NC0044725_Report_19850905

NPDES DOCUMENT SCANNING COVER SHEET
NC0044725
LMAC WWTP
NPDES Permit:
Document Type:
Permit Issuance
Wasteload Allocation
Authorization to Construct (AtC)
Permit Modification
Complete File - Historical
Engineering Alternatives (EAA)
Correspondence
Owner Name Change
Report
Instream Assessment (67b)
Speculative Limits
Environmental Assessment (EA)
Document Date:
September 5, 1985
This document is printed on reuse paper - ig7nore any
content on the reirerise side

f/uvi° cz-(,-
State of North Carolina
Department of Natural Resources and Community Development
Division of Environmental Management
512 North Salisbury Street • Raleigh, North Carolina 27611
James G. Martin, Governor R. Paul Wilms
S. Thomas Rhodes, Secretary September 5, 1985 Director
MEMORANDUM
TO: Mick Noland
Dennis Ramsey
FROM: Steve W. Tedder
SUBJECT: Toxicological Evaluation/Laurinburg-Maxton
Airport Commission WWTP
Attached is the final report concerning an intensive toxi-
cological evaluation of the Laurinburg-Maxton facility in Scotland
County.
If there are any questions, please contact myself or Ken
Eagleson at 733-5083.
SWT/gh
Attachment
cc: Ken Eagleson
Larry Ausley
Bob DeWeese
Meg Kerr
Jay Sauber
Jim Overton
Pollution Prevention Pays
P.O. Box 27687, Raleigh, North Carolina 27611-7687 Telephone [phone]
An Equal Opportunity Affirmative Action Employer

LAURINBURG/MAXTON AIRPORT WWTP
TOXICITY EXAMINATION
NPDES #NC0044725
C1I1U{ffl) IHHffl)
North Carolina Department of Natural
Resources & Community Development
MOBILE
Bioassay and Biomonitoring
LABORATORY
NORTH CAROLINA DEPARTMENT OF NATURAL
RESOURCES AND COMMUNITY
DEVELOPMENT
WATER QUALITY SECTION
SEPTEMBER,1985

LAURINBURG-MAXTON AIRPORT COMMISSION
WASTEWATER TREATMENT PLANT
NPDES NO. NC0044725
April, 1985

TABLE OF CONTENTS
Page
List of Tables
List of Figures ii
Introduction 1
Toxicity Examination 2
Chemical Sampling _ 10
Benthic Macroinvertebrate Analysis 13
Conclusions • _ 23
Recommendat ions _ • 24
Appendix 25
- Daohnia pulex Test Procedure �... •26►
- 96 Hour Flow -Through Teat Procedure... 27
- Ceriodeohnie Reproduction Test Procedure 19
- Benthic Macroinvertebrate Procedure 30

LIST OF TABLES
Page
Table 1. Final Mortality Results of 96 Hour Flow -Through Test 4
Table 2. Sampling Site Descriptions 8
Tabte 3. Results of Chemical Analyses 11
Table 4. Benthic Macroinvertebrate Taxa Collected.... 17
Table 5_ Benthic Macroinvertebrate Taxa Richness. 22
LIST OF FIGURES
Page
Figure 1. Schematic Diagram of Laurinburg-Maxton Airport WWTP 3
Figure 2. 96 Hour Flow -Through Test Mortality 5
Figure 3. Mean Cumulative Reproduction of Ceriodaohni=e< Test ;.. 7
Figure 4. Study Area and Sampling Locations 9

INTRODUCTION
An on -site toxicity examination was conducted at the Laurinburg-Maxton
Airport Commission Wastewater Treatment Plant (NC0044725) April 1-6, 1985.
This investigation was accomplished to provide baseline toxicity data on the
wastewater treatment facility in order to evaluate the effects of proposed
future additions to the industrial contributors to the facility. This facility,
located in Scotland County, treats primarily domestic and industrial wastewater
from nearby industries. These industries discharge approximately 219 thousand
gallons of wastewater each day to the Laurinburg-Maxton Airport facility for
-trea-tment. Individual contributions of these facilities are listed below.
Carolmet, Inc. (cobalt ore processing) 151,000 GPD
Johns Manville (fabricated rubber prod) 12,000 GPO
Charles Craft (textile) 16,000 GPD
Lee L. Woodard (metal fabrication) 17,000 GPD
Scotland Mfg. (metal fabrication) 23,000 GPD
This document details findings of chemical and biological sampling,
including the following:
1.) 48 hr. static bioassay using paohnia,eulex on effluent samples to
determine acute toxicity.
2.) 96 hr flow -through acute bioassay using Pimephales promelas (fathead
minnows) performed on effluent collected at the final clarifier prior
to chlorination.
3.) Chemical samples collected from effluent, influent, and receiving
stream.
4.) Collection and analysis of macroinvertebrate samples to determine the
impact of the effluent on the receiving stream populations.
5.) Seven-day Ceriodaohnia reproduction test to assess sub -lethal (chronic)
toxicity.

