Table 17a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01464000, Assunpink Creek at Trenton, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; jig/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05

significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 42 ay 42 ay -0.367 0.633 NA NA
Hardness, mg/L as CaCO, . 79 (13) mat (63) ~.259 741 NA NA
Total organic carbon, mg/L as C 5.3 (7) 6.6 (30) 0 1.102 NA NA
Suspended sediment, mg/L 9 ql) 12 (21) 837 1,837 NA NA
Dissolved solids, mg/L 182 (dl) 173 (36) -.260 .739 NA NA
Dissolved sodium, mg/L as Na 25 (13) 20 (65) -387 613 NA NA
Dissolved chloride, mg/L as C1 34 (13) 29 (70) -365  * 635 NA NA
Dissolved oxygen, mg/L 10.0 (21) 8.7 (109) 149° * 1.149 NA 0
Fraction of dissolved oxygen at 95 (18) 88 (101) 078 * ND NA 0
saturation, Y%
Total phosphorus, mg/L as P 30 © (21) 50 (61) -340 659 NA NA
Total nitrogen, mg/L as N 4.0 (21) 4.0 (100) -336 664 NA NA
Total nitrate plus nitrite, mg/L as N 3.17 (21) 1.80 (101) 392 608 NA 0
Total nitrite, mg/L as N 022 (20) 036 (90) -432* 568 NA -
Total ammonia plus organic nitrogen, 90 (21) 1.60 (109) -212 788 NA NA
mg/L asN
Total ammonia, mg/L as N 08 = (21) 76 (96) 0 816 NA NA
Total boron, pg/L as B 100 3) 120 (4) ND ND NA NA
Total lead, pg/L as Pb 4 (5) 13 7) ATS 1.474 NA NA
Fecal coliform bacteria, MPN/100 ml 3500 (21) 1300 (110) 0 * ND NA 0

Table 17b. 1993 AMNET impairment status in the vicinity of water-quality station 01464000, Assunpink Creek at Trenton, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream:
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station

At WQ-station location

Downstream from WQ station

AMNET station

Impairment status

ANO116

Moderately impaired

None

ANOI18

ND Moderately impaired

51


combined chlorine residual. Contributions of ammonia to surface water from ground water are
usually small because ammonia readily adsorbs to soil particles and clays and does not leach from
soils (Hem, 1985).

The toxicity of ammonia to fish is dependent on its speciation. Un-ionized ammonia is
considered to be the toxic form to aquatic organisms (Rand and Petrocelli, 1985). The relative
concentrations of ionized (NH4*) and un-ionized (NH) ammonia are a function of the pH,
temperature, and ionic strength of the aqueous solution. When the pH, temperature, and total-
ammonia concentration are measured in a solution, the relative concentrations of NH; and NH,*
can be calculated. Decreased dissolved oxygen concentrations are often coincident with
increased ammonia toxicity.

Relation of trends i ation tof jit

The trends in total ammonia concentrations during high flows are negative at the one
station on the Cohansey River (4128), indicating a decrease in the contribution from storm runoff
over time at this station, and insignificant at the one station on the Cooper River (46715) (figs. 36a
and 37a). The trends in total ammonia concentrations during low flows are negative at the
stations on the Doctors Creek (464515) and North Branches of the Rancocas (4670) and
Pennsauken (467069) Creeks, indicating a decrease in the contribution from point sources and
ground water over time at these stations (figs. 36b and 37b). Total ammonia concentrations
during low flows show no trends at all stations on the Mullica River (409387), Hammonton Creek
(409416), Batsto River (4095), Oswego River (4100), East Branch of the Bass River (41015),
Great Egg Harbor River (410784, 4110, and 41111), Crosswicks Creek (4645), South Branches of
the Rancocas (46585) and Pennsauken (467081) Creeks, Raccoon (47712) and Oldmans (47751)
Creeks, Salem (4825) and Cohansey (4128) Rivers, and the downstream station on the Maurice
River (4118).

Relation of load to streamflow

The range categories of regression slopes of total ammonia load are depicted in figures
36c and 37c. The slopes range from 0.415 at the downstream station on the Maurice River (4118)
(table 32a) to 1.732 at the station 4080 on the Manasquan River (table 5a). Slopes are in the high
range at the stations on the Manasquan (4080) and Batsto (4095) Rivers, where the contributions
to instream total ammonia load from storm runoff are larger and less influenced by constant
sources than at other sites in the study area. The slopes are in the low range at the stations on the
Toms (4085), West Branch of the Wading (409815) and East Branch of the Bass Rivers (41015),
Great Egg Harbor River (4110), Doctors Creek (464515), South (46588) and North (4670)
Branches of the Rancocas Creek, and South Branch of the Pennsauken Creek (467081), and the
downstream station on the Maurice River (4118). At these sites, the contributions to instream
total ammonia loads from point sources and (or) ground water are larger and less influenced by
storm runoff than at other sites in the study area. Slopes at stations on the Maurice River decrease
in the downstream direction, indicating a decrease in the relative influence of contributions from
storm runoff along the river.

115


surface-water gaging station on Big Timber Creek or either branch of Big Timber Creek. One
water-quality station is located on the South Branch of Big Timber Creek, a second-order stream,
at Blackwood Terrace (01467329), where the period of record for water-quality-data collection is
water years 1976-93 (fig. 6) (Bauersfeld and others, 1994).

