ML20024E984
| ML20024E984 | |
| Person / Time | |
|---|---|
| Site: | Hope Creek  |
| Issue date: | 09/08/1983 |
| From: | Mittl R Public Service Enterprise Group |
| To: | Schwencer A Office of Nuclear Reactor Regulation |
| References | |
| NUDOCS 8309080065 | |
| Download: ML20024E984 (157) | |
Text
__-____-
I O PS G PublicService Electric and Gas Company 80 Park Plaza, Newark, NJ 07101/ 201430-7000 MAILING ADDRESS / P.O. Box 570, Newark, NJ 07101 Director of Nuclear Reactor Regulation U.S. Nuclear Regulaf.ory Commission 7920 Norfolk Avenur Bethesda, MD 200'4 Attention:
Mr. Albert Schwencer, Chief Licensing Branch 2 Division of Licensing Gentlemen:
HOPE CREEK GENERATING STATION DOCKET NO. 50-354
-ENVIRONMENTAL. REPORT QUESTION E291.10 (a)
Enclosed are the available reprinted copies (12) of journal and professional conference proceedings publications as requested in Environmental Report Question E291.10(a).
Should you have any questions in this regard do not hesi-tate to contact us.
Ve ry t uly you s, I
R.
L.
Mittl General Manager -
Nuclear Assurance and Regulation JM:df Encl.
CC D.
H. Wagner USNRC Licensing Project Manager
.coe/
'lI BB10 8309080065 830908
~
PDR ADOCK 03000354 C
PDR The Energy People -
940942
w a,g THE ATLANTIC STURGEON, ACIPENSER OXYRHYNCHUS, IN THE DELAWARE RIVER ESTUARY ll ARoLD St. BRUNDAGE !!! AND Rostar E. 51EADoWst v.
s ABSTRACT r
Records of Atlantic sturgeon. Aciprnaer oxyrhynchus, captured in the Delaware Riverestuary from 1958 through 1980 were obtained from the literature, unpublished data, and logs maintained by commercial fishermen who took Atlantic sturgeon incidental to their operations for other species.
During the period reviewed, there were 130 Atlantic sturgeon reported captured 64 in commercially fished gilt nets and 66 incidental to fishery and ecological studies. Atlantic sturgeon were most abundant in Delaware Bay triver km 0 55)in spring and in thelower tidal river (river km 56-127) during summer. This seasonal distribution appeared similar to that described for the Hudson River estuary. Atlantic sturgeon between 800 and 1.300 mm totallength were relatively more abundant in the Deleware River estuary than had been reported in other estuaries, suggesting utilization of the Delaware system during a greater portion of the life cycle.
- .**v
&....U:2;;
- i The Atlantic sturgeon Acipenser o2yrhynchus, As a preliminary step towards an assessment all inhabits large estuaries and Atlantic coastal availt.ble recent records of Atlantic sturgeon waters from Labrador to eastern Florida; a capture in the estuary were compiled. Reliable, souther i subspecies, A. o. desotoi, occurs quantitative data were found for the period 1958 throughout the Gulf of Mexico (Vladykov and through 1980. Most records were obtained from Greeley 1963).
the substantial body of published and unpub-The Delaware River estuary, historically one lished data generated by recent fishery and of the major spawning and nursery areas for the ecological studies. Further information was ob-Atlantic sturgeon, once supported the largest tained via personal communication with the and most profitable sturgeon fishery on the staffs of the Delaware River Anadromous Atlantic coast (Ryder 1890). The fishery in the Fishery Project of the U.S. Fish and Wildlife
_. _'.~ m '
Delaware River estuary was extremely short Service, the Delaware Division of Fish and lived, however, and followed a pattern of rapid Wildlife, and Ichthyological Associates, Inc. In decline observed in most other estuaries. The addition, during spring 1979 and 1980, three commercial fishery, which began in the mid-commercial gill netters who had previously 19th century and expanded rapidly after 1870 as worked with the authors maintained logs of smoked sturgeon and caviar gained acceptance, Atlantic sturgeon captured incidental to their
@. wgd declined precipitously about 1900 and virtually operations for other species. Some 25 other
~
collapsed by 1905 as the population declined (see fishermen were interviewed to obtain their im-l Ryder 1890: Cobb 1900: Murawski and Pacheco pressions of Atlantic sturgeon occurrence and 1977).
abundance. Inherent in this approach was the Overfishingof adultsonthespawninggrounds premise that representative trends might combined with late maturity appears principal-become apparent when a body of incidental ly responsible for this decline, although destruc-records and anecdotal accounts are considered l
tion of benthic food organisms by coal silt pollu-together. Aparent trends must be interpreted i-l tion and g'eneral deterioratio_n of water quality cautiously, hvwever, since sampling gear and i
and destruction of juvenile Atlantic sturgeon by effort varied considerably between and within American shad Alosa sapidissima, fishermen years.
pricably contributed.
To aid in the delineation of spatial-temporal Little is known of the present status of the trends the estuary was divided inta three regions Atlantic sturgeon in the Delaware River estuary.
based on physiography and salinity regime.
" Delaware Bay" extends from the mouth (river l
km 0) to the vicinity of the Leipsic River (river
,1chthyoiogical Associates. Inc 100 south cas.: street. -
Middletov*n. DE 19709.
km 55). is shaped like a flattened funnel and has EsEItis'EdtTYoOE'No.2.19ss.
4
_.s S'
(
E j
e ed *.
. :s s
FISHERY B11LLETIN. v0L m). NO. 2 extensive shoals along the New Jersey shore (Fig.1). The estuary narrows considerably at about river km 56 to form the " lower tidal river" n=5vtvAnia which extends to Marcus Hook. Pa. (river km u
3 127). The " upper tidal river" extends to the fall s'
line juet north of Trenton, N.J. (river km 222).
Delaware Bay is generally polyhaline (18-um
.a i
307 ), the lower tidal river :=esohaline to oligohaline (0.5-187 ), and the upper tidal river c,,ts,,
g*g l.
limnetic (0.0 0.57 )(Tudor 1980). These zones of O su-u j
salinity may be displaced considerably,however, w'u-c'o" depending upon freshwater flow. tidal stage. and sew ansey 0 'Att p
a local meteorological conditions.
_,;g,, 2
- a wc.us..~o Cao CAMai RESULTS t
usio,Jo.m
' cg.pr o
- 20 From 1958 to 1980 there were 130 documented q
we,ct captures of Atlantic sturgeon in the Delaware i
River estuary (Table 1. Fig.1): 68 in Delaware Ltir$sC etvte "m
e
-@ QL,'**"
add.,,enei ame,d, ocumao seacw 2 Dete.m,e soy
/
^
O
(,,,'
, = *
, te e.ceae-ere Ficuss 1.-Imations of recorded esptures of Atlantic sturgeon in the Delaware River Estuary,1958-80. Seasons are D"^*^"'
.g defined as winter-December through January: spring-a
', G AftAsric March through May; summer-June through August; fall-September through November. Records for which precise C"' "'"#"
capture loestions are not known are also given.
TAsLe 1.-Reix>rded captures of Atlantic sturgeon. AcipenarroxyrAynchus,in the Delaware River estuary. November 19584uly 1980.
salin.
Total R6ver ity Temp.
sength Date Area km
- /..
(*C)
Method of capture No.
(mm)
Source anwg 14Noe 1958 Lower Delaware Bay 9.1 m trawl 1
sos deSylva et al.1962 sept 1967 Martpor of Refuge. Dec.
3
- 91 m trawi 1
Ostier and Wockley 1968 Oct.
Joe Flogger Snoal. Del.
42
- 91 m trawi 1
i 31 July 1968 Liston Point. Del.
77 Daitier and Wochtey 1968 l
26 cm gru not S
414. 1,143.
IA. Inc ' Ed@etown; Det 1.165, 1.193.
1.431 1Aug Liston Poet 77
- 29 cm gdi not 5
600.1.157 IA. Inc Eddetown 1.172. 1.321 1.431
$ f.,mif. k 'of.
9Aug.
Liston Point 77
- 28 cm gitt not 1
809 IA, Inc.. Eddletown r%
1,*
Mar.-Apr.1960 Uttle hiver. Det.
45 13-14 cm gia not 5
DRBAFP'unputti, data
'*i L S, 28 Sept.1971 Delaware Point. Dus.
72 35 22 0 4 9 m trawl 1
IA. Inc Middetown t
- 20 June 1972 Artsficial Island, N J.
79 30 22 0 4 9 m trawi 1
IA. Inc Middetown i4
' 24 Sept.1973 Newbold Island, N.J.
203 4 9 m trami 1
196 IA. anc Ed@etown Mar -Dec.1974 Surtengton Island. N.J 190
- Cooling water intake 1
DRBAFP unputW. data 23 May Artshesat estand 79 1.0 20.1 4 9 m trews 1
340 IA. Inc Eddletown Aug Sorcentown, N J.
206
- 4 9 m trewt 2
ORBAFP unpuol. data 8 May 1975 Artshcial asiand 79 50 175 14 cm Odi not 1
700 IA. Inc. %deetown t
19 May Artsficial leiand 82 1.5 19 0 8 cm gdi not 1
IA. Inc Eddletown 10-11 June Newtpold taland, N J.
200
- 4 9 m trawl 1
'349 Maren Manetta Corp.1976 Oct. Oec.
Delaware Power Plant 163
- Coohng water intake 1
ORBAFP unpubl. date
[
24 Mar 1976 Arhhoal Island 79 0
86 8 cm gdi not 1
765 IA. anc. uddletown 1
10 May.
Freneng Creek. N.J.
75 50 16 0 14 cm gell net 1
553 lA. Inc.. Midsetown 17 Mar.1977 uttle Rever 45 O,n not 1
1.117 Dowel 1979 4 Apr.
Appoquitument River, Del.
32 4 a m trawe 1
501 tA. Inc uddietown 13 Apr.
Lettle Rever 45 Geli nel 1
457 Doves 1979 12 May Artshoat Island 86 50 16 0 4 9 m trawa 1
519 IA. lac.. Ed@etown June Pea Patch leiend. Dec.
96
- Gdi not t
DRSAFP unputW, data 27 June Artshcial estand 82 7.0 24 2 8 cm gdi net 1
720 IA. fac uddletown 21 July Arlincial Island 42 50 28 0 4 cm gds not 1
680 lA. Inc Ed@etown 18 Mar.1978 Sowers Beacn Del 38
- G u ne*
1 Dovei 1979 22 Mar.
Utne River 45 Gdi pet 2
Dovet 1979 23 Mar.
Sowett Beacn 38 Gil nel 1
Dowel 1979 27 Mar.
Little Rever 45 G.a not 1
Dovei 1979 10 Mar Fonder Beach. Del.
15 Gil nel 1
Dowel 1979 3 Apr Utite River 45 Gdi net 1
Dovei 1979 338 f
9 y
P. I 7-e
~
- .g f
O d
- 's*
\\
=
.h
d' O, BRUNDAGE and MEADOWS ATIANTIC STURGEON IN del. AWARE RIVER ESTUARY TASLE I.-Recorded captures of Atlantic sturgeon. Aetpenaer orvrhynch hs. in the Delaware River es:uary. November 195Nuly I'JtD.-
Continud.
Salm-Totas River rey Temo lengm Date Area km
- /..
f*Cp Method of caoture No immi Source 7 Apr bette River 45 Ge#1 net 1
Dowel 1979 8Apr Det Haven. N J 17 Gdt net 1
Doves 1979 15 Apr bttle Rever 45 Gal not t
Dovei 1979 22 Apr Conansey her. N J 6
80 17 0 4 9 m trawt 1
760 IA. Bac,. uddletown 29 aor Det Haveri t7 Gdi not 1
Dowel 1979 May brtes River 45 G.tl net 2
Dowel 1979 3 May Del Haven 17 Gdi net 1
Dove 1979 6 May Deiseare Bay Gsti nel 2
Dowel 1979 30 uy Mart >or of Refuge 3
- Moon and line 1 1.524 Del Dep. Finn and Wddi.
r.
24 July Arnhose island 80 40 27 0 4 9 m trawi 1
604 IA. bnc., Middletown 24 Ju y Eisenboro Point. N J 92 40 27 5 4 9 m traws t
674 IA. lac., Mod @etown e
24 Ju y Artehoal Island 82 70 27 6 4 9 m trawi 1
$18 IA. Inc uddletown s
15 Aug Burung.on Island 190 4 9 m teawi 1
157 IA. Inc., Absecon. N.J.
17 Aug NE of Harbor of Refuge 1
29 0 25 2 4 9 m trs=1 1 2.000 IA. Inc.. M ddletown 24 Aug Artshoal island 42 50 27 7 4 9 m trawi 1
690 IA. Inc., uddetown 29 Aug Burl *ngton Island 190 0
25 0 4 9 m trawl 1
175 IA lac., Absecon 6 Sept '
Burhngton tsland 190 0
25 0 4 9 m erswi 1
175 IA. Inc, Absecon 20 Sept Arhhose island 80 70 23 4 4 9 m trswa 1
648 1A Inc M dsetown 16 Apr 1979 Old Bare Shoal. Del 17 91 m trawa 1
855 Smita 1940 16 Apr Hope Creet. N J 78 le em gdi not 1
760 Commercal hanerman 20 Apr Hope Creet 78 14 cm g*ll not 1
890 Commercal hsnerenan 20 Apr Kitts Hurnmock. Del 41 13 cm ga ne.
t 610 Comaneroal hsherman 22 Apr Kstts Hummock 41 10-13 can gdi nel 2
900. 1.030 Commercal hsherman 23 Apr Kitts Hummock 41 13 cm gde not 2
830. 960 Cornmercal hsherman 24 Apr Katts Hummoca 41 13 cm gm not 2
865. 680 Cornmercal hanerman 25 Apr Port Manon. Del 47 10 cm gdi not 1
$64 Comaneraal hsnerman
... ;j 23Apr Kitts Hummoct 41 13 cm giti eet t
660 Commercial hsherman J-e,**,
25Apr Hope Creen 78 14 cm gdi pet 1
914 Commercsai hsherman IZ, N*
=
26 Apr Port Manon 47 13 cm geti nel 1
$70 Commercal hsnorman i
26Apr Ketts Humanoca 41 13 cm gde net 1
665 Commeroaa hsnorman 29 Apr Port Manon 47
- 13 cm gda pet 1 1.067 Commercial fisnerman 5
29 Apr Port Mahon 47
- 13 cm gdi pet 1
580 Commercsai hsnerman i
30 Apr Katts Hummock 41
==
- 13 Cm gdi net 2
711, 865 Commerosi fisherman 1 May Port Mahon of 13 cm gd4 not 1
810 Comenercal hoherman i
2 May Port Mahon 47 13 cm gdt met 2
720.940 Commercias frenerman I
3May Port Manon 47
- 13 cm gdi not 1
890 Commercial heherman 6 May Port Manon 47
- 13 cm gdi not 1
860 Comenercial honerman 9 May Port Manon 47
- 13 cm gitt not 1
810 Commeraal honerman t1 May Port Manon 47 13 cm gell not 1
914 Cornenercial ilsherman 12 May Port Mahon 47
- 13 cm gdt nel 1
96$
Commercal hsherman 21 May W of Joe Flogger Shoal 42 20 0 16 7 91 en trawi 1
860 Saneth 1960 22 May Offshore Smyrna her. Del 71 13 0 18 3 91 m trawi 2
935, t.117 Smith 1980 22 May Ship Jonn Shoal 58 17 0 18 1 91 m trawl 1
95$
Smetn 1980 12 Ju e Hope Creet 77
- Dead on surface 1
889 1A. Inc.. M deetown n
21 June W of Joe Flogger Snoal 42 24 0 19 6 91 m trawi 1
960 Smith 1983 neumwk aw
'e**+"
22 June Sn p John Snoel 58 16 0 20 8 91 m trsel 2
1.190. 750 Smitn 1980 7
12 Jufy Smyras her 71 12 0 24 8 4 9 m traws 1
960 IA. Inc, Meddietown a
My Snio Jonn Shoal 58 17 0 25 2 91 m Irawt 1
8tS Smstn 1980 9 Aug N of Pea Paten Island 101 10 28 1 4 9 m trawl 1
128 tA, Inc, Middletown 25 Seol-Bowers-Pickenng Seaches. De 38-44 Gdi not 1 1.090 Commercal finnerman r-s' Sept.
Snio Jonn Sncal
$8 18 0 22 7 91 m treet 1 1.150 Smitn 1980 J
22 Oct.
Harpor of Refuge 3
13 2 4 9 m trawl 1
810 IA. Inc udsetown
(. -
Oct.
Fourteen Ft. Bank. Dei 34 25 0 14 7 91 m trawl 1
875 Sm th 1980
';.9 I Now Offsnore Pnene Hook Beacn. Det.
T 27 0 tt 3 91 m trawi 1
1.100 Smith 1980 grg M Iq.. Q4'- h 3%Y3 2 Now Artshoai lsland 80 60" 15 0 Coohng water intane 1
936 IA. inc, Middietown Pf*
16 Fee 1980 Artshoal Island 80 10.0 05 Coohng water miske 1
692 IA.tnc Medsetown
..*fC.
24 Mar.
P6caer ng Beacn. Del 44 Gdi not 1
760 Commercal Asnorman 25 Mar.
Pictoring Beacn 44
- Gdi net 4
457. 457 Comaneraat haherman i
760. 1.066 26 Mar Pictoring Beach 44 Gdi pet 1 1.220 Commerosi honerman a
29 Mar.
Pictermg Beacn 44 Gdi not 1 1.5?4 Commerosi hsnermar.
8 Apr Athhoal island 80 10 9$ Coolmg water inf ame 1
- t50 IA. Inc, uddietown 22 Apr Pickermg 8*acn 44 Gdi not 1
760 Commerical hsherman
}
May Oid Bare Snoas. Del 17 27 0 15 6 91 m trawl 1 1010 Del Dep. Finn a,=1 Wisde 6 May Arnhoal Isiand 80 40 17 0 Coolmg water mtame 1
689 IA. Inc, udd;elown 19 May Blame Cnannel 40 18 0 17 5 4 9 m trane 1
927 1A. Inc, Middletown 28 May Art.hoal isiand 80 70 21 0 Coohng water intake 1
942 LA. Inc Meddletown r
24 June -
Peedy Isiand Dike. Dec 84
- Dead on surface 1
620 IA. Inc. Middletown to Jusy Sunkers Shio Cove. N J 80
- Dead on beach I t 010 IA. Inc Meddletown 16 My Artshoas tsiand 80
- Cooling werer intame 1
'637 tA. inc. udsetown v 7 uy Ortsnore Srnytna River 71 14 0 25 3 91 m trawi 1 1.035 Det. Dep Fesn and Wdde 24 July Artshcasi IslaNf 80 10 0 28 0 Coohng asterintate 1
1.015 iA. lac., Meddietown 31 My Attrhaas faland 80 80 29 0 4 9 m trawl fsur+ acel t
1.230 BA Inc. uddletown ichtnyoto9.cM Associa,es. ine rDesaw.re R,v., Son Anadromous F,snery Pro,ect
' Converted froen fort lengin.
o 339
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e l'
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e r
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r-
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5'!SiiERY BULLETI.k VOL R NO. 2 Bay, 53 in the lower tidal river, and 9 in the "l;'" 3 upper tidal river. A total of 64 specimens were i
captured in commercially fished gill nets, most R
l r.s a bycatch of operations for American shad, and weakfish, Cynoscion regalis. The remaining 8e 66 specimens were taken incidental to various fishery and ecological investigations: 23 by 4.9 m mvenm.su bottom trawl.17 by 9.1 m bottom trawl.12 by l
experimental gill net, 9 at industrial cooling j
p.
y 1 -
water intakes, I by 4.9 m surface trawl, I by hook l
and line, and 3 we4 e dead on the water's surface i
or on shore.
i as.
In Delaware Bay Atlantic sturgeon were taken
- c. sm
-~
from March through November (Fig. 2). Catch was greatest during March through May (14-23/mo), low during July through August s
(1/mo), and increased somewhat dr ring Septem-o,.,
ber through November (2 or 3). The spring peak l
was composed largely of specimens captured in 1979 and 1980 by the cooperating commercial Ficcar 2.-Number of Atlantic sturgeon captured monthly in
". 4:
gill netters who logged incidental Atlantic three regions of the Delaware River estuary, 1958-80.
M$
b (*
sturgeon captures while fishing shallow waters off of Kitts Hummock (river km 41) and Port gill nets along the bottom from about I h before s
- Mahon (river km 47), Del.,in 1979 and Pickering to about I h after low tide (Beck'). These were, to Beach (river km 44), Del., in 1980. Their records the best of our knowledge, the last successful reflect 27 specimens taken during 20 April-14 commercial efforts directed specifically at May 1979 and 8 during24 March-22 April 1980.
Atlantic sturgeon. Although the above men-Additionally, all 18 Atlantic sturgeon reported tioned 11 specimens are the only quantitative from Delaware Bay by Dovel(1979) were taken accounting of their catch available, anecdotal during March May(see Table 1). Although this accounts indicate considerable success with as abundance pattern may be biased by the greater many as 191 specimens taken in a 2-wk period l
fishing effort ex pended during spring relative to (Beck 1973).
--,re other seasons, essentially all other commercial In the upper tidal river, Atlantic sturgeon
~ --.
gill netters interviewed reported the highest were captured in June (1), August (4), and i
frequency of incidental sturgeon capture during September (2) (Fig. 2). Only one specimen was spring. Most A tlantic sturgeon taken in the gill taken in the Wilmington. Del., to Philadelphia, net fishery are apparently below marketable size Pa. (river km 114-170), reach. In this region and are released. Records indicate that survival mean dissolved oxygen concentrations approach
'W %
$,D in gill nets was very high if the nets were tended zero during summer and are typically below 5 44 W,'!*
daily.
ppm during May through October (Freiders-S N.
In the lower tidal river Atlantic sturgeon were dorff et al.1978). This fish was taken sometime g-taken from February through September and in during October-December 1975, when oxygen December (Fig. 2); most during July (16), al-concentration was considerably higher.
j
[
though moderate numbers (6-10) were taken Available data showed that Atlantic sturgeon from April through August. Eleven specimens occurred over a wide range of water temper-( _
were taken in late July and early August 1968, by ature (0.5'-28.1*C) and salinity (0.0-29.0 7 ). The two part-time commercial gill netters purposely varying availability of temperiture and salinity fishing for Atlantic sturgeon. These men fished, data by region, however, precludes further dis-l typically for a 2-wk period in summer, between cussion. Values were available for 62% of the Delaware City (river km 98) and Liston Point specimens captured in the lower tidal river but (river km 77), Del., during the late 1940's through the early 1970's. They employed essentially traditional methods, as described by Cobb
'Robut A. Bak artment of Natural Rewurces and Environmental Contro: ivision of Fish and Wildlife. P.O. Box (1990), and drifted 9 X 572 m,28 cm cotton mesh 1401. Dover. DE 1990L pers. commun. December 1978.
340 ij;,n..- q37.Q. '.r.z ~
y-m ~ T '
. ~ ~ w p mm
'+ :
~'*
N 0
m
.;s
'r a>'
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BRUNDAGE and MEADOWS; ATLANTIC STURGEON IN DELAWARE river EsTUARf only 10% of those from Delaware Bay and 22% of within the estuary can be inferred. In early those taken in the upper tidal river.
spring substantial numbers of juvenile Atlantic Length data were available for 97 Atlantic sturgeon occurred in the shallow waters of sturgeon. Reported fork length (FL) for li speci-Delware Bay; later in spring, abundance mens were converted to total length (TL) with increased in the lower tidal river and this the relationship FL = 0.878 TL - 6.551, r = 0.999.
upstream movement continued through early calculated from measurements of 19 specimens.
summer. This is similar to the pattern described Total length ranged from 457 to 2,000 mm (f =
by Dovel (1979) for the Hudson River, i.e.,
L 885 mm: n = 45) for specimens taken in Delaware juvenile Atlantic sturgeon overwinter in the Bay, from 128 to 1,431 mm (X= 863 mm; n = 48) deeper waters of the lower estuary and move up-in the lower tidal river, and from 157 to 196 mm stream and inshore in spring in response to in-(f = 176 mm: n = 4)in the upper tidal river (Fig.
creasing water temperature. However, in the 3). Based on age-length data for the Hudson Delaware River estuary, juvenile Atlantic River estuary (Dovel 1979), the probable age of sturgeon ranged to the the fallline at Trenton, specimens taken in Delaware Bay ranged from whereas in the Hudson River they were found 0+ to ca. 20+ and from 0+ to ca.14 + in the lower only to river km 145 (Kingston, N.Y.), some 100 tidal river. Only age 0+ specimens were taken in km below the limit of tidal intrusion.
the upper tidal river. No individuals in spawning During summer, Atlantic sturgeon were most N3 -#,
condition were reported.
abundant in the lower tidal portion of the Dela-
'fYT ware River and probably use this region as a S-foraging ground. Numbers in this reach de-uma rica' creased somewhat during August, the month of maximum water temperature. Dovel (1979) reported that Hudson River Atlantic sturgeon io seek cooler waters during summer and may move south before water temperature peaks. In
- towen ricat the present study, however, no such movement to nwanc..se>
Delaware Bay during August was evident, although numbers in the bay increased slightly I
4 in September.
jo j,
rl e
i Abundance in the Delaware system decreased a* e -+
~
in the upper and lower tidal river in September 3
octawaar ear and increased somewhat in Delaware Bay during September through November, suggest-a ing a return to overwintering areas. Some indi-1 R
viduals may have left the estuary at that time to h%
,6
,6 g,
,jo, overwinter in the nearshore ocean. Interviews conducted in 1978 and 1979 with commercial if k
rotat tener i,
trawl fishermen operat, g out of Ocean City, m
t.
i-Facunt 3.-Length frequency distributions of Atlantic Md., indicate that Atlantic sturgeon are sturgeon captured in three regions of the Delaware River commonly taken near the mouth of Delaware estuary,19ss-sa Bay in fall. Most of these fish are small. ranging from 0.6 to 1.5 m long, with occasional captures DISCUSSION of larger individuals of 2.5-3.5 m.