The Laurinburg-Maxton Airport WWTP discharges into the Lumber River (Class
"C") in the Yadkin/Pee-Dee River Basin. The 7010 (low flow) for the Lumber River
is 130 cis. The permitted flow of the facility is 1.0 MGD. During 7010 low
stream flow and average permitted effluent flow conditions, the effluent from
Laurinburg-Maxton Airport WWTP comprises 1.2% of the receiving stream. Results of
past compliance sampling inspections have recorded permit violations in levels of
TSS, sodium, cobalt, and pH.
Waste treatment processes include bar screening and grit removal, aeration
by oxidation ditch, clarification, chlorination, and sludge drying beds. A
schematic of the Laurinburg-Maxton Airport WWTP appears in Figure 1.
TOXICITY EXAMINATION
An on -site toxicity examination was requested for the Laurisnburg-Maxton
Airport WWTP by the Division of Environmental Management's Fayetteville. Regional
Office. The request was made in anticipation of future Increases in the number
of industries the facility serves. One 48 hour static test was performed prior
to the examination on October 20, 1983. This test yielded an LC..o value of 71%.
A second test was performed on the effluent april 29, 1985 with an LCso result of
83% The LCso value is the effluent concentration lethal to 50% of the teat
organisms.
The flow -through bioassay was performed on effluent collected prior to
chlorination at the final clarifier. Dilution water for this teat was obtained
from Juniper Creek at SR-1405 in Scotland County.
The flow -through bioassay was initiated at 9:40 A.M. on April 2, 1985. The
test organisms, fathead minnows, were 26-31 days old and obtained from cultures
at the Aquatic Toxicology Laboratory. These fish were acclimated to Juniper
Creek water on March 28.1985. The fathead minnows were transferred to test
chambers with dilution water approximately 20 hours prior to test initiation.

Grit Chamber
tf Iuent
Bar Screen
Influent Sampling Pt.
(Station 02A)
Discharge
FIGURE 1. LAURINBURG— MAXTON AIRPORT
Chlorine Contact
WWTP SCHEMATIC DIAGRAM
-3-
Bioassay Sampling
Pt. (Station 02)

Ten fish were placed In each chamber with replicates of six concentrations end a
control (dilution water). The toxicant delivery system cycled 372 times during
the course of the test. The final 96 hour mortality data is as listed In Table
Table 1. Final Mortality Results of 96 Hour Flow -Through Test
Effluent Concentration No. of Organisms Mortality
100 10 4
100 10 6
75 10 4
75 10 1
50 10 1
50 10 2
25 10 2
25 10 2
10 10 0
10 10 0
5 10 0
5 10 0
C 10 0
C 10 0
This data is depicted graphically in Figure 2. The 96-hour LC•o value was
-determined to be 100%. This value indicated an effluent concentration of 100%
will cause a 50% kill of the test population within a 96 hour period.

Toxicant
Concentration
Figure 2. 96 Hour Flowthrough Test Mortality
9
8
7
6
5
4
3
•
a
1
1
LC =100
50
0 10 20 30 40 50 60 70 80 90 100
%Mortal ity

A seven-day Ceriodaohnia static replacement bioassay was performed on
dilutions of effluent in order to assess sub -lethal toxicity. This test was
conducted at the Aquatic Toxicology Laboratory using dilution water obtained from
Lake Johnson (Raleigh, N.C.). This dilution water was chosen for the test in
light of the low pH of the dilution water used on -site (Juniper Creek). Data
from this teat is presented in Figure 3. At the end of the seven day test
period, a significant reduction in reproductive success of the test organisms was
noted at the 10% effluent concentration. Reproduction similar to that of the
controls was recorded for the 0.01%, 0.1%, and 1.0% effluent concentrations.
Reproductive success at the 25% and 50% concentrations were drastically reduced
to mean values of 0.6 and 0, respectively. No significant mortality was noted in
any of the test concentrations up to the highest tested of 50%. Since the
on -site Investigation was conducted, two additional self -monitoring bioassays
have been accomplished by this facility. Test results of June and July showed
Daphnia pules, LCso values of 89% and 72% respectively. These values compare
closely to the 71% LCso measured by DEM prior to the on-s4te investigation.

25
20
15
10
Oi
Figure 3.Mean Cumulative Reproduction
Ceriodaphnia Chronic Bioassay
Mean Young Produced
Significant chronic
impact at
10.0% effluent
0 2
4
Day of Test
8
LAURINBUiG-fAXTON AIRPORT MP
Control
0
0.01 t
0.10t
•
1.0%
10. 0%
O
25. 0%
50. 0%
■
-7-

Table 2. Sampling Sites
Station 01 Lumber River at NC-71 approximately 175 meters above the
Laurinburg-Maxton Airport WWTP. At this point the Lumber River is
approximately 25 meters wide with a sandy substrate.
Station 02 Laurinburg-Maxton Airport WWTP collected from the final clarifier,
prior to chlorination. This is the bioassay sampling point for
the Daohniapulex static testa, Ceriodaohnia reproduction teats,
and the flow -Waugh bioassay.
Station 02A Laurinburg-Maxton Airport WWTP influent collected immediately
prior to the bar screen.
Station 028 Laurinburg-Maxton Airport WWTP effluent collected at end of the
chlorine contact chamber.
' Station 03 Lumber River at SR-1303 approximately 6400 meters below the
Laurinburg-Maxton discharge. At this point the Lumber River is
approximately 30 meters wide with a sandy substrate.
Station 04 Juniper Creek at SR-1405. Here the substrate is sandy with bottom
vegetation and the creek is approximately 4 meters wide. This is
the dilution water site for all site bioassays.

