Figure 9), most
(60.84%) occurred between markers 1100 and 1200, where organic detr
thickest and waterhyacinth (Eichhornia crassipes) often was the dom
vegetation (Table A2). In the section with little organic matter
(markers 1000-1090), all captures occurred in the Panicum hemitomon
Fuirena scirpoides zone between markers 1000 and 1020. Trap static
nated by Typha latifolia or Pontederia lanceolata (1030-1090) produ
captures.
73. After habitat modification (Figure 10), only one individu
(a Rana utricularia larvae) was collected in 122 trap days on the d
section (markers 1000-1120); 12 individuals representing 6 species
taken in 180 trap days before this section was cleared (Figure 9).
26
ammmmmmmmmmmmmmmmmmmm
30l
1).
0-
ed
On the undeveloped section (markers 1130^-1190), 10 individuals of 4
species were collected in 50 trap days before the adjacent section was
cleared; 24 individuals of 9 species were recorded in 70 trap days after
clearing. These data suggest that (1) clearing of the emergent
vegetation severely reduced herpetofaunal populations in the altered
areas and (2) surviving individuals may have emigrated to the adjacent,
undisturbed habitat.
74. The spatial distribution of salamanders and reptiles observed
on Middle Pool herp-patrols before and after habitat modification is
given in Figures 11-14. The clearing of this site resulted in the
removal of all aquatic vegetation on the 2000 series transect from 2000
to 2120 but left intact a narrow finger of cattails extending along the
3000 series from 3000 to 3120. Habitat between meters 130 and 190 on
both herp-patrol transects was not altered (see Middle Pool site descrip-
tion, paragraphs 39-41).
75. In the zone of habitat alteration (meters 0-120), significant
changes in the local abundance of organisms occurred on both the 2000
series and the 3000 series transects. On the disturbed portion of the
2000 series transect (2000-2120 of Figures 11 and 12), 87 specimens (7
species) were seen on 14 herp-patrols before clearing (x=6„21 individuals/
trip); only 4 specimens were observed in 10 trips after clearing (x=0,40).
On the adjoining portion of the 3000 series transect (3000-3120 of
Figures 13 and 14), which was sampled on the same trips, 146 individuals
were recorded before clearing (x=10.43) but only 13 afterwards (x=1.30).
In contrast, no major changes in the abundance were noted on the
undisturbed sections of either transect (2130-2200 predisturbance
x=1.20, postdisturbance x=1.20; 3130-3200 predisturbance x=2.10,
postdisturbance x=1.36).
76. The spatial distribution of calling frogs also varied as a
result of habitat modification (Figures 15 and 16). Unfortunately, rigorous
recording of the exact locations of calling males did not begin until
December 1977 (see Part II: "Methods and Materials"); thus, the predistur-
bance period is underrepresented. However, four frog species called
from markers 1000 to 1120 before disturbance (Figure 15), but only two
27
species were recorded from this section thereafter (Figure 16), Acris
gryllus and Bufo terrestris can inhabit and successfully call from shore
grass or bare beach environments. However, both Hyla einerea and Rana
grylio require thick emergent vegetation; these species apparently were
extirpated from the disturbed zone,
77. Trip analysis. The temporal distribution and abundance of
herpetofaunal species taken in funnel traps on the disturbed (1000-1120)
and undisturbed (1120-1200) sections of the Middle Pool site are given i
Figures 17 and 18, respectively. On the disturbed section (Figure 17)
total trap success was significantly greater prior to habitat destructlo 2 than afterwards (% =5.33, P<.05). On the undisturbed section (Figure 18
more animals were collected after habitat modification, but the differen
was not significant (x2=2.92, .05<P<.10),
78. The distributions of salamanders and reptiles observed on the
two Middle Pool transects during herp-patrol trips are provided in
Figures 19-22. As previously noted, the abundance of animals decreased
markedly on the disturbed sections of both transects after habitat
alteration (Figures 19 and 21), but the adjoining, undisturbed sections
showed no changes (Figures 20 and 22). The high number of Sternotherus
odoratus recorded on 7 December 1977 (Figures 19 and 21) was the result 2
a remarkable concentration of 53 stinkpots in a 10-m. area between
markers 60 and 70 of the 2000 and 3000 series transects. Such localized
concentrations were not observed again on the Middle Pool site during
the baseline study period.