Land use in the basin is mostly urban and suburban. There are forests at the headwaters of
the creek and cities where the creek flows into the Delaware River (New Jersey Department of
Environmental Protection and Energy, 1993).

Raccoon Creek

Raccoon Creek is about 19 miles long and drains an area of 40 mi’. Tidal marshes are
present at the mouth of Raccoon Creek, and the lower half of the creek is tidal (New Jersey
Department of Environmental Protection and Energy, 1993). Mean annual flow for water years
1966-93 is estimated to be 40.3 ft?/s at the surface-water gaging station on Raccoon Creek near
Swedesboro (01477120) (Bauersfeld and others, 1994). One water-quality station is located on
Raccoon Creek at Swedesboro (01477120). The period of record for water-quality-data
collection is water years 1965-93 (fig. 6) (Bauersfeld and others, 1994).

Land use in the basin is mainly agricultural and rural. Industries are located along the
lower tidal section of the creek (New Jersey Department of Environmental Protection and Energy,
1993).

Idmans Cre

Oldmans Creek is 20 miles long and drains an area of 44 mi?. Tidal marshes are present at
the mouth of the creek, and the lower third of the creek is tidal (New Jersey Department of
Environmental Protection and Energy, 1993). Mean annual flow for water years 1932-40 is
estimated to be 29.0 ft?/s at the discontinued surface-water gaging station on Oldmans Creek near
Woodstown, New Jersey (01477500) (Gillespie and Schopp,1982). One water-quality station is
located on Oldmans Creek at Porches Mill (01477510), where the period of record for water-
quality-data collection is water years 1975-93 (fig. 6) (Bauersfeld and others, 1994).

Land use in the basin is mainly agricultural and forested. There are some residential and
industrial areas (New Jersey Department of Environmental Protection and Energy, 1993).

Salem River

The Salem River is 32 miles long and drains an area of 114 mi*. Most of the lower part of
the river is tidal (New Jersey Department of Environmental Protection and Energy, 1993). Mean
annual flow for March to September 1940, December 1941 to January 1985, and June to
December 1989 is estimated to be 19.3 ft/s at the discontinued surface-water gaging station on
the Salem River at Woodstown (01482500) (Bauersfeld and others, 1990). One water-quality
station is located on the Salem River at Woodstown (01482500), where the period of record for
water-quality-data collection is water years 1973-93 (fig. 6) (Bauersfeld and others, 1994).

17


REFERENCES CITED—Continued
Wershaw, R.L., Fishman, M.J., Grabbe, R.R., and Lowe, L.E., 1987, Methods for the

determination of organic substances in water and fluvial sediments: U.S. Geological
Survey Techniques of Water-Resources Investigations, book 5, chap. A3, 80 p.

146


chloride, total nitrogen, and total nitrate plus nitrite; at three stations for dissolved sodium,
fraction of dissolved oxygen at saturation, and total ammonia; and at six stations for total
ammonia plus organic nitrogen.

Trends in concentrations during high flows are positive (increasing intermittent-source
contributions) at one station for hardness, dissolved solids, and dissolved sodium and at two
stations for dissolved chloride. Trends during high flows are negative (decreasing intermittent-
source contributions) at one station for dissolved solids, total nitrogen, and total ammonia plus
organic nitrogen, and at two stations for total phosphorus and total nitrite.

Two of the 28 water-quality stations have insufficient data to determine trends during both
high and low flows. Sufficient data are available to determine trends during low flows at all
water-quality stations in the Atlantic Coastal Basin and 12 stations in the lower Delaware River
and Delaware Bay Basins. Sufficient data are available to determine trends during high flows at
only one station in the Atlantic Coastal Basin and five stations in the lower Delaware River and
Delaware Bay Basins. Trends tests were conducted only if there was at least one measurement in
each period of not less than four of the six water years in each one-third of the period of study (18
years); a lack of data results in no trend.

Concentration-to-streamflow relations show seasonal dependency at one or more stations
for 17 of the 18 constituents. Seasonal dependency is not evident at any station for total boron
and at only one for total lead. Seasonal dependency is evident at 14 or more stations for hardness,
total organic carbon, dissolved sodium, dissolved oxygen, fraction of dissolved oxygen at
saturation, total phosphorus, total nitrogen, total nitrate plus nitrite, total nitrite, and fecal
coliform bacteria. Dissolved oxygen shows seasonal dependency at all stations, possibly because
of its relation to bioactivity in surface water. Dissolved sodium and hardness show seasonal
dependency most likely as a result of road salting; however, dissolved solids shows seasonal
dependency only at six stations.

The change in the load-to-streamflow relations along a river reach in the downstream
direction indicates the changing relative importance of intermittent sources along the river. The
magnitudes of the load slopes for hardness, total phosphorus, total nitrogen, total nitrite, and total
ammonia plus organic nitrogen increase along the Great Egg Harbor River, indicating an increase
in the relative influence of contributions from storm runoff along the river. The magnitudes of the
load slopes for alkalinity, hardness, dissolved solids, dissolved sodium, dissolved chloride, total
phosphorus, total nitrogen, total nitrate plus nitrite, total nitrite, total ammonia plus organic
nitrogen, and total ammonia decrease along the Assunpink Creek as do the load slopes for total
organic carbon, dissolved sodium, dissolved chloride, total ammonia plus organic nitrogen, and
total ammonia along the Maurice River, indicating a decrease in the relative influence of
contributions from storm runoff along the rivers.