Figure 4. Laurinburg—Maxton Airport WWTP Study Area

CHEMICAL SAMPLING
A series of chemical samples was collected during this evaluation and sent
to the Division of Environmental Management Chemistry Laboratory for analysis. A
description of the sampling stations is found in Table 2. All samples were
collected as instantaneous grabs with the exception of Station 02 samples
(toxicity sampling point) which were taken as 24 hour composites. Figure 4
contains a map of the study area and includes sampling site locations. Results
and summaries of chemical analyses are documented in Table 3.
Metals analyses reported zinc concentrations of 150 ug/1 on April 3 and 280
ug/1 on April 6 in the effluent. At these concentrations and 7010 conditions,
the concentration in the receiving stream would average 2.53 ug/1. At average
stream flow and average facility flow, the instream concentration of zinc is
estimated to be .205 ug/I. The N.G. Water 0uality Action Limit for zinc is 50
ug/1. Zinc concentrations of 90 ug/1 and 120 ug/I were detected in the influent
on April 3 and April 6 respectively. All other sites had concentrations of (20
ug/I on both sampling dates, which is the lower detectable limitfor zinc.
Metals analyses also reported copper concentrations in the effluent of 40
ug/1 on April 3 and -60 ug/I on April 6. At low flow conditions these would
indicate an instream average concentration of 0.59 ug/I of copper. Levels of 30
ug/I and 80 ug/l (April 6) were detected in the influent. Upstream, downstream
and dilution water sites were found to have (20 ug/1 of copper which is the lower
detectable Limit. At average stream flow and average facility discharge, copper
concentrations instream are predicted to be .048 ug/I. The N.C. Water Duality
Action Level for copper is 15 ug/1.
Organics analyses revealed influent concentrations on April 3 of 420 ug/1
butanoic acid, 170 ug/1 of chloromethyl benzene, 1200 ug/I of isooctanol, 700
ug/l of trichlorobenzene, 90 ug/I of butyl octanol, 430 ug/I of phosphoric
tributyl ester, and 11,000 ug/1 of a petroleum oil and other unidentified peaks.
—10—

Table 3. Results of Chemical Analysis
A
1
C
0
j E
F
0
N
I
PERNITTEO FLOAT (KAX)
1
AVE1OGE OISA3ARRCE (AGO)
.2a3
AVERAGE511(0O FLOAT (ff S)
460
7Q10 (ffS)
130
Olenictl/Faysicsl
units
' Aster Quality
Station 01
Station 02
Station 021
Station 028
'Station 03
Station 04
Analyses
Standards
85/04/13
85/04/03
15/04/03
85/04/03
85/04/03
85/04/03
I:::
PPO
1
5.4
no1
1.1
FF8
17
4a
230
17
16
:Califon: OF Fecal
!100 rl
6200
2800
1401000
20
11000
Califon: Tube Fecal
11
lesidae. TOT11
PPO
57
1300
1100
63
33
• volatile
PPR
41
140
230
44
30
• fixed
FPO
13
1200
1500
19
3
;Reside SOSFEO0E0
PPS
11
20
23
9
7
volatile
PPS
7
16
20
5
5
fixed
FPN
4
4
3
4
2
4
"O (standard wits)
6.01.0
6.9
8.1
7.9.
6.4
5.6
Oddity
PPN
1
5
6
7
14
Alkalinity
PPR
10~
460
410
10
3
4
Chlorides
PPO
7
380
390
4,
7
4
loftiness
FPO
12
36
40
32
16
'Phenols
FPO
<5
<5
30
<5,
<5
<.011
WO
PPO
.03:
.5S
1.6,
.04
"TAN
PFO
.3
1.3
4.3
.3
.2
102,103
FPO-
.4
.19
.18
.42
.14
P. total
FPO
.1
15
16
.14
.03
Aleniaoa
PP8
<100
<in
<100
<100
<101
'Caddell
FP8
2
<20
CO
<20
<20
c20
Chronic' I
FPO
50
<50
<50
<50
<50
<50
,Cobalt
FP8 1
1000
<100
300.
3200
<100
<100
Copper
PM
- 15(11)t
<20
40
30
<20
<20
Iran a
FPO
1018(AL)
300
300
500'
410
2408
'1Aercary
FPO
.2
<.2
<.2
<.2
(.2
,
Nickel
FPO
50
<100
<100
<100
<100
<100
Lead
FPO
25
<100
<100
<100
<100
<100
Zinc
PP8
50(11)
<20
150
90
<20
<20
1ri 1utyl Tin lyydride
PP8
.0th
<.02
<.02
(.02
c.02
<.02
Oaideatified- Orsardc Peeks
6
1
3
101E
'Botanic Add
FM
420
CAlormketby1 benzene
FPO '
190
Iseoctsuol
PHI
1200
yTridllorobeazeoe
FPO
NC-
1 att0501
�Phot$aric
PP8
30
tributyl ester
PHI
430
Petrslees sil aideat.peaks
FPI
11000
leszeoedicarbssylicsdd, -
ittosyttkylaster
FPO
$ eeedinrbeuy c;,-
dioctylester
FPO
_
t (AL) Values represent action levels as specified in .0211 (6)(4)
Fresh Water Classifications Standards.