79. The temporal distribution of calling anurans recorded on the
Middle Pool site is presented in Figures 23 and 24. On the disturbed
section (Figure 23), a decrease in the abundance and diversity of frog
species apparently occurred after habitat modification. Because the
predisturbance period (prior to December 1977) was poorly documented
for calling frogs, seasonal fluctuations in calling activity on the
undisturbed section (Figure 24) were difficult to detect. Most species
appeared to call during the warmer summer months.
East Pool
80. A total of 15 amphibian and reptile species were observed on
28
~^^7^
the East Pool site during the baseline study period. The relative
densities of three species (Amphluma means, Siren lacertina, Hyla cinerea
larvae), as measured by funnel trap success, were significantly higher
at East Pool than at all other sites (Table 4). In addition, East Pool
was the only site where the dwarf salamander, Eurycea guadridigltata,
was found. All of these species were associated with, the mats of
waterhyacinth (Eichhdrnia crassipes) that dominated much of the site.
81. Point analysis. Compared with other permanent shoreline sites,
the distribution of funnel trap captures on East Pool was more uniform
(Figure 25). However, trap stations 1090 to 1200, which were dominated by
waterhyacinth. (Table A3), produced the greatest number of captures.
Amphluma means was the most frequently collected species on this site
(Table 4) and was recorded from all trapping stations. Siren lacertjna
was taken at all stations except 1050 to 1100. Nerodia cyclopion appeared
more common at stations with greater plant diversity. Only 2 of 15
N. cyclopion collected in East Pool funnel traps during the baseline
study period were recorded from stations dominated by waterhyacinth.
82. Although sample size was small (N-62), most reptiles observed
on herp-patrols (75.8%) were recorded from the second half of the transect,
between markers 2110 and 2200 (Figure 26). Calling frogs also were most
abundant on the latter half of the transect (Figure 27) . Hyla cinerea
was especially common at this site and frequently called from water-
hyacinths and cattails between markers 1160 and 1180.
83. Trip analysis. Figure 28 shows the distribution through time
of funnel-trapped amphibians and reptiles on the East Pool site, East
Pool showed less variance than other sites during the baseline study
period with no marked decline in trap success. Activity was lowest
during the winter months of 1977-78, but increased in spring and stayed
high in the summer and the fall of 1978. Anuran larvae (Hyla cinerea,
Rana grylio, R. utricularia) were collected from May through September
of 1978.
84. In contrast to funnel trapping, the number of nonfrog species
observed or collected during herp-patrols on the East Pool site declined
through time (Figure 29). This was due primarily to the relatively
29
large numbers of Sternotherus odoratus collected on early trips, which
were not seen as frequently later in the study period.
85. The temporal distribution of calling frogs on East Pool was
similar to that of other sites (Figure 30), Greatest activity for most
species occurred from spring through early fall with a peak in late
summer. Rana utricularia was the only species to call frequently in the
winter.
West Pool
86. The West Pool permanent shoreline site had the lowest number
of amphibian and reptilian species (N=12) recorded for any site (Table 4
This was caused by an apparently depauperate snake fauna: only one spec
(Nerodia cyclopion) was recorded on the West Pool site but seven were
known from the Lake Conway system (Tables 3 and 4). Four turtle species
(Chrysemys floridana, C\ nelsoni, Sternotherus odoratus, Trionyx ferox),
which were common on most of Lake Conway, were relatively rare on the
West Pool site (Table 4). However, the greatest total number of
observations of three frog species (Hyla cinerea, Gastrophryne
carolinensis, Rana utricularia) were recorded from this site,
87. Point analysis. The spatial distributions of amphibians and
reptiles collected in funnel traps on the West Pool site are given in F:
ure 31. Trap stations 0 through 70 were located on beach habitats in s<
stages of succession (Table A4). These stations produced no captures e^
though 24.1% of the total number of traps set in West Pool during the
baseline study period were located in this region. On nonbeach trappin;
sites (80-370), the 13 stations dominated by waterhyacinth (Table A4)
produced the greatest proportion of captures, accounting for 59,7% of
the total captures but only 26.5% of the traps set.