The relation of load to streamflow provides a qualitative estimate of the relative
contributions of nonpoint storm runoff and ground water, and point sources, to surface-water
quality and represents preliminary results for the total maximum daily load process for the State’s
watersheds. The results of this study, along with identification of constant-rate sources, additional
water-quality data collected during low and high flows, and ground-water data (water-quality
data, water levels, flow rates, and travel times) could facilitate a more detailed analysis of the
overall hydrology of these river basins.

141


U.S. DEPARTMENT OF THE INTERIOR
BRUCE BABBITT, Secretary

U.S. GEOLOGICAL SURVEY
Charles G. Groat, Director

For additional information
write to:

District Chief

U.S Geological Survey
Mountain View Office Park

810 Bear Tavern Road, Suite 206
West Trenton, NJ 08628

Copies of this report can be
purchased from:

U.S. Geological Survey
Branch of Information Services
Box 25286

Denver, CO 80225-0286


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11


Table 23a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01467069, North Branch Pennsauken Creek near Moorestown, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; j:g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient

data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression  Low- High-
eee Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 16 (26) 14 (73) 0 0.976 NA NA
Hardness, mg/L as CaCO, 81 (27) 78 (108) 089 * ou 0 NA
Total organic carbon, mg/L as C 5.2 (27) 6.2 (108) 0 * 1.028 0 NA
Suspended sediment, mg/L 20 ay 18 (22) 0 1.110 NA NA
Dissolved solids, mg/L 170 (on) 172 (105) 0 * 956 0 NA
Dissolved sodium, mg/L as Na 14 (27) 16 (109) 0 * 960 - NA
Dissolved chloride, mg/L as Cl 29 (27) 27 (110) 0 * 959 0 NA
Dissolved oxygen, mg/L 8.4 (26) 79 (107) 0 * 1.056 + NA
Fraction of dissolved oxygen at 86 (26) 80 (107) 0 ND 0 NA
saturation, %
Total phosphorus, mg/L as P AS (27) 22 (79) 0 * 996 NA NA
Total nitrogen, mg/L as N 13 (27) 23 (92) 0 1.002 - NA
Total nitrate plus nitrite, mg/L as N 50 (27) 60 (96) 0 * 1.065 - NA
Total nitrite, mg/L as N 016 (26) 030 (78) =193 * 807 NA NA
Total ammonia plus organic nitrogen, 17 (27) 1.60 (104) 0 920 - NA
mg/L as N

Total ammonia, mg/L as N 18 (27) 58 (97) 0 * 872 - NA
Total boron, g/L as B 40 © 40 (19) 0 1,097 NA NA
Total lead, pg/L as Pb 3 6) 7 (22) 0 956 : NA
Fecal coliform bacteria, MPN/100 ml 230 (25) 205 (106) ) * ND 0 NA

Table 23b. 1993 AMNET impairment status in the vicinity of water-quality station 01467069, North Branch Pennsauken Creek near

Moorestown, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WA station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream

from the WQ station; ND, undetermined impairment status}

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO179 None ‘ANO180
Impairment status Moderately impaired ND Moderately impaired

60


REFERENCES CITED—Continued

Hochreiter Jr., J.J., and Kozinski, Jane, 1985, Quality of water and bed material in streams of
Logan Township, Gloucester County, New Jersey: U.S. Geological Survey Water-
Resources Investigations Report 85-4300, 39p.

Hutchison, N.E., 1975, WATSTORE: National Water Data Storage and Retrieval System: user’s
guide: U.S. Geological Survey Open-File Report 75-426, 791 p.

Ivahnenko, Tamara, and Buxton, D.E., 1994, Agricultural pesticides in six drainage basins used
for public water supply in New Jersey, 1990: U.S. Geological Survey Water-Resources
Investigations Report 93-4101, 56 p.

Keighton, W.B., 1965, Delaware River water quality, Bristol to Marcus Hook, Pennsylvania,
August 1949 to December 1963: U.S. Geological Survey Water-Supply Paper 1809-O,
57 p.

Keighton, W.B., 1966, Fresh-water discharge-salinity relations in the tidal Delaware River:
U.S. Geological Survey Water-Supply Paper 1586-G, 16 p.

Keighton, W.B., 1969, Water quality in the Delaware estuary for two years of drought; 1965 and
1966 from Trenton, New Jersey to Reedy Island, Delaware: U.S. Geological Survey
Hydrologic Investigations Atlas 335, 2 sheets, scale 1:1,000,000.

Mansue, L.J., 1972, Suspended-sediment yields of New Jersey Coastal Plain streams draining
into the Delaware estuary: U.S. Geological Survey Open-File Report, 26 p.

New Jersey Department of Environmental Protection and Energy, 1993, New Jersey 1992 State
Water Quality Inventory Report: New Jersey Department of Environmental Protection
and Energy, Office of Land and Water Planning, Trenton, New Jersey, 472 p.