Evidence on occurrence of older juveniles in Despite the limitations imposed by reliance on the Delaware system disagrees with reports j
l incidental catch records, a number of generali-from other systems. Murawski and Pacheco zations regarding the Atlantic sturgeon in the (1977) reported that these fish emigrate from the Delaware River estuary can be made. The data estuary when they reach 760-915 mm long and do strongly indicate that there is a viable population not return for a number of years until mature.
of Atlantic sturgeon in the Delaware system Dovel (1979) found that Atlantic sturgeon be-which utilizes different regions of the estuary to tween about 800 mm(ca age 5)and 1,300 mm TL varying degrees depending on season and life (ca. age 12) were rare in the Hudson River l'
stage. A definite pattern of seasonal movement estuary and inferred that these individuals re-341 l.i
~*
qt l
~.
l C_;
- r.
4 H
, $;h,
.<l.
- 3.,,.
., ;-:.4 - : g,p.
<j,.
',. -( y u y,
,s s
N ' *%.
Fl8HERY BUI.LETIN: VOL Ao. No. 2 mained at sea. However, in the Delaware River first reproduction, and spawning time and loca-estuary Atlantic sturgeon between 800 and 1.300 tion. In any event, the value ofincidental capture mm were common and composed 62% of the records and anecdotal accounts should be recog-measured specimens from Delaware Bay and nized and continued monitoring of available 48% of those from the lower tidal river. It is sources is advisable. The potential for restora.
possible that the Delaware River estuary is tion of the stock is high. based on the lack of utilized during a greater portion of the Atlantic industrial development in the lower estuary and sturgeon's life cycle then is the Hudson.This may the fact that as yet undammed, the Delaware be associated with the relatively unimpacted River still features relatively natural run-off and i'
condition of Delaware Bay and the lower Dela-river flow patterns. Pollution abatement ware River as compared with the heavily indus-programs, particularly those involved with trialized and degraded lower Hudson River improvement of dissolved oxygen levels in the estuary. It is also possible that an Atlantic Chester to Philadelphia reach will undoubtedly sturgeon which has left the Hudson River may enhance this potential.
utilize other estuaries. including the Delaware systein. during this portion of its life. Recapture ACKNOWLEDGMENTS of tagged Hudson River sturgecn in the Delaware River and more distant estuaries We are grateful to Victor J. Schuler and Alan (Dovel 1979) may substantiate this view.
W. Wells of Ichthyological Associates. Inc., for No specimens in spawning condition were re-their' critical reading of the manuscript. Joseph S.'
corded from the Delware River Estuary; most Miller of the U.S. Fish and Wildlife Service.
reported were probably immature. Most Atlan-Richard J. Seagravesof the Delaware Division of tic sturgeon captured in the Delaware River Fish and Wildlife, and Robert G. Howells of estuary were <112 cm TL minimum for mature Ichthyological Associates. Inc., supplied collec-males and <200 cm for mature females reported tion data for several specimens. We also thank by Dovel (1979). Larger mature specimens are Robert G. Howells for drafting the figures and
~
almost certainly present in the estuary but are Holly J. Jones for assistance with manuscript not vulnerable to the small-mesh gear typically preparation.
fished by commercial fishermen and fishery biologists. Even though spawning location could LITERATURE CITED i*
not be ascertained it is perhaps signficant that the smallest specimen recorded (128 mm) was BEcx.R.A.
W taken near Pea Patch Island. Del.(river km 101).
1973. Sturgeon-alive and well. Del. conserv.17(2):4 g-an area historically described (Borodin 1925) as go,,,f,, y, a prmespal spawmng area for Atlantie sturgeon.
1925. Biological observations on the Atlantic sturgeon This compilation of incidental catches and a (Aripenarr st rio). Trans. Am. Fish. Soc. 55:184190.
substantial body of anecdotal information sug Coss. S. N.
i gests that Atlantic sturgeon may be far more 1900. The sturgen fishery of the Delaware River and abundant in the Delaware River estuary than
,rg.d{p Bay. Rep. U.S. Comm. Fish. 1899:369-380.
DAIBER. F. C, AND R. C. WocxLEY.
s commercial catch statistics and the impressions 1968. Annual Dingell. Johnson Report. 1967 1968.
..g of other fishery scientists indicate (floff'). The Univ. Del., Newark. 35 p.
v W'
reported scarcity of Atlantic sturgeon may be otSYLVA. D. P F. A. KAs.sER. JR., AND C. N. SCHUSTER.JR.
1962. Fishes and ecological conditions in the shore zone I/
more the result of not fishing the appropriate ig of the Delaware River estuary, with notes on other gear in the r. ht locations at the right times orof species collected in deeper waters. Univ. Del. Mar.
a not monitoring fishermen who are. A more I.ab.. Inf. Ser.. Publ. s.164 p.
,p definitive status evaluation will require quanti.
DovEt. W.I tative investigation todetermine population size.
1979. Biology and management of shortnose and Atlan-t.
tic sturgen of the Hudson RM Dnal Rep. 53 p.
h mortality rate, age.sE*Cific fecundity, age at FREtornsoonrr, J. W.1. ImTow. AND R. C. REtCHARD.
1978. Performance report Delaware River Basin anad-romous fisherr study.
U.S. Fish Wildt. Serv..
' James G. Hoff. Biology Department. Southern Massachu-Rosemont. NJ. 34 p.
setts University North Dartmouth. M A o2747. pers. commun.
M ARTIN MARIE 1TA CORPORATION.
in Monitoring fish migration in the Delaware River.
t'he' At'lant sturge n Art us o the at so oryrhyncAus (Mitchill). Southeastern Massachusetts Univ.,
Final Report March 1976. Martin Marietta Corp..
-r.
North Dartmouth.136 p.
Baltimore. 86 p.
342 k
s.
we:.. ~ ~.
e t
f'e
- 9 g
9 1 p
4'
's.,'
,J
~
- 'N L
{'hf
- ,y
-?
~.
L w
i e
a k.
,.sy.l l-BRUNDAGE. sad MEADOWS. ATLANTIC STURGEON IN DE1. AWARE RIVER ESTUARY l
f MURAW$KI. S. A., AND A. L PACHErO.
selected shore zone areas. Final Rep.. Doc. No. 40-1977. Biological and fisheries data on Atlantic sturgeon.
05/80/03/3. Del. Dep. Fish Wildt 70 p.
<teipraarr cryrhynchus. Sandy Hook Lab. Tech. Ser.
Tt: dor. R.A.
I Rep.10. 69 p.
National Marine Fishenes Service.
1980. The Delaware River Estuary. la V. J. Schuler Highlands. NJ.
(editor). An ecological study of the Delaware River t
(
RYDE R. J.A.
near Artificial Island 1 % 8 1976: A summary, p. 3-9.
1890. The sturgeons and sturgeon industries of the east.
Ichthyological Associates. Inc Middletown. Del 303 ern coast of the U nited States, with an accountof experi-p.
menta bearing upon sturgeon culture. Bull. U.S. Fish VuDvKov. V. D. AND J. R. GRtti.tY.
j Comm.1231329.
1963. Onfer Acipenseroidei. In Fishes of the western Smitu. R. W.
North Atlantic. Part three, p. 24-60. Mem. Sears
- e s g.
1980. Marine fish populations in Delaware Bay and Found. Mar. Res Yale Univ.
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OZONE: SCIENT AND EIGINEERING 0191-9512/81/030155-14502.00/0 Vol. 3, pp. 155-168, 1981 International Ozone Association Pergamon Press ttd ropyright (c) 1982 Printed in the USA A COMPARATIVE EVALUATION OF THE EFFECTS OF OZONATED
-E'" W P D.
AND CHLORINATED CONDENSER DISCHARGES ON THE WHITE PERCH, MORONE AMERICANA
- Q.t r
.h John W. Meldrim, Ernest R. Holmstrom a George E. Balog,b and Richard Sugam i'{
J Ichthyological Associates, Inc.
[
Middletown, DE 19709 r
Public Service Electric and Gas Companyl i
Newark, N.J.
07101 Abstract W..,.g?-
'p:
c
- y ?g
,.....s s f-v
.j; As part of a program designed to examine the feasi-A bility of ozonation as an alternative to chlorination
~'
for control of biofouling in once-through cooling systems,
'd.w/ IW the biological effects of ozonated and chlorinated 4
m,s TYY.' 8' condenser discharges were evaluated with white perch at a low salinity estuarine site having despoiled waters,
. N "Y l
and a relatively good quality freshwater site.
Results N./ p' [W of tests evaluating lethal effects at salinities between
, 4,;.;.;-p t(.j.y jI 0.5-2.5 g/kg indicated that the biological effects of 3.qg;- g$:f 1 +
ozone were less severe than those of chlorine.
Con-versely,.results of toxicity tests in freshwater indicated f R,.; :.TMQ that the biological effects of chlorine were less e i,.g; "/f.V M severe than those of ozone. In general, the relative
^'VA v ' ' 'i spggili& % i M; jud gd effects of ozone and chlorine in behavioral and physiographic studies were consistent with those observed U,:
t s. M 1
in toxicity studies. Differences in the oxidative cA TXMM Wh by-products formed by ozone and chlorine in estuarine
,. I"f y '. g 3 and fresh waters may account for some of the site-
'., b, y.My' specific biological effects.
. f ip
.[
- 4. k. 4..Y ;Q
./
Chlorine is the predominant chemical treatment used by the f
<j h*d N 8 %~
steam-electric power industry to control biofouling in condenser
...h
[/j.,
systems. During 1975, the most recent year for which figures are
-'g?$_.Tedis7
- 1 available, 559 cf the 791 generating stations surveyed in the U.S.
t h' [. ' i c. ',6.3.,y.
(J3 added a total of 27,339 tons of chlorine to their cooling waters
' %'Q3.
(1).
However, recognition of the potential for environmental
.,,g damage from chlorine has prompted consideration of methods to minimize and/or eliminate discharges of chlorinated effluents.
as T;Q..q.
As a possible alternative to chlorination for controlling
<.o biofouling in utility plant condenser systems, Public Service
' Electric and Gas Company has been evaluating the effectiveness,
- C-and technical and economic feasibility of ozonation (see Reference
,T 2).
A pilot-scale condenser system is used to simulate plant con-denser operations. Three model condensers operated in parallel facilitate the simultaneous evaluation of chlorine and ozone com-pared to an untreated control.
~
aPresent Address: Ichthyological Associates, Inc., Absecon, N.J.
08201 bPresent Address: Mercer Aquatic Associates, Trenton, N.J.
08160 155
- n. $ :~. 4 % ** ;.
.s,
.W-
~
,,e 3 = * *
/
-r :j -
I L
' R j r...
7,,.,
156 J. Meldrim et al.
In conjunction with this ef fort some biological ef fects of the ozonated and chlorinated condenser discharges have been eval-uated (3).
This evaluation compared the effects of ozonated and chlorinated thermal discharges on several species of estuarine and freshwater fish in acute (96 hr) toxicity tests, and in behavioral (avoidance) response and physiographic
(" cough" response) studies.
This paper will address those studies involving the white perch,
"*r'f.",'d.
Morone americana.
- f..>,1
' ' ][.
The white perch, which ranges from the Gulf of St. Lawrence to South Carolina, was chosen as a test species because it is e
found around many power plants located on the tidal portions of y
mid-Atlantic drainages. The biological evaluations were conducted JI at PSE&G's Bergen Generating Station (February-June 1979), a polluted, brackish water site, utilizing the pilot-scale condenser a
system; and at pSE&G's Mercer Generating Station (November 1979-July 1980), a relatively clean, freshwater site, where the pilot-scale condenser system was replaced by a chlorinator, ozonator and heat exchanger.
4 M.f ??* p -
The experimental approach taken in this study was based on h*
the hypothesis that motile organisms, such as the white perch, g
will avoid lethal conditions. Avoidance concentrations would
' i s
"I M %g therefore be lower than.those which resulted in mortality.
m.'
However, if white perch remained in the area of a discharge and f
y.
g.
were exposed to concentrations lower than those which elicited
- ',,r'
-4g avoidance, they could experience some detrimental physiological or s.dfh$
pathological effects. It was therefore important to determine if
% -S g g. y such concentrations wnuld be detected. Because of its reported
.G 4
o sensitivity (4), gill purging
(" coughs") was selected as the V M ',l method to determine physiological detection of a biocide.
MJ Y+^. % 1?'/.gh w.. <. v., ;
.h;; ** M x
Facilities Description I '.'
.UM komeA%sG W k).#II W A 12 ft x 46 ft (3.7 m x 14 m) mobile trailer was used as a
. g"[.,f, ;,7 '. ; ;."'
laboratory for the biological evaluation. Treated and untreated
',M 7
.T water were supplied to the experimental systems through separate
- J,- ne'9 r;
pipes for each water condition (untreated, chlorinated, and
- *' M M M ozonated).
U,
.. ' ? k g y...
Qpg While at the Bergen Generating Station, the Biological
@j y..y Evaluation Laboratory was located adjacent to overpeck Creek, a
- w. p,,
T tributary of the Hackensack River, and to a second mobile trailer Vggyg,[,k, %.#
v.
"./
which was equipped with the pilot-scale condenser system.
l xAr)?,
- ~
Discharge water from each of the three test condensers (untreated, P f/;, Ph' " '.W chlorinated, and ozonated) was piped separately to the delivery
- d
~"
system in the Biological Evaluation Laboratory. However, most of 7
_.p:
the biological tests were conducted independently of the dosing schedule for the condenser system because the levels of chlorine d.-
and ozone employed in the evaluation of biofouling control were M
too low for biological testing purposes.
A For testing at the Mercer Generating Station, the Biological Evaluation Laboratory was located adjacent to the Delaware River
.. f from which ambient untreated water was withdrawn. A water intake 4
system and biocide dosing system independent of the pilot-scale y
condensers were incorporated into the delivery system. Ozone was produced from oxygen by a water-cooled Welsbach Model T-816 laboratory ozonator. Chlorination was accomplished by injection of chlorine gas with a Capital Controls Co. Model 201 advance gas chlorinator. A heat exchanger designed to produce a 2-3"C tem-perature rise was used to simulate the effects of the thermal effluent from the generating station.
F r.: 5.~.c s ': - ;
- .y p.
i e
a j
g,*
J
=
's s
g
'e Effects of Discharges on White Perch 157 Testing Procedures Toxicity Studies The toxicity system consisted of two 4 ft x 8 ft (122 cm x 244 cm) tanks, each containing twelve 10-gallon (39 liter) testing chambers surrounded by a water bath. One set of tanks was used to test chlorine and the other to test ozone. Test concentrations were delivered to the test chambers below the surface of the water g
by mixing untreated water with treated water in the appropriate proportions from the delivery system. Chlorine and ozone tests
- I were C,onducted concurrently.. Five test concentrations and one
, Su
'N control were normally used for each biocide.
Y Initial toxicity testing at Bergen and all tests at Mercer f
were conducted using flow-through exposure to chlorinated or ozonated water for two hours per day with a continuous flow of untreated water between exposure periods. White perch were exposed for a duration of two hours once every 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br /> for 2 to 4 consecutive days at several concentrations of chlorinated or ozonated water. Aeration was not provided. Controls were maintained in untreated water. However, because of poor water quality and low levels of dissolved oxygen at Bergen, the results
' F W"-3. ait 5 $'! %*.f* b.
using this procedure were unsatisfactory at that location.
- .M% '.M Modifications in the testing procedure were then implemented to
h
'T '
improve survival.
s, The test condition between exposure periods at Bergen was
'.f )
modified from the continuous flow-through to a static aerated t
< kr condition. Test chambers were filled with untreated water and
',* c.4 '; t aerated to acceptable levels of dissolved oxygen. When this had been accomplished, organisms were introduced and test concen-O.., d.... ff; trations were set.
During the 2 hour2.314815e-5 days <br />5.555556e-4 hours <br />3.306878e-6 weeks <br />7.61e-7 months <br /> exposure period the test i.!I
-f"/
was conducted in a continuous flow-through mode and aeration was (supplemental aeration of the ozonated water was not necessary).
$'X t
supplied to the untreated control and chlorine chambers
.. j At the conclusion of the exposure period all test chambers were 4.ggg l, %Wei lM returned to the aerated. static condition.
q
.y
('-
Daily average test concentrations for each of the ozone Jy levels were determined by averaging five measurements taken during
.t 5
l
. 'Q each 2 hour2.314815e-5 days <br />5.555556e-4 hours <br />3.306878e-6 weeks <br />7.61e-7 months <br /> exposure period. The daily average chlorine con-l,,.
centrations were determined by averaging four to eight measure-
.. j
><a ments. The final. test concentrations were determined by averaging 4 2,J 'qP
- c%., %,
these daily averages. Water temperature, dissolved oxygen, pH, y
A o
and salinity were measured before and during each exposure period.
gg ;<
/
k['
observations were made periodically during each test. Time T,!
7 p*m,
.J'-
of loss of equilibrium and death (defined as cessation of
- '/~
opercular activity and lack of response to prodding with a probe)
~A were recorded for periods up to 96 hours0.00111 days <br />0.0267 hours <br />1.587302e-4 weeks <br />3.6528e-5 months <br />. Dead organisms were
[
removed when observed, measured, and in some cases, weighed and preserved by freezing. At the end of a test the remaining (live) i organisms were measured, and in some cases, weighed, examined and preserved. Gill tissues of selected specimens which survived and of most specimens which died were examined for damage with a dissection microscope.
Avoidance Studies Behavioral responses of organisms to chlorinated and ozonated waters were evaluated in an avoidance system consisting of two modified Shelford-Allee avoidance apparatuses (5).
Each apparatus was 2 ft x 6 ft (61 cm x 183 cm), subdivided into 1 ft x 6 ft (30 cm x 183 cm) sub-troughs, and made of 3/4 inch (2 cm) exterior I
l V
U.,. :.. g ;..
e- - ( -.
R.
e
(*,
- d' 4
a-
-$s 7).( a
.h
?,,
A; ;'
', Y
~ W.<
,?"
a
-1
- i..
e,
f.,+
t
..=
158 J. twidrum et al.
plywood coated with inert epoxy resin. The system was enclosed in black plastic to permit movement around it without disturbing the test organisms and for light control. A Duro-Test " Vita-Lite",
which has a similar spectral distribution to sunlight, was used for lighting. Light level, measured with a Weston Model 614 light meter having a precision to two foot-candles, was maintained at 430 lux.
Each apparatus had a dose box which was divided into two compartments. One side received untreated water from the delivery PA 4-system. The other side received untreated and treated water from
- s the delivery system to produce a desired concentration. Water from each side cf the dose box flowed to diagonally opposite ends r
of the sub-troughs and then drained in the center. Due to a sharp
-j.
gradient at the center drains, each apparatus was " divided" into quadrants. Concentrations in the dose box were produced by adjusting flowmeters and the flow into each sub-trough was further s
regulated by flowmeters. Organisms were exposed to successively increased concentrations of ozone or chlorine in a " step-gradient" fashion and their responses observed.
At the beginning of a test equal numbers of white perch were placed into each sub-trough of the respective apparatus. After a five minute orientation period the amount of time spent in each M*, 4.I..,.S%. I;fi.*(
h..,@,:.f quadrant (formed by the center drains) was determined for a dura-s.
^ 2" C
t'
. -g-; ;," -
tion of five minutes and a frequency distribution of organisms-times was formed. A test continued until an avoidance response i^ '
with a 2:1 ratio of time in control to time in treated water, or fu death was exhibited. Concentrations of the biocides were deter-D mined throughout each test.
Water temperature, dissolved oxygen,
~
pH, and salinity were measured before and at the end of each test.
I'
~
At the end of each test, organisms were measured and in some cases, weighed and examined. Because of the size limitations of
'. 'g/ t, were not utilized.
ypg cdfr;m.,,
' ; '. '(g './ /5' (
.g.
T, the testing facility, white perch exceeding 200 mm total length
, f:
O M; '(* '3 7 M y 3g Physiographic (" Cough" Response) Studies
7#'
$$1YY
'4 The physiographic system consisted of four testing chambers 6 Ls ..., N-v hfy*Q.
and a four channel Narco Desk Model DMP-4B physiograph. The test EQQA Y
J Q~ > *Js,..gy;/;
/(. ;
.chembers were based on a design given by Spoor, et al (6) with "Jj#1,4
'E. 4 some modifications. Each chamber was made of 1/1 inch (0.6 cm)
-n~f
L 'l 4 J ff-. 54 Plexiglas and divided into three compartments: (1) intake, (2)
"gk'*ff I t EJ. Si""l middle compartment which housed the fish, and (3) drain.
et 'T1-'-
1 Plexiglas dividers were placed in the midile compartment forcing JI.f$iidd)J,f*S$
the fish to assume a position perpendicular to the ends of the
'. e
>4
%j gdkT chamber. Stainless steel wire electrodes were placed at each end
{3
.ip fC;[ i p,.7
'- 1,
- -[;d-t W'l of the middle compartment. The electrodes were then connected to
. j' the physiograph which recorded respiratory responses of the test
,;,j;, wc s,
organisms.
'i'
,i
'? t ! '..
" W.. J ",
Two chambers received a continuous flow of untreated waters
.d
'.~
V
-u.
4p"[
- one chamber received chlorinated water and the other chamber a
i received ozonated water. Usually, at least two chambers were used
- during a test; one with untreated water and one with a biocide.
~ ~ -
All water was taken from *.he avoidance system dose boxes. Each chamber was placed in a three-sided compartment with the fourth 1
side covered with black plastic. Initially, observations were made via small slits in the black plastic. Later, one-way mirrors were added to the system to f acilitate observations. Lighting was provided by a Duro-Test " Vita-Lite" connected to an~ electric timer to simulate the natural photoperiod. Light level during daylight was maintained at 430 lux.
Because of the size limitations of the chambers and the sensitivity of the physiograph, test organisms were chosen which ranged in size from 57 to 105 mm total length.
h ;-py-l[ * ***h, k
s
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'*UL y
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,.=
Effects of Discharges cm White Perch 159 r
" Cough" response tests were usually conducted concurrently with avoidance tests. One fish was placed in each chamber and subjected te a continuous flow of untreated water for approxi-mately 48 hrs.
If turbidity was high this period was shortened to 24 hrs.
During this time the fish were allowed to acclimate to the test chamber and to establish a normal respiratory pattern.
i;.@s c.#6"ht
. fj Pnysiographic traces of this pattern were made just prior to the i
exposure period for comparison with traces taken during exposure s
fi;
- I,)
periods. Traces were taken at concentrations which were gradually Ftd increased to levels beyond the avoidance concentration. Traces for fish in untreated water were taken simultaneously with each
' t/
biocide concentration to compare differences in cough rate, 3-breathing pattern and behavior of the fish. Exposure to a con-7 centration was from 5 to 45 minutes before a trace was taken,
^
depending on the behavior of the fish. The fish were given ample f
time to adjust to the increase in concentration. This permitted i
better observations and enabled the physiograph to record distinct
,[
" coughs" in the respiratory pattern without interference from
.k excessive activity. A five minute trace was taken at each con-
,"..-s.'
o
%s'{%. *(* @b y
.%/
f; 64 centration. Observed and physiographic (traced) " coughs" were N.f M644
.M)
~
used to calculate " coughs" per minute (CPM) at each concentration.
f p.g Biocide concentrations were determined throughout each test.
'";f*f id Water temperature and dissolved oxygen were measured after each
'N
.c s
^d,/
2.*,3 C,d$ (((g
$.. V test.
Salinity and pH were determined at the beginning and the end of each test. Test organisms were measured, and in some cases
' ' * 'S '
weighed and examined.
{'?. & q x' M;.
y ll.
.hfh.. :j
[s Water Chemistry
)
Water temperature was measured with hand-held immersion ther-dy 9 y@'h mometers scaled in 1.0*C intervals. The level of dissolved oxygen EW.M V-'.?J-4 QmW was measured with a YSI Model 57 temperature compensated oxygen sp3gsiMQM Wylf??f%e y"M-?.di n *'.
meter. A Corning Model 610 A pH meter was used to measure pH.
,f44.
...s h * ?,", (,.
Salinity was measured with a YSI Model 33-S-C-T meter.
?' q% ;
,,> $'j d.pd W Y ufg%' ;W*T _'
- .h Chlorine residuals were determined using a Wallace and
%W 4s - M;-
Tiernan amperometric titrator according to Method 409 C in M.
- 1. dF f *.ijg,Jj Standard Methods for the Examination of Water and Wastewater (7).
'VQ It is important to note that, as a result of the ditterent water f.?
13 quality conditions at Bergen and Mercer, chlorine produced a dif-6.. Y-yF ferent set of oxidant species at each site. Considering salinity, Y,,$Mdhh.
m g.g?Q-/' #,ip {
N,R--q g *. '.!;';k pH and amino-nitrogen, the following oxidant species are most l ' ; *'."',.*
probably produced by chlorine (2,8):
j,ji, p ' ? y,.
,.'..n.
3 N./ i t
Bergen - chloramines, organic chloramines and traces of
/2 bromamines; L ;t.
'. f ;y.a n
- c~'-
-r p /
Mercer - free chlorine and chloramines.
,,[$
i,:
p' Free chlorine, as operationally defined by Method 409 C was M ',, j ;
/
rarely detected at Bergen and accounted for only a fraction of the 4
g total chlorine at Mercer.
4 Ozone was to be measured using the same procedure as for total chlorine (amperometric titration at pH 4).
However, when dosed with ozone, the river water at Bergen did not reveal any residual when measured at pH 4.
It was found that a measurable residual did exist when analyzed at pH 2.
Routine analysis of this ozone produced oxidant at Bergen was therefore carried out
(
using amperometric titration at pH 2.
o
,'c.
.. 'q.
p * * '. 5, N.
.--a.
.; --- ~--
...... y - <.-.,, (
a
', ' l
,h
-g
l.
4
~
160 J. Meldrim gt al.
Further testing for ozone at Bergen corroborated the finding that the residual being measured at pH 2 was an unidentified oxi-dative by-product of ozone and not ozone itself (2).
In contrast to Bergen, ozonation of the river water at Mercer did produce an ozone residual which could be measured by ampero-metric titration at pH 4 or at pH 2.
Analysis at pH 2 included a r@.M r> W M-H natural background which had to be subtracted from each deter-j, -i.?
'sfr i i
mination. No background was measured at pH 43 the background at
, !,.- N pH 2 accounted for any differences in the results at pH 2 and pH 4 J.7-M,$ 'f.1<., '....'
at Mercer.
.Y-
.5
. A, s
3>
Test organisms s.