88. As noted for South Pool, the distribution of salamanders and
reptiles observed on West Pool herp-patrols appeared to be dependent
primarily on offshore habitat preferences of the component species,
Sternotherus odoratus was the most commonly encountered gpecies, and ov
21% of the observations of this species on West Pool were recorded at
marker 30 (Figure 32). This spot was offshore from beach habitat but
was the only area on the West Pool site where dense stands of Potomoget
30
"TtrwnByyt- M^%(dg#KeR^#^#i^^'jgi;«*y^ •• H^ff li^Wil
occurred in shallow water,
89. The distribution of all species of calling anurans on the West
Pool site appeared clumped (Figure 33), The most abundant species, Hyla
cinere a. requires erect vegetation for calling sites. It called primarily
from four areas containing dense stands of Fontederia lanceolata or
Typha latifolia (markers 120-130, 160, 220-240, 290-310). The second
most common frog, Gastrophryne carolinensis, vocalized most frequently
from grass clumps along four sections of the West Pool site (Figure 33).
90. Trip analysis. Figure 34 presents the temporal distributions of
funnel-trapped amphibians and reptiles on the West Pool site. When the
frequency of captures was adjusted for the gradual increase in trapping
effort, seasonal trends in activity became more apparent. Total trap
success was lowest during the cold winter months (x=0; 0 individuals/119
trap days), gradually increased in spring (x=0,057; 9/159) and summer
(x=0.206; 46/223), then decreased in fall (x=0.168; 19/113). These
trends are due primarily to Amphiuma means, the most commonly trapped species
on the site.
91. The temporal abundances of reptiles and salamanders encountered
during herp-patrols on the West Pool permanent shoreline site are given in
Figure 35. Peaks of abundance appeared in the fall of 1977 and the spring
of 1978, but the total sample size was small (N=65 observations). On 10
of 29 herp-patrol trips made to the West Pool site during the baseline
study period, no salamanders or reptiles were observed.
92. The seasonal activity of calling frogs on the West Pool
site (Figure 36) was similar to that on other sites on Lake Conway, Hyla
cinerea was the most common species on West Pool and called primarily in
summer with a secondary peak in spring. Although most calling of
Rana utricularia occurred in fall and winter, some individuals of this
species called on warm, wet summer nights from West Pool.
Gatlin Canal
93. For a disturbed man-made habitat, the Gatlin Canal site contained
a surprisingly high number of species (N=14). This may be because of the
diverse array of microhabitats within the canal (Table A5) and/or because
of the accessibility of the two other major, alternate habitats (West
31
Pool and Lake Gatlin), Gatlin Canal was the only site where all species
of aquatic turtles were known to occur, and the relative densities of thr
species (Chrysemys floridana, £, nelsoni, Sternotherus odbratus) were
relatively high (Table 4). However, for the effort expended at the
Gatlin Canal site the diversity and abundance of snake species was low
(Table 4), probably because of the proximity of development and the
tendency for land owners to kill most snakes,
94. Point analysis. The spatial distributions of amphibians and
reptiles at funnel trap stations along the Gatlin Canal site are represen
in Figure 37. Only 27 captures were recorded in 420 trap days at this
site. As a result no between-habitat differences in abundance in Gatlin
Canal were apparent for the baseline study period,
95. Figure 38 shows the distribution of salamanders and reptiles
observed during herp-patrols on the west (100 series) and east (1000
series) sides of Gatlin Canal during the baseline study. Slightly more
individuals (54.2% of 387 total observations) were sighted on the east
side than the west side. Sternotherus odoratus was the most common
reptile at this site. The largest concentration of stinkpots occurred
near the entrance of Gatlin Canal into West Pool, where a large patch
of Nuphar luteum was established (markers 10-40), The species also was
common along the shore opposite the Nuphar bed, which was bordered by
Paspalum sp. and beach habitat. Other areas in Gatlin Canal also produce
large numbers of stinkpots (e.g. markers 1300-1340) but the association
of the turtle with specific habitats was not obvious,
96, Compared with other sites relatively few frogs were heard callir
in Gatlin Canal, but their spatial distribution appeared patchy (Figure
39). For example, the southern toad, Bufo terrestris, called only from
beach habitats or where the grass was mowed to the water's edge. Hyla
cinerea was heard calling mostly from stands of Pontederia lanceolata
or Typha latifolia.