New Jersey Department of Environmental Protection, 1989, Nonpoint Source Assessment and
Management Program, Division of Water Resources, Trenton, New Jersey, 97 p.

1996a, Ambient Monitoring Network: Atlantic Coastal Drainage Basin, 1994-95 benthic
macroinvertebrate data: Trenton, New Jersey, Executive Summary, January 1996, 22 p.

1996b, Ambient Monitoring Network: Lower Delaware Drainage Basin, 1995-96 benthic
macroinvertebrate data: Trenton, New Jersey, Executive Summary, July 1996, 22 p.

Novotny, Vladimir, and Chesters, Gordon, 1981, Handbook of nonpoint pollution sources and
management: New York, Van Nostrand Reinhold Company, 555 p.

>

Parker, G.G., Hely, A.G., Keighton, W.B., and Olmsted, F.H., 1964, Water resources of the
Delaware River basin: U.S. Geological Survey Professional Paper 381, 200 p.

144


Table 31a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01411500, Maurice River at Norma, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO3, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; 1g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO; 6 (30) 6 (77) 0.540 * 0.459 NA NA
Hardness, mg/L as CaCO, 20 (30) 18 (118) -060 * 940 + +
Total organic carbon, mg/L as C ND (0) 5.8 (62) 585 * 1,584 NA NA
Suspended sediment, mg/L 6 (29) 5 (100) 582 * 1,582 NA NA
Dissolved solids, mg/L 56 (30) 57 (118) 057 1.057 0 -
Dissolved sodium, mg/L as Na 5 30) 5 (ly) -.072 928 - 0
Dissolved chloride, mg/L as Cl 9 0) 9 (121) 0 * 980 + 0
Dissolved oxygen, mg/L 8.6 (30) 8.8 (123) 0 * 986 0 0
Fraction of dissolved oxygen at 88 (29) 88 (120) 068 * ND 0 0
saturation, %
Total phosphorus, mg/L as P 01 (30) 02 (116) 0 * 1.037 0 -
Total nitrogen, mg/L as N 19 (29) 1.9 (108) -179 * 821 0 0
Total nitrate plus nitrite, mg/L as N 1.50 (29) 1.50 (110) -351 * 648 0 0
Total nitrite, mg/L as N 006 (20) 008 (34) 0 18 NA NA
Total ammonia plus organic nitrogen, 40 (30) 50 (120) 1920 * 1.192 0 0
mg/L as N
Total ammonia, mg/L as N (04 (25) 04 (81) 0 977 NA NA
Total boron, pg/L as B ND (0) 40 @) ND ND NA NA
Total lead, j1g/L as Pb ND (0) 5 (16) tv) 1.025 NA NA
Fecal coliform bacteria, MPN/100 ml ND (0) 33 (44) 0 * ND NA NA

Table 31b. 1993 AMNET impairment status in the vicinity of water-quality station 01411500, Maurice River at Norma, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status}

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO0733 ANO0740 ANO751
Impairment status Moderately impaired Non-impaired Moderately impaired

71


the extent of dilution during periods of high flow will be reduced. The use of loads (mass per
time) instead of concentrations (mass per volume) removes the influence of changing streamflow
(volume per time) on instream constituent amounts (Buxton and others, 1998).

The instream load also can be affected by contributions from ground water and streambed
sediment. Ground-water contributions to streams during low flow can be significant, but are less
likely to affect surface-water quality during high-flow conditions when ground-water
contributions are diluted. In some hydrologic systems, the scour of streambed sediment during
high flows can contribute to the instream load. Rosensteel and Strom (1991) collected water-
quality samples from the Pompton and Passaic Rivers during storms and found that most of the
observed increase in the load of total phosphorus at high flows was attributable to the dissolved
fraction of the phosphorus load, indicating that the load contributed by sediment scour probably
was significant.

Comparisons of trends in constituent concentrations during high and low flows can
indicate changes over time in the contributions from intermittent and constant sources,
respectively. Positive trends during high flows indicate an increase in the storm runoff
contributions over time, whereas negative trends indicate a decrease in the storm runoff
contributions. Positive trends during low flows indicate an increase in the contributions from
point sources and ground water or both over time, whereas negative trends indicate a decrease in
the contributions from point sources and ground water.

The study involved several phases of multidisciplinary activity starting with the selection
of the surface-water-quality stations (table 1), constituents, and the period of record. Water-
quality and instantaneous-streamflow data were retrieved from the National Water Information
System (NWIS) data base (Hutchison, 1975), which is maintained by the USGS. The water-
quality and instantaneous-streamflow data underwent extensive quality-assurance procedures.

The data base created for this study was maintained with the Statistical Analysis System
(SAS), a statistically based integrated software system that provides data access, management,
analysis, and presentation. With SAS, median concentrations and relations of surface-water
quality to streamflow were determined for each constituent at cach station. The types of relations
analyzed are concentration to streamflow, load to streamflow, and concentration trends during
low- and high-flow conditions.

Graphs, schematics, and tables were generated to show the statistical results. Results are
presented in the text first by basin and compared with the impairment index generated by the
NJDEP’s Ambient Biomonitoring Network (AMNET) biological assessment, and then by
constituent. Results of the three surface-water quality to streamflow analyses are presented
graphically by constituent for each station in appendixes 1-187.