Most of the white perch used in the study were collected from
.[- '
the watersheds of the Delaware River and upper Chesapeake Bay l
drainages by seine and transported to the laboratory in insulated
'Y holding vessels. Test organisms were fed a variety of foods but not during or 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br /> prior to testing.
-i Results and Discussion
.~.
.-,..s, Toxicity Studies P @ M E* M E
Due to the poor water quality of Overpeck Creek only a single N *i f
chlorine and a single ozone toxicity test were completed at
[b, N[.,."(. E
- g-Bergen. In the chlorine toxicity test, white perch were exposed k
a p
Q
'I to total chlorine concentrations averaging from 0.02 mg/L to 0.87 M->;-q; lSg;j - }6 ag/L at 14.5 C and 1 g/kg salinity. Concentrations above 0.37 mg/L resulted in 100% mortality. The 96 hr LC50 for a 2 he inter-E'
'(q N,j 5/'hTp.w.#., #
mittent exposure (ILC50 2)) was determined graphically to be 0.10 mg/L total chlorine (96,In contrast, no ILC 3.
[if-50(96
- could be calculated for the ozone test. No mortality occurre,d)in any ozone
. " h. '
i--
N concentration at a temperature of 15.5'c and salinity of 1 g/kg, even when white perch were exposed to 0.66 mg/L ozone (the highest m:n O It M N,%'W l9,.'.. g
concentration tested).
, j *.
Five chlorine toxicity and five ozone toxicity tests were iN.8W Q %
(
l'
- g c.
.a conducted in the freshwater at Mercer. In the chlorine tests, i J:,
white perch were tested at average temperatures between 2-26*C and M W*. M L
t.
at concentrations of total chlorine between 0.1-1.49 mg/L. The l
[A [y[c tests at 2'C were ignored due to high mortality in the control.
However, the ILC50(96,2 at 11, 19, 22, and 26*C was about 0.87,
~
g.
,J 0.69, 0.61, and 0.74 mg/)L total chlorine, respectively.
The mean b
4
- ..77 ILC50 was 0.73 mg/L and the standard deviation was 0.11 mg/L.(962doughtheseresultsandthoseobtainedat2*C(no
)4,rgd. % % p{
7
,(, I Alt g
.M ? >
mortality at 0.78 mg/L total chlorine) indicate an inverse 2, 3, 7 H '.s. f./ q 1
relationship between temperature and chlorine toxicity, no signi-M].,'P. t [,.:.', j vi id ficant (P 1 0.05) correlation (r= -0.67, d.f. 2) was found.
,. 3 s
^.s m;,.
In the ozone tests, white perch were tested at average temp-Wy:...., ' '
- eratures of about 2-27'C and at ozone residuals between 0.04-0.97 7.T:7 *. 4'T M4 ag/L. Again the test at 2*C was ignored due to high mortality 4.Y "
in control organisms. The ILC50(96 2 at 11, 19, 21, and 27'c (sj.i...
' ;i 0.37, 0.26, 0.22, and 0.25 m)g/L ozone, respectively.
"Q:/
was about The mean ILC50 deviationwasb962)was0.28mg/Lozoneandthestandard M?
.0Y.
No significant (P y 0.05) correlation (r =
yr-1
-0.60, d.f. 2) war found between test temperature and the ILC50(96,21 of ozone. However, when the results obtained at 2*C K" ' 3 /
~
(404 morality at 0.77 mg/L are considered, an inverse relationship between temperature and ozone toxicity is strongly suggested.
"4
- . y.
- g If['M
~
r.
0.^h.-l,:v. e.,. w.. -. !
i
'I h.f
' V.;,
.p.;
. Q":
- ,l - ?YQ%, % x.,..y * ' '
u.
v
- ,b T: C
- ?.
r, q <,
a.- --+ '., ~
,n
.. (. p a-4
.9
.t Effects of Discharges on White Perch 161 Avoidance Response Studies Chlorine avoidance tests were conducted at Bergen over a range of average experimental temperatures which extended from 22.5-28"C, levels of dissolved oxygen from 3.3-5 7 mg/L, salinity fecm 0.2-2.5 g/kg and pH from 7.2-7.5.
The avoidance con-centrations, plotted against their respective test temperatures in y
Figure IA, extended from 0.01-0.20 mg/L total chlorine with a
/ -- A L #-
if, mean avoidance concentration of 0.04 mg/L. Howsfer, the standard deviation (0.05) was greater than the mean.
If the 0.20 mg/L p
avoidance concentration is considered erroneous and removed from g.
the calculation, the mean becomes 0.02 mg/L with a standard p
deviation of 0.01.
Of the twelve chlorine tests, two were con-4 ducted with a 0.5"C AT accompanying the biocide. The avoidance concentrations (both 0.01 mg/L total chlorine) in these OT tests
[
were within the range of those found at ambient temperature.
y
+
Ozone tests at Bergen were conducted at average experimental I
temperatures extending from 20-27"C, levels of dissolved oxygen from 6.7-11.8 mg/L, salinities from 1-2.5 g/kg and pH from 1
7.3-7.6.
The avoidance concentrations extended from 0.03-0.20 D.hs.1[,..W Uh4sMy mg/L ozone with a mean of 0.07 mg/L ozone and a standard deviation M. v6 rD
' M.7.?< -
of 0.06.
The highest available test concentration failed to eli-
^%"M.M cit avoidance in two tests. The ozone avoidance concentrations
. ~f #$ f A
are plotted'against their respective test temperatures in Figure s
1B.
.# :'+:W " Q l
p-
.g Chlorine avoidance tests at Mercer were conducted over a M
If range of average conditions which extended from 7.8-26.8*C,
'D N<.: @[I
$'.f)f.4%
i 6.2-11.2 mg/L dissolved oxygen, and pH from 7.1-8.4.
Avoidance f.
r' concentrations extended b'etween 0.10-0.36 mg/L total chlorine with QM ik a mean of 0.20 mg/L and standard deviation of 0.08.
The avoidance 24W$;VGf.p
?
concentrations are plotted against their respective temperatures 9.f. 4.R s
in Figure 1C.
g
. {gf appespdp a g
Ozone avoidance tests at Mercer were conducted over a range qqjiil
...U of average experimental temperatures from 6.8-25.8"C, levels of Wh,. rad.p M.[M.%p M-
'Ify /F4 dissolved oxygen from 9.7-12.3 mg/L, and pH from 7.1-7.9.
(.
MM f.E - W Avoidance concentrations extended from 0.04-0.16 mg/L ozone with a
@'M {
l ^~' 7tg.
mean of 0.11 mg/L and a standard deviation of 0.04.
The avoidance i.b KEN s.j p fi4 concentrations are plotted against their respective test tem-W 71 % s.br.
@ %.G.y. -
peratures in Figure 1D.
Correlation analysis showed a significant Y@@ ~?ff' 5
(P < 0.01) inverse relationship between the ozone avoidance con-N
+
h.
j/
centration and test temperature.
h'{Tln [
- k... hwN#N 3
~
m-Physiographic (" Cough" Response) Studies
( ;[.'
d, 1C J.$.,."[?:)
white perch exposed to chlorinated, ozonated, and ambient water.
Physiographic traces of " cough" responses were conducted with 3.*Y 1
.l D
~.Ybg 23 4
" Coughs" (gill purges), " yawns" (perhaps another purging c3
'*ES y.(
pp 4
behavior), respiratory, and behavioral changes were evident with
.r' s-i, '
-t" N {
. increases in biocide concentrations. However, " coughs" are con-
' m sidered the most quantitative measure in the study (4).
Sprague -
(9) reported that respiratory impairment in fish was a good indi-k~
Oi -
,a cator of toxicant stress, but that the rate of " coughing" showed
~ 4 more promise than opercular rate as a meaningful response to sublethal concentraticns.
- c White perch had large, distinct " coughs" with increasing biocide concentrations.
However, the rate of," coughs" did not increase continually with increasing biocide concentrations.
Rather, a peak in " cough" rate was followed by a gradual or rapid decline in
- coughs'.
The concentration which produced an initial f
ydn:
- p. w. Q
- ~
- w.
g_
hk e
y
- p
[,
s S W.N: W
'5.,. c b,
~
.,e-m-n.
s u,..; p..
.s
. e f.
s.
162 J. Meldrim et al.
0'O' 040-A B
Q30-030-E.,,..
V ts.. 'g
'h Q20-020-
- ta
..s.y O.10-alG-c.
'n N
s 40, O
p i
CO C.O 200 30.0 00 00 200 300 TEST TEWERATURE PC)
TEST TENFERATURE (*C) 4
~.611 s A.
, T.h ;b.1 '.*a...
f t.MQ*
- r I
a
~
b.
't
.ht g.
g.
.\\
q4c.
C D
4 q.v y,
q3o q30.
1:..rs;;.?
w O
,4 Q&
- i.*?-}
i N
,,'. -;.' _ s 'j.'
gQ20-O GO20-s'i.
~
.c t:
5 i
- c
.f
.r s
u
.c."~d'h " '
41 LT. ?
Q0-
~^,'$$=1&:::t.
!'2: s. a alO-a i (25:;T f
a.
. a u :,.
. Jip,pW/.t.g$st e.
U wm[E ?y 30.0 00 00 20.0 300
'+7 00 00 20 0
',,.';'M,,M y-.>,
. s..,$.. m ),; 7.:w- "..
e.
< r,t.s.'>&.. J.
TEST TEWERATURE (*C)
^
c' ?
TEST TEWERATURE (*C)
- - ey y
- n. t,
,4, y!,s,.
- .* *p 7 y g...- a's *.,.,. ;
.i E
-,.. w..Pf
$ ?
I 3
7 k.d ;h,;:
c:. )v.,,.:.
>.7).r%
.n.
- .y.~;
- ?.<..... ve r
>s
< s,,.
A., s
-~p v
i 2,w FIG. 1
.' : /., " ffi'l J 'i.1.
Ap-,.?
^*;
- 3
+
9,- c.v Biocide avoidance concentrations of white perch, Morone
?'
pj f,[,M
. ij. N '.
americana 2 vs. test temperatures (A, B - Bergen site; C,D-y.,
a.
.~/
Mercer site; the number of data points is indicated numerically).
c.f.,
- a
.. -e..:.
s..*f.
j,..u.
~
s
?
i l
- 9......:...
- .i+: <iv : -i. A.. ~. t.
QY@.}
g.
~.
>;.,,. 1 c.,.
..,,, :. c
.,..;,.e 3
,~
.w.
(
9 1
~
.:J.
.a Effects of Discharges on White Perch 163 I
" cough" response was chosen as the physiologically detected con-centration. The initial " cough" response was defined as an increase of at least one " cough" per minute (during an exposure period) over the " cough" rate prior to exposure. An increase of less than one " cough" per minute was considered within the range of a " normal" cough response. Although determination of the ini-tial " cough" response was the major objective of this study, phy-
%C n."hV (
>a siographic traces were conducted at concentrations beyond this p.
,./1.f initial level to those which elicited avoidance and occasionally to toxic levels.
j-q.:
.h A summary of the total chlorine and ozone concentrations 4
which elicited an initial " cough" response at Bergen is given in N
Table 1 and in Table 2 for tests at Mercer. Avoidance con-i 7
- centrations which occurred in concurrent avoidance tests are also
-{
3 presented in these tables. White perch exposed to the chlorinated ef fluent at Bergen at 24*C, 4.5 mg/L dissolved oxygen, 2 g/kg I
salinity, and a pH of 7.2, exhibited an initial " cough" response 5..
at 0.02 mg/L total chlorine. This was similar to the chlorine
-1 avoidance concentrations (0.02 and 0.03 mg/L) observed in con-M i-h h b
.f 9,5d d
current avoidance tests. Ozone tests at Bergen were conducted p?pW over a range of average conditions which extended from 15-28.5'C,
- M -
l 3 8-8.5 mg/L dissolved oxygen,1-2 g/kg salinity, and pH from
- ?
d
'."NE ' "' MM[%
. :.A %
6.7-7.3.
Although white perch exhibited an' initial " cough" r
s, response when exposed to 0.02 mg/L ozone at 15*C, the " cough" rate
. 8., r 'f ;f g;7 decreased with increasing ozone residuals at 23.5-28.5'C and no t.?{ M, WA.L,,4.-@/.
initial response could be determined. In concurrent avoidance A
tests conducted at 23.5'C, white perch avoided 0.04 mg/L ozone, 4.g.?Ig g4
- 4. M but in the replicate did not avoid 0.07 mg/L (the highest con-7.. < '
centration tested).
n-Mg"g ;
L-we
. f 'Mjip M p~ :y:U.y ogh.*
O'h At Mercer, a series of physiographic traces were taken with
'((s i white perch over a range of average conditions which extended from
$~ lS:V,9'; ;,
^^ 4 L, h' M 5
' 'f T *,*.y
- w.. Y '
5-24'C, 7.2-11.6 mg/L dissolved oxygen, and pH of 7.2-8.4.
y
-M-Initial " cough" response concentrations extended from 0.03-0.25 4, M " 2f mg/L total chlorine with a mean of 0.13 mg/L and a standard
...y.
%.. IN -
g[Tf%yJG ImdO deviation of 0.09.
Test temperature was significantly (P < 0.01) 3M 3?2N
' fN" * '-
inversely correlated (r = -0.88 5 d.f. ) with initial "cougE"
- -M.g/qfw 7
- [
g%;>T
,jr' NMl response concentration. Except for the concurrent avoidance test
' W;9 d d
at 7.5'C, avoidance concentrations were greater than initial 4g - %.gg M;,
" cough" response concentrations. The difference between avoidance
" ~~
and initial " cough" concentrations became greater as the test tem-y" r
perature increased.
hy y
h Ozone tests at Mercer were conducted over a series of average
[I.g.,q.
d[
[W c
r. /,
conditions which extended from 6.5-23*C, 11.1-13.7 mg/L dissolved
( $U,s.%l
- .?".i,ql d j. >q-Q.?
l, oxygen, and pH from 7.3-8.2.
Initial " cough" response con-s
- 9 centrations were from 0.09-0.17 mg/L ozone with a mean of 0.14
,;h;k
'.i
. o.7
- r. J mg/L and a standard deviation of 0.01.
Three tests resulted in no
/
TMH i f. W J4 ij.5
',' $ ' K ' * [77. N initial " cough" response even though the mean concentration was MN exceeded in one such test.
There was a significant (P f. 0.01)
'C
- d T inverse correlation (r= -1.00, 1 d.f.) between temperature and the n'
~
'f
,E M, concentration of ozone wh'ich elicited an initial " cough" response.
- y y
However, the number of data points (3) is extremely limited and C
more data should be obtained to confirm the correlation. In tests
.Q. :
5 in which an initial " cough" response was observed and a concurrent
- ' dil j j
avoidance test was conducted, the initial " cough" response con-i 5
centration was within the range of avoidance concentrations.
7y; Conclusions s.
The results of tests evaluating the lethal effects of chlorine and ozone on white perch at Bergen indicate the biologi-
!.fl'
~- *-'
9 n.
3-t,y
-h " ~3;$ Q'-
~
-M s
.M
' W.t r
a
.r
.y ?f; j ' *
.,1 P
- l-'
a
,.v r.,
. D;.,,rm;. s
.u.--
%c s
I,~
e c.
y.
y.
r.,
9 164 J. Meldrim et al.
c cal effects of ozone were less severe than those of chlorine.
Conversely, the reSJ1ts of toxicity tests at Mercer indicate the biological effects of chlorine were less severe than those of ozone.
At Bergen, the ILC50f96 2 for chlorine with white perch was about 0.10 mg/L. Contras ting,ly),
levels of 0.68 mg/L ozone failed perch exposed to chlorine was higher than that fo,2) p g g ^ g-to cause any mortality. At Mercer, the ILC50(96 for white t,-
,x.
r ozone.
... w.4 H,%1Ql ?
. 4 % p2 i The relative effects of ozone and chlorine in the behavioral 3
G' d C Q/ ")'
studies were consistent with those observed in the toxicity stud-2'# 4 ies. At Bergen, white perch avoided an average 0.07 mg/L ozone,
.[
- @:k.
but accepted no more than an average 0.04 mg/L total chlorine. At i' '
Mercer, the average chlorine avoidance concentrations were higher avoidance concentrations observed at Mercer and Bergen were less d
than the average ozone avoidance concentrations. As expected, all 3
than lethal levels.
1 Initial " cough" response concentrations at Bergen were lower 7,Q.,/
when white perch were exposed to chlorine than when they were p'$"ss.W exposed to ozone. At Mercer, however, white perch exhibited a E
g.. N,*
lower initial " cough" rate when exposed to chlorine than when e g}@'%$.g~
exposed to ozone. In general, the initial " cough" response con-
- j ff *M centrations elicited at Bergen and Mercer were either about the r
same or only slightly less than avoidance concentrations in con-P,.l/[ j current physiograph-avoidance tests. Apparently, avoidance occurs m :. '
shortly af ter detection of a biocide (at least, detection as TJN measured by gill purging).
9 y
b
'M A comparison of the differences in the biological effects of h'd chlorination and ozonation at Bergen and Mercer are limited
..d because more tests were conducted over a wider temperature range hf.{dfy at Mercer than at Bergen. Nonetheless, it is apparent that white
@hih>
perch were less tolerant of, and more sensitive to, chlorine at s
7'[h W_f yQ%
Bergen than at Mercer. Conversely, they were less tolerant of, 3,
Af.7 and more sensitive to, ozone at Mercer than at Bergen. This dif-y %([W@2 y
ference may largely be due to differences in the chemistry of n
N GjfAr chlorine and ozone in estuarine and fresh waters. Oxidative by-
- g M'N Ig!.
Products resulting from chlorination and ozonation depend upon the s
Q.Y<
oxidizable components in the aquatic system. As these components a
tg f 5.d. E;g y(;
vary significantly between estuarine and fresh waters it is to be k
', Mf,Q,
'%p expected that the by-products, and hence, the biological effects h -
4Q '
of ozone and chlorine will be site-specific. In fact, white perch M.p./w were not subjected to ozone at Bergen, but to an unknown by-
[
j ;
f.'
E..
product of ozonation. The effects of chlorination and ozonation t
[.F. V'N
'. / p 5,9 [i.f.'
were undoubtedly further affected by the despoiled water at g
-k, y q
,; Ql.{,.-.'
Bergen.
f M. W h p. t AD... n
,. r c c.
- i, Y' M./10 ' 7# - '
Although not statistically significant (P < 0.05), there d' ' ' hdtj,h appears to be an inverse relatonship between teiiiperature and the gliMg lethal concentrations of chlorine and ozone in freshwater. More c.
Tff.X tests are needed over a wide range of temperatures to confirm the relationship. Ozone avoidance concentrations in freshwater were Mc ?$%i
.e/'
k r
$:-M@i
^~
significantly (P f,0.01) inversely related to temperatures, as
.yJ ; I p.
were the concentrations of ozona or chlorine which produced a phy-siological ef fect measured by gill purcing.
. G '., 'fg
. &#, R Evidence of gill damage on fish tested at Mercer was rare.
..M i t-1 Some aneurisms and hemorrhaging were noted in both experimental
' g7 and control fish. Considerably more aneurisms and hemorrhaging
('-.
- v. i.
were noted on the gills of fish tested at Bergen. However, gill
'( s.
~
damage was observed in both experimental and control groups at Bergen and was likely attributable to the poor quality of the dilution water.
,, ~ ~
~
. ~,.,' ?,
.s o
.kh c
w:s
~
~
- x, n.
.... _6.
.s a
M.
.gg,.. q. i g.p'.. g,. y *q.,
. ~..
4,,; # '. :p).q._ ~ ' ' o" '. 3:;p.?;":m.
.n.
. u.s.
p.a.., g..
4 %;.i
.y...
,'.... %.,7
- y%. ;
.. 7_
.Q, 7
y" Q:m,
?L+.
M.a c.
,.r.,
- o. m..,.
e,,
e.b f
Effects of Discharges on Whi.ta Perch 165 TABLE I Initial " Cough" Response and Concurrent Avoidance Concentrations at Bergen Initial Cough Concurrent V9':'t6v,5 sh-l$W'.A).
5
's. 4 Test Response Concentration Avoidance W [ v.'. j.C, :: ". ' '
( i j,,', i'.,* *,fg ;.
Biocide Temperature (C)
(ag/L)
Concentration (rg/L)
- ::6.',M'; P '
F -Yf,* '.'{ ",*. :;y Q:
' g,-
Chlorine 24 0.02 0.02, 0.03
'.,'*t
,y Ozone 15 0.02 s
e
~
23 5 0.07' O.07** O 04 7
28.5 0.26'
{.
-h I..
<.:,.g.
pg,!j s g.
e highest test concentration did not elicit response.
. A..;
...r.e 8
,4
,e
- g t' f ,; ;
s.
- n m n i> %. W.!9 s.. y.
g g 7;... q,, g.b:Q;.?,g TABtX. II
- ,, M'y>c < 'Q j. 'i
,gt g Initial Cough Concurrent
'y T",*k Initial " Cough" Response and Concurrent Avoidance Concentrations at Mercer
'Ni r'8.3 g,
- sxszo:f..s 7
Test Response Concentration Avoidance
- t. k //<
Biocide Temperature (C)
(ag/L)
Concentration (ag/L)
'i f,. f:,:pgy,4S{k
, t~ ;.. h c;
,g '.'f p,, G:..
Chlorine 5
0.19
.iWMM cEY..
'. '.),.: x#'M"p.7:+.d 7
N
-- EW',%1 7.5 0.25 0.10, 0.10
..o M5t n # -.m
,qtus[4;fym.pT~ggfpiFj w
.'r( ',
8 0.22 0.25, 0 31
- u
.g.., ff. 9 10.5 0.09 0.17, 0.10
.. ~...
7.j gg,4d*:
aa
-r Fi
21.5 0.03 0.21, 0.15 r
m.--
h @ ly,'
23 0.05 Ji s Ryg%
%. ~.. Q.. "
~. J-i
,po' 24 0.05 0.23, 0.36
.QggQ,,,7.*;z,'P s' Op.Wpt. t
't Ozone 6.5 0.078 o,og o-y i.--1 s d.f;"
.".4
- r"W6*?.,s.Q"4y[Ml b
- p. w ;3 I2.,;.
7 0.17
'.'Q.yg.y.1.,p::n..q_Q.
- < 5.
g.
9,
. ~....,
,.u,:(..'.1..:f, 3.
.wy,.
8.5 0.098
- ~
u...,
,,.. - ~.
c 9
0.43' O.14, 0.14
- f. ',7.g.-
- y n. ;.~,
9.5 0.16 0.14, 0.16
,g.0 4 l
i x:
1 23 0.09 0.08
'. ;:~ ;.'
- a highest test concentration did not elicit response.
f,4f...I f.W.IN.i-I. '.
- 4 '.e p
.e
+
n 4
,1 y " '
6,'.
- . *t. /,. *, if
, _..Yy p.,,(-
4-..
e
....,.'h
'g.,[e
. y !. ' * '..
^,, :.
3.,,,
g,;.
n.
? ",
e'
,1,
" " "- ' ' ~ - ^ ^
v
E.~
?
v.%.'
~ e !g.
>l.
166 J. Meldrim et al.
The results of these studies can be compared with those obtained at other laboratories. The biological effects of any oxidizing biocide on a given species, however, are highly depen-dont on the time of exposure and usually are site-specific. Some dif ference in results at dif ferent locations is due to laboratory and test population dif ferences but most can be attributed to dif-ferences in quality of dilution water. This is especially true for tests conducted in waters of dif ferent salinities.
,,,tG;3 9,,,,;.,
>: :~ n.c.
In chlorine toxicity tests with white perch the
, /i ILC was 0.10 mg/L total chlorine at Bergen and an average
. If,.
0.7h0(962gotalchlorineatMercer. The mean 96-hour LC50 for i -
t mg/l white perch continuously exposed to chlorine proportionally Rf diluted with water from the Delaware River estuary was 0.22 mg/L g'
total chlorines standard deviation was 0.08 (10).
It is probable a
r
'that an intermittent chlorine exposure to white perch using the
?
higher salinity water of the Delaware River estuary would result in an ILC50(96 2) exceeding 0.22 mg/L. However, whether it would approach the IbC 0(96 2 at Mercer is unknswn. The chlorine avoidance concentratio,ns) of white perch tested at Bergen and 5
Mercer averaged 0.04 and 0.20 mg/L, respectively, whereas the
- 4 average total chlorine avoidance concentration of white perch in
-c - s '
g$pid.y, Delaware estuarine waters was 0.06 mg/L (11).
e 3,
fh.,hy[.
v Because of the time dependent nature of the toxicity of these
~
c, f;\\ ' '
biocides it would seem appropriate to base water quality criteria K.
'x on site-specific sub-lethal ef fects rather than on toxicity data.
J
. s As expected, lethal concentrations of biocides were detected and
..g, 4 f, 3 l f. ',
avoided. Although the physiologically detected levels were M.*.], g,.C,&M, s'J D, '.
- g,..
p.-'
@Ti? r jW[Dpp
, A;,p. ;
slightly lower than avoidance concentrations, it is likely that
. ' f $. M M.s.
L'glphS irritating levels would eventually be avoided in longer exposure
? I N V.'.
tests. Consequently, if their use is intermittent, the most TN' '
likely environmental impact resulting from the use of these bioci-U$gMQc% V 4
-+:
'a. Q,.g
} '/f."gh c',' M:.:
des in electric generating stations would be temporary loss of b@d4[*1 j'7S:
. ^
3
?M habitat. When used in despoiled waters, ozone would probably even
<:Q]Jg..{
be beneficial by virtue of the addition of dissolved oxygen as sm
-, w -f,y m,- 4 UT'p 3*-
its major by-product.
- y 3
4 -4Ase.c c >. :NW L
[%.
s b.
This study represents an initial attempt to define the eco-
- 3
$/[f, 7;d..
M/ $
logical effects of ozonation when used for condenser biofouling
.,N W.&
control at electric generating stations. The results reported f
4 9 M;lf%.1W 5$,
here and in a previous paper (12) suggest that levels of ozone Q'M 3
53 M..J bij necessary for effective biofouling control at Bergen
(> 0.5 mg/L) are not high enough to elicit a lethal effect with white perch.
Y Obviously much more work needs to be done, but the results reported here are encouraging enough to warrant further investi-gg
.-y - M1
/M. y M.y,
Q gation.
g 3 1 S r..