Table 3. (Cut:)
1
K
L
8
0
0
P
o
a
1
PERMITTED ROD (IIGO)
1
AVERAGE DISCHARGE (S130)
.283
AVERAGE STREAM fUOY (CFS)
460
•
7g10 (CFS)
130
Chtnical/Physicsl
snits
Station 01
Station 02
Station en
Station 03
Station 04
Predicted Mark
Predicted stress*.
Analyses
15/04/86
, 85/84/06
85/04/06
85/04/06
85/04/05
canaaVetien at
anceatretl� et
7010 creditless
eve.disdterge t fie
PM
20
138
2380
17
15
Califon: if fecal
/180 N1
Fanfare: Tube Fecal
Resides. TOTAL
FPI
78
1308
2180
53
30
15.32
1.238
volatile
PPO
32
188
558
25
17
1.81
.152
fixed
PPS
38
1180
1108
28
13
13.55
1.535
Residue SOSPEEEO
PPI
7
50
360
12
3
.65
.052
volatile
-PM
4
66
340
3
' 3
.48
.533
fixed
_ PPO
3
24
14
3
<1,
.15
.013
,11 (standard nits)
6.7
7.5
7.8
6.1
6.1
Oddity
PP6
7
2
25
5
Alkalinity
PPI
3
340
350
0
5
Chlorides
PPM
8
370
520
8
3
Oardness
MO
60
64
68
10
30
Phenols
PPS '
(5
<5
8
<5
4 _ <5
4:5
<5
*1113 ,
- FPI
.04
.11
3.3
.04,
.51
.5814
.0001
Ta
fM1
.4
3.5
6.1
.3
.3
.83
.002
Kft,503 _
PPA•
.44
- ' 1.7
.34
.42
.15
, .01
.801
P. total
PPII
.11
16
15
.1
.02
.16
.015
aliNiaEUE
'Cadmium
-FPO
- 180
480
200'
200
100'
<100
<1011
-PP8
<20
<200
<2
<20
<20
<20,
<20
CAteulan
FPO
(50.
<50
<50
<50
,
<50
<50
<50
Cobalt
'CoPrier
4
PP8
3.53
.285
PP8
<20
60
_
f0
<20
<20
.51
.048
Ina ,
!P5
300
750
4250
3804.
250,
5.53
.475
8ermry
FPO-
<.2
.2
<.2
<.2
<.2
<.2
<.2
ilidcel
fP8
<100-<100
<100�
<108
<100
<180-
(100
Lead
PPS
<100
<100
<180
<100
<100
<100
<100
Zinc
PP8
<20
280
120
<20
<20
2.53
.205
4Tri Butyl Tie Mydride
FPO
(.01
4.01
4.01
(.01
<.02
(.02
(.02
Unidentified -Organic Peaks
Malt
+
15
2
8011E
4 eceaic Acid
PP8
Chloranethyl Wrest
PP8
_
14 Iseactaaol
PP8
Tricalarobee:ene
PP6-
-
IIdyl aCtanol
PP 8
Ptoric trlbetyl ester
PP8
htreleav eillei/eet.peeks
PPI
tlenzeaedicerboxylicac1d,-
,
botexyetbylbeyletter
1P8
12
leaseneditarboxylies•
dlectylester
PP8
740
* This value represents predicted instream concentrations using average
effluent concentrations and assuming upstream concentrations of 0.
***** Sample not analyzed.

The April 6 influent contained 16 unidentified organics ranging from 14 ug/I to
7100 ug/I. Trichlorobenzene is used largely as a dye carrier or
herbicide intermediate and is an EPA priority pollutant. Isooctanol is
used as a plasticizer, an antifoaming agent, and a surfactant. Uses of
chloromethyl benzene include a solvent agent for intermediate organic
chemicals and dyes. Analysis of the April 3 effluent sample found one
unidentified organic substance at 15 ug/i. Organics were not performed on the
second day's effluent sample due to laboratory problems.
BENTHIC MACROINVERTEBRATE ANALYSIS
Benthic macroinvertebrates were collected on April 3 and 4, 1985 at three
locations on the Lumber River in conjunction with a flow -through bioassay
performed at the Laurinburg-Maxton WWTP. The Lumber River meanders through the
coastal plain in this area and is considered a kblackwater" river due to leaching
of tannic acids from backwater and swampy areas along its banks. The section of
the river sampled was about 10-20 meters wide and 1-3 meters deep. Numerous
snags provided good habitat for the benthic fauna.
Samples were collected using the Division of Environmental Management's
standard qualitative collection techniques (DEM 1983) at the NC-71 bridge (above
the WWTP) and at the SR-1303 bridge (approximately one-half mile downstream and
below the discharge point of the WWTP). The third sampling site was another
one-half mile downstream, at the SR-1393 bridge. Deep water at this third
station required using a boat to collect samples here, resulting in a
semi -qualitative collection (all samples taken except kicks).
The sample at Station. 01, above the WWTP, yielded a total taxa richness
value (ST) of 95, and a taxa richness value for the intolerant groups
Ephemeroptera, Plecoptera and Trichoptera (Se'T) of 37. This site had a large
number of snags covered with podostemunt, and a lower flow backwater area with

much detritus. These two habitats were both diverse and productive. Some taxa
from all the major benthic groups were found to be abundant. The dominant taxa
were mayflies (LeotoDhlebia, Eohemerella catawba, Furvloohelle
temDo►alis. Peeudocloeon, Stenonema modestum). a stone fly species,
Isooerle sp. 10, caddisflies (Cheumatoosvche, j'ivdroosvche decalda) and
dragonflies (CaloDterYx and Enallaoma). Also, most of the taxa in the intolerant
groups were common or abundant which is another indication of good water quality.
A complete listing of taxa found at all stations with their abundance is given in
Table 4.
Station 03, below the discharge from the WWTP, had a lower 8T value (76) and
a slightly lower SlpT (32) value. However, a change in the habitat at this
station, could account for the lower total taxa richness. This site had fewer
snags to sample, no backwater area, more exposed sand and less detritus. Most of
the intolerant taxa that were common or abundant at the other two stations were
also common or abundant below the discharge. This diversity and abundance
indicates that the WWTP discharge is not having a significant toxic influence at
this station. This is reinforced by the fact that the taxa not found at Station
03 were tither rare at the other locations or found associated with detritus or
low flow habitats not found here. Of the 139 total taxa from all three stations,
only 10 were collected at Stations 01 and 05 but not at Station 03.
Comparison of taxa richness values for major benthic. groups Viable 5) shows
the largest reduction at Station 03 occurred in the trichoptera. Again, the taxa
net collected at this site were found in the backwater and detritus areas of the
other stations.
Station 05, at SR-1393, was sampled using a boat, because the river was too
deep to allow for regular qualitative sampling. As a result more snags were
sampled et Station OS than et either Station 01 or 03. This may have influenced
the high Sap? value (39) recorded at this station. A total of 89 taxa were