2 Appendixes 1-18 containing relations of surface-water quality to streamflow are available on a CD-ROM;
contact the New Jersey District Office of the USGS in West Trenton, N.J., for more information or to obtain copies of
the CD-ROM.


Total Boron

Boron is a minor constituent in most surface water. Small amounts of boron are essential
for plant growth. Boron minerals are present in some igneous rocks; water in volcanic areas and
thermal! springs may contain considerable concentrations of boron (Hem, 1985). Boron from the
cleaning agent, sodium tetraborate (borax), can be present in surface water as a result of the
release of treated sewage and industrial-use water.

I i f j ati fl iti

Insufficient data are available to determine trends in boron concentrations during high and
low flows at all stations in the study area (figs. 38a, 39a, 38b, and 39b).

Relat to strea

The range categories of regression slopes of total boron to streamflow are depicted in
figures 38c and 39c. Sufficient data were not available to determine slopes at 12 of the stations.
The slopes range from zero at the downstream station on the Great Ege Harbor River (41111) and
the stations on the Crosswicks (4645), Doctors (464515), and Oldmans (47751) Crecks (tables
15a, 18a, 19a, and 28a, respectively) to 1.655 at station 4128 on the Cohanscy River (table 30a).
Slopes are in the high range at the stations on the Mullica River (309387), North Branch of the
Rancocas Creck (4670), and Cohansey River (4128), where the contributions from storm runoff
are larger and less influenced by point sources and ground water than at other sites in the study
area. All four stations with zero slopes and station 467081 on the South Branch of the
Pennsauken Creek have slopes in the low range, indicating that the contributions from constant
sources (most likely ground water) are larger and less influenced by storm runoff at these sites
than at other sites in the study area.

Total Lead

Lead is occasionally present in surface water in trace amounts, which can be toxic to
aquatic organisms. Lead is widely dispersed in sedimentary rocks; however, its mobility is low
(Hem, 1985). The many uses of lead have dispersed the element throughout the environment.
Dry fallout and rain-out of particulate lead is probably a factor of major importance in the
circulation of the clement. Concentrations of lead in rain and snow are greater in areas subject to
substantial air pollution than in more remote areas. Storm runoff is a potential source of lead in
surface water.

R

Insufficient data are available to determine trends in lead concentrations during high flows
at all stations in the study area (figs. 40a and 41a). The trend in total lead concentrations during
low flows is negative at the one station on the North Branch of the Pennsauken Creek (467069),
indicating a decrease in the contribution from point sources and ground water over time at this site
(figs. 40b and 41b).

120


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Table 28a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01477510, Oldmans Creek at Porches Mill, NJ.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter, CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; jg/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression Low- High-
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 25 (27) 26 (73) 0378 * 0.622 NA NA
Hardness, mg/L as CaCO, 60 (27) 69 (108) -.156 843 0 NA
Total organic carbon, mg/L as C 46 (27) 46 (110) 0 * 1.034 0 NA
Suspended sediment, mg/L 10 9) 16 (20) 0 1.439 NA NA
Dissolved solids, mg/L 120 (26) 124 (101) -.087 913 0 NA
Dissolved sodium, mg/L as Na 5 (27) 4 (108) 0 * 962 + NA
Dissolved chloride, mg/L as Cl 16 (27) 14 (109) -077 922 0 NA
Dissolved oxygen, mg/L 9.6 © (27) 9.0 (110) 097 * 1.097 0 NA
Fraction of dissolved oxygen at 88 (25) 90 (107) 0 ND + NA
saturation, %
Total phosphorus, mg/L as P 0B (27) 10 (79) 0 * 1.092 NA NA
Total nitrogen, mg/L as N 22 (27) 24 (99) 201 * 1.201 0 NA
Total nitrate plus nitrite, mg/L as N 1.66 (27) 1.66 (100) 292 * 1.292 0 NA
Total nitrite, mg/L as N 023 (26) 019 (80) 0 * 1.044 NA NA
Total ammonia plus organic nitrogen, 54 (27) .60 (108) 0) * 924 0 NA
mg/L as N

Total ammonia, mg/L as N 06 (27) 09 (96) 0 964 0 NA
Total boron, pg/L as B 20 ©) 20 (7) s-ND 0 NA NA
Total lead, pg/L as Pb 1 (a) 3 Ql) 0 0 NA NA
Fecal coliform bacteria, MPN/100 ml 110 (25) 170 (105) 0 * ND 0 NA

‘Table 28b. 1993 AMNET impairment status in the vicinity of water-quality station 01477510, Oldmans Creek at Porches Mill, N.J.

[AMNET, Ambient Biomonitoring Network, WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WOQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station AN0687 AN0688 AN0689
Impairment status Moderately impaired Moderately impaired Moderately impaired

66


Sp,
LOpp = Uppt [x [LO ce-Ucrl>

(6)
where
LOpr = the base-10 logarithm of the partial-record streamflow,
upg = the mean of the logarithms of partial-record streamflow,
Spr = the standard deviation of logarithms of partial-record streamflow,
LOcr = the base-10 logarithm of the index continuous-record streamflow,
ucr = the mean of the logarithms of the index continuous-record streamflows, and
Scr =the standard deviation of logarithms of the index continuous-record streamflow.