~ fQ.Q.
}1,., n K:
yl}' S '.,4. 0.' q q 3.N,-
[. a -
Acknowledgements
?!
4 t.&'d I, J M t
- ' Y ~ ~ R.W(ye.o W/:'
' ' ?.'
'54 J # J. #.'
This work was supported by the U.S. Department of Energy.
' Yf*..i The contributions of C.
R. Guerra, J. L. DelMonaco, J. H.
- d'[ [9 % 5[j;
,.( j':'.
Singletary, W. A. Sandvik and personnel from Bergen and Mercer r5'
'e 3.
s Generating Stations are gratefully acknowledged.
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Ef fects of Discharges on White Perch 167 References f'
1.
Steam-Electric Plant Air and Water Quality Control Data, Federal Energy Regulatory Commission, Washington, D.C.
DOE /FERC 0024 (1979).
[W" 3*/W '
41,w.s (p.s p
.fi J'
d 2.
R. SUGAM, C. R. GUERRA, J. L. DELMONACO, J. H. SINGLETARY AND W. A. SANDVIK, Biofouling control with ozone at the
, p...,,J Bergen Generating Station, Report CS-1629, Electric Power T
- Q ?' %
Research Institute, Salo Alto, CA ( 1980 ).
.... ; ; ; ; 3 ?/.3,i y
C. E. BALOG, Comparative evaluation of effects of ozonated
',h 3.
C. R. GUERRA, R. SUGAM, J. W. MELDRIM, E.
R. HOLMSTROM AND t-i and chlorinated thermal discharges on estuarine and fresh-water organisms, Final Report under U.S. Department of
{
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Energy Contract No. DE-ACO2-77EV04384, Washington, D.C.
(1980).
h,. M. g.;/.e ?
e
'ra. f.' 3 OJ.
4.
R. A. DRUMMCND AND R. W. CARLSON, Procedures for measuring t.
cough (gill purge) rates of fish, U.S. Environmental Pro-
%.,,.c.,,/ '
tection Agency, EPA-600/3-77-133, Washington, D.C. (1977).
^ ^F.}l g.g
//khh
~
5.
J. W. MELDRIM, J. J. GIFT AND B. R. PETROSKY, The effect of F-
.f;I',Yb-Y,Nk[x 1
2r - i f-N temperature and chemical pollutants on the behavior of
,,...f ssveral estuarine organisms, Final Report to the Office of j
-d
'I
?
- y v.Jg; Water Research and Technology, U.S. Department of the M
A[v.. hh Interior, NTIS Report PB-239347, Washington, D.C. (1974).
.s
- W....'
6.
W. A. SPOOR, T. W. NEIHEISEL AND R. A. DRUMMOND, An electrode W '2.
k'rj/
5 Yi gT.,
.y#;s?
chamber for recording respiratory and other movements of
.yd'f;W J.
ff;t JIJ.'.9 free-swimming animals, Transactions of the American Fisheries b. ':.';g.
t J. Q
,g..,J -
j{,' g,jy; Society.
100, 22-28 (1971).
,y dit M.h{
.o.
- 4.
Standard Methods for the Examination of Water and Wastewater, KhN't)6 7.
14th ed., American Public Health Association, Washington, w ;.fidi~qigp'i3-F 7."$.8Mh-y p,h N
D. C. (1975).
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R. SUGAM, W.
SWALLOW AND J. TROUT, Field evaluation of
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R. SUGAM, J. H. SINGLETARY, W. A. SANDVIK AND C. R. GUERRA,
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Condenser biofouling control with ozone, Ozone Science and 1*
l _ ; 's.,,'; i.
Engineering.
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- J. Melodim et al.
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Die biologische Wirkun. von ozoniertem und chloriniertem Kahlwasser in salzhaltigem und frischem Wasser wurde bestimmt. In Wassern mit 0 5-2 3 g/kg Salzgehalt ist Czon in frischem Wassern Chlor weniger schadlich.Unterschieden in den Oxydationnebenproduk-ten die Ozon und Chler in diesen Wassern ergeben bestimmen wahr-
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An Experimental Study of the Behavior of Estuarine Fishes to a 5
Proposed Thermal Effluent
- John W. Meldrim g
Ichthyological Associates
,,3 Middletown, Delaware 18 November 1970 In recent years there has been considerable concern expressed about the 1
offects of industrial effluents '(including thermal plumes) on fishes.
Much of the work resulting from this concern has been the determination of median Although this approach has provided valuable information, lathal tolerances.
ID50 or Tim values for a given period of time do not provide for the import.
rub-lethal behavioral aspect of motile aquatic organisms.
cnt It is, obvious, for example, that if spawning migrations are bipcked or interrupted by sub-lethal temperatures or sub-lethal chemical concentrations, population reductions equivalent to those produced by lethal te=peratures or Perhaps, then, one concentrations may ensue over a longer period of time.
of the more important sub-lethal effects of industrial efflue'n'ts is behavioral (There is little difference in an affected area whether high temp-cvoidance.
In either case eratures or toxic effluents are lethal or produce avoidance.
~
k
.5 the species is absent).
In conjunction with an ecological study of the Delaware River in the vicinity of a proposed nuclear generating station on Artificial Island and i
as,part of a study to develop methods of sub-lethal chemical bicassay based 8
upon fish behavior, experimental studies of temperature avoidances have been i
- This research was supported by funds from.Special Project W-3C of the I am indebted to Messers. George Manufacturing Chemist's Association.
and H.E. Robbins,' Secretaries, '4ater Resources Co=mittee and to committee Robert Ealmer and E.C. Ladd for their encouragement and Best members Messers.
Victor J. Schuler and Dr. James s. Gift of Ichthyological cdvice. Mr.
Associates critically evaluated the manuscript.
f.
i f'
f carried out on the Eshes of that are a since August 1969. The Delaware in this region is estuarine. Salinities extend from 0-16 /oo, but in 1969 were usually between I. /oo and 12 /oo. Oxygen values were usually between 6.0 ppm r
and 12.0 ppm and pH was usually between 6.8 and 7.8..
.1 General Faterials and Methods While it would be desirable to study the. temperature avoidance patterns of all the species present in the Delaware River estuary, this becomes im-practical due to the amount of time required for testing. Consequently.
t.pecies are selected for study on the basis of their ecological and/or co=m-ercial importance.
Selected on the basis of their ecological importance (as deter =ined by the con-current ecological study of the Delaware River estuary) are:
the F
L blueback herring (Alosa aestivalis), and alewife (Alosa pseudoharengus), the bay anchovy (Anchoa mitchilli), the mummichog (Fundulus heteroclitus), the Atlantic silverside (Menidia menidia), the tidewater s'ilverside (M'enidia hervilina), and the hogchoker (Trinectes maculatus).
I Although both young and adults of the above fishes are studied, emphasis is placed on the young of those species considered to be of commercial import-These latter species,, although not a distinct category from the ecolog-ance.
ical group, include:
the American shad (Alosa sapidissima), the Atlantic menhaden (Brevoortia tyrannus), the white perch (Morone americana), the striped bass (Morone saxatilis), the bluefish (Pematomus saltatrix), and the weakfish (Cynoscion regalis). The study of a given species is on an annual basis, or for the length of time the species is present in the estuary.
w E
N L. __.
v
- 4.,
. Due to their delicacy, all fish are taken by seine (usually from Augustine Beach located 3 Siles south of the Chesapeake & Delaware Canal).
They are then transported to the laboratory (a distance of approxi=ately 4 miles) in a styrofoam cooler.
Upon arrival, they.are ic=lediately placed in the laboratory holding facil' ties which consist of three 32-gallon plastic i
r, garbage pails imersed in a water bath.
These pails are aerated, filtered, p.
and contain water of differing salinities. All fish are usually held 18-24 h
hours prior to testing and are not fed prior to nor during experimentation.
J 7
The water bath is maintained at the field collection temperature by i~
two (Is hp) salt-water refrigeration units and is surrounded by a canopy of 1i black polyethylene sheeting to provide light control.
Light levels are main-taf,ned for the appropriate photoperiod at 40 foot-candles at the surface of the water using two Duro-Test 40-watt " Vita-Lite" flourescent bulbs (which have the spectral energy distribution of sunlight at 5500 K).
The experiments are conducted using water from a nearby tributary of the Delaware River - Appoquinimink Creek. Water is taken at high tide to approxi-mate Delaware River quali~ty'at high tide.
La i
Avoidance Studies Two avoidance designs have been found to be successful to date. Both designs are conducted in a trough six-feet long, two-feet wide and one-foot deep, which has been divided into six-foot by one-foot sub-troughs. The entire trough is painted with a non-toxic light gray aquarium paint.
(The unmodified trough employed in the first avoidance design is illustrated in Figure 1).
Two all stainless steel. Forma-Scientific 20-gallon capacity temperature
!p controlled circulating baths serve as reservoirs. Connections to the troughs L
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4 5-C are through innert %-inch "Tygon" tubing, and are such that the sub-troughs can be filled with water from either circulating bath, both separately or jointly.
~
The trough apparctus is enclosed in a canopy surrounded by black polyethy-lene sheeting to provide light control and permit movement around the apparatus.
Lighting is provided by four " Vita-Lites" and is indirect so that illumination is equal over the trough'and no shadows occur.
i Avoidance Design: Moving Gradient The first avoidance design found to be successful (Figure 2) is essentially
.a 1
a modification of a design used by Moss (1970).
(The initial design per=it-y-
3~
ting fish exchange between sub-troughs proved to be too ec= plicated for most species' tested. The " break" was thus screened to prevent cross-over). Tests J_
are performed using the following procedure: Equal numbers of fish are placed l5. -
on each side of the divided trough described above. Initially, water of the
,1,
acclimation temperature ("T") flows down both sides and is recirculated via F
the te=perature controlled circulating baths. Af ter suitable orientation time, water of increased (or decreased) temperature ("T+") is introduced in one side of the trough to produce a moving thermal gradient on that side.
(The other side of the trough continues to carry water of the initial temp-erature and serves as a control). When the gradient reaches the screened A
This results in a slight change
" break" in the partition, mixing occurs.
in "T" and "T+" (usually 1 F degree). These temperatures are then exchanged in the sub-troughs to produce a " replicate" test.
The avoidance respons'e to the gradient may be no response at all, subtle (in which case the fish increase their a'ctivity in the species specific C
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1 T+ CIRCULATION SYSTEM
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" search pattern") or " ultimate" (in which case the fish =ove ahead of the
.I gradient as it moves down the trough). Wile subtle responses are cataloged,
~
the tests are concluded when the " ultimate" response is given.
If ultimate avoidance is not shown, the acclimation temperature, "T", is then changed er in the direction of "T+" (but to a slightly less extreme temperature) and "T+" is changed (usually 5 F degrees) beyond its former point.
(Consequently,
~
the control proceeds through a series of step-gradient changes which lag behind the series introduced experimentally.)
In order for this design to work a E
.E species must orient to a low velocity current. It was found, however, that many of the :pecies in the Delaware would not orient sufficiently to permit use of this design. When the following design change was built into this teough, the " break" was eliminated, producing two separate troughs.
Avoidance Design: Modified Shelford-Allee Design This design (Figure 3) is a modification of the design employed first by Shelford and Allee (1913) in a study of reactions of fishes to concentrations
.of atmospheric gases and then by J.R.E. ~ones, et. al. (1956), Whitmore, et.
.. a l. (1960), Hill (1968), Sprague.(1964, 1968), and Sprague,.et. al. (1965, and 1969).
In this design, the Forma Scientific temperature controlled circu-lating baths again serve as storage reservoirs. Water fro = the respective baths flows (via gravity-flow) into each end of the sub-troughs and drains from their centers, where it is recirculated to the te=perature baths. Dye tests show a sharp boundary at the center drain. The apparatus is thus ef fectively divided into quadrants.
Equal numbers of fish are placed into each quadrant. Two of the quadrants (on opposite ends of the respective sub-troughs) contain water of the acclima-tion temperature ("T"), while the remaining two contain water of increased 1
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(or decreased) te=perature ("T+").
After a five minute orientation period, the amount of time spent by each fish in each quadrant is measured for a period of ten minutes (which constitutes a trial). The number of occurrences of fish in each quadrant is then multiplied by the amount of time they spent in the respective quadrants to give a frequency distribution for each quadrant.
~
is then performed to determine if a significant" difference (P.05)
A t-test (and thus avoidance) exists between the distributions.
If no significant difference exists, the respective temperatures are then. increased in the step-gradient fashion employed in the moving gradient design.
Because an avoidance response to "T+" may result from the action of factors other than temperature, those most probable (such.as oxygen and pH) '
are' monitored at the input and outflow of each sub-trough throughout a test.
(This is done to assure the validity of the test).
Oxygen is monitored in per cant saturation (since the ppm value is temperature dependent) using temperature compensated YSI oxygen analyzer The themal con-probes. pH is monitored using a multi-channel Orion pH meter.
ditions in the trough am monitored by a Leeds and Northrup 24 channel tempera-ture recorder (connected to themocouples at 6-inch Etervals along each sub-Because the trough is enclosed, observation is made via closed trough).
i Each test is recorded on videotape and re-analyzed using circuit television.
the temperature recorder output as a check on original observations.
Because this area of the Delaware is estuarine and has uneven light pene-l.{
tration due to " patchiness" of turbidity, reactions to similar temperature con-l.
ditions are tested under different conditions of light and salinity. Thus, reactions to similar changes in temperature are usually tested at three different light levels at the salinity at which the fish were collected and again (at
the different light levels) at salinities above and below the collection salinity.
Results and Discussion Of the species selected for study, avoidance tests have been performed
~
on all except Alosa sacidissima.
In' addition, two invertebrates, the grass shri:np (palaemonetes'vultaris), and the blue crab (callinectes sapidus) were tested. While the moving gradient design was found to be inappropriate for f,. heteroclitus, M. americana, and T. maculatus (since' these species apparently
'1 do not orient to low current velocities), all species mentioned (except A.
sapidissima) have been successfully tested.in the modified Shelford-Allee design.
s-The effects of light and salinity on the upper temperature avoidances of two ecologically i=portant species, the Atlantic silverside (M. menidia),
a 9
and the striped bass, @. saxatilis), are summarized as illustrative of the varying responses. Generally, an inverse relation between light level and avoidance temperature and salinity and avoidance temperature was found for the silverside (Figure 4). As light level'and/or salinity decreased,
}
the upper avoidance temperature increased. However, acclimation temperature h
and innate rhythms (particularly in opring and fall) also determined the upper I:
I avoidance temperature. The reversed salinity effect for Menidia menidia in l
December was likely due to a change in salinity preference. This is now
=
-under study. Light levels apparently also had similar. effects on the avoidance t
temperatures of Brevoortia tvrannus, Alosa aestivalis, Alosa pseudohareneus, L.
Fundulus heteroclitus, and Menidia bervilina.
Althoughtherewasnglighteffec'tontheavoidancete=peraturesof L
lI Morone saxatilis, (Table 1) there was an inverse relationship between salinity b
~
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LIGHT LEVEL (FOOT CANDLES)
P THE RELATIONSHIP OF LIGHT LEVEL, SALINITY' TIME OF TESTING, AND UPPER ULTIMATE AVOIDANCE
)
TEMPERATURE OF THE ATLANTIC SILVERSIDE, Menidia menidia h
g PWW. ACCUM.t.T@ TEMPERATURE
-"*"e
I and upper avoidance tempefature. This was also apparently true for the. white perch (M_. americana). However, in both these species acclimation' temperature vas (as expected) the primary factor determining avoidance temperature. Tests
~
on the effects of light and salinity are not yet conclusive for the other species. This is under current i vestigation.
~
Table 1. -- The effects of light. level and salinity on the upper avoidance
[
temperature of the striped bass, Morone saxatilis (32=m-60=m total length).
Date Salinity Light-level Initial Upper j
(ppt)
(ft. candles) acclimation avoidance temperature temperature (OF)
( F) o l-a 21 Oct.
I 1969 6
20 64 84 k
5 Nov.
1969 6
10 56 80 5 Nov.
1969 6
5 56 80 24 June
.5 1970 4
20 70 89 1 July L
1970 1
20 70 91 3 July 1970 1
2 70 91 I.
Because the modified Shelford-Allee design is simple, yet reliable, it a
is felt that this design would be suitable for an "in-plant" rapid information bioassay technique. The suitability of this design for use with various organic chemicals is now under study.
~4
r-
~~
r e-,-
Litersture Cited Hill, L.G. 1968.- Oxygen preference in the spring cavefish, Cholocaster agassizi. Transactions of the American Fisheries Society, 97(4):
,14 448-454.
Jones, J.R.E. 1952. The reactions of fish to water of 16w oxygen concentration.
Journal of Experimental Biology, 29: 403-415.
~
Moss, S.A. 1970. The responses of young american shad to, rapid temperature changes. Transactions of the American Fisheries Society, 99(2):
381-384.
Shelford, V.E. and W.C. Allee. 1913. The reactions of fishes to gradients of dissolved atmospheric gases. Journal of Experimental Zoology, 14: 207-266.
Sprague, J.B. 1964 Avoidance of copper-zine solutions by young salmon in l.
the laboratory.
Journal of Water Pollution Control Federation, 36(8): 990-1104
, 1968. Avoidance reactions of rainbow trout to zine su-1phate solutions.
Water Research, 2: 367-372.
Sprague, J.E., P.F. Elson, and R.L. Saunder.1965.
Sub-lethal copper-zine pollution in a salmon river - a field and laboratory study.
International r
Journal of Air and Water Pollution, 9: 531-543.
Sprague, J.B. and D.E. Drury.1969. Avoidance reactions of salmonid fish to representative pollutants. Advances in Water Pollution Research, h
Proc. 4th Int. Conf., Prague, 1969. Pergamon Press, New York.
(
Whitmore, C.M., C.E. Warren, and P. Doudoroff.
1960. Avoidance reactions of b
salmonid'and centrarchid fishes to low oxygen concentrations. Trans.
- )
Amer. Fish. Soc., 89(1):
17-26.
ai!
- J
/.,
l.
, I l
t l
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Reprinted from Underwater Naturalist, Eclietin of,t'he Americar. Littoral Society; Vol. 13, No. 2; Spring 1981.
NOTES ON ATLANTIC AND SHORTNOSE STURGEONS by HAROLD,M. BRUNDAGE Ill The sturgeons. Acipenseridae,are an is short. blunt, and rounded wherens ancient family of fish dating back some that of the Atlantic sturgeon is con-70 mi!! ion years. Of the 23 species siderably more clongate. slightly up-distributed throughout the northern turned, and flat on the bottom. Snout hemisphere two, the Atlantic sturgeon, appearance must be used with caution.
Aciperuer oxyrhynchus and the short-however, with specimens between about nose sturgeon. Aciperuar brevirostrum.
3.5 4 feet in length. In this size range are found along the Atlantic coast of the snoutlength of the Atlantic sturgeon the United States and the Atlantic relative to head length begins to de-Provinces of Canada.
crease, as sexual maturity is reached.
All sturgeons are characterized by and the snout may actually appear blunt fusiform, nearly cyclindrical bodiest in older specimens.
elongated snouts which extend over The mouth of the shonnose sturgeon small, protrusable toothless mouthst is broad,its width nearly 75% of the dis-and essentially cartilagineous skeletons.
tance between the eyes. The Atlantic Their scales have degenerated to form sturgeon's mouth is narrower typica!!y five longitudinal rows of heavy bony less than 50% of the distance between scutes or shields which are pronounced the eyes.
in young individuals but become blunter The appearance and arrangement of and less defined with age. Allsturgeons the bony scutes provide the best charac-have four fleshy barbels set close in teristics for field identification. In short-front of the mouth.
nose sturgeon the seules anterior to the Atlantic and shortnose sturgeon can anal fin are arranged in a single row and be differentiated easily in the field using there are no scutes behind the dorsal the follo. wing guidelines. It may be fin. In the Atlantic sturgeon the preanal l
possible to differentiate the two species scutes are arranged in a double row and
[
simply on the basis of size. The maxi-postdorsal scutes are paired. Further, j
mum length of the shorinose sturgeon in adult shortnose sturgeon the scutes I
is about 4 feet w hereas Atlantic sturgeon along the back are not closely set and commonly attain a length of 12 feet and are rather weakly developed compared may grow to 18 feet. Sturgeon larger to Atlantic sturgeon. In young short-than 4 feel are almost definitely Atlantie nose the scutes are more strongly de-sturgeon although the other distinguish-veloped but are still weak relative to f,,
ing characteristics should be checked Atlantic sturgeon of the same size. In on all specimens.
young Atlanticsturgeon the scutes may l
The snout of the shortnose sturgeon even feature pronounced books. In very old Atlantic sturgeon, however, the Brundage u.a research biologbt for lehrhy.
scutes nte less defined and eventually olopocal Anocates in she Middletown. Del-
- P3 T3 -
aware office. The illussrations are from The Atlantic sturgeon ranges from
~Fuhes of the Western North Atlantic."
Sears foundation for Marine Research.
Labrador to eastern Florida and a l
13 l
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FIELD GUIDE FOR DIFFERENTIATING SHORTNOSE ATLANTIC STURGEON Acipenser oxyrhynchus Mitchill I
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C 3.u 4 ner..t ri - p.ir.4 southern subspecies A.o. desoroi, oc-in the Hudson River, and age 22-24 in curs throughout the Gulf of Mexico, the St. Lawrence River, Canada. Fe-along the northern coast of South mal,:s mature at age 8-12 in Florida, a America, and possibly in Bermuda.
minimum of age 18 in the Hudson, and Adult Atlantic sturgeon are anadro-age 27-28 in the St. Lawrence River.
mous, spending most of their life in Further, spawning does not occur coastal waters or the high salinity annually, and some mature females may l
reF ons of large estuaries, but move in rest fopr to seven years between i
spring into brackish waters, near the spawning.
salt front, to spawn. Juveniles generally During the mid to late nineteenth remain in their natal estuary until they century the Atlantic sturgeon was the are 5 to 12 years old but undertake srbject of a considerable fishery, par-regular seaspnal movements within the ticularly in the Hudson and Delaware estuary. They typically overwinter in rivers.They were sought for their flesh, deeper, higher salinity, waters of the which was smoked, and more import-lower estuary, move upstream in spring antly, for their eggs which were prepared into brackish waters where they forage as caviar. The history of the Atlantic through the summer, and in fall return sturgeon fishery was one of great early to the lower estuary or possibly venture abundance followed soon after by de-into nearshore ocean waters.
cline and, eventually, virtual collapse.
Atlantic sturgeon eat polychaete Consider the Delaware River fishery.
worms, marine molluscs. shrimps, am-In 1890 over 5 million pounds, valued phipods, and isopods while in high at between 5100.000 and 5200.000 (1890 salinity waters or at sea, and aquatic dollars) were reported taken. Seven insect larvae and oligochaete worms years later, landings were less than 2.5 when in brackish or fresh waters.
million pounds, and by 1905 landings Atlantic sturgeon mature very slowly:
had declined to negligible levels. Over-age at maturity is greatest at northern fishing of adults on the spawning latitudes. Males mature at age 7-9 grounds combined with late maturity (years)in Florida, a minimum of age 12 are cited as the principal factors re-14
AND YOUNG ATLANTIC STURGEON nem 2.
SHORTNOSE STURGEON Acipenser brevirostrum Lesueur
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Maximum Length ' f t.
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O Along 3.ek - plates separated by sp.ca h Sefore Anal no - single tw CY C s.hina rar 1 nn - typte.117 ab. e sponsible for this precipitous decline, spring from overwintering areas in the although water pollution and habitat lower estuary to spawn near the limit of destruction undoubtedly contributed.
tidal intrusion. Adults typically move The present status.of the Atlantic downstream after spawning to a brackish sturgeon is not entirely known, although foraging area where they remain for studies by William L Dovel indicate a the summer. Juveniles generally remain substantial population in the Hudson in tidal freshwater throughout the year River Estuary and other evidence sug-until they are about 45 cm in length.
gests considerable numbers in the Saint Older juveniles and adults between John River Estuary. New Brunswick.
spawning periods, however, generally Canada: the Kennebec River Maine:
remain in the lower estuary during spring the Delaware River estuary: along the and summer. In fall most adults and coasts of North and South Carolina; some juveniles move back to the over-and in Florida.
wintering areas in the lower estuary The shortnose sturgeon ranges from although some ripening adults may New Brunswick. Canada, to Indian migrate upriver and overwinter near River, Florida. It is protected as an en-the spawning area.
dangered species in the United States Juvenile shortnose sturgeon eat ben-and is classified as rare and possibly thic crustaceans and insects. Adults endangered in Canada.
prefer molluscs but also eat benthic In the northern portion of its range crustaceans and insects, and occasion-the shortnose sturgeon principally in-ally, small flounder.
habits large estuaries and occasionally Shortnose sturgeon mature somewhat nearshore ocean waters. Southern popu-earlier than do Atlantic sturgeon al-lations however, spend most of theyear though maturation is still quite slow in the lower few miles of the estuary or and va(ies directly with latitude. Males in coastal water, occurring upstream mature at age 2 in Georgia and age 10-only during spawning in February and 11 in the Saint John River. Canada:
March.
females at age 6 in Georgia and age 12 in northern estuaries adults move in in Canada. First spawning. however. may 15 e
be delayed I to 2 years after maturity in thought. The Saint John River. Canada:
males and up to 5 years in females.
Montsweag Bay and the Kennebec Moreover, after spawning is initiated.
River. Maine: the upper Connecticut females apparently spawn a maximum River. Massachusetts: the Hudson River, of once every three years, and resting New York: the Altamaha River. Geor-periods of 5 to 11 years are suggested gia: and the Delaware River Estuary by absence of spawning checks in the are now thought to support substantial annual growth rings seen in cross-shortnose sturgeon populations.
sections of the pectoral fin ray.