collected with close to 60% of those being rare in abundance. Dominant organisms
were basically the same at this station as at the other stations. The high
proportion of taxa in sensitive groups (39/89) is another indication of a healthy
fauna. Heavy Podostemun growth on Togs provided a complex habitat, yielding many
of the organisms collected. Bottom sand was relative coarse and fairly
unproductive.
One mayfly, Ephemerella arco, was common at all three stations, but was not
previously recorded from North Carolina. It will be tentatively listed as a new
state record until verification of the species determination is made.
All three stations were given an Excellent biological classification using
the criteria for "Coastal A" (shallow, fast moving) rivers. The SfPT values for
all stations (Station 01 = 37, Station 03 = 32, Station 05 = 39) were well above
the criteria level of 27 for an Excellent rating. However, April is a time of
peak abundance for benthic macroiavertebrates. Winter species may still be
present, as well as the early fosters of the summer fauna. In order to determine
if these were seasonally high Selby values, a comparison was made with Benthic
Macroinvertebr-ate Ambient Network samples taken from the Lumber River at Pembroke
in July, 1983. That site was also given an excellent rating based on ST/SepT
values of 89/28. In the mayflies, the summer paetis species were replaced by
Ephemerella species, but other taxa were similar. The caddisfly taxa were also
similar during both sampling periods, however, five additional stonefly species
were present during this sampling which would not be present during the summer.
Even if these were subtracted out from the Sappy values, an Excellent rating would
still be given, although this ratomg wpiid be marginal for Station 03.
There was a minor reduction in benthic macroinvertebrates at Station 03,
below the discharge of the WITP. However, the high number of abundant taxa in
groups intolerant of.toxic and organic -effects indicated that the reduction in

total taxe richness was associated with habitat change, rather than any toxic
influences. Benthic macroinvertebrate sampling indicated excellent water quality
in this section of the Lumber River.

Table 4. Benthic Macroinvertebrates Collected from the Lumber River,
April 3 and 4, 1985 with abundance values (R. Rave, C =Common, A =Abundant )
Taxon
Stations
1 2 3
NC 71 SR 1303 SR 1393
Oligochaeta
LuMbric ulidae C C C
Limnodrilus hoffmeisteri R - -
Derodigitata C - R
Dero obtusa C - -
Nais sp. C R -
Slavina appendiculata - - R
Spirosperma carolinensis - A -
Quistadrilus multisetosus - - R
Vejdovskyella comata R - -
Ephemeroptera
Baetis pygmaeus C C C
Centroptilum sp. - R
Pseudocloeon sp. A A A
Stenonema modestum A A A
S. smithae C - C
S. exiguum - R -
S. integrum - R -
S. terminatum - C
Heptagenia marginalis R - C
Hexagenia sp. - - R
Siphlonurus marginalis A C R
Leptophlebia sp. A A A
Paraleptophlebia sp. R C R
Caenis sp. - R -
Ephetnerella argo C C C
E. Catawba A A A
Ebrylophe1la bicolor - C -
Eu. temporalis A A A
Dannella simplex C - C
-17-

Taxon
Stations
1 2 3
NC 71 SR 1303 SR 1393
Pleooptera
Acroneuria abnormis R R
A. mela C R
Amphinemura sp. C R
Prostoia sp. R -
Pteronarcys dorsata C C
Neoperla clymene C A
Perlesta placida C C
Perlinella n. sp.? C A
Isoperla bilineata C -
I.sp. 10 A A
A
Tiichoptera
Chimarra sp. R A A
Phylocentropus sp. C - C
Polycentropus sp. C R R
Nyctiophylax sp. - - _R
Brachycentrus sp. R - R
Lepidostoma sp. R - -
Lype diversa C - C
Macronema carolina - - C
Cheumatopsyche spp. A A A
Aydropsyrhe decalda A A A
H. venularis C C C
Cecetis sp. A A C
Nectopsyche exquisita R C -
¶1 iaenodes tardus A R C
Ceraclea nepha C R C
Ceraclea resurgens C R R
Ironoquia punctitissima R - -
Psilotreta sp. - C -
Odonata
Argia sp. R
Enallagma sp. A
Calopteryx sp. A
Gomphus spp. C
A
A
A
R
A
C
C

Stations
1 2 3
Taxon NC 71 SR 1303 SR 1393
Drom gomphhus sp. - - R
Progomphus obscura - R -
Hagenius brevistylus R R R
Boyeria vinosa - C R
Nasiaeschna pentacantha R - -
Macromia sp. R C C
letragoneuria sp. C R C
Somatochlora sp. - C -
Libellula sp. - R -
Coleoptera
Ancyronyx variegatus R - -
Macronychus glabratus C C A
Dubiraphia quadrinotata - - R
Optioservus sp. - R -
Stenelmis sp. C A A
Dineutus sp. R C -
Berosus sp.` - - R
Peltodytes sp. R - C
Hydroporus sp. A R A
Hydrobius sp. R - -
thochrus sp. - - R
Megaloptera
Corydalus cornutus - R R
Climacia areolaris
Crustacea
Palaemonetes paludosus
Procambarus sp. - R
Asellus sp. A R
Hyallela azteca - C
CrangonYx sp. R A
Diptera
Tipula sp. R C
Simulium (phosterodorus R R
group)
SNP ,M11,
MOD
IMM
-19-