The flow-duration value for partial-record station 01409815, West Branch Wading River
at Maxwell, New Jersey, was estimated using drainage area adjustments from nearby surface-
water gaging stations (table 3).

Statistical Method

Concentration measurements were selected only if they had an associated, nonzero value
of streamflow (instantaneous or estimated); only one observation per constituent per day was
used. Concentration values were reported as “uncensored,” “less-than,” and “greater-than”.
Concentrations of constituents other than fecal coliform bacteria were either uncensored or less-
than values; some measurements of fecal coliform bacteria were greater-than values.

Median concentrations and relations of surface-water quality to streamflow were
determined for each constituent and station. The following types of relations of surface-water
quality to streamflow are presented graphically by constituent for each station in appendixes 1-18:
concentration to streamflow, load to streamflow, and trends in concentrations during low and high
flows.

Calculation of Medians

Medians were calculated for measurements made during two periods—the entire period of
study (water years 1976-93) and the last 5 years of the period of study (water years 1989-93). The
method of calculation depended upon whether the data set contained censored values. For data
sets with only uncensored data, the values were ranked, and the median was calculated as the 50th
percentile. For data sets with less-than values but no greater-than values, medians were
calculated by using the adjusted maximum likelihood method (AMLE) described in Cohn (1988)
and Helsel and Cohn (1988). If the data set contained either an insufficient number of
observations for this method or greater-than values, the median was determined by manually
ranking and identifying the 50th percentile value.

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concentrations, the regression slopes of concentration and load to streamflow, and the directions
of the trends in concentrations during low and high flows for all constituents along with the
AMNET impairment status at and near the station. Third, relations are presented in schematics
showing the regional trends in concentrations during low and high flows and the slopes of load to
streamflow by constituent.

Appendixes 1-18 illustrate the relations of surface-water quality to streamflow by
constituent for each station with three graphs. Figure 7 is an example page from appendix 12.
The first graph shows the relation of concentration to streamflow. Plots of concentration to
streamflow indicate how instream constituent concentrations vary with streamflow, but do not
indicate the relative contributions of constant and intermittent sources. Data for stations on
streams that drain developed areas show the most scatter, especially for inorganic constituents
such as sodium, chloride, and hardness. Relations between concentration and streamflow were
developed by using (1) all measurements, (2) only measurements collected during the growing
season, and (3) only measurements collected during the nongrowing season. Growing-season
measurements are shown with open symbols and nongrowing-season measurements are shown
with crisscross symbols. Different symbols are used to show uncensored and censored values.
For each group of measurements, the number of observations and values of slope and intercept
are listed, and a regression line is shown when the slope of concentration to streamflow is
different from zero at the 0.05 significance level. A seasonal dependency is indicated when the
relations of concentration to streamflow for the growing- and nongrowing-season measurements
are different. The 75 and 25 percentiles of the flow duration also are indicated.

The second graph in figure 7 shows the relation of load to streamflow. The regression
slope of load to streamflow indicates the relative contributions of constant and intermittent
sources to the instream load. The steeper the slope, the greater the contribution during increased
streamflow from storm runoff (intermittent sources). Relations between load and streamflow
were developed using all measurements. Different symbols are used to show uncensored and
censored values. The number of observations and values of slope and intercept are shown, and a
regression line is drawn when the slope is different from zero at the 0.05 significance level. A
smoothed relation between load and streamflow is shown when there are 10 or more observations.
The 75 and 25 percentiles of the flow duration also are indicated.

The third graph in figure 7 shows the trends in concentrations during low and high flows.
Trends in constituent concentrations during high and low flows can indicate changes over time in
the contributions from intermittent and constant sources, respectively. Positive trends during high
flows indicate an increase in the storm runoff contributions over time, whereas negative trends
indicate a decrease in the storm runoff contributions. Positive trends during low flows indicate an
increase in the contributions from point sources and ground water over time, whereas negative
trends indicate a decrease in the contributions from point sources and ground water.
Measurements during low flows are shown with open symbols, and measurements during high
flows is shown with crisscross symbols. Different symbols are used to show uncensored and
censored values. The number of observations and water years during which at least one
measurement was made is shown for each group of measurements. Trends are indicated by
regression lines and slope values when the seasonal Kendall tau value is significant.