Public awareness of the biology, Although the shortnose sturgeon was identification, and perhaps tenuous never the subject of a large commercial status of the Atlantic and shortnose fishery, substantial numbers were re-sturgeon is essential to their manage-ported sold at the Philadelphia market ment and recovery. Sturgeon are oc-during the late 1800's. LeSueur, who casionally taken by anglers (and some-providd the original taxonomic descrip-times recorded in the tagging reports tion of the species, reported in 1818 section of this journal) and quite fre-that the shortnose sturgeon was more quently by commercial gillnetters and sought after and commanded a higher coastal draggers. By virtue of its en-price than the Atlantic sturgeon. Its dangered status, it is against federal and small adult size and small quantity of in most cases state law, to take or possess caviar relative to the Atlantie sturgeon, a shortnose sturgeon. If a shortnose however, precluded wide commercial sturgeon is taken incidentally while interest. It was nonetheless impacted fishing for other species it must be by the fishing industry in that during returned to the water, unharmed, as the late 1800's numerous " young"stur-soon as possible. It is also unlawful to Econ, r,any of which were probably possess a dead shortnose sturgeon or adult shortnose sturgeon, were killed any part thereof. If one is found. ho~w-by shad gillnetters because they became ever, a state or federal fish and game entangled in and damaged the nets. This authority should be notified so that the impact was reduced.somewhat when specimen can be salvaged and perhaps New Jersey, in 1891, and Delaware, useful information obtained from it.
several years later, enacted legislation Atlantic sturgeon should also be prohibiting the taking or killing of released. Although the species is not sturgeon less than three feet in length, considered endangered its status is The present true status of the short-uncertain and it serves no purpose to rose sturgeon is even less known than remove any from the system. Moreover, that of the' Atlantic sturgeon. Its legal most states have minimum size, season, classification as endangered however, and gear regulations and it is illegal to has prompted investigations which have take or possess Atlantic sturgeon in shown it to be more abundant in some several states, including Virginia and drainages than had been previously Mississippi.
REQUEST The author of the preceding paper. Harold M. Brundage, 111. and colleague Robert E. Meadows are compiling records FOR of incidental capture of Atlantic and shortnose sturgeon in STURGEON New Jersey, Pennsylvania. and Delaware waters. Individuals CAPTURE with capture records (including date precise location. length, INFORMATION and gear,if possible) or anecdotal accounts re;srding sturgeon in these waters, particularly the Delaware River Estuary, are requested to send them c/o Ichthyological Associates. Inc.,
100 South Cass Street, Middletown. DE 19709.
16 6
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By James A. Fava and John W. Meldrim i
r 1
l Ichthyological Associates, Inc.
l 100 South Cass Street Middletown, Delaware 19709 5 April 1977 a
G e
O
INTRODUCTION Increased use of estuarine waters by steam elec ric generatin
$.'.0 b'.*!a.l dl at 04,N d,
stations has resrited in problems independent of e-crr mra. Almost all plants use chlorine as a biocide to control fouling on intake structures and condenser systems. The environmental impact resulting from the amount of chlorine released. into the estuary from these discharges is a cause of concern.
We have been studying the effects of chlorine on the fishes and macroinvertebrates of the Delaware River estuary for several years. The studies have dealt primarily with the behavioral responses of these species to chlorin'e but also have included studies of lethal limits.
Thechemistryofchkorineinmarineandestuarinewatersiscomplex.
Chlorbe 4A reacts with the bromide ion to form a omgl,ex miptgre of oxidants.
% s2 W 5 h b P.L Since we don't know the exact ~ chemical nature it is more proper to speak of " total residual oxidants" when referring to chlorinated
- estuarine waters. However, for the purposes of this paper I will continue to refer to this mixture of oxidants as " total residual chlorine", although " chlorine" itself may not be among them.
In addition to the direct effect of chlorine itself, salinity, 3
temperature, oxygen, and light have been found to interact with chlorine to produce stressful conditions for several estuarine fishes.
This MI)i paper describes our studies with the Atlantic silverside, Menidia i
3 ls t menidia, a fish common to most mid-Atlantic estuaries.
MATERIALS AND METHODS Tne effects of chlorine on the Atlantic silverside have been under
'study at our lab sines. 1973. Fish used in testing were taken by seine
d 2-sble from the Delaware River and upper Chesapeake Bay drainages. Atlantic t
silverside were collected at temperatures from 6 C to 28 C and salinities from 2 to 7 ppt. They were transported to the laboratory in aerated coolers and were maintained at least 24 hours2.777778e-4 days <br />0.00667 hours <br />3.968254e-5 weeks <br />9.132e-6 months <br /> close to the temperature and salinity at which they were collectedjPMe P-fo he e,A Water for the study was taken from a tidal tributary of the Delaware River estuary and allowed to " settle" in two 1,250-gallon gl D s t4.,,_
polyethylene tanks prior to use. Since the water intake is located about 2 miles up the Appoquinimink, the salinities used in testing were low, being between 2 ppt to 7 ppt. Since Atlantic silverside are generally present in the Delaware River estuary throughout the year, testing was conducted over the annual range of ambient water temperatures.
Behavioral responses to residual chlorine were determined using the S i 3 en).e_._
modified Shelford-Allee apparatus.
Briefly, in this system water was taken at high tide from Appoquinimink' Creek and pumped into the polyethylene-storage tanks to settle.- It then flowed via gravity flow into a temperature controlled water bath. Water was conditioned to the r
acclimation temperature and Ehe desibed oxygen level (by e&n ww.
v yya --
stripping with nitra ;e-when reduced oxygen levels were desired) in the bath. The water was then pumped into a dose box which was divided into two 1-ft3 boxes. One side of the box received a chlorine dose from a-constant head reservoir (1-A-^
n:3 arca). -The dose was determined by a flowmeter. Whenever the float valve dropped, the solenoids' opened and released water from the bath and the chlorine dose into the experimental side of the dose box.
It also contained a heater which raised the
3 experimental water temperature when desired. The other side provided control conditions as it did not receive a chlorine dose, was not heated, and in the case when receiving water of reduced oxygen level, was aerated.
to regain near air saturated conditions. Water from the respective sides of the dose box then flowed into the modified Shelford-Allee apparatus which is a divided trough further divided into quadrants by center drains. Flowmeters monitored the raIte of flow into the apparatus and was generally about 3 liters / min through the system.
Thi: ;;nc: ally
?-r21ted in prad:minantly f;c-mLlwu us um=1Jm 1.. -IIewover, in same the-does i,o... law & mased--to-produce w.
+k.
mn eo, - H m=
4n p: 0 '
r-r'; ::stincd chleciae.
. Briefly, the general experimental procedure was (1) establish the conditions in the troughs such that water in diagonally opposite quadrants (formed by the center drains) had the same temperature and oxygen conditions and chemical composition, (2) place equal numbers of fish into each quadrant, (3) after a 45-min orientation time, determine the amount of time during a 10-min test period the fish spent in one of the two respective quadrants per trough, and (4) analyze the fish-time distribution by t-test to determine.,1f a :significant response had taken place.
If no significant avoidance. response occurred, the concentration of chlorine was increased.
Responses to residual chlorine were tested under the following conditions:
(1) near saturation oxygen levels and ambient temperatures v
in all quadrants, (2) near saturation oxygen levels in all quadrants with ambient temperatures in the control quadrants (which contained no chlorine) and ambient temperatures plus approximately 2-3 C in the e
1
. experimental quadrants (which contained a chlorine dose), (3) near saturation oxygen levels in the control quadrants and levels approximately 3 ppm below saturation (which is about 70-80% saturation) in the experimental quadrants with ambient temperatures in all quadrants, and (4) near saturation oxygen levels with ambient temperatures in the control quadrants and oxygen levels approximately 3 ppm below saturation with ambient temperatures plus approximately 2-3 C in the experimental quadrants.
These conditions were tested at both high-1,076 lux (100 f-c) and low-430 lux (40 f-c) light levels.
Ambient temperatures refer to ambient collection temperatures and were the temperatures at which the fish were held prior to testing.
Tests were conducted throughout the year at seasonally apprcpriate ambient temperatures. Oxygen levels and temperatures were monitored in each quadrant using YSI Model 5450 temperature compensated oxygen' probes, a RACO automatic multi-channel oxygen (and temperature) probe scanner, and a YSI Model 54 oxygen meter.
Chlorine (oxidant) levels were monitored with a Fischer and Porter Model 1010T amperometric titrator.
Table of Parameters
- Slidef_,
The mean, minimum, and maximum values of the water quality and the parameters used in the evaluation of chlorinc on Atlantic silverside are shown in this slide. Temperatures ranged from 5 C to 28 C.
Salinity ranged from 2.0 ppt to 7.0 ppt.
The dissolved oxygen concentration ranged from 57 to 100% saturation.
In the saturated DO tests, the DO level was always greater than 90% saturation, while in the reduced D0 tests, the DO level was generally 60-70% saturation. Two light levels
> + -
.,,,-.,,e,
-,-c.~,-.
sn-
+,
-5 were tested (470 lux and 1,076 lux).
The mean total fish length was 69 an, with a minimum length of 27 m, and a maximum length of 104 mm.
The mean chlorine demand of the Appoquinimink Creek water used was 0.61 mg/l and the mean ammonia concentration was 0.11 mg/1.
The data were subjected to a preliminary multiple regression i
/
analysis using nost of these parageter,s,/and th ir (nteqactions as%c Edq.ld 67ft
.tO_ cat %dacc_ dul i:R !v(,f l
M independent variables. gTemperature, salinity, and level of dissolved CtA oxygen "ere thedominant variables,found to influence the-avoidance Ii4 o
ooncentratiour Categorizingthedataaccordingtolow(lessthan3.5) or high (greater than 3.5 salinity and saturated or reduced dissolved oxygen, the respective mean avoidance concentrations were plotted against temperature.
In this slide the solid lines represent tests conducted under near saturated levels of dissolved oxygen and the dashed lines tests under reduced levels of DO.
The numbers on the lines indicate the number of tests used to calculate the mean avoidance concentration point. Generally there was an inverse relation between temperature and the avoidance concentration.
~
.is temperature increased up to about 15 C the concentration eliciting an avoidance response decreased. Above 15 C the effect of temperature
. shifted to a direct effect at higher salinities and reduced DO's.
Salinity also had an inverse effect on the avoidance concentration.
Reducing the level of DO was found to reduce the avoidance concentration.
!" i 1 Since the plots of these results are somewhat sigmoid and the Q l s c _6_
independent variables had large variances, the independent variables were transformed by log transformation and the multiple regression
~
4
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. analysis was repeated. The results of this cnalysis are shown in this slide. The R2 value (.38) is not very large here but the standardized regression coefficients show the effect of salinity and temperature to be about equally i=portant.
The level of dissolved oxygen is by contrast, 3
only about half as i=portant in determining the avoidance concentration.
Using the equation generated by the multiple regression analysis, the avoidance concentrations were plotted against their respective temperatures for saturated DO, reduced DO, and salinities of 3 and 6 ppt.
311d7 Estimat d lin;s The lines were found to correspond fairly well with the actual data.
Cenerally, the fish were more sensitive to chlorine as the temperature and salinity increased End percent oxygen saturation decreased.
A discharge from a power plant contains not only chlorine but usually has water te=peratures which are slightly elevated above the surround'ing water. To help in the evaluation of the discharge on, fish, 311d2 4L T a series of tests was initiated to study the effect of a slight temperature increase (2-3 C) in association with chlorine on the avoidance concentration. Tests were conducted at 6-8 C, 15 C, 21 C, and 27 C at salinities greater than 3.5 ppt. Atlantic silverside were exposed to two test conditions, one with a AT presented in association
$ t. b tt-with chlorine, and-ews with no AT presented in association with chlorine.
The results of this prelbainary study are shown in this figure.
The cuqai s.tf avoidance concentrations are plotted.on-temperature.
The solid line indicates the avoidance concentrations at the tested temperatures when a 6T was tested while the broken line indicates tests conducted without a AT.
As you can see, at temperatures of 21 C and higher, the AT in association with chlorine does not seem to affect the avoidance concentrations.
' However, at temperatures of 15 C and lower, the increased temperature causes an increase in the avoidance concentration over tests without the odle.w increased te=perature. At the lower temperatures, the preference 3g AT behaviar of the Atlantic silverside $6Pthe incre :ed t pcreture appears to partially override the effect of chlorine.
TOLERANCE Materials The tolerance of Atlantic silve'rside to chlorinc was determined at
~14da various temperatures. Tests were conducted under a light level of 215 lux,
.1B Diluter saturated dissolved oxygen concentrations, and salinities of 3.0 ppt to 5.0 ppt.
The apparatus shown here was used in these studies.
This is a diluter system developed by Don Mount and Bill Brungs and has almost become a standard piece of apparatus for bioassay studies.
This system delivers to the test tanks five different chlorine concentrations and one control. The concentrations are adjusted so that an LC50 value can be determined. A total of eight series of experiments was tested resulting in approximately 40 individual tests.
i Tests were conducted at mean temperatures of 10 C and 22 C.
LC50 L__i d a -
values were determined for 24, 48, and 96 hours0.00111 days <br />0.0267 hours <br />1.587302e-4 weeks <br />3.6528e-5 months <br />.
LC50 values were 1
pig. LC50 difficult to determine since generally the fish showed an all or none response.
That is, usually all the fish died or none of the fish died.
So in the determinati11.ef a LC50, generally a line was drawn between the maximum concentration resulting in zero or very little mortality and the minimum concentration resulting in 100% mortality. This may be the best way to estimate LC50 with chlorine. Other researchers have had Ie
similar problems with LC50 determinations of chlorine. At 10 C, the minimum total chlorine concentration causing 107. or less mortality is 0.04 mg/1, and at 22 C, the concentration is 0.08 mg/1. The maximum concentration causing 1007. mortality was 0.21 mg/l at 10 C and 0.29 mg/l at 22 C.
As temperature increased, the LC50 values increased. A t-test showed that the LC50 values for 48 and 96 hours0.00111 days <br />0.0267 hours <br />1.587302e-4 weeks <br />3.6528e-5 months <br /> were not significantly different.
In these tests, then, 'if fish mortality is going to result from exposure to chlorine it would occur within 48 hours5.555556e-4 days <br />0.0133 hours <br />7.936508e-5 weeks <br />1.8264e-5 months <br />.
Due to the difficulty in estimating LC50 values, the time to 507.
mortality was determined. Of the 40 test concentrations, 25 tests
= Slide -
resulted in 507. or more mortality. The effect of free chlorine, MST combined chlorine, total chlorine, and temperature on the median survival time was analyzed with a multiple linear regression analysis.
The; results showed that only total chlorine was important in the evaluation of the median survival time. The log-log relationship of the median survival time and total chlorine concentration is shown in this slide.
Finally, to place the behavioral and toxicity data in perspective, g q c
the both are shown on this slide.
Effects of chlorine conce grations i
d assunEVafYewc.,
are shown as a function of time. The circles represent LC50 values and 3
i' the triangles, avoidance concentrations. These data encompass all BD ambient temperature, salinity,3and light conditions,h : au fu W " P ad L. is ;f "^ ::1. The dashed line encloses the LC50 data.
7 Following the method of Mattice and Zittel (1976) the acute toxicity threshhold (that is, 07. mortality) was calculated. This threshhold is shown by the solid 1/ne.
7.'.'.::.2 ?"
For example, if a discharge is 0.1 mg/l total chlorine for 30 minutes (show line on slide), then the fish should survive.
The range of the avoidance concentrations are plotted at 30 minutes since this is the time between tests in the avoidance procedure. The minimum total chlorine concentration avoided was 0.02 mg/l while the maximum was 0.64 mg/1. By using the same conditions as for the toxicity eva.luation (a 0.1 mg/l discharge for 30 minutes), then the Atlantic silverside may behaviorally avoid the discharge resulting in some loss of habitat. The exact arer, of habitat lost would depend on the salinity and temperature of the discharge.
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STIRRER N
u INPUT CHEWCA1.
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SOL NOIDS V
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WATER INPUT L_..I REGl* LATED NITK0 GEN
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WATER /
s WA TER INPUT AREAS INPUT APIAS s
EXPERIMENTAL TANK f qare 2. - Schecatic dia;r+ 'of th mad,ified SheiferJ,111..' a;,nratus rd sy st.:: u:cd for chaicil studic:.
E portion of tas.!:h ct. :icil; C - portian of %d *ith rive. ? :r.
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3V PARAMETERS MEAN MIN MAX
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TEMP, (C )
17.8 5
28 S A L. (ppt) 4.6 2
7 D.O. (% S at.)
89.4
' 5 7.
100 L'IG H T ( l u x )
685 430 1076 PH 7.5 7.2 7.8 N H --N ( m g/ )
0,11 0.04 0.32 l
3 30 Sec Cl2.
0.61 0.50 0.70 DEMAND (mg/l)
T. LEN Gi-JT} (mm )
69 27
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1 Avoidance data 60 0.3 Sat.D.O.
23 c., t
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a q
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v 19
-U Sat.D.O.
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8
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3,110 = 23.161*
a = 0.237 F
N = 114 S.E. of Est. = 0.0 9 R = 0. 6 2*
b..
-1
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PARTIAL REG.
STAND. PARTIAL EFFECT COEF.
REG. COEF.
LOG TEMP (C)
- 0.274*
-0.527 s
a.
LOG 'D.O. ( % S t. t.)
0.278*
O.217 LOG SAL (ppt )
0.472*
-0,528
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Avoidance Concentration Es?ir.ictos
- 0. 4 -.
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Avoid, Conc. = 0.237 - 0.274 Log Ter.,p
,'t
+ 0.278 Log D O - 0.4 72 Lo g Sa l 4't i
- 0. 3 -
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RESPONSE AND TOLERANCE OF ATIANTIC SILVERSIDE AND WHITE PERCH TO CHLORINE By James A. Tava and John W. Meldrim Ichthyological Associates, Inc.
100 South Cass Street Middletown, Delaware 19709 Presented At National American Fisheries Society Meeting in Vancouver, British Columbia, September 14-17, 1977 1
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INTRODUCTION Many power plants utilize chlorine as a biocide to eliminate or reduce biofouling. With the increased use of estuarine waters for cooling purposes the amount of chlorine released into the receiving waters has caused concern regarding its environmental impact. However, the impact is not strictly a function of the amount of chlorine released. Estuaries are a dynamic environment, in which variables such as salinity, oxygen, and light may interact with te=perature to produce conditions which may affect this impact.
To determine the environmental impact of chemical co= pounds (such as chlorine), tolerance studies have been used for many years. However, recently studies 'have shown the importance of behavioral avoidance in the evaluation of discharges. Therefore, the objective of this study was to investigate the effects of various environmental factors on the avoidance behavior and tolerances of two fish species to chlorine.
The two species tested were the Atlantic silverside, Menidia menidia;
. nd the white perch, Morone americana.
MATERIAIS AND METHODS The effects of chlorine on fish ha ve been under study 'at our lab on Appoquinimink since 1973.
Fish used in testing were taken by seine from the Delaware River and upper Chesapeake Bay drainages. The Chesapeake Bay is located to the west and southwest of this area.
Water for the study was taken from the Appoquinimink River, a tributary of the Delaware River estuary and allowed to " settle" prior to use in two 1,200-gallon polyethylene tanks which are contained in the supported building. This water served as the source for both the avoidance and tolerance studies.
2 Behavioral responses to residual chlorine were deter =ined using a modified Shelford-Allee apparatus. Briefly, in this system water flowed via gravity from the storage ' tanks into a ta=perature controlled water bath. Water was conditioned in the bath to the acclimation te=perature and the desired DO level. When the DO level was regulated by nitrogen stripping, reduced oxygen levels were desired. The water was then pumped into dose boxes.
One box received a chlorine dose from a constant head reservoir. The dose was regulated by a flowmeter. The other box provided control conditions as it did not. receive a chlorine dose, and in the case when receiving water of reduced oxygen level, was aerated to regain near air-saturated conditions. Water from the respective sides of the dose box then flowed at approximately 3 liters /
min. into the experimental tank. This tank is two separate troughs located side by side. Each trough is divided in half by center drains.
Briefly, the general experimental procedure was (1) establish the conditions in both troughs such that water is diagonally opposite halves (formed by the center drains)' had the same oxygen exditions and > chemical composition, i.e. the~ sides marked E contained the experimental conditions
~
while the sides marked-C contained the conditions to which the fish '
were acclimated, (2) place equal numbers of fish into each half per trough, (3) after a 30-min orientation time the fish spent in one of the two respective halves per trough, during a 5-min test period, and (4) analyze the fish-time distribution by t-test to determine if a significant response had taken place.
If no significant avoidance response occurred, the concentration of chlorine was increased. The chlorine was increased in a stepwise fashion until an avoidance response occurred.
Responses to. residual chlorine were tested under the following conditions:
(1) near saturated DO levels in both troughs, and (2) near
3 saturated D0 levels in the control side of each trough and levels approximately 3 mg/l below saturation (whien is about 70-80% saturation) in the experimental side of *each trough. These conditions were tested at both high light levels - 1,076 lux (100 f-c) and lov light levels -
430 lux (40 f-c).
Since Atiantic silverside and white perch are generally present in the Delaware River estuary throughout theyear, testing was conducted over the annual range of ambinet water te=peratures and salinities.
The salinities used in testing were low, ranging from 0 to 7 ppt.
For each test, water quality was determined. Chlorine levels were measured with a Fischer and Porter a=perometric titrator.
AVOIDANCE STUDIES Results A total of 124 tests was conducted on the Atlantic silverside while a total 148 tests was conducted on the white perch under varying '
conditions. The mean, minimum, and maximum values for the indesendent variables (temperature, salinity, DO, light, pH, length, and co=bined chlorine) are shown. Also the simple correlation coefficients between these parameters and the dependent variable, the avoidance concentration, for each species are also shown. The percent combined chlorine was calculated by dividing the concentration of combined chlorine by the concentration of total chlorine.
The simple correlation coefficients indicate for the Atlantic silverside that as the te=perature, salinity, and light level increase, the avoidance concentration decreases. However, the opposite is the case with DO, pH, length, and percent combined chlorine. The direction of the ef fects are the same for white perch as for Atlantic silverside except the ef fects of light and length are reversed.
4 The data for each species were subjected to a stepuise =ultiple regression analysis using these parameters and their interactions as independent variables. The avoidance concentration was the dependent variable. Log transformations of the data were also conducted. The results for the Atlantic silverside showed that the best equation to estimate the avoidance concentration contained three parameters, log temperature, log salinity, and percent cachined chlorine (Table 2).
These parameters explained $7% of the variation in the avoidance response.
The standardized partial regression coefficients showed that percent combined chlorine was 2.8 times as important as temperature in estimating the avoidance concentration and 1.6 times as important as salinity.
Categorizing the data according to low salinity (less than or equal to 3.5 ppt) or high salinity (greater than 3.5 ppt) and mainly free chlorine (less than 407. combined chlorine) shown by the dashed lines, and mainly combined chlorine (greater than or equal to 40% combined chlorine) shown by the solid lines, the respective mean avoidance concentrations were plotted against te=perature for the Atlantic silverside (Figure 1).
The numbers indicate the number of tests used to calculate the mean avoidance concentration at that point. Generally when the chlorine c:
entration is mainly free chlorine (i.e., dashed lines) the avoidance concentration is generally much lower than when the chlorine concentration is 'nainly combined chlorine. There appears to be an inverse relationship between salinity and the avoidance concentration.
Also, when the chlorine concentration is =ainly co=hined chlorine (i.e., solid lines) there was inverse relationship between te=perature
. and the avoidance concentration.
1 Using the equation generated by the multiple regression analysis,
7-S the avoidance concentrations were plotted against their respective temperatures for combined chlorine values of 25 and 75% and salinity of 3 and 6 ppt,(Figure 2).
The solid lines indicate 757. co=bined chlorine while the dashed line indicates 25% co=bined chlorine. The lines were found to correspond fairly well with the actual data. Generally, Atlantic silverside were more sensitive to chlorine as the temperature and salinity increased and the percent combined chlorine decreased.
A similar stepwise multiple regression analyses was conducted on the white perch data. As with the Atlantic silverside, te=perature, salinity, and percent combined chlorine were found to be the parameters which provided the best equation to estimate the avoidance concentra' tion (Table 3).
These parameters explain 51% of the variation in the avoidance respons'e. Using the standardized regression coe'fficients, percent co=hined chlorine was 5.1 times as important as te=perature and 4.2 times as important as salinity in estimating the avoidance response.
Categorizing the white perch data as was done with the Atlantic silverside data, the mean avoidance concentrations were plotted against temperature (Figure 3).
The solid 1.ines indicate mainly combined chlorine and dashed lines indicate mainly free chlorine. When the c hlorine concentration is mainly free chlorine, the avoidance concentration is mainly free chlorine, the avoidance concentration is reduced. Generally, there was an ' inverse relationship between temperature, salinity, and the avoidance concentration.
Using the equation generated by the multiple regression anayises, the avoidance concentrations were plotted against their respective te=peratures for combined chlorine values of 25 and 75% and salinity of 3 and 6 ppt.
Solid lines indicate 75% combined chlorine and dashed
7 lines indicate 25% cc=bined chlorine.
There again, these lines were found to correspond fairly well with the actual data.
Generally, the white perch were more sensitive to chlorine as the temperature and salinity increase and the percent co=bined chlorine decrease.
TOLEp.ANCE Materials The tolerance of Atlantic silverside and white perch to chlorine was determined at various te=peratures and salinities.
The diluter system developed by Don Mount and Bill Brungs was used in these studies.
This system delivers to the test tanks five different chlorine concentrations and one control. A total of 12 series of experiments was conducted on the Atlantic silverside and 11 series of experiments was. conducted on the white perch.
LC50 values were dif ficult to deter =ine because the fishes showed an all or none response. That is, usually all the fish died or none of the fish died.
Therefore, median survival times were used as a measure of toxicity for both species. A total of 42 median survival times were deter =ined for the Atlantic silverside and were subjected to a stepwise multiple regression analyses. The independent variables used in this analysis, and with the white perch, were temperature, salinity, length, pH, total chlorine, and percent combined chlorine.
The best equation to estimate the median survival times for the Atlantic silverside contained the parameters total chlorine, te=perature, and salinity (Figure 5).
Th'e" solid lines indicate a salinity of 3.0 ppt while the dashed lines
. indicate a salinity of 6.0 ppt.
These three parameters explained 837.
f of the variation in the median survival time. Total chlorine is 5.5
8 times as important as temperature and 6.0 times as important as salinity in explaining the variation.
Chlorine is more toxic to Atlantic silverside at higher salinities, higher te=peratures, and of course higher concentrations.
A total of 40 median survival times were calculated for the stite perch and were subjected to a similar stepwise multiple regression analysis (Figure 6). The best equation to estimate the median survival time contained the parameters total chlorine and pH.