Taxon
Stations
1 2 3
NC 71 SR 1303 SR 1393
Chrysops sp. R - -
Pseudolimnophila sp. R -
Palpomyia group C - C
Corynoneura C R R
Th enemaniella sp. R C -
Cticotopus bicinctus gr. R - A
Qrthocladius nr. clarkei group C A A
symposiocladius acutilabis - R -
Rheocricotopus robacki A - C
Rheosmiittia sp. - - R
Nanocladius balticus C - -
Hydrobaenus - R -
Xylotopus par C R -
Parakiefferiella triquetra R - -
Dukiefferiella gracei gr. R - -
Rheotanytarsus sp. R - R
Tanytarsus sp. R R -
- Ablabesmyia parajanta A A A
Conchapelopia gr. A C C
Nilotanypus sp. A - R
iabrundi ni a sp. - C -
Clinotanypus pinguis C - C
Polypedilum scalaenum - A -
P. convictum R C C
P. halterale R - R
P. failax R - -
Microtendipes pedellus R - -
3Yibelos sp. C A C
Cryptochironomus fulviventrus - R -
ChirononWs sp. - - R
Robackia demeijerei - R -
Stelechomyia perpulchra - - R
Stenochironomus sp. - - R
Stictochironomus sp. - R -
Potthastialongimanus R - -
-20-

Taxon
Mollusca
Menetus dilates
Physella sp.
Ferrissia rivularis
Other
Ranatra sp.
Hydracarinidae
Dugesia tigrina
Placobdella papillifera
Mooreobdella/Erpobdella sp.
Pelocoris sp.
Pyralidae
Corixidae
Stations
1 2 3
NC 71 SR 1303 SR 1393
A
C
MUD
C
R
R
R
OMR
OOP
C
R
R
MEW MMIN
R
R
A
R
R
/11
R
R

Table 5. Taxa Richness Values for Major Benthic Groups
Lumber River, April 3 and 4, 1985
*
Station 1983
B-MAN Et
Groue 1 2 3 Pembroke
Ephemeroptera 12 13 15 12
Plecoptera 10 8 9 4
Trichoptera 15 11 15 13
Oligochoeta 6 3 4 2
Cdonata 9 10 9 9
Coleoptera 7 5 7 10
Megaloptera 1 1 1 1
C rustacea 2 4 3 2
Diptera (misc.) 5 2 2 3
Diptera-Chironomidae 21 16 17 26
Mollusca 2 0 2 2
Other 5 3 5 5
**ST 95 76 89 89
***SST 37 32 39 28
Biological
Classification: Excellent Excellent Excellent Excellent
* BMAN sample taken near Pembroke in July 1983
** Total Taxa
*** Ephemeroptera, Plecoptera, Trichoptera taxa

CONCLUSIONS
Results of chemical analyses indicate that no significant increase in
measured parameters is occurring downstream of the Laurinburg/Maxton Airport WWTP
discharge. Total fixed residue and chloride values indicate a waste stream of
high ionic content and based on various other parameters, highly variable in
nature.
Effluent constituents that would be predicted to cause some of the observed
toxic effects on test organisms would include zinc concentrations of 150, and 280
ug/I and copper concentrations of 40 and 60 ug/l, though these would not
translate to concentrations of concern when diluted by the receiving stream.
Toxicity tests performed on the effluent seem to indicate little
toxicological variability based on 48 hour Daphnia aulex,static tests. Results
of these ranged from 71% to 89% for four tests, including 2 self —monitoring tests
performed for the facility. The 96 hour fathead minnow flow —through LCso of 100%
would indicate that this organism is slightly Tess sensitive to the effluent
while still indicating the same relative toxicity level. Ceriodaphnia
reproduction data indicate that a population suppression will occur at an
effluent concentration of 10%, while 1% would show no significant effects to the
population. These levels of toxicity may be associated in part with the levels
of copper and zinc measured in the effluent discharge. The toxicity of metals,
however, may be minimized when discharged in an effluent containing domestic
waste. It is because of this, that other unidentified constituents are probably
also contributing to the whole effluent toxicity. Relating this information to
an instream waste concentration of 1.2% during 7010 stream flows, end 0.33%
during average stream flows, the effluent is not predicted to cause any
significant damage to biological communities in the Lumber River.
Benthic macroinvertebrate sampling and analysis of the Lumber River upstream
and downstream of this"discharge indicate a community change in the river below
—23—

the discharge. This phenomena is attributed to habitat differences rather than a
toxic impact based on intolerant species common to both upstream and downstream
sampling locations.
In summary, it appears that even though toxicity testing shows that the
Laurinburg/Maxton Airport WWTP effluent does exert an acute toxic effect on
aquatic life, the effect is negated by the dilution received as it enters the
lumber River.
RECOMMENDATIONS
1.) Due to the presence of at least one EPA Priority Pollutant organic substance
in the influent, the sources and concentrations of organic chemicals should be
closely monitored to prevent any degradation of wastewater treatment efficiency
and/or discharges in excess of present levels.
2.) Toxicity abatement procedures and pretreatment programs should continue to
strive for moderation of the influent levels of zinc, copper, and cobalt.
3.) Future chronic toxicity testing should be considered using a species
resident in the low pH waters encountered in the Lumber River basin. This low pH
can show dramatic differences in observed toxicities of effluents and must be
addressed in setting appropriate chronic toxicity limitations for discharge.
4.) Future acute toxicity testing should be accomplished upon addition of any
further contributors to the waste water treatment system and the resulting
toxicities compared against those encountered during the scope of this
investigation.