97, Trip analysis. Figure 40 shows, the temporal abundances of
amphibians and reptiles captured in funnel traps in Gatlin Canal, No
individuals were taken in traps from November 1977 through February 1978,
Like other sites, most captures occurred during the warm summer months.
32
^^^^
98. The distribution of reptiles and salamanders observed on each,
sampling trip to Gatlln Canal is provided in Figure 41, Sternotherus
odoratus was very common early in the study period (July^December 1977),
but decreased in abundance thereafter with a secondary peak from June
through September 1978, Chrysemys floridana and _C. nelson! exhibited
a similar pattern. Changes in abundance for these-species may represent
seasonal movements between the canal habitat and adjoining lakes or
differences in seasonal activity within Gatlin Canal.
99. . Distinct seasonal differences in the calling activity of frogs
were observed in Gatlin Canal (Figure 42), Rana utricularia called
mostly in the winter; other species called primarily in the summer.
Deepwater Trapping Stations
100. Only one salamander (a Siren lacertina) was collected in 244
trap days at deepwater sampling sites (Figure 1) during the baseline
study period, This specimen was taken in 1,2 m. of water on the East
Pool site during the July 1978 sampling period, Thus, the mean trap
success of amphibians and reptiles at deepwater sites was 0,41 indivi-
duals/100 trap days. This value was 40.92 times lower than the mean
for all amphibians and reptiles (5=16.77 individuals/100 trap days) and
5,72 times lower than the mean for £, lacertina (5^2,34 individuals/
100 trap days) trapped at permanent shoreline sites during the
baseline study period.
33
PART V: DISCUSSION
101. Baseline studies of the herpetofauna of Lake Conway indicate
that the lake system contains a complex and diverse assemblage of at
least 27 species. A number of these species (e.g., Hyla cinerea,
Amphiuma means, Alligator mississippiensis, Sternotherus odoratus,
Chrysemys floridana) are common and conspicuous components of the Conway
ecosystem whose functional role in food webs and community dynamics
generally remains unappreciated. All of the species contribute to the
diversity of the system. As such they are important in maintaining
community stability, and changes in their populations provide an excellen
means of monitoring the effects of environmental perturbation. In future
poststocking periods, the authors' task will be (1) to determine whether
any changes in the herpetofauna of Lake Conway are the result, directly
or indirectly, of the white amur aquatic plant control program, and
(2) to consider if these changes (if any) are consistent with the object!
of the LSOMT.
102. Unfortunately, no detailed integrative studies of a community
of amphibians and reptiles inhabiting a large aquatic environment such as
Lake Conway have been published. Indeed, the herpetofaunal project on
Lake Conway will provide the most complete ecological data base available
for a number of species, especially Amphiuma means. Siren lacertina,
Chrysemys floridana, _C. nelson!, Kinosternon subrubrum, and Sternotherus
odoratus. Thus, at present it is not possible to compare the herpetofaur
of Lake Conway with populations inhabiting other aquatic ecosystems.
103. In general, the amphibian and reptile populations of Lake
Conway can be characterized as dynamic, varying in both time and space.