31


Table 20a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01465850, South Branch Rancocas Creek at Vincentown, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration, concentration load to trend trend
tostreamflow streamflow direction —_ direction
Alkalinity, mg/L as CaCO, 4 (26) 4 (73) -0.425 0.575 NA NA
Hardness, mg/L as CaCO, 20 (26) 20 (105) -086 * 914 0 NA
Total organic carbon, mg/L as C 10.6 (24) 11.0 (103) 0 * 1.088 0 NA
Suspended sediment, mg/L 6 (i) 7 (19) 0 952 NA NA
Dissolved solids, mg/L 59 (27) 60 (107) 0 984 0 NA
Dissolved sodium, mg/L as Na 5 (26) 4 (107) ~181 0 * 819 0 NA
Dissolved chloride, mg/L as Cl 8 (26) 7 (106) 059 * 941 + NA
Dissolved oxygen, mg/L 8.5 (27) 7.8 (106) 146 * 1.146 0 NA
Fraction of dissolved oxygen at 80 27) 78 (105) 064 * ND - NA
saturation, %
Total phosphorus, mg/L as P sll (27) 13 (79) -489* S11 NA NA
Total nitrogen, mg/L as N 1.2 (27) 1.2 (93) 139 861 0 NA
Total nitrate plus nitrite, mg/L as N AT (27) 40 (95) -174* 826 + NA
Total nitrite, mg/L as N 012 (27) 010 (81) -.127 873 NA NA
Total ammonia plus organic nitrogen, 10 (27) 78 (106) -104* 896 0 NA
mg/L as N
Total ammonia, mg/L as N .09 = (27) il (95) -495  * 505 1) NA
Total boron, pg/L as B 20 (6) 30 (18) 0 864 NA NA
Total lead, g/L as Pb 4 6) 5 (22) 0 1.194 NA NA
Fecal coliform bacteria, MPN/100 ml 140 (24) 110 (103) 0 * ND 0 NA

Table 20b. 1993 AMNET impairment status in the vicinity of water-quality station 01465850, South Branch Rancocas Creek at Vincentown, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO1S6 None ANO161
Impairment status Severely impaired ND Moderately impaired

56


SUMMARY

The U.S. Geological Survey, in cooperation with the New Jersey Department of
Environmental Protection, investigated the quality of surface water in the Atlantic Coastal, lower
Delaware River, and Delaware Bay Basins during water years 1976-93. After selection of the
appropriate surface-water-quality stations, constituents, and period of record, the water-quality
data, instantaneous streamflow data, and flow durations were compiled and checked for accuracy.
A project data base was maintained, and statistical parameters, such as median constituent
concentrations, slopes of regression for load to streamflow and concentration to streamflow, and
trends in constituent concentrations over time, were determined. Eighteen water-quality
constituents at 28 surface-water-quality stations were investigated. The relative contributions of
constant and intermittent sources of water-quality constituents were evaluated by testing for
trends in concentrations during low and high flows, and qualitative values of source contributions
were estimated by statistically defining the relations between concentration and streamflow, and
load and streamfiow.

Results of trend analysis can indicate the relative contributions of constant and
intermittent sources to stream-water quality over time within a basin. A trend in concentrations
during high-flow conditions can indicate increasing or decreasing intermittent source
contributions over time, and a trend in concentrations during low-flow conditions can indicate
increasing or decreasing constant-source contributions over time. A conservative method was
used to determine trends during low and high flows. The use of flow duration values covering a
greater range would possibly allow additional significant trends to be determined.

The slopes of load to streamflow were grouped into low (less than or equal to 25 percent
of the interval between the minimum and maximum slopes of each constituent), medium (greater
than 25 percent to less than 75 percent of the slope interval), and high (greater than 75 percent of
the slope interval) ranges in order to compare sites by constituent. At sites with slopes in the high
range, contributions to instream loads from storm runoff probably are larger than at other sites in
the study area, indicating an increased relative importance of intermittent (nonpoint storm runoff)
source contributions. At sites with slopes in the low range, contributions to instream loads from
intermittent sources probably are smaller than at other sites in the study area, indicating an
increased relative importance of constant (point sources and ground water) source contributions.
For constituents with large slopes of load to streamflow; greater than 0.8, (for example, total
organic carbon and suspended sediment), storm runoff is most likely the significant contributor to
instream loads, even for stations with slopes in the low range. Constituent concentrations cannot
be related to streamflow in the same way as load because contributions from storm runoff are flow
dependent. Overall, slopes of load-to-streamfiow relations tend to be higher for stations in this
study area than in the Hackensack, Passaic, Elizabeth, and Rahway River Basins, indicating a
greater relative influence of contributions from intermittent sources.

Trends in concentrations during low flows are positive (increasing constant-rate source
contributions) at one station for total nitrate plus nitrite; at two stations for hardness, dissolved
oxygen, and fraction of dissolved oxygen at saturation; at three stations for fecal coliform
bacteria; at six stations for dissolved sodium; and at nine stations for dissolved chloride. Trends
during low flows are negative (decreasing constant-rate source contributions) at one station for
total organic carbon, total phosphorus, total nitrite, and total lead; at two stations for dissolved

140


Each set of seasonal relations was developed and reported by using the methods just
described if an analysis of covariance (described below) indicated that the scasonal relations were
different from one another at the 0.05 level of significance. The analysis of covariance was
conducted only if there were at least nine uncensored measurements during each season.

The analysis of covariance followed the approach in Helsel and Hirsch (1992), except that
Tobit regression was used in place of ordinary least-squares regression. The analysis determined
whether a complex model with a seasonal component was significantly better than a simple model
without a seasonal component. The simple model is given in equation 7; the complex model is
given in equation 8.

log (CONC) = [SLOPE, x log (FLOW) +INT,] + [SLOPE, x log (FLOW) + INT, xi], (8)

where
log = base-10 logarithm;
CONC = constituent concentration, in indicated units;
FLOW = streamflow, in cubic feet per second;

I = an index for season (I= 0 for the nongrowing season, and I = | for the growing
season);

SLOPE) = the slope for the nongrowing season;

INT, =the intercept for the nongrowing season;

SLOPE) = the difference between the growing- and nongrowing-season slopes; and

INT, =the difference between the growing- and nongrowing-season intercepts.