APPENDIX

48 Hour Oa hnia pulex Screening Bioassay
Aquatic oxicology Group
N. C. Division of Environmental Management
The Aquatic Toxicology Group performs 48 hour static bioassays using the cladoceran
Daphnia pulex to estimate the toxicity of waste discharge to aquatic life in receiving
streams. All test and sampling glassware and equipment are washed with soap and
hot water, then rinsed in nitric acid, acetone, and distilled/deionized water. to
remove all toxins and contaminants. Effluent samples are collected by OEM Regional
Office or Aquatic Toxicology personnel. All samples are collected chilled and above
chlorination unless otherwise specified. Each sample is collected as a grab or 24 hour
Laboratory
using an automatic sampler and is sent chilled to the Aquatic Toxicology
Cory by state courier or bus. The sample must be received within 24 hours
after collection.
The samples are prepared for testing by being thouroughly mixed. adjusted to
standard test temperature, and aerated if dissolved oxygen is below 40% saturation.
Chlorine is removed with Sodium Thiosulfate if applicable. Initial pH and DO are
also recorded. The effluent is then diluted with D. ulex culture waer, typically to
P tYP Y
seven concentrations (with replicates) from 0 to 90% effluent. Each test chamber
receives 100 mis total volume and ten 24 hour old D. pulex test organisms. The test
is conducted in a 20 degree centigrade incubator with a 14:10 hour I ight:dark cycle.
Mortality of the D. pulex is recorded after 48 hours, along with final pH and
dissolved oxygen.
A 48 hour- LC5a, or concentration of effluent lethal to 50% of the test organisms in
48 hours, is calculated from the mortality data. An instream waste concentration
(IwOO for the effluent in the receiving stream is calculated using the treatment
system design flow and low —flow (7Q10) stream flow. The LC50 and IWC are then
used to predict instream toxicity. If the effluent toxicity and/or the !WC are high, a
persistance bioassay may be conducted. This involves a second 48 hour static D. pulex
bioassay on the same effluent sample after it has been exposed to light and aeration
for an additional 48 hours. if there is a 100% reduction in the LC50, the effluent is
considered to be non—persistant.

96 Hour On —site Flowthrough Bioassay
Aquatic Toxicology Group
N. C. Division of Environmental Management
Candidacy for an on —site toxicity evaluation by the Aquatic Toxicology Group is
determined on the basis of acute toxicity of the effluent in comparison with
instream waste concentration. Acute toxicity is determined by a 48 hour screening
static bioassay using Daphnia pulex.
For each on —site, flowthrough bioassay, a pre —test site inspection is performed in
order to:
1) Determine appropriate areas for physical placement of the mobile laboratory.
2) Acquire proper equipment and installation needed for electrical service.
3) Determine appropriate areas for effluent sampling and equipment needed for such.
Sampling is done above chlorination unless otherwise specified.
4) Determine possible areas for dilution sampling (actual receiving waters or other
unstressed streams in the area) and equipment needed for such.
5) Collect additional samples of effluent and possible dilution waters for further
static Daphnia pulex acute and static renewal Ceriodaphnia sp. reproduction bioassays
to determine the range of concentrations of effluent for the f l owthrough bioassay, to
test for potential toxicity of possible dilution waters, and for fish acclimation to
the chosen dilution water.
6) Determine route suitability to the facility for the mobile laboratory (eg. low
clearances, poor road conditions).
7 Discuss test procedures and requirements with appropriate facility personnel.
8 Determine appropriate sampling sites and techniques for benth i c
macroinvertebrate surveys.
Upon actual arrival on —site with the mobile laboratory, dilution water is obtained
and dilution and effluent pumping systems are set up and tested. Two to three week
old fathead minnows are wet transferred to the test chambers (containing
approximately one 1 iter of dilution water), ten fish to a chamber. Seven
concentrations (with replicates) including a control are used. The second day on —site
the dilutor and the dilution and effluent pumping systems are turned on and the
fathead minnow flowthrough bioassay is begun. A water bath is utilized to bring the
effluent and dilution water to a constant 20 degrees centigrade. Test organisms are
fed newly hatched brine shrimp twice daily throughout the test.
A Ceriodaphnia static renewal reproduction bioassay using newborn organisms is
begun the first day on —site. The organisms are transfered to fresh dilution and
effluent solutions daily and initial and final pH and dissolved oxygen are recorded.
The number of young born per organism per day is recorded and mean cumulative
reproduction is calculated for each concentration. The test is conducted in a 25
degree centigade incubator with 10 light:14 dark photoperiod. Test organisms are fed
a mixture of yeast and algae.
Individual chemical/physical parameter meters are calibrated daily according to DEM
standards. Hydrolab systems measure and record dissolved oxygen, pH, temperature,
and specific conductance in the test chambers with the highest and lowest
concentration of effluent at 15 minute intervals throughout the test. These systems
• are calibrated at test initiation, the mid —point of the test, and test
terminatlon.0ata from these systems is recovered daily and stored on magnetic tape
and hard copy. On alternate days, samples of dilution water, effluent at the sampling
site, final effluent, and the receiving stream upstream and downstream of the
-27-