Temperature and salinity were not found to be significant variables.
Total chlorine and pH accounted for 657. of the variation in the median survival toe.
Total chlorine is approximately 1.5 times as i=portant as pH is estimating the median survival time.
The results indicate that chlorine is more toxic to white perch at lower pH values and higher concentrations.
DISCUSSION The relationship between environmental f' actors and chlorine concentrations which the Atlantic silverside and the stite perch avoid or tolerate has been shown. Temperature, salinity, pH, and percent combined chlorine are the most important environmental factors influencing the behavioral response and tolerance of these fish to chlorine.
The si nificance of these findings indicate that when estimating E
how these fish will behaviorally respond to or tolerate, if trapped, a chlorinated discharge, the,se factors have to be taken into account. A blanket statement that either Atlantic silverside or white perch would avoid or would survive exposure to a certain chlorine concentration wo ld not.be sufficient. Therefore, in order to evaluate the impact of chlorinated discharges, envirennental factors present at the specific site must be known.
-a
- ] - l, ' '..o TEMPERATURE PREFERENCE AND AVOIDANCE RESPONSES OF THE WHITE PERCH JOHN W. MELDRIM AND JAMES J. GIFT Ichthyological Associates Middletown, Delaware Introduction The following research was supported by Consolidated Edison of New York, New Jersey Public Service Electric and Gas, and the Manufacturing Chemists Association.
- The whf te perch, Morone americana is a common fish found in most western Atlantic coast estuaries from the Gulf of St. Lawrence to South Carolina. As a result of its relative abundance and responses to temperature this fish has been found to be a problem in the vicinity of nuclear generation stations.
- In conjunction with an ecological study of the Delaware River estuary, experimental studies on the temperature preferences and avoidances of the white perch have been conducted since,1969.
Unlike many other estuarine species the white perch has'been found'to be present in the Delaware estuary all year long. ! Because estuaries are in a continual state of change in salini,ty f
and turbidity, the objectives of this study were to determine the temperature preferences and avoidances of the white perch under varying conditions of light level and salinity, througout the year. Due to laboratory space limitations, the study has been performed on specimens less that 200 mm total le ng th.-
General Materials and Methods
- Most white perch used in the study were taken by seine from either the
. Delaware River drainage or the upper Chesapeake Bay drainage. *They were transported to the laboratory (a 60' by 12' trailer with an addition) located along Appoquinimink Creek, a tidal tributary of the Delaware, and held in the polding facilities 18-24 hours prior to testing. *These facilities consisted of three 32-gallon plastic garbage pails immersed in a water bath. Each pail was aerated and contained water of approximately 3 ppt, 6 ppt, and 9 ppt salinity respectively.
(On several occasions water of 0-1 ppt was also used.)
The water bath was maintained at the field collection temperature by a series of thermostatically controlled heaters and refrigeration units. Water in the respective 32 gallon holding pails was pumped through protein skimmers and tron filtered through 10 micron polypropylene filter bags before return to the pails. The protein skinners removed nitrogenous wastes from the water and permitted maintenance of natural pH levels in the holding waters. Passage through the filtet-removed any particulate matter from the water. Light levels were maintained for the appropriate photoperiod at_60 foot-candles at the surface of the water using Duro Test "Vith-Lite" fluorscent bulbs (which have a spectral energy distribution comparable to natural daylight). The fish were not fed either prior to or during testing. As.a general procedure, all_ avoidance tests were conducted in the af ternoon (thus allowing for any activity effects due to circadian rhythms). Most temperature preference tests i
were'also conducted in the afternoon with the exception of days when multiple testing was conducted. During these days, temperature preference tests were run in the late morning followed by af ternoon avoidance tests.
Water used in all tests was taken from Appoquinimink Creek (a tributary of the Delaware) at high tide to approximate the quality of the Delaware at high tide. Due to its great turbidity, it was allowed to " settle" prior to
. use. Nearly saturated levels of dissolved oxygen and pH of 7.0-8.0 were maintained throughout testing.
Temperature Preference Studies
- The apparatus used for the preference study consisted of a trough 13 l
feet in length, 6 inches wide, and 1 foot deep, having a 24-gauge (Type 304).
4
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stainless steel bottom in the center 12 feet. Cold water was introduced at one end of the trough from a temperature controlled circulating bath. As the water flowed down the trough it was heated by three banks of infra-red 1
bulbs beneath the stainless steel bottom to form a stationary horizontal thermal gradient. Eagh_b_ank consisted of four 250 watt bulbs connected to
,,7 a dimmer switch and a temperature regulator.
(Thus, the intensity of each bank could be varied as well as the length of time the bank w'as on). Upon
~
reaching the other end of the trough, the water was returned to the circulat-
.ing bath. Lighting was provided by thre'e " Vita-Lites" which extended the length of the trough.
- Initially the trough was filled to a depth of 2 inches with water of the acclimation temperature. Three to five fish were then placed in the trough without the gradient having been established.
(This provided a control for position effects.) Observations were made via overhead mirrors every 5 minutes for a 45 minute period. These controls demonstrated that the water velocity of less than 1 fpm flowing down the trough had no perceptible effect on the fish distribution. Upon completion of this control the fish were removed and a thermal gradient extending approximately 40 pf degrees above and below the acclimation temperature was established in the trough. The fish were then re-introduced at the place in the trough having their acclimation g
temperature, that is their field collection temperature. Observations were
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. again umde at 5 minute intervals.' The_ temperature __at the position of each fish was then recorded using one of 23 thermistors (placed at 6 inch intervals along the trough) which were connected to a temperature readout. The test was concluded when the same temperature was selected continuously for 20 minutes.
Results - Temperature Preference Since 1969, 45 preference tests have been performed on whiite perch.
- The restits are illustrated in the next slide showing the regression relationship of preferred temperature and acclimation temperature. Two regression equations were calculated. One for falling field temperatures and the other for 1daing field temperatures. The reasons for this procedure are twofold. First, it is well established that acclimatign in fishes is more gapid to temperature increases than to decreases in temperature. Second, Sullivan and Fisher in their 1953 study of seasonal fluctuations in the preferred temperature of brook trout have demonstrated the existence of an innate temperature preference which follows the annual temperature cycle but is independent of acclimation temperature. Thus, a fish captured and tested at the field temperature when the temperature is dropping can be expected to give a result quite different from that which would be yielded at the same temperature when the field temperature is rising. Th.eg elative _effectsaf_temparntura ner14mation
,and such innate mech,inisms will be discussed in a later section of this paper.
As can be seen, a high correlation exists between the acclimation temperature and the preferred temperature. It is also apparent that the regression lines are different. Analysis of covariance confimed this to be true.
Initially temperature preferences were determined under conditions of varying salinitics and light icvels. However, preliminary findings demonstrated no effect due to varying light _, _1cve1s and subsequently all
. studies were conducted at a fixed light level of 40 foot-candles, varying only the salinity.
Multiple regression analyses were then applied to the data to determine the effect of salinity on temperature preference. *The next slide shows the multiple regression equation for falling field temperatures. Both the r.egression coefficients for acclimation temperature and salinity were found to be significant at the P.01 level, although'the effect of field or acclimation temperature was greater than the salinity effect. *(Next slide) The effect of salinity was also found to be significant on rising field temperatures, but again, not as great as acclimation temperature. It is interesting to note, however, that the effset of salinity _.wa u reat_er,on falling field temper-ature_s than on rising field temperatures. This difference in effect is best seen in the shape of the response surface calculated for falling field temper-atures and comparing it with the shape of the response surface for rising field temperatures.
- The inverse salinity effect shoun here for falling field temper-atures is quite strong - as is the direct effect of acclimation temperature.
- (Next slide) In the calculated response surface for rising field temperatures the inverse salinity effect is significantly less although the direct effect of rising acclimation temperature remained as strong as for falling field temperatures.
I will now turn the presentation over to John who will discuss temperature avoidance and the relationship of temperature preference and avoidance to field observations.
Temperature Avoidance Studies
- The avoidance design found to be successful with white perch is a modification of the design employed first by Shelford and Allee (1913).
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l_In this design temperature controlled circulating baths serve / as storage reservoirs. Water from the respective bath flowed- (via gravity-flow) into eachendof.thesub-troughsanddrainkfromtheircenters,whe#it recirculated to the temperature baths. Dye tests showed a sharp boundary
'4 at the center drain. The apparatus was thus effectively divided into quadrants.
Equal numbers of fish (usually two or three and all of the same size group) were placed into each quadrant. Two of the quadrants (on opposite ends of the respective sub-troughs) contained water of the acclimation temperature ('*f), while the remaining two contained water of increased temper-usu.a.lly 3 -i;' F
- ature ("T+"). Thus, controls for position effects and simultaneous replicate g
are built into the design. After a 5 minute orientation period, the amount of time spent by each fish in each section was measured for a period of 10 minutes. (This constituted a trial). The number of occurrences of fish in each quadrant was then multiplied by the amount of time they spent in the respective quadrants to give a frequency distribution for each section. A l
l t-test was then performed to determine if a significant difference existed l
l between the' distributions. In this design, incidentally, both preference and avoidance responses can be measured.
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- If no significant avoidance existed, the respective temperatures t
l were then increased in a step-gradient fashion by increasing "T" and '*r+"
3 i
to 5 F degrees beyond their former points. This was continued until significant avoidance took place. (/
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Tests were repea ed for two light levels and at least two salinities for each acclimation temperature.}
M
- Because an avoidance response to "T+" could result from the action of factors other than temperature, those most probable (such as oxygen and l-t I
. pH) were monitored at the imput o'f each sub-trough throughout a test to determine its validity.
Oxygen was monitored in percent saturation (since the ppm value is temperature dependent) gng temperature compensated YSI oxygen analyzer probes. pH was monitored using an Orion multi-channel pH meter. The thermal conditions were monitored by a Leeds and Northrup 24 channel temper-ature recordar (connected to thermocouples at 6 inch intervals along each sub-trour'.4). *Because the trough was enclosed (for light level regulation
]
g as well as to permit movement around the trough area), observation was made via-closed-circuit television. Each test was recorded on videotape and re-analyzed using the temperature recorder output.
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. 1 Results - Temperature Avoidance 3 Q&"
Since 1969, 106 avoidance tests have been performed on white perch.
- As can be seen in the slide, a significant correlation exists between_ avoidance temperature and acclimation or field temperature. Again, two regression equations were calculated, og for rising field temperatures and one for falling field temperatures. The reasons for this procedure were described by Jim, but briefiv were the expected differences in_ rates _of acclimation and the_ existence of an innate temperature response rhythm. Again the
- regression lines appear to be different and this was confirmed by analysis f covariance.
I Multiple regression analyses w g also applied to the data to determine
}l the ef fects of light level. and salinity. *The next slide shows the multiple regression e quation for falling field temperatures. All the regression co-efficients were found to be s_ignificant at the P.01 level including the inverse relation of avoidance temperature with the size of the fish. The 4
calculated response surface for this equation appears in the next slide.
- As g
g can be seen an inverse relation is shown for light level and salinity, while the relationship with acclimation or field temperature is direct.
The multiple regression equation for rising field temperatures is shown
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. in the next slide. *Again gthe regression coefficients were found to be M u) significant at the P.01 level, but the relationships are see quite different.
The relationships of light level and size on teraperature avoidance are now not inverse as they were for falling field temperatures, but rather are direct.
It was also found that the salinity effect is significantly less. *The direct 3 %
relationships of acclimation temperature and light level and the inverse relation with salinity are illustrated in this slide showing the calculated response surfaces.
Now, the next question is how does all this relate to temperature preference 4
! rt r and h6w do these responses relate to what is taking place in nature? Taking l ed.e.,
the questions one at a time: With both rising and fallinh; field temperatures, the preferred temperature was below the avoidance temperature as one would o.Moa/w, d a.ppeit-3 to here.3 l
expect. However, the relationship 3was not found to be constant. Also, the i
relative effects of salinity were the same. That is, the relation was inverse in both preference and avoidance and in both cases was significantly less on rising field temperatures.
I However, the effects of acclimation temperature with rising and falling field temperatures were reversed for the preferred temperature and avoidance temperature. This may be an artifact or it may be due to mechanisms which place preferred temperatures under greater innate control than avoidance L temperatures. That is, the avoidance temperature may be more affected than the preferred temperature by the acclimation temperature.
Now, when field h
9-temperatures are rising, acclimation is expected to be more rapid than when field temperatures are falling. The avoidance temperature for rising field temperatures may thus reflect a more realistic avoidance temperature for a given acclimation temperature than the avoidance temperature determined at that given acclimation when the field temperatures are falling. We suggest the reason for this to be that on falling field temperatures, the "true" acclimation is actually at a higher temperature than the field collection temperature. The preferred temperatures, however, do not follow this relation-ship. Instead, preferred temperatures seem to be either higher than expected when field temperatures are rising or lower when field temperatures are falling.
The work by Sullivan and Fisher may help with an explanation. They found that the preferred temperature of brook trout dropped more rapidly than the clrepped acclimation temperature'in late fall and rose more rapidly than acclimation 4
i
- ruse, temperature in early spring. In fact, such changes in the preferred temperature g
occurred even when acclimation was kept constant. We suggest then that Oe_.
preference data reficct and are due to this change which is likely innate and is independent of acclimation temperature.
Toexplainhowthisrelatefwithwhatwhiteperchdoinnatureabrief explanation of what they do is in order.
- Evidence from both our ecological 1941 studies of the Delaware and from Mansueti's study of white perch in the j
Patuxtent estuary of' Chesapeake Bay have shown the white perch to be a schooling -
gregarious species which undertakes seasonal movements.
It can be considered an anadromous species, although the distance travelled for spawning and the changes in salinity experienced are not as great as most species which are designated as anadromous.
In the spring when field temperatures are rising, i,,-h rt kriw O the greatest movement,t'akes placa. This is a movement from lower estuary
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and high salinity waters to tida1 freshwater areas and can be as great as 10 to 20 miles. Our studies have shown that much of the spawning takes place in the shallow freshwater areas - (such as spi 11 pools below dams) of tidal creeks. After spawnine, movements are local and random and remain so until the field temperatures begin to drog,in the fall and then minor movements downstream t_oward deeper and higher salinity water begin. During the winter, white perch r? main in deep water of moderate salinity until the spring migrction again begins.
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- Lets examine first the relation of the temperature responses to the field movements when the field temperatures are rising. Here we see the relation of temperature preference and avoidance in the superimposed response surfaces. The relations of acclimation temperature, light level and size are direct, while the salinity effect is inverse. At this time, the larger white perch are moving into shallow freshwater areas to spawn.
The shallow freshwater areas not only have higher sub-surface light intensities, but also warm faster than the deeper, darker higher salinity areas. Thus, the adaptations are obvious. Avoidance takes place at a Ligher temperature when light icvels are higher, salinities are lower, and the size of the fish l
is large. Preferred temperature follows suit except no significant light I
nor size effect was found.
(This may be due to the limited data examining these effects.)
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- When field temperatures are falling the relation of temperature LJleER.
preference and avoidance (again shown as superimposed response surfaces)
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follow the seasonal movements. During this time the fish, both large and t
small, are moving into deepen darker, water having a higher salinity. The larger fish-nove out first. The shallow freshwater areas still have higher
e
. s,ub-surface light levels, but now are cooling faster than the deeper,' darker, higher saline waters. Consequently, the temperature gradient is the reverse of what occurs in spring and the inverse relation of light level and avoidance temperature relates quite well to this. The strong inverse relation of salinity would also relate to the downstream movement being minor. That is, the avoidance or preferred temperature is more likely to be encounted sooner as the fish moves downstream than was the case in the spring when it moved upstream.
It is not to be denied, however, that acclimation temperature is the major factor determining both temperature preference and avoidance and is also likely to be the major factor which triggers movement. Nonetheless, the results of this research indicate that light level and salinity are significant modifying factors. Such factors must be taken into consideration not only when examining distributions of estuarine fishes throughout the estuary, but also when attempting to predict their preferred and avoidance rw d.aU le.
kp m dm A temperatures for areas of thermal effluents.4nd particularly3w en determining thermal requirements for water quality criteria.
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THE;EFFECT OF REDUCED IIVELS OF DISSOLVED CIYGEN ON THE TEMPERATUP2 AVOIDANCE RESPONSES OF THE WHITE PERCH, Morone americana
- s JOHN W. MELDRIM AND. JAMES J. GIFT Ichthyological Associates, Inc.
~
Middletown, Delaware INIRODUCTION
$ ne of the objectives of qur _research on the Delaware River estuary O
+
is to determine. the 'l'imits of habitab'le conditions for the fishes and macroinvertebrates of the estuary. Because fishes are motile and generally prudent, the approach we have taken to express these limits s
is in terms 'of behavioral avoidance; With the increased use of estuarine waters for coolingnpurposes, one of the major factors of concern is the Ihmits of tempera ure increase. As,you know, salinity, oxygen, and light are impor$ ant variables in estuaries which' interact uith temperature to produce. stressful conditions to affected organisms.
84 0f the fishes of the Delaware River estuary, the white perch, nx Morone americana, is among the dominant,enh abounds in most. western
~
Atlantic coast estuaries from the Gulf of St. Lawrence to South Carolina.
As a repukt of its relative abundance and responses to temperature, it has been found_to be a problem in the vicinity of steam electric generation stat. ions.:*In con' junction with an ecolegical study of the
- /
De'i' aware River estuary', experimental studies on _the temperature preferences
~
.and avoidances of the = white. perch have been conducted since 1969. However, for this presentation I want to focus on the temperature avoidance respenses
. of the white perch, and the effects of light level, salinity, and level of dissolved oxygen on this response throughout the year.
I MATERIALS AND METHODS General
- Most white perch used in the study were taken by seine from either r-the Delaware River drainage or the upper Chesapeake Bay drainages.,Due to laboratory space ILnitations, experiments were generally confined to specimenslessthan200mmtotallengt{* Fish'weretransportedto,and kept in, the laboratory holding facilities 18-24 hours prior to testing.
These facilities consisted of three 32-gallon plastic garbage pails
~
Lumersed in a water bath. - Water' in each pail was aerated, pumped through a " protein skimmer" to remove nitrogenous vastes, and filtered. Salinity levels in the pails were maintained near the salinity at which the fish were collected.
The range of salinities employed in the holding facilities and during testing extended-from'O.0 ppt to 12.0 ppt. Such salinities cover the general range. encountered in -the Delaware River estuary.
The water bath was maintained at the field collection temperature. ~
It'was assumed that the field collection temperature represented-(or nearly so) the acclimation temperature. Studies were thus performed i
i over the normal range of ambient acclimations throughout the year.
t Light levels were maintained for the appropriate photoperiod at 60 (445 lux 1 foot-candles at the surface of the water using Duro Test " Vita-Lite" g
P flourescent bulbs, which have a spectral energy distribution comparable to, natural daylight. The fish were not fed either prior to or during testing.
Water used in all tests was taken from Appoquinimink Creek (a f I
3 tributary of the Delaware) at high tide to approximate the quality of
~
the De1 aware at high tide. Due to its great turbidity, it was allowed to " settle" prior to use. Nearly saturated levels of dissolved oxygen (except, of course, in reduced oxyger tests) and pH of 7.0 to 8.0 were maintained throughout testing. Such levels again are representative of
-the lower Delaware estuary. Duro Test " Vita-Lites" were used for lighting in all tests and levels were varied by theostats.
Temperature Avoidance Studies
- The avoidance design found to be successful with white perch is a modification of the design employed first by Shelford and Allee (1913).
Briefly, in this modified design,. a control and a replicate were deter-mined at the same time.
The apparatus was constructed such that water
(
of differing temperatures flowed from Forma Scientific temperature controlled circulating baths into the opposing ends of a divided trough and-then. drained at the respective centers. Due to the sharp gradient at the center drains, the apparatus was effectively divided into quadrants.
The temperature was thus the same in diagonally opposed quadrants, but different in those directly opposed. One set of diagonally opposed quadrants was designated as experimental, the other. set as controls.
Temperatures in the directly opposing quadrants were increased in a step gradient fashion with the experimental quadrants ("T+") being. 3 to 5 F higher than tIhe controls ("T").
Equal numbers of fish (usually two and all of the same size group) were placed in each quadrant. The amount of time spent in each respective quadrant was determined over a 10-minute period from which a frequency distribution was formed. The frequency distribution was then analyzed statistically to determine the significance
1 4
i of the response to the temperature increase.
- Tests began at ambient temperature and continued through the step gradient until a significant (P.05) avoidance response was given in both subtroughs.
Oxygen and pH were monitored throughout all tests. The thermal conditions were monitored by a Leeds and Northrup 24 channel temperature recorder connected to thermocen,a. at 6 inch intervals along each sub-trough. A complete temperature "as'p" of the avoidance apparatus was thus f
recorded every 48 seconds. The trough was enclosed for light level regalation as well as to permit movement around the trough area. SDue to the increase in fish activity v'ich accompanied temperature increases, h
observations were made via, closed-circuit television, recorded on video-tape, and then re-analyzed by replaying the video-tape in conjuction with
.the temperature recorder output.
M In the reduced oxygen studies, the level of dissolved oxygen was ir
.i.
reduced approximately 3 ppm below saturation by_. passing the water'in one j
of the temperature controlled circulating baths through a,3-foot long, 3-inch diameter ple% as-column filled with glass marbles.. As -the water 1
flowed through the column, nitrogen gas was bubbled,through in a counter-current direction, thus. " stripping" off the dissolved oxygen.. (I know there is a school of thought which prefers vacuum degasing to nitrogen stripping, but having worked experimentally with behavioral responses to L
gas supersaturated water, I am not convinced nitrogen stripping is all that bad.) In any case, the water of. reduced oxygen content was heated as "T+" in some studies, as "T" in others, and not heated at all in still others. Incidentally, all reduced oxygen tests began with a control
'to test the response to reduced dissolved oxygen alone.
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- -.. -,. - -, ~..
-.-,--.-r--,
,,,-.,m,,,,,w.,-
,----,,,m,---.-.me,-,--n---,,,,,w.~.--,
m..--..,,.,m.-
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i RESULTS AND DISCUSSION i
i Since 1969, 317 temperature avoidance tests have been conducted with I
f white perch.
159 of these were conducted under saturated levels of dissolved oxygen, the remaining 158 under reduced levels. *Because the study was multi-parameter, multiple regression analysis was used to analyze the i
results.
(For those wishing to see the original data these will be i
published in two forthcoming publications: one available from NTIS, 3
I and the other from I.A.)
However, to facilitate the presentation, a generalind multi d (a,t the, top of the Jun a *.s Oe : ple regression e$uation is present9se d.sd ' h-1-84c /o.4. 4 '/; O.t de v!A
.*-) : icr *. < j slide),and the components given separately (beneath). For both saturated i
and reduced oxygen tests, two regression equations were calculated:
one for falling field temperatures and the.other for rising field 4
I j
temperatures. The reasons for this procedure are twofold.' First, it is well established that acclimation in fishes is more rapid to temperature increases than to decreases in temperature. Second, Sullivan and Fisher,in l
their 1953 study of seasonal fluctuations in thg preferred temperature of e......
brooktroutlhavedemonstratedtheexistenceofaninnatetemperaturepre-J h
ference $hich fo11cws the annpal temperature cycip{but is ' independent of i
22m kas the M.4 t.d acclimation temperature.g Barans and Tubb also recently demonstrated this with Lake Erie fishes. Thus, a fish captured _and tested et the fis14 temperature when the temperature is dropping can be expected to give a result quite different from that which would be yielded at the same temperature when the field temperature is rising. We have, in fact, found this to be true with white perch.
l Now,on the slide, notice that the constants are not particularly different, (except for rising reduced dissolved oxygen) which means i
that when the effects of the variables are averaged out, the average i
1 L
n avoidance temperatures were similar. The rising reduced dissolved oxygen co. fad eveeese is significantly higher. Looking first at responses under saturated D.O. conditions, the. dominant factor (as expected) is the acclimation temperature. And (as expected) it is directly related to the avoidance temperature. Salinity, on the other hand, was inversely related on both rising and falling field temperatures. The effect of light level was varied.
On rising, field temperatures, the avoidance temperature was directly related to the light level but on falling field temperatures the relationship was inverse. Total length was directly related on both rising and falling field temperatures.
In an earlier paper we suggested that these relationships reflected the normal migration movements of white perch within the estuary.
- Evidence from both our ecological studies of, the Delaware, and from Mansueti's 1961 study of white perch in the Patuxtent estuary of Chesapeake
..- 7 Bay have shown the white perch to--be a schooling-gregarious species j
whichundertakesseasonalmovements,hcanbeconsidered,ananadromous species, although the distance travelled for spawning and the changes.in
^
salinity experienced are not at great as most species which are designated
-r an anadromous In the spring when field. temperatures are rising, the p
greateImovement (for spawning) takes place. This is a move, ment from [,-
lower estuary and high salinity waters to tidal freshwater areas and can be as great as 10 to 20 miles. Our studies have shown that much of the spawning takes place in the shallow freshwater areas (such as spi 11 pools below dams) of tidal creeks. After spawning, movements are local and random and remain so until the field temperatures begin to drop in the fall and-then minor movements downstream toward deeper and higher salinity water begin. During the winter, white perch remain in deep water of moderate salinity until the spring migration again begins. Considering
. these mo'vements separately, when field temperatures are rising, white perch are moving into the sharlow low salinity waters to spawn. Since such waters warm faster than the deep areas of the estuary and have higher light levels, t'he direct relationship between light level and avoidance temperature is ae expected.
On the other hand, when field temperatures are falling, white perch are moving from the shallow high light areas, which cool quickly, to the deeper, darker more saline waters which are more thermally stable. The inverse relationship between light level and avoidance temperature is thus also expected.
When the level of dissolved oxygen is reduced in these studies, however, both the relationships and their magnitudes change.
Looking first at acclimation temperature, the direct relationship between acclimation and avoidance temperature continues. However, the magnitude of the effect is significantly reduced. The effects of salinity and light level are also altered. Of major interest, of course, is the effect of reduced D.O.
itself. As expected, when levels of dissolved oxygen were reduced in conjunction with the increased temperature ("T+"),
the avoidance temperature was significantly reduced. When the 1 vel of D.O. was reduced in conjunction j
with the control temperature ("T"), the avoidance temperature was signi-i ficantly raised. This translates into an inverse relationship between the avoidance temperature and the level of D.O. in "T" and a direct relationship in "T+".