Presumably, future work will show that many of the temporal density
fluctuations observed during the baseline study period represent seasonal
changes in activity. In other cases, long-term changes in herpetofaunal
populations may have occurred (e.g., shoreline development on South and
Middle Pool permanent sites). Trapping and other sampling results indie*
that most species of amphibians and reptiles are restricted to the
littoral zone. Only a few species regularly inhabit open-water habitats,
34
1:4 j^iliwyijj^jaipjj^
and even these species are dependent upon the shoreline for some portion
of their life cycle. Across all permanent shoreline sites, the diversity
and abundance of amphibians and reptiles generally was greatest at those
stations that contained an abundance of aquatic vegetation; sparsely
vegetated stations or stations that were converted to beach habitats by
man had a'depauperate herpetofauna. If white amur have a-major impact
on the shallow-water emergent and submergent plants, detrimental effects
on the herpetofauna are expected.
35
REFERENCES
Addor, E. E., and Theriot, R. F. 1977. "Test Plan for the Large-Scale Operations Management Test of the Use of the White Amur to Control Aqua Plants," Instruction Report A-77-1, U. S. Army Engineer Waterways Exper ment Station, CE, Vicksburg, Miss.
Barr, A. J. et al. 1979. SAS User's Guide, 1979 Edition, SAS Institut Raleigh, N. C.
Brown, W. S., and Parker, W. S. 1976. "A Ventral Scale Clipping Systei for Permanently Marking Snakes (Reptilia, Serpentes)," Journal of Herpetology, Vol 10, pp. 247-249.
Cagle, R. F. 1939. "A System of Marking Turtles for Future Identifica tion," Copeia, Vol 1939, pp. 170-172.
Freund, J. E. 1973. Modern Elementary Statistics, Prentice-Hall, Englewood Cliffs, N. J.
Godley, J. 5. 1979. "Foraging Ecology of the Striped Swamp Snake, Reg; alleni, in Southern Florida," Masters Thesis, University of South Flori, Tampa.
Gosner, K. L. 1960. "A Simplified Table for Staging Anuran Embryos am Larvae with Notes on Identification," Herpetologica, Vol 16, pp. 183-191
Guillory, V. 1979. "Large-Scale Operations Management Test of Use of White Amur for Control of Problem Aquatic Plants; Report 1, Baseline Studies; Volume II: The Fish, Mammals, and Waterfowl of Lake Conway, Florida," Technical Report A-78-2, u. S. Army Engineer Waterways Experi- ment Station, CE, Vicksburg, Miss.
Nail, L. E., and Schardt, J. 1978. "Large Scale-Operations Management Test of Use of the White Amur for Control of Problem Aquatic Plants; Report 1, Baseline Studies; Volume I: The Aquatic Macrophytes of Lake Conway, Florida," Technical Report A-78-2, U. S. Army Engineer Waterways Experiment Station, CE, Vicksburg, Miss.
Pough, F. H. 1970. "A Quick Method for Permanently Marking Snakes and Turtles," Herpetologica, Vol 26, pp. 428-430.
36
ll-l '.CWWpT" T .p f ws •
Table 1
Checklist of amphibians and reptiles known from the Lake Cbriway system,
Scientific Name Common Name Species Code*
AMPHIBIA CAUDATA
SIRENIDAE Siren lacertina Greater siren L
AMPHIT3MIDAE Amphiuma means Two-toed amphiuma A
PLETHODONTIDAE Eurycea quadfidigii :ata Dwarf salamander
ANURA
BUFONIDAE Bufo tefrestris Southern toad B,%
MICROHYLIDAE Gastrophryne carblinensis Eastern narrow-mouthed toad G
RANIDAE Rana grylio Rana utricularia
Pig frog Southern leopard frog
R,+ U,&
HYLIDAE Acris gryllus Hyla cinerea Hyla femoralis Hyla squirella
Florida cricket frog Green treefrog Pinewoods treefrog Squirrel treefrog
Y,* H,$ M P
REPTILIA CROCODILIA
CROCODILIDAE Alligator mississippiensis American alligator E
(Continued)
* If applicable, the code for the adult life stage is followed by a larval life stage code. The codes explained here are used in Figures 3-42.