discharge point are analyzed for hardness. On variable effluents, daily residual
chlorine measurements will be made at the above described sites.
During the on —site evaluation, Biological Monitoring Group personnel collect benthos
samples at the upstream, downstream and dilution sites (see Benth i c
Macroinvertebrate Survey appendix). Where appropriate, electrofishing is undertaken
upstream and downstream of the discharge to obtain resident fish population data.
On a site —specific basis, various other efforts are undertaken, such as monitoring
dissolved oxygen levels in the receiving stream.
On a daily basis, test chamber screens are cleaned, dilution water is collected (where
appropriate), effluent and dilution pumping systems are checked and adjusted as
necessary, and pH, dissolved oxygen, and fish mortalities are recorded for each
chamber.
Two separate 24 hour composite samples of effluent are collected by means of an
automatic sampler for chemical analysis. Receiving stream and dilution water
samples are also taken for chemical testing.
Static 48 hour Daphnia pulex bioassays are conducted on a 24 hour composite sample
of the effluent and a grab sample of the influent.
A photographic record is made of the treatment facility, sampling points, receiving
stream, and sampling procedures while on —site.
At the end of the 96 hour test period, the dilutor is turned off and final mortality
observations are made. Breakdown and packing routines are performed and the mobile
laboratory is transported back to the Cary Aquatic Toxicology Laboratory.
Several special care operating procedures should be mentioned. At facilities that
discharge for only a portion of the day, effluent samples are compos i ted by the
dilutor system into a large reservoir on board the mobile laboratory for use as the
effluent while discharge is not in progress. If the effluent has a high oxygen demand,
aeration systems for the test chambers are utilized and dissolved oxygen levels in the
chambers are monitored closely in order to prevent levels from dropping below 44%
saturation at test temperatures. In the event that actual receiving waters are
deemed unfit for the test (i.e. potentially toxic), an alternate source of dilution
water is sought in the vicinity.

Ceriodaphnia .1E. Reproduction Bioassay Procedure
Aquatic Toxicology Group
N. C. Division of Environmental Management
The Ceriodaphnia aquatio bioassay is oonduoted to estimate the effect of an
effluent or other water sample on reproductivity. The cladoceran Ceriodaphnia
sue. is used as test organism in a 7 day static renewal bioassay. A control and 8
concentrations of effluent ranging from 0.01% to 100% are typically used. There
are 10 animals per concentration, each animal in a one ounce polystyrene test
chamber with 15 mis of solution. The test is conducted in a 25 degree centigrade
incubator with a 14 light/ 10 dark photoperiod.
The test is initiated with newborn animals, or neonates. Adults having brood
sacs of 5 or more eggs with visible eyespots (indicating eggs are about to be
released) are isolated and checked periodically. Neonates are removed and
grouped according to time of birth. Selected groups are then composited to make
the youngest set of 90 or more neonates born within a 4 hour period. The test is
begun when the neonates are introduced into the test chambers. Temperatures must
be within 2 degrees centigrade for transfer.
The animals are transferred daily to new test chambers containing freshly mixed
solutions. Chemical/physical parameters are measured twice for each batch of
solutions. The initial value is taken before the animal is introduced and the
final value after the animal has been transferred out the next day. Dissolved
oxygen of greater than 40% saturation is necessary.
The animals are fed daily, just after transfer. Each animal receives 1/2
standard dose of yeast and 1/2 standard dose algae (one drop or 0.05 mis of a
solution made by dissolving 0.25 grams active dry baker's yeast in 100 mis of
distilled water plus one drop of a solution of 1.71 x 106 cells/ml Selenastrum
capricornutum).
As reproduction begins, only the adult is transferred to a new chamber. A drop
of concentrated nitric acid is added to the old chamber. This kills the young so
they can be easily counted under a dissecting microscope. A mean number of young
produced per adult is calculated for each concentration. Mortality of greater
than 10% in control test organisms invalidates a test.

Benthic Macroinvertebrate Procedure
Biological Monitoring Group
N.C. Division of Environmental Management
The sampling methodology requires that a stream or river be
wadable. High water conditions may severely impair sampling
efficiency by making critical habitats unaccessible. A fixed
number of samples are collected for each station. These include:
2 kick net samples of riffle and snag areas; 3 sweep net samples
of bank areas and macrophyte beds; 2 fine mesh washdown samples
of rocks and logs; 1 elutriated sand sample; 1 leafpack sample;
and 1 visual search of rocks, logs, leaves, and substrate. The
benthic macroinvertebrates are picked out with tweezers and
preserved in alcohol. A collection card is filled out which
includes such data as canopy cover, dissolved oxygen, pH, stream
temperature, substrate composition and stream morphology at the
site. Organisms are identified to the lowest possible taxonomic
level, generally to species. Density of each taxon is rated as
Rare (1 or 2 individuals), Common (3 to 9), Abundant (10 or
more). Most organisms may be identified using only a dissecting
microscope, but Oligochaeta and Chironomidae must be mounted and
identified with a compound microscope. Reference collections are
maintained and all samples are kept and stored by study area.
The first level of analysis summarizes the data by total number
of taxa or "taxa richness" (S) and density (N) for each
station.The association of good water quality with high taxa
richness is intuitively obvious even to the non -biologist.
Increasing levels of pollution gradually eliminate the more
sensitive taxa, leading to lower and lower taxa richness. Clean,
unstressed, aquatic communities are characterized by a density
(N) end taxa richness (S) above average levels. Toxic stress
(including pesticides and metals) reduces both S and N below the
average. Sediment stress, especially at low levels, tends to
decrease density, but affects taxa richness only slightly.
Finally, nutrient enrichment tends to increase the total number
of organisms, while selectively favoring a few types of organisms
tolerant to this type of pollution.
The second level of analysis summarizes data by taxonomic groups
(mostly orders of insects). A particularly useful parameter is
the "EPT" value: the sum of the taxa richness for the intolerant
insect groups Ephemoroptera, Plectoptera, and Trichoptera. The
EPT value is consistantly related to water quality.
The final step in data analysis is to summarize the data
separately for each taxe.The presence or absence of individuals
of "indicator species" is, in itself, insufficient for
characterizing water quality. Tolerant species are present in all
aquatic habitats, however these species will usually become
dominant only in polluted systems. Information on pollution
tolerance of any given taxon, combined with quantitative data on
-30-

its distribution can often be related to specific chemical or
physical changes in the environment. -