We have observed these D.O. effects in the field.
I l
Unfortunately, and as you might suspect, these numbers do not tell i
ze l
the whole story, because the effects of echese variables are, in fact, I
more compicx. Although this is the subject of another paper, we found I
through modeling the data that multiple linear regression with interactions i
(
was a significantly better model than simple multiple linear regression.
Since this model revealed interactions of these factors to be as l
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significant as the factors the=selves, the effects of the variables on the avoidance temperature are no longer consistent.
Perhaps the easiest way to see the effects of both the individual variables and their interactiv'ons is by looking at contour plots of the avoidance temperatures.'h.Considering saturated D.O. conditions for rising field temperatures first, we see contours of the avoidance temperature (in degrees C) plotted against acclimation temperature (in degrees C) and salinity (in ppe). The dotted line set of contours are avoidance temperatures at high light level, the solid line set are contours for low light level.
Notice that the contours are higher going from lef t to right, reflecting the direct effect of acclimation on the avoidance temperature. Also notice that the high light level contours are generally slightly to the right of those for low light level. This reflects the direct relationship between light level and avoidance temperature (i.e., avoidance temperatures being higher at high light levels). ' But notice the contours also cross., The inconsistent effect of salinity is also seen. Notice that these contours are not straight and that, while at low salinities and low acc1Laation temperatures the salinity relationship is inverse, for both light levels, at higher salinities,and acclimation, temperatures the relat'ionship shifts
% c.c,t-rcl4 c. '.' E rk *.t-st O.i.er 's q 1. t ' s.. *..* v : <... e.', : * \\ vt The crossed lines and the shifts in relationship}are o
to being direct.3
' he effects of interactions.
t
' t. When field temperatures are falling, we again see the increasing r
avoidance temperature contours accompanying increasing acclimation temperature. But notice now the inverse light effect, which is significantly stsonger at the lower acclimation temperatures. The change in salinity effects are also strong. However, instead of shif ting from inverse to direct (as on rising field temperatures), the shif t is fro.m, direct to y.,.n
- tr o ~. w
- v. i..
inverse (again for both light levels).
Mo';sutbs,s
.c'. E <
-;f 9 c r ea t H vh.
,. t t,py
-- - ~.
,...., 2$ Under conditions of reduced D.O. the contours reveal major shifts in the effects of the variables. The dotted lines are now the avoidance temperature. contours when the level of dissolved oxygen was reduced to about 60% saturation in conjunction with the experimental temperature udNL i-increase ("T+"),.and the cooler temperature ("T") remained near saturation.
The solid lines represent the avoidance temperature contours when the as.r D.O. in "T" was reduced to 607. saturation and. he D.O. in "T+" remained
.t near saturatien.
On rising field temperatures we again see the direct relationship between acclimation and avoidance temperature, However, a significant shift to the lef t in the avoidance temperature contours is I
now evident when the level of dissolved oxygen in the control temperature l
("T") was reduced. The opposite effect is seen when the level of D.O.
was red, uced in "T+".
This shows that the avoidance temperatures were higher when the D.O. was reduced in "T" (the control temperature) and lower when the D.O. was reduced in conjunction with the temperature j
increase ("T+"). The change 'in the effect of salinity is also seen.
Although at saturated D.O. the effect of salinity on rising field i
temperatures had bene. inverse at low acclimation temperature and direct t
[
at high,. when the level of D.O. was reduced in "T+", the effect remains continually inverse, but is continually direct when the D.O. is reduced
' in"T. *At high light levels, these effects are nere exaggerated, t
l Further, avoidance temperatures are significantly higher at the high
~i light level.
- When field temperatures are falling, the avoidance temperature c'ntours are again directly related to acclimation and higher for o
reduced D.O. in "T" than for reduced D.O. in "T+".
However, the effects i
i i
of salinity are opposite of those when field temperatures are rising.
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1
.,., That is, salinity effects are now direct when the D.O. was reduced in
'*I+",
but inverse when the D.O. was reduced in "T".. )i, b'ight level ef fects,are direct again as with rising field temperatures k However, as seen in this -
slide of effects at high light conditions, the salinity effects are not as exaggerated as on rising field temperatures.
In conclusion, it is not to be denied that acclimation temperature is the major factor determining temperature avoidance of white perch and is also likely to be the major factor which triggers movement. Nonetheless, the results of this research indicate that interactions with light level, salinity, and level of dissolved oxygen are significant modifying factors.
Such factors must be taken into consideration not only when examining distributions of estuarine fishes throughout the estuary, but also when attempting to predict their avokiance temperatures for areas of thermal effluents.
This should be particularly kept in mind when determining thermal requirements for water quality criteria.
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e, BEHAVIORAL AVOIDANCE RESPONSES OF ESTUARINE FISHES TO CHLORINE By John W. Meldrim and James A. Fava, Jr.
Ichthyological Associates, Inc.
100 South Cass Street Middletown, Delaware 19709 INIRODUCTION The amount of chlorine released into estuarine 'and marine waters has caused concern regarding its environmental impact. Although toxicity tests reveal what levels can be tolerated, sub-lethal effects are of equal importance. This paper is concerned with a major sub-lethal e'ffect: behavioral avoidance. Although considerable data have been accumulated on several species, analysis of the results of tests with white perch, Morone americana, and Atlantic silverside, Menidia menidia, are presented because they exemplify avoidance behavior in estuarine waters. However, since this is an ongoing study, the analyses and conclusions drawn from them are tentative and subject to revision.
NETHODS Avoidance responses were determined under varying conditions of temperature, salinity, light level, and level of dissolved oxygen throughout the year following the ambient temperature and salinity cycles of the Delaware River estuary. Tests were conducted using the modified Shelford-Allee apparatus, which is a divided trough further divided into quadrants. The apparatus and experimental design is described in detail by Meldrbu, Gift, and Petrosky (1974). Experimental
2 chlorine concentrations were achieved using a solution of calcium hypochlorite and were measured using a Fischer and Porter amperometric titrator. However, since the chemistry of chlorine in estuarine waters is complex and the ratios of halogens in these tests unknown, concentrations sre expressed as residual oxidant. The salinities used in testing were between 0 and 7 ppt. However, since the Atlantic silverside is generally not found in low salinity waters, no tests were conducted on that species at salinities less than 2.5 ppt.
Since both white perch and Atlantic silverside are generally present in the Delaware River estuary throughout the year, testing was conducted over the annual range of ambient wat2r temperaturea.
- Respcases to residual oxidant were teste'd under the following conditions:
(1) near saturation oxygen levels and ambient temperatures in all quadrants,' (2) near saturation oxygen levels in all quadrants with ambient temperatures in the control quadrants (which centained no i
oxidant) and ambient temperatures plus approximately 2 to 3 C in the j
experimental quadrants (which contained a chlorine dose), (3) near i
~
saturation oxygen levels in the control quadrants and levels approximately 3 ppm below saturation (which is about 70-80% saturation) in the experi-mental quadrants with ambient temperatures in all quadrants, and (4) near saturation oxygen levels with ambient temperatures in the control quadrants and oxygen levels approximately 3 ppm below saturation with ambient temperatures plus approximately 2 to 3 C in the experimental quadrants, l
These conditions were tested at both high (1076 lux) and low (430 lux)
(
i light levels.
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RESULTS AND DISCUSSION The tiae of exposure to test concentrations of oxidant employed in these studies was relatively short. Under this experimental regime the initial (and lowest concentrations) usually elicited preference, particularly in tests in which a AT accompanied the experimental concentration. As the oxidant concentrations were increased the response changed from preference to random movements - neither preference nor avoidance.
Increasing the concentration further elicited an avoidance response.
Mean avoidance concentrations (expressed as total residual oxidant) of the white perch tested at ambient te=peratures (without 6T) are summarized in Table 1.
Results of tests conducted with a 6T acco=panying the test concentration are summarized in Table 2.
Of the variables under study, temperature and salinity appeared to most influence the avoidance concentration. Applying a 6T to the test concentration generally increased the avoidance concentration and indicates temperature
~
preference can override chlorine avoidance.
Mean avoidance concentrations of the Atlantic silverside are sunnarized in Table 3 for tests conducted at ambient temperatures and in Table 4 for tests conducted with a 6T accompanying the test concentration. The effects of the variables and the 6T were similar to those observed for white perch.
The results of the responses of the white perch and the Atlantic silverside tested at ambient temperatures (without a 6T) were subjected to multiple linear regression analysis using BMD 02R (Dixon 1971). Due to limited data, tests incorporating a 6T accompanying the experimental chlorinc concentration were not subjected to analysis. The independent variables incorporated into the analysis were:
temperature, salinity,
4 pH, light level, length of fish, level of dissolved oxygen and the 15 first order interactions of these variables. The dependent variable was the estimated avoidance concentration as total residual oxidant.
Results of the analysis are shown in Table 5 for white perch and in Table 6 for Atlantic silverside.
Since the data are preliminary, the purpose of the analysis is not to provide a predictive equation, but rather to show the effect of environmental variables on the response.
To facilitate comparisons, the regression coefficients have been standardized.
The components for the equation for white perch show a highly significant multiple regression coefficient (R) with about 73% of the variation explained by the variables under study. The partial regression coefficients for all but two of the main effect variables were found to be sighificant. Of the 15 possible interactions, four were significant.
Salinity was the dominant factor, being only slightly more important than an interaction of salinity with pH. Test temperature and an interaction of test temperature were pH were the next most important variables. Although a significant variable, pH was less important as a main effect than as a factor interacting with other variables. The correlation (r) of the main effects with the dependent variable indicates the avoidance concentration was inversely related to l
salinity, test temperature, and size of fish. Avoidance concentration was directly related to pH, light level, and level of dissolved oxygen.
The components of the equation for Atlantic silverside show similar results. Of the 21 variables under study 11 were significant. Of these, seven were interactions. As with white perch, the four most import $nt variables were salinity, the interaction of salinity with pH, temperature, and p.
-n n-
_=
=.
5 the intaraction of temperature with pH.
Interactions were more Laportant in tests with Atlantic silverside indicating an understanding of their i
I responses to be more complex. The avoidance concentration was inversely related with temperature and salinity. Light level, a significant variable in these tests, also resulted in an inverse relationship with the avoidance concentration. As with white perch, pH was more important as a factor in interactions than as a main effect. By way of contrast, the larger Atlantic silverside had higher avoidance concentrations, whereas the relationship with white perch was inverse.
One would expect an inverse relationship between temperature and 1
the avoidance concentration if chlorine affects hemoglobin and thus impairs
- respiration (Grothe and Eaton 1975). The inverse relationship with salinity, however, is more likely a function of the dhemistry of chlorine in saline waters..These effects are thus, synergistic.
Examination of the effects of environmental variables on the avoidance response is only one aspect of the complexity of this
~
l phenomenon. The length of exposure to' the oxidant, the chemical l
nature of the oxidant, the nature of exposure - whether sudden or gradual, and the effects of previous exposure - learning or physio-l logical impairment all contribute to a greater complexity in the understanding of the ability of fishes to avoid chlorinated effluents in nature.
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6 ACKNWLEDGMENTS This study supported in part by the United States Department of the Interior as authorized under the Water Resources Research Act of 1964, Public Law 88-379, as amended; and by Public Service Electric and Gas of New Jersey, and the Manufacturing Chemists Association.
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7 LITERATURE CIIED Dixon, W. J. (Ed. ).
1971. Biomedical Computer Programs. University of California Publications in Automatic Computation.
No. 2.
Univ, of California Press, Los Angeles. 600 pp.
Grothe, D. R., and J. W. Eaton.
1975. Chlorine-induced mortality in fish. Trans. Am. Fish. Soc. 104(4):800-802.
Meldrim, J. W., J. J. Gift, and B. R. Petrosky.
1974. The effect of temperature and chemical pollutants on the behavior of several estuarine organisms.
Ichthyological Associates, Inc. Bull. 11.
129 pp. Available from NTIS as PB-239347.
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-. - - -,,, -,, - + -
,.v.-
8 Table 1. - Mean (X) avoidance concentrations (as total residual oxidant) for white' perch, Morone americana, under various conditions of ambient temperature, salinity, light level, 'and level of dissolved oxygen (D.O.).
No 6T was applied to the test concentration.. N is the number of data points per condition.
Salinity (ppt) 0-2 3-7 Test Temp. (c) 0-12 13-27 0-12 13-27 Low Light
__ 430 lux)
X N
X N
X N
X N
(
Saturated D.O.
0.23 16 0.06 6
0.10 6
0.07 9
Reduced D.O.
0.35 2
0.05 8
0.15 10 0.05 6
High Light
_ _ _ (1076 lux)
Saturated D.O.
0.27 4
0.04 2
0.18 7
0.06 4
Reduced D.O.
0.28 2
0.07 2
0.17 4
0.06 4
O e
4 4
9
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9 Table 2.'- Mean (X) avoidance concentrations (as total residual oxidant) for white perch, Morone americana, when a 6T o.f 2 or 3 C was applied to the test concentrations, under various conditions of ambient temperature, salinity, light level, and level of dissolved oxygen (D.O.) N is the number of data points per condition.
Salinity (ppt) 0-2 3-7 Control Temp. (C) 0-12 13-27 0-12 13-27 Exp. Temp.,(C) 2-14 15-29 2-14 15-29 Low Light N
X N
X N
X N
(430 lux)
X Saturated D.O.
0.08 2
0.15 2
0.28 6
0.06 2
Reduced D.O.
0.10 2
0.11 4
High Light (1076 lux)
Saturated D.O.
0.07 2
Reduced D.O.
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10 Table 3. - Mean (E) avoidance concentrations (as total residual oxidant) for Atlantic silversidei Menidia menidia, under various conditions of temperature, salinity, light level, and level of dissolved oxygen (D.O.).
No 6T was applied to the test concentration. N is the number of data points per condition.
Salinity (ppe) 2.5-4 5-7 Test Temp. (C) 0-12 13-27 0-12 13-27 Low Light (430 lux)
X N
X N
X N
X N
Saturated D.O.
0.64 2
0.10 12 0.11 6
0.08 10 Reduced D.O.
0.15 2
0.12 6
0.03 6
High Light (1076 lux)
Saturated D.O.
0.06 2
0.20 4
0.15 5
0.05 4
Reduced D.O.
0.03 2
- 0. 13 4
0.04 4
11 Table 4. - Mean (X) avoidance concentrations (as total residual oxidant) for Atlantic silverside, Menidia menidia, when c AT of 2 or.3 C was applied to the test concentrations, under various levels of dissolved oxygen (D.O.).
N is the number of data points per condition.
Salinity (ppt) 2.5-4 5-7 Control Temp. (C) 0-12 13-27 0-12 13-27 Exp. Temp. (C) 2-14 15-29 2-14 15-29 Low Light (430 lux)
X N
X N
X N
X N
Saturated D.O.
0.34 2
0.09 6
0.28 2
0.18 4
Reduced D.O.
0.11 4
High Light (1076 lux)
Saturated D.O.
Reduced D.O.
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Table 5. - Results of the multiple regression analysis of the avoidance responses of the white perch, Morone americana, to total residual oxidat.t.
F(23, 78) = 16,486**
N = 92 Multiple Correlation (R) = 0.8563**
R2 = 0.7332 MAIN EFFECTS SIGNIFICANT INTERACTIONS CORREIATION (r)
STANDARD PARIIAL STANDARD PARTIAL WITH AVOIDANCE REGRESSION RECRESSION VARIABLE CONCENTRATION COEFFICIENr VARIABIE COEFFICIENT Salinity (ppt)
- 0.073 27.092**
pH X Salinity
- 25.435**
Temperature (C)
- 0.571**
20.976**
pH X Temp.
- 20.436**
U Total Length (m)
- 0.495**
12.649**
pH X Total Length
- 11.962**
pH 0.374**
2.132**
Temp. X Salinity 0.518**
Dissolved 02 (7. sat.)
0.203 n.s.
Light 0.055 n.s.
- Significant at P <0.01
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Table 6. - Results of the multiple regression analysis of the avoidance responses of the Atlantic silverside, Menidia menidia, to total residual oxidant.
F(14, 54) = 13.697**
N = 69-Multiple Correlation *('R) = 0.8833**
R2 = 0.7803 MAIN EFFECTS SIGNIFICAN"' INTERACTIONS CORREIATION (r)
STANDARD PARTIAL STANDARD PARTIAL WITH AVOIDANCE REGRESSION REGRESSION VARIABE CONCENTRATION COEFFICIENT VARIAB M COEFFICIENT Salinity (ppt)
- 0.186 25.422**
pH X Salinity
- 23.576**
Temperature (C)
- 0.366**
21.036**
pH X Temp.
- 19.680**
Light
- 0.095
- 2.282*
Lux X Total Length 3.753**
Ce pH 0.393**
2.204**.
Dissolved 02 X Tota 11ergh 1.998**
Dissolved 02 (7. sat.)
0.245*
n.s.
Sal. X Total Length 1.712**
. Total Length (nun) 0.252*
n.s.
Dissolved 02 X Total
- 1.468 Length 1.250**
Temp. X Salinity
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- Significant at P <0.01 J
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AVOIDANCE RESFONSES OF TWO ESTUARINE FISHES TO CHLORINE John W. Meldrim Ichthyological Associates, Inc.
Middletown, Delaware INTRODUCTION In recent years considerable concern has developed over the amount of chlorine released into the estuarine environment, particularly as a biocide in the cooling waters of large power stations. In this regard several questions can be posed concerning the effects of such releases.
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,Among them is t determine how estuarine fishes respond to chlorine 2 d E-
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. i, :,i.. ( ',,'.3 Responses to chlorine in estuarine systems can be expected to be affected by several variables. The temperature of thermal effluents even when put through a cooling tower will obviously be somewhat higher than the temperature of the receiving waters. Such effluents can be expected to attract fishes at certain times of the year. Moreover, the level of dissolved oxygen in the effluent could be expected to be lower than the receiving waters, especially if dechlorination with sodium bisulfite, or sodium thiosulfate is used. Light level and salinity have been found to significantly alter the response to temperature change and can be expected to alter responses to chemical compounds. Consequently, the Mm Q.
. objectives of the present study have been to determine the responses of 3
estuarine fishes to residual chlorine under varying conditions of light level, salinity, temperature, and dissolved oxygen.
Before proceeding, a brief and simplified description of the chemistry of chlorine in water is in order. When chlorine is added to natural waters a certain amount is used up by the chlorine demand of the water.
2 What remains is referred to as residual chlorine. Such residuals may be free (being an equilibrium between hypochlorous acid and hypochlorite ions) or this free residual may combine with nitrogenous compounds, ammonia being the most common. When enis occurs, the residual is called the combined residual and is comprised primarily of chloramines. There is, of course, considerably more to the chemistry of chlorine in water, but that's about all that's needed to follow this paper.
i MATERIAIS AND METHODS Since 1973 we have been studying the responses of two ecologically important estuarine fishes, the white perch, Morone americana; and the Atlantic silverside, Menidia menidia; to both free and combined residual g
chlorine. Water for the study has been taken from a tidal tributary of 5{ sc 6.
'the Delaware River estuary (and allowed to " settle" in two 1250-gal poly-ethlyene tanks prior to useh Since the water intake is located about 2 miles up the Appoquinimink, the salinities used in testing were low, being between 0 ppt to 7 ppt. However, since the Atlantic silverside is generally not found in low salinity waters, no test were conducted on fg{.s i U L~$N 4t--t%peclu l
ei4ver+14e at salinities less than 3 ppt.g Since both white l
j perch and Atlantic silverside are generally present in the Delaware River 1
estuary throughout the year, testing was conducted over the annual range of ambient water temperatures.
((g, Behavioral responses to residual chlorine were determined using the modified Shelford-Allee apparatus. Briefly, in this system water was taken at.high tide from Appoquinimink Creek and pumped into the poly-ethylene storage tanks to settle. It then flowed via gravity flow into l
a temperature controlled water bath. Water was conditioned to the acclimation temperature and the desired oxygen level (by oxygen stripping
3 with nit'rogen when reduced oxygen levels were desired) in the bath. The water was then pumped into a d'ose box which was divided into two 1-ft boxes. One side of the box received a chlorine dose from a constant head reservoir. The dose was determined by a flow meter. Whenever the float valve droppad, the solenoids opened and released water from the bath and the chlorine dose into the experimental side of the dose box. It also contained a heater which raised the experimental water temperature when desired. The other side provided control conditions as it did not receive a chlorine dose, was not heated and in the case when receiving water of reduced oxygen level, was aerated to regain near air saturated conditions.
Water from the respective sides of the dose box then flowed into the modified Shelford'-Allee apparatus which is a divided trough further Flow me'ers monitored the rate divided into quadrants by center drains.
t of flow into the apparatus and was generally about 3 liters / min through the system. This generally resulted in predominantly free chlorine residuals. However, in some tests, the contact time in the dose box was increased to produce predominantly combined chlorine.
l Briefly, the general experimental procedure was (1) establish the conditions in the troughs such that water in diagonally opposite quadrants (formed by the center drains) had the same temperature and oxygen conditions and chemical composition, (2) place equal numbers of fish into each quadrant, (3) after a 5-min orientation time, determine the amount of time each spent in one of the two respective quadrants per trough and (4) analyze the fish-time distribution by t-test to determine if a significant response had taken place.
If no significant avoidance response occurred, the concentratien of chlorine was increased.
Responses to residual chlorine were tested.under the following
4 conditions:
(1) near saturation oxygen levels and ambient temperatures in all quadrants, (2) near sacuration oxygen levels in all quadrants with ambient temperatures in the control quadrants (which contained no chlorine) and ambient temperatures plus approximately 2-3 C in the experimental quadrants (which contained a chlorine dose), (3) near saturation oxygen levels in the control quadrants and levels approximately 3 ppm below saturation (which is about 70-80% saturation) in the experimental quadrants with ambient temperatures in all quadrants and (4) near saturation oxygen levels with ambient temperatures in the control quadrants and oxygen levels approximately 3 ppm below saturation with ambient temperatures plus approximatley 2-3 C in the experimental quadrants.'h.gtd dc. wdd.e
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Ce t-e 1D7 6 }ud (/co4d 0.wcl lot.o-93o /c (4c { t h li k4 level.s.
i Ambient temperatures refer to ambient collection temperatures and were the temperatures at which the fish were held prior to testing. Tests were conducted throughout the year at seasonally appropriate anbient temperatures. Oxygen icvels and temperatures were monitored in each quadrant using YSI Model 5450 temperature compensated oxygen probes, a RACO automatic multi-channel oxygen (and temperature) probe scanner, and a YSI Model 54 oxygen meter. Chlorine levels were monitored with a Fisher and Porter Model 1010T amperometric titrator.
RESULTS AND DISCUSSION The results of the responses of both the white perch and the Atlantic silverside tested at ambient temperatures (that is, without a 6 T) were subjected to multiple linear regression analysis. The results of this analysis to date are shown in this slide. At the top is the model of the regression equation: where Y=the estimated concentration of residual chlorine avoided or avoidance concentration &n this case,
~
free chlorine); "a" is the constant; the b's, the regression coefficats; and I's the independent variables..The regression coefficients shown in the slide are standardized. That is, they have been corrected for units of measure. The purpose of using standardized regression coefficients is that it permits co=parison of the importance of the independent variables.
Please bear in mind that this is an ongoing study and these numbers will be subject to revision. However, we do have enough data to point out some interesting relationships and effects.
Looking first at the components for the equation for white perch, you can see that the multipic regression coefficient (R) is a highly significant.9068, showing that about 82% of the variation can be explained by the variables under study. The partial regression coefficients for all the variables w'ere found to be significant at the P.01 level. Of these variabics, acclimation temperature was the dominant factor, being about one and a half times more important than the next most important variable, salinity. Total icngth was next, then light level and level of dissolved oxygen.
However, when we look at the components for the equation for Atlantic silverside, things didn't turn out quite so nicely. The R value,.6912, l
while significant shows that only about 48% of the variation is explained.
This may be due to the reduced sampic size, a limited range of test l
conditions, or more likely that the simpic linear multiple regression l
l model does not fit the data very well. Only two partial regression coefficients were significant: acclimation temperatue and salinity.
Note that acclimation is again the dominant variabic.
l The effects of the variabics on the avoidance concentrations of both white perch and Atlantic silverside are similar. Acclimation I
4
6 temperature, the dominant independent variable, was invessely related to the avoidance concentration.. The'same 3as true of salinity, ' dissolved oxygen and length. Light icvel was the only variable in which a direct 1
relationship was observed. One would expect an inverse relationship between temperature and the avoidance ' concentration if chlorine does damage the gill tissues and thus imp 51r respiration. The inverse relationship with salinity, hwever, is more likely a function of the chemistry of chlorine in saline waters. At the present time, chlorine is thought to react with the bromine in sea [ater,to produce another oxidation 7
s
' ' compound, possibly bromine chloride. The effects are thus synergistic, c
g Why the other variables affect the response the way they did would be 4, '
speculation.
s Regrescion ana' lysis of responses of these fishes when a A.T was associated with the chlorine concentration'was not done due to the low number of tests completed.- (As I said, this is.an on-going si.udy.)
~
E However,.cne can see the effect of the' A T on thc.next slide. In this Braph the avoidance concentrations are plotted against the dominant
/
independenti variable, the acclimation temperature. The circles represent
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avoidance concentrations when no AT. was associated with the chlorine concentration. The triangles represent the avoidance concentrations
. when a 2-3 c AT was associated with the chlorine ' concentration. The l
^
1 solid circles and triangles represent the free chlorine residual, the i
open ones the total resid'ual. As a generality, ' adding a 2-3 C AT in-creased the avoidance concentration. Thi.t means temperature preference r
will overrido chlorine avoidance. This effect does not show up too well 7
in the graph due to the salinity effect, since these points are results s
-'of' tests conducted at different salinities However, the inverse r'clation between acclimation (= test) temperature and the avoidance T
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7 concentration is clearly shown. Another aspect which appears to stand out is the change in the response to combined chlorine with increasing test (acclimation) temperature. At temperatures below 10 C, the response to combined chlorine (the difference between free and total) appears to
[
be greatly reduced. Unfortunately this graph only shows endpoints and not the ratios of concentrations of free and combined residuals leading up to them. Without going into detail let me explain that in some tests i
as the test concentrations increased, the level of combined chlorine increased much faster than the free component. As a result, the free residual often remained stable while the combined residual increased.