Table 1 (Concluded)
Scientific Name Common Name Species Code
TESTUDINATA
CHELYDRIDAE Chelydra serpentina
KINOSTERNIDAE Kinos ternon bauri Kinosternon subrubrum St smother us odoratus
Florida snapping turtle
Striped mud turtle Eastern mud turtle Stinkpot
I K s
EMrDIDAE Chrysemys floridana Chrysemys nelson! Deirochelys reticularia
TRIONYCHIDAE Trionyx ferox
Peninsular cooter F Florida red-bellied turtle C Chicken turtle D
Florida softshell
SQUAMATA
COLUBRIDAE Coluber constrictor Farancia abacura Nerodia cyclopion Nerodia fasciata Regina alleni Thamnophis sauritus Thamnophis sirtails
Black racer V Mud snake X Green water snake N Florida water snake W Striped swamp snake Peninsula ribbon snake Z Eastern garter snake Q
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FREQUENCY
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Figure 38. Herp-patrol point analysis of salamanders and reptiles on the Gatlin Canal site. Point « midpoint of 10-m. section of herp-patrol transect. See Table 1 for
species codes
FREQUENCY BAR CHART
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Figure 39. Herp-patrol point analysis of calling frogs on the Gatlin Canal site. Point = midpoint of 10-m. section of herp-
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APPENDIX A: SUMMARY OF PLANT SPECIES AND SUBSTRATUM TYPE FOR ALL
PERMANENT SHORELINE HERPETOFA.UNAL TRAPPING STATIONS ON LAKE CONHAY
DURING THE BASELINE STUDY PERIOD. Given are the three most abundant
plant species or habitat conditions coded (1, 2, or 3) in order of decreas-
ing percent cover within a 2-sq.-m. area of each trapping station averaged
over quarterly samples. If a significant proportion of the quadrat contained
no vegetation but was in natural surroundings, it was coded as "Bare
bottom"; likewise, "Beach" means man-made white sand beach; and "No
other vegetation present" means that other plant species were mono-
dominant or codominant in the quadrat. If plant cover changed as a
result of man-made habitat modification during the baseline study
period, the date of change and new conditions are given in parentheses.
Substratum types are coded as follows: 1 = sand; 2 = 1-5 cm. mud;
3 = 6--10 cm. mud; 4 = 11-15 cm. mud; 5 = 15-20 cm. mud; 6 = > 20 cm. mud.
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In accordance with letter from DAEN-RDC, DAEN-ASI dated 22 July 1977, Subject: Facsimile Catalog Cards for Laboratory Technical Publications, a facsimile catalog card in Library of Congress MARC format is reproduced below.
Godley, J. Steve Large-scale operations management test of use of the
white amur for control of problem aquatic plants : Report 1 : Baseline studies : Volume V : The herpetofauna of Lake Conway, Florida / by J. Steve Godley, Roy W. McDiarmid, G. Thomas Bancroft (Department of Biology, University of South Florida). — Vicksburg, Miss. : U.S. Army Engineer Waterways Experiment Station ; available from NTIS, [1981].
Ill p. in various pagings : ill. ; 27 cm. — (Technical report / U.S. Army Engineer Waterways Experiment Station ; A-78-2, Report 1, Volume V)
Cover title. "June 1961." "Prepared for U.S. Army Engineer District, Jacksonville
and Office, Chief of Engineers, U.S. Army under Contract No. DACW39-76-C-O0U7."
"Monitored by Environmental Laboratory, U.S. Army Engineer Waterways Experiment Station."
Bibliography: p. 36.
Godley, J. Steve Large-scale operations management test of use of ... 1981.
(Card 2)
1. Amphibians. 2. Aquatic plants. 3. Fishes. k. Lake Conway (Fla.) 5. Lakes. 6. Reptiles. I. McDiarmid, Roy W. II. Bancroft, G. Thomas. III. University of South Florida. Department of Biology. IV. United States. Army. Corps of Engineers. Office of the Chief of Engineers. V. U.S. Army Engineer Waterways Experiment Station. Environmental Laboratory. VI. Title VII. Series: Technical report (U.S. Army Engineer Waterways Experiment Station) ; A-78-2, Report 1, Volume V. TA7.W3** no.A-78-2 Report 1 Volume V
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