In some cases this was by design, in others not. Consequently, additional research needs to be done to determine whether this decrease in responsiv-ness to combined chlorine with an increase in test (= acclimation) tempera-ture is real or.is an artifact of testing sequence. The results of tests i
with the Atlantic silverside suggest the phenomenon to be real, especially since the.results of both species cover several years' data.
l' In the results of tests with Atlantic silverside, the increased avoidance concentration resulting from the overriding effect of temperature preference can be seen. The decrease in avoidance concentration ani the
-apparent decrease in responsiveness to combined chlorine with an increase t
in the test (= acclimation) temperature is also shown. Note that the breakpoint for the change in response to the combined residual comes I
about 15 C for the Atlantic silverside. This points to one of the directions L
I l
for our future resesrch.
There are several additional areas of needed research. In these tests, the trials were one hour apart. That is, the fish were exposed tothetestconcent[ationforaboutonehourpriortodeterminingthe i
8 response'. Since the objective was to determine the maximum acceptable level of chlorine this exposure time is not unreasonable, and the prudence of the fish can be tested by acute and chronic toxicity tests. However, if the objective were ' o determine the minimum level of chlorine which t
would be avoided, these tests are far too short. To determine minimum avoidance levels long-term (possibly 30-day) tests are required. One s
problem to overcome in such tests, however, is where in the apparatus should feeding be done. If done in the chlorine, the fish learn to feed in it and this can result in unrealistically high avoidance concentrations.
If done in the unchlorinated water, the avoidance concentration can be unrealistically low.
I'm sure you can think of other puzzles to be solved.
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.t Temporal-Spatial Occurrence of White Perch (Morone americana) in the Delaware River System Alan W. Wells Ichthyolcgical Associates, Inc.
Middletown, DE 19709 I.
Scope of Study Ichthyological Associates has been conducting intensive studies in the Delaware River.near Artificial Island since 1968.
During the period 1970 through 1978 effort was concentrated between the Cohansey River at rkm 64 through Pea Patch Island at rkm 100.
Beginning in 1979 the study area was expanded to cover from the mouth of Delaware Bay (rkm 0) to just north of the Delaware Memorial Bridge at rkm 117.
Although these programs were not designed to specifically sample white perch, it was a major component of the catch.
To supplement this information a white perch mark recapture program was initiated during the fall of 1980 in the region south of Artificial Island at rkm 74 to near Camden at rkm 164.
This presentation examines the white perch catch statistics resulting from 4.9 m bottom trawls in the vicinity of Artificial Island (rkm 64-100) during the years 1970 through 1980 and our efforts to explain the variability observed in these data.
II.
Data Base The catch record was expre'ssed as the semi-monthly mean number p'er 10 minute trhwl.
Of a possible 264 observations 42, or 164, were missing.
Each semi-monthly mean consisted of approximately 4510-minute tows except af ter 1979.
With the expansion of the study area, fewer samples were allocated to the rkm 64-100 region.
Generally after this date only 10-20 10-minute tows were conducted in this region.
All CPUE values were transformed to natural logarithms.
A constant of 0.01, or 1 fish per 100 tows, was added to the data to prevent taking the log of zero.
The catch was not separated by age class, but represents the total white perch catch.
However, age group 0+ and 1+
ind.ividuals are typically the most prevalent.
III.
Physical-Chemical Factors Along with catch pe. effort information, physical and chemical measures such as temperature and salinity were recorded.
Flow rates, measured at Trenton, were obtained from U.S.G.S.
records.
Our first approach was to see if there were any significant relationships between CPUE and some of these physical-chemical factors.
Indeed, sign.ificant associations were found.
Correlation coefficients indicate that greatest
l catches occurred during periods of low salinity, cool temperature, and high flow.
However,' significant intercorrelations were also found among the three physical-chemical factors, especially between flow and salinity.
It appeared as if we were dealing with a complex of factors, in this case a seasonal phenomenon.
This suggests that a time-series approach to the catch record would likely be more appropriate.
IV.
Time-Series Model Of the available time-series approaches, the Box-Jenkins method will certainly produce the most parsimonious model.
However, since our goal was not only to produce a predictive model but also gain an understanding of the under' lying processes, it was believed that a more-or-less classical series decomposition would be more appropriate.
Following this approach the catch per unit effort at any given time (CPUEt) may be expressed as the summation of:
1)
A long-term trend, the long-term direction of the population.
2)
A deterministic cycle, any periodic behavior in the population.
3) autocorrelated error, the degree to which the current catch may be predicted from preceeding catches.
- and, 4) white noise, or random error.
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V.
Long-Term Trend Component The trend component was adequately modeled with a simple log linear regression.
It was significant at the 0.01 level and explained approximately 24% of the total variability.
The most.important aspect is the downward slope.
Since the data is log transformed, the population appears to be undergoing an exponential decay at a rate of approximately 15% per year, or over the 11 year study period, a decline of 97%.
VI.
Test for Cycles The next step in the modeling procedure was to check for the presence of cyclic behavior in the data.
At this point, in order to simplify further analyses, missing values were replaced with detrended seasonal mean values.
This is not an entirely satisfactory procedure in that it will artificially increase R values.
However, this increase is slight and does not significantly alter the outcome.
To test for cyclic behavior, the residuals from the trend model were examined by autocorrelation analysis.
A plot of the autocorrelation coefficients displays a highly l
significant positive peak at lag positions 24, 48, 72, 96, 120.
Since the data was semi-monthly, this clearly suggests an annual cycle.
There is little evidence of dampening over time indicating a pattern that persists relatively unchanged year after year.
I
VII.
Cycle Component The seasonal cycle was modeled using a Fourier transformation and a fundamental period of 24.
Harmonics of the fundamental period were added successively until there was no significant gain in the variability explained by the model.
The final model required the first 4 harmonics and explained 58% of the variability lef t unexplained by '.he trend component.
At this point the combined trend + cycle model explained 68% of the total variability.
The cycle displays a sharp peak in November followed by a moderate decline during January.
This is followed by a slight but protracted peak during the spring.
There is a precipitous drop with low catch during the summer followed by rising catch during the fall.
VIII.
Test for Autoregressive Component The next step was to examine the residuals from the combined trend + cycle model for evidence of autoregressive behavior.
i l
A plot of the autocorrelation function displayed a dampening l
exponential process while in the partial autocorrelation l
l function, only the first two coefficients were significantly different than zero.
This combination is indicative of a second-order autoregressive process.
i l
Essentially, these results indicate that if the catches were higher than expected in the two previous sampling periods, l
r
it is likely to again be higher in the current sampling period.
Conversely, if catches were lower than expected in the two previous sampling periods, the current catch will also likely be lower.
This sort of situation can easily be brought about by changes in year-class strength.
For example a strong year class would produce greater than normal catches for an extended period of time.
IX.
Autoregressive Component The autoregressive parameters were fit using a non-linear least-squares procedure.
Both terms were significant at the 0.01 level and the model satisfied the conditions for stationarity.
The autoregressive terms explained approximately-16% of the remaining variability and brought the total model R to approximately 73%.
Inclusion of these coefficients produces a rather adaptive model which accentuates the peaks and t
i troughs.
Analysis of the residuals from the trend + cycle +
l autocorrelated error model indicated that the series had been reduced to white noise.
i At this point, as part of the validation process, we must ask "Does the model make any biological sense?".
I will I
restrict my discussion to the two largest variance components, 1) the cycle and 2) trend, since I have briefly mentioned the possible interpretation of the autoregressive component.
X.
Interpretation of Cyclic Component The largest source of variance in our data is explained by the cyclic component.
The origin of this component is easily understood when seasonal distribution patterns outside the primary study region are analyzed.
However, before continuing I should offer a brief explaination concerning these distribution maps.
When the study area was expanded ~in 1979, the entire region was divided into just over 1000 grid squares (LORAN based).
Approximately 70 of these grid squares were sampled during a given sampling period.
These maps are produced by an automated routine which estimates the density of organisms at each of the 1000 grid co-ordinates from an average of a given number of observed points obtained by nearest neighbor search.
The process is essentially a two-dimensional moving i
average.
The number of points averaged determines the i
l smoothness of the surface and in the following sequence, 6 nearest neighbors were averaged.
The computer program allows for the selection and plotting of any specified size range of individuals.
Therefore, given growth rate i
information, selected age groups may be examined.
i
_,__.,c
t The basic component of the cyclic term is the annual periodicity.
This is the result of the annual fall down-river movement to the dbwn-bay overwintering areas and the spring return to the upriver spawning / feeding regions.
This may be illustrated by the following sequences.
A.
(Nov. 15) Age group 0+ migrants begin to appear in the Artificial Island region about mid-November in 1979.
The leading edge of the population was at approximately rkm 70.
Densities throughout the region were less than 3
0.02/100m,
B.
(Dec. 4-7) By early December densities had increased in the north and the leading edge had pushed southward to approximately rkm 60.
Peak densities were less than 0.04/100m.
C.
(Jan. 28-29) By late January the extent of the southward movement appeared to reach its maximum.
Highest densities extended as far south as approximately rkm 60, while the front pushed as far south'as approximately rkm 50.
Peak density was 3
0.130/100m,
D.
(Mar. 24-27) By late March the bulk of the population appears to have moved northward.
The southern extent of the range could not be determined due to lack of-
samples.
Densities remained high, 0.06.157/100m, in the northern part of-the study area.
However, the necessity of including 4 harmonics to fully describe the cycle indicates a more complex structure.
Analysis of older age groups offer an explanation.
A.
(Oct. 11) Age group 1+ fish occurred in the Artificial Island region approximately a month earlier and at higher densities than the 0+ individuals.
The first occurrence was in mid-October.
The leading edge occurred at approximately rkm 50.
Densities were as 3
high as 0.105/100m,
B.
(Jan. 16-18) The maximum southward movement appeared to occur by mid-January.
Notice that the bulk of the population had moved through the Artificial Island study area and to the south as far as rkm 30.
By compari' son, the furthest extent of the 0+ fish was only to rkm 60.
C.
(Mar. 24-27) By late-March most of the population had moved northward.
The retreat appears to be more advanced than for the 0+ during the same time period.
D.
The complex shape of the cyclic corponent is likely the result of this dif ferential temporal-spatial movement.
v The sharp fall peak probably results from a more nearly synchronous southward movement of all age classes.
The shallow dip probably is the result of the older fish proceeding through the study area while the 0+ fish remain.
The protracted low peak and sharp decline is likely the result of a less synchronous upriver movement.
X I *.
Interpretation of the Tend Componet The second greatest source of variance in our data arises from the trend component.
The interpretation of this component is the most important consideration from a management standpoint, but at this point, is the one that requires the m'st speculation.
o There are numerous factors which could cause or contribute to a population decline of this magnitude.
However, the analysis seems to suggest a mechanism operating over at least a moderate period of time and that there is relatively constant reduction each year.
l l
One potential factor which deserves further investigation is.
l l
the degraded water quality between rkm 132 and 161.
l l
Although lessening in recent years, a seasonal pollution condition exists in the Philadelphia-Camden region wherein, during late spring through late summer, dissolved oxygen levels may become lethally low.
Combining our data with 1
I
that of several other investigators indicates that most spawning occurs in the Burlington-Trenton region.
Spawning takes place in late May-early June and with growth there is a progressive down river movement.
By mid-June most of the larvae are centered near rkm 189.
Further downriver displacement could bring life stages with little or no avoidance capability into this region of poor water-quality.
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214
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J.,
Time-Series Analysis An Annotated Bibliography with Special Emphasis on Fisheries Biology Compiled by Alan W. Wells, Ph.D.
Ichthyological Associates, Inc.
Middletown, DE 19709 General References Anderson, T. W.
1971.
The statistical analysis of time series.
John Wiley & Sons, Inc., NY.
1 Thorough coverage.
Chapter 4 deals with cyclical trends.
Bloomfield, P.
1976.
Fourier analysis of time series:
An introduction.
John Wiley & Sons, Inc., NY 258 p.
Readable text but requires calculus to obtain full benefit.
Includes FORTRAN listings.
4 Box, G. E.
P.,
and G. M. Jenkins.
1970.
Time series analysis, forecasting and control.
Holden Day, San Francisco, CA.
575 p.
Thorough and detailed development of autoregressive (AR), moving average (MA) and mixed (ARIMA) time ~ series models.
Box, G. E.
P.,
and G. C. Tiao.
1975.- Intervention analysis with applications to economic and environmental problems.
J.
Am. Stat. Assoc. (Theory and Methods Section) 70:70-79.
I Technique for comparing a time. series before and after an intervention.
An intervention may be an event such as the passage of a law, br!.nging a power plant on-I line, etc.
Davis, J. C.
1973.
Statistics and data analysis in l
geology.
John Wiley & Sons, Inc., NY.
550 p.
Readable discussions of procedures for analyzing serial events, both temporal and spacial.
Includes filtering, l
autocorrelation, cross-correintion, Fourier series, l
double Fourier series, and m3pping techniques.
Fuller, W. A.
1976.
Introduction to statistical time series.
John Wiley & Sons, Inc., NY.
470 p.
l Rigorous treatment of ARMA and spectral theory.
I.A. Research/ Consulting i
s.--,-
c-
,r,,,.--,---.--,-,,-,-
i'.. ',
- Hipel, K. W.,
D.
P.
Lettenmaier, and A. I. McLeod.
1978.
Assessment of environmental impacts, part I:
Intervention analysis.
Environ. Manage. 2:529-535.
Not seen.
Bull, C. H. and N. H. Nie (eds.).
SPSS update 7-9.
New procedures and facilities for releases 7-9.
McGraw-Hill Book Co., NY.
402 p.
Release 9 of SPSS contains a Box-Jenkins procedure for identification, estimation, and forecasting of univariate time series.
Pfaffenberger, R. C. and J. H. Patterson.
1977.
Statistical methods for business and economics.
Richard D.
Irwin, Inc., Homewood, IL.
750 p.
Good, simple introduction to classical time-series analysis and forecasting.
Includes classical decomposition, seasonal indices, moving average forecasts, exponential smoothing, sinusoidal models, and autoregressive approaches.
- Platt, T.,
and K.
L.
De nman.
1975.
Spectral analysis in ecology, p. 189-210.
In R. F. Johnston et al.
(ed.).
Annual review of ecology and systematics.
Annual Reviews Inc., Palo Alto, CA.
1 Readable review of general principles and methods of spectral analysis.
- Ripley, B.
D.
1981.
Spatial statistics.
John Wiley &
Sons, Inc., NY.
252 p.
Mapping of spatial distributions can be considered.a two-dimensional extension of time-series analysis.
l l
Many techniques are common to both.
SAS Institute Inc., SAS/ETS user's guide 1980 edition.
Econometric and Time-Series Library.
SAS Institute Inc., Cary, NC.
User's guide for running various time-series models under SAS.
l f
i I.A. Research/Conalting I
I l
Fisheries Applications Jensen, A. L.
1976.
Time series analysis and forecasting of Atlantic menhaden catch.
Chesapeake Sci. 17(4):305-307.
Utilizes a second order autoregressive model for year ahead predictions of catch and associated confidence intervals.
Mendeltschn, R.
1981.
Using Box-Jenkins models to forecast fishery dynamics:
Identification, estimation, and checking.
Fishery Bulletin 78(4):887-896.
Excellent example of Box-Jenkins ARIMA approach applied to Hawaiian skipjack tuna landings.
Includes model identification, parameter estimation, model validation and estimation of transfer functions.
Rust, B. W. and B. L. Kirk.
1978.
Inductive modelling of population time series.
P. 154-192 In H. H.
Shugart, Jr. (ed.), Time series and ecoT5gical processes.
Soc. Industrial and Applied Mathematics.
Includes an example utilizing both classical Fourier techniques and Maximum Entropy Spectral Analysis (MESA) to estimate long term periodicity in striped bass landings.
l Saila, S.
B., M. Wigbout, and R. J. Le rm it.
~19 8 0.
l l
Comparison of some time series models for the analysis l
of fisheries data.
J. Cons. Int. Explor. Mer. 39:44-52.
Not seen.
Stocker, M. and R. Hilborn.
1981.
Short-term forecasting in marine fish stocks.
Can. J. Fish. Aquat. Sci.
38(10):1247-1254.
Predictive power of stock production models and simple time series methods was compared for five marine fish stocks.
l Thompson, K. W.,
et al.
1982.
Application of time-series intervention analysis to fish ventilatory response data.
Can. J. Fish. Aquat. Sci. 39(3):518-521.
Demonstrates use of intervention analysis in detecting changes in fish ventilatory response to changes in water quality.
I.A. Research/ Consulting
(
l
Van Winkle, W.,
B. L. Kirk, and B. W. Rust.
1979.
Periodicities in Atlantic coast striped bass (Morone saxatilis) commercial fisheries data.
J.
Fish. Res.
Board Can. 36(1):54-62.
Classicial Fourier spectral-analysis and Maximum Entropy Spectral Analysis (MESA) methods are compared using commercial landing data for striped bass.
l l
l I.A. Research/ Consulting l
4 THE USE OF LABORATORY BEHAVIORAL AND TOLERANCE DATA IN THEF.vM, IMPACT ASSESSMENTS a
By John W. Meldrim Ichthyological Associates, Inc.
Middletown, Delaware o
A paper presented as'part of a symposium:
" Fish Behavior Studies-Can They Aid Environmental Impact Assessment?"
conducted at the 110th Annual Meeting of the American Fisheries Society Louisville, KY, 21-24 September 1980 23 September 1980 M
1 l
The Use of Laboratory Behavioral and Tolerance Data in Thermal Impact Assessments by John W. Meldrim Ichthyological Associates, Inc.
Middletown, Delaware 23 September 1980 In assessing the impact of a thermal discharge it is of ten necessary to predict how aquatic organisms would respond under specific environment conditions.
Often this can only be accomplished using laboratory data; especially when field conditions do not accommodate the investigator and required field data are inadequate or impossible to obtain at the time.
The most common thermal impact assessment in recent years is the 316(a) demonstration.
Section 316(a) of the U.S. Federal Water Pollution Control Act provides for non-compli'ance of strict thermal effluent limitations if the discharger can demonstrate such limitations are "more stringent than necessary to assure the protection and propagation of a balanced indigenous community of shellfish, fish, and wildlife" in or upon the receiving waters.
The balance indigenous community has come to be represented by
" Representative Important Species" - generally fishes.
If I
the thermal discharge is into " despoiled waters", in which the selected representative important species are not yet representative, or if field data are insufficient, laboratory data can be effectively used to estimate the pkh 67'~
response Ao-the RIS to the discharge.
(
t c
n
2 Utilization of laboratory behavioral data has been accepted for incorporation in 316(a) demonstration " Plans of Study" by the USEPA and by at least one state (New Jersey).
As a usual part of these demonstrations the " passage and maintenance" of representative fishes must be assured.
We have utilized both behavioral temperature preference and avoidance data and cold shock tolerance data in numerous such demonstrations.
In conjunction with thermal plume maps, life history and species distribution information, these laboratory data can be used to estimate the potential loss of habitat, blockage of migratory routes, or mortality due to sudden plant shutdown for a species on a seasonal basis.
This potential use of laboratory data in thermal impact assessments has been previously suggested and published by my friend and former colleague, Jim Gift.
Rather than reiterate his presentation for this symposium I want to illustrate some of the ways behavioral data can be used to evaluate the effects of a thermal discharge.
For this illustration I will use the plume data for a hypothetical power plant which was described some years ago by Chuck Coutant, and is shown in the " Blue Book", and real data for two typically RIS estuarine fishes, the white perch, Morone americana; (SLIDE 1) and the Atlantic silverside, Menidia menidia.
(SLIDE 2) Although this illustration is for a thermal impact, the technique can be applied to other types of discharges.
3 We begin with the thermal plume.
(SLIDE 3) This is the
" Blue Book" Hypothetical Generating Station which I have named the "Coutant Station".
Note that it is unique in that it has one intake and two separate thermal discharges:
a long discharge canal and a " rapid dilution" submerged discharge.
The AT across the condensers is a typical 10 C.
This AT does not dissipate much in the long discharge canal, but rapidly declines in the submerged discharge to a 5 C maximum.
Question:
What are the predicted impacts of these respective plumes on the maintenance and passage of the white perch, and the Atlantic silverside? We will assume that the "Coutant Station" is located on a typical mid-Atlantic meschaline estuary which has an annual temperature cycle from about 4-28 C and that populations of both white perch and Atlantic silverside may be present in the vicinity of the plumes throught the year.
Now fishes, being motile, may respond in three ways when they encounter a thermal plume.
They may prefer it, avoid it or simply pass through it with only slight physiological adjustements.
As far as maintenance and passage is concerned we will only examine plume preference, its potential consequences, and plume avoidance.
Looking first at preference effects I will assume temperature preference data are available over the range of acclimation or ambient temperatures each species may be g'/'
affected by the plume (in this case about 4-C).
The data f
s
E 4
I will present were determined in a typical horizontal gradient (SLIDE 4) with one data point (or preferred temperature) determined for a group of 3-4 fish.
Similar l
data can be obtained by other techniques.
Ovet-hy l (SLICE 1) Plotting the data so that the preferred temperatures are plotted against acclimation we can draw the respective plume maximum AT's on the graph.
A regression line (in this case a quadratic) can also be shown.
The data in this scatterplot are for the Atlantic silverside.
The number of data points for each preferred temperature is shown numerically.
At ambients up to about 14 C, the maximum
..? of the discharge canal (10 C) may be preferred; while Atlantic silverside could prefer the maximum available aT of the rapid dilution discharge up to ambients of 20 C.
OFOy%
(EL!D-1-) The white perch on the other hand might prefer the A10 C up to ambients of 23 C and the 65 C up to 25 C.
However, the final temperature preferendum of the Atlantic silverside is about 26 C and that for white perch' is about 31 C.
Using taese, other things being equal, the canal maximum AT (10C) would only be preferred by white perch at ambients up to 21 C (instead of 23 C) but by Atlantic silverside at ambients up to 16 C (instead of 14 C).
The rapid dilution 65 C would be preferred by Atlantic silverside at ambients up to 21 C (instead of 20 C) and by white perch at ambients up to 26 C (instead of 25 C).
Not much difference, really, from the estimates based on the
5 total scatterplot.
Knowing all this we could procede to L/
makeallkindsofprodhndstatementsregardingthe consequences to the fish of preferring the plume or the discharge canal.
However, there is only one consequence I wish to touch on here; that is cold shock.
Because plant shutdown and its resulting cessation of the thermal plume is not a planned operation in most cases, the potential effects of cold shock are generally best obtained from laboratory data.
These data are usually obtained using standard bicassay procedures to determine a lower lethal threshold temperature.
Such tests are not behavioral in the context being discuss d and I wish to consider them only in passing for illustrative purposes.
Behavioral tests, such as the predator-prey studies conducted by Chuck Coutant at Oak Ridge, were presented this l
morning.
However, if a large number of RIS species are to be evaluated, these studies can be quite complex, and we may discuss them later.
l To determine the potential for cold shock with our two RIS for the Coutant Station I have plotted the data for cold l
shock tests which resulted in 30% or more mortality.
The 30% point was arbitrarily chosen as one which represents an OMy'3 experimental effect.
(CLIr_
) In these scatterplots l
experimental I. ambient) temperature is the Y axis and l
acclimation (or plume) temperature is on the X.
Looking first at Atlantic silverside we can see the potential for l
l cold shock in the discharge canal exists when ambient 1
l L
d
6 c
temperatures are 19 C or below; and in the rapid dilution discharge 35 C at ambients below 11 C.
However, velocity of the rapid discharge may preclude availability of the AS C.
090dt (SLIr!y,j) White perch, on the other hand, would not experience cold shock in either discharge system.
Probably the most detrimental behavioral impact of a thermal plume is the loss of habitat (or space) due to avoidance.
Plume avoidance can cause blockage of migration but usually results in little more than loss of some habitat.
The temperature avoidance data I will present here were determined in a modified Shelford-Allee design (SLIDE h)usinga2:1timeratioasthecriterionofavoidance.
The design utilizes a thermal " step-gradient" and yields two data points per test.
0"dt (SLIO /,Egg) Looking first at the results for Atlantic n
silverside, the avoidance temperatures are'again scatterplotted against acclimation with the number of avoidance data points at an acclimation indicated numerically.
The a5 C and A10 C lines are shown as well as the quadratic regression line.
Although avoidance of the A10 C discharge canal may occur at ambients as low as 13 C, avoidance is not expected at ambients bel'ow 20 C.
Only the highest avai14 Die submerged discharge ar (5 C) would likely be avoided and only when ambient reached 27 C.
Oreels i
'EL!O]'si As for white perch, surprisingly some g
avoidance of the maximum cr's of both plumes may occur during winter.
However, avoidance of the 610 C is not J
y expected until amibent reaches 22 C and avoidance of the A5 C is not expected until ambient is 28 C.
To interpret what these avoidance data mean for the respective Coutant Station discharges we return to the plume to plots.
(SLIDE
) Looking first at a median cross section plot of the discharge canal plume we see it goes shore to shore.
(SLIDE ITherespectivepercentcross-sectional area and surface width are determined for each AT of the plume.
The percent volume within the affected reach can also be calculated for each AT.
However, lacking a model of the plumes I will consider only the cross-sections and surface widths for purposes of illustration.
Using these one could predict from the lab data that when ambient temperature reaches 20 C, and the A10 C is avoided, about 1%
of the cross-sectional area and about 4% of the surface width will be denied to Atlantic silverside.
Avoidance of the A10 C and the above stated habitat loss would not occur I
with white perch until ambient reached 22 C.
At the maximum summer ambient of 28 C when both species begin to avoid the A5 C about 34% of the cross-section and about 47% of the l
width would be denied as habitat.
(SLIDE hLookingatthemediancro'ss-sectionplotof the submerged rapid dilution thermal plume, much less of the receiving water is affected.
(SLIDE t Recalling that only at the maximum summer ambient of 28 C was the maximum available 5 C AT avoided by either of our RIS, this means l
that only about 1% of the cross-section and 2% of the l
l surface width would be denied habitat.
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8 Clearly, then, the submerged discharge has less impact than the discharge canal.
But, of course, you already knew that.
What I hope to have illustrated is the relative magnitude of the difference.
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