A test statistic different from that used by Helsel and Hirsch (1992) was calculated
because of the use of Tobit regression in the analysis of covariance (T.A. Cohn, written commun.,
1995). The value, X, was determined from the results of the simple and complex models, then
compared to the value of the chi-square distribution with 2 degrees of freedom and a 0.05 level of
significance. If the value of X equalled or exceeded the corresponding value of chi-square
distribution, the seasonal relations differed from one another in SLOPE or INT or both. Whether
SLOPE was different or INT was different was not determined. The value of X was calculated as
follows:

= -2x In[ (LKHD,) /(LKHD,)] , (9)
where
x = the test statistic,
In = natural logarithm,
LKHDy = the likelihood of the simple relation, and
LKHD¢ = the likelihood of the complex relation.

The detection level of each constituent at each station is required to conduct Tobit
regression. The detection limits for constituents with only uncensored values were determined by
considering the method of analysis and the smallest concentration measured at all stations. These
values (table 4) are either equal to the smallest less-than value or slightly less than the smallest
uncensored value measured at all stations during water years 1976-93.

27


Pennsauken Creek

The Pennsauken Creek Basin has two water-quality stations—station 01467069 on the
North Branch of Pennsauken Creek near Moorestown and 01467081 on the South Branch of
Pennsauken Creek at Cherry Hill. The 5-year medians are smaller than the period-of-record
medians for TN, NO2, TAON, and NH4 at station 01467069; 5-year and period-of-record
medians are similar for all other constituents (table 23a). The 5-year medians are smaller than the
period-of-record medians for TP, TAON, and NH4 and larger for NO2 at station 01467081 (table
24a). At station 01467081, the period-of-record medians for HARD, DS, NA, CL, NO2, B, and
BACT are the largest for these constituents at all stations in the study area. The regression slopes
of concentration to streamflow for HARD, TOC, DS, NA, CL, DO, TP, NO32, NO2, NH4, and
BACT show seasonal dependency at station 01467069. The concentration slopes for HARD, DS,
NA, CL, DO, FDO, NO2, and BACT show seasonal dependency at station 01467081.

The regression slope of load to streamflow is in the high range only for ALK at station
01467069, indicating greater contribution of ALK from storm runoff relative to that at other sites
in the study area. The load slope for ALK at station 01467069 is the largest for this constituent in
the study area. Load slopes are in the low range for TOC, SS, and TAON at station 01467069 and
for HARD, DS, NA, TN, NO2, TAON, NH4, and B at station 01467081, indicating smaller
contributions of these constituents from storm runoff relative to that at other sites in the study
area. The load slopes for NO2 and TAON at station 01467081 are the smallest for these
constituents in the study area.

During low flows, trends are positive for HARD and CL at station 01467081, indicating
an increase in the contributions of these constituents from point sources and ground water over
time. Trends are negative for NA, TN, NO32, TAON, NH4, and PB at station 01467069 and for
TN at station 01467081, indicating a decrease in the contributions of these constituents from
storm runoff over time. Trends are insignificant during low flows for TOC, DS, FDO, and BACT
at both stations, for HARD and CL at station 01467069, and for NA, DO, NO32, TAON, and
NH4 at station 01467081. Insufficient data are available at both stations to determine trends for
all other constituents during low flows and for all constituents during high flows.

The AMNET impairment status is moderately impaired upstream and downstream from
station 01467069 (table 23b). The AMNET impairment status is severely impaired upstream and
downstream from station 01467081 (table 24b).

Cooper River

For the one station on the Cooper River, station 01467150 at Haddonfield, the 5-year
medians for TP, TN, NO32, NO2, TAON, and NH4 are smaller than the period-of-record medians
(table 25a). The period-of-record medians for SS, TP, TN, TAON, NH4, and PB are the largest
for these constituents at all stations in the study area. The regression slopes of concentration to
streamflow for HARD, DO, FDO, TP, NO2, and BACT show seasonal dependency. The
regression slopes of load to streamflow are in the high range for ALK, NA, and NO2, indicating
larger contributions of these constituents from storm runoff relative to that at other sites in the
study area. Insufficient data are available to determine trends during low flows for all

59


Dissolved Oxygen

Dissolved oxygen (DO) concentrations in surface water depend on the physical, chemical,
and biochemical activities occurring in the water body and are a function of water temperature,
atmospheric pressure, and concentrations of other solutes. The higher forms of aquatic life
require oxygen for survival, and the measurement of DO is used widely to evaluate the
biochemistry of surface water (Hem, 1985). Photosynthesis and water turbulence are important
mechanisms that replenish DO consumed by respiration and decomposition of organic matter.
Oxygen supersaturation can occur in slow moving systems in winter and when photosynthesizing
biota are abundant during the summer. The presence of organic compounds and abundant algae in
surface water can cause oxygen demand. Positive trends and steep slopes of load to streamflow
can indicate improved water quality.

Relation of trends i . fl iti

Dissolved oxygen concentrations during high flows show no trend at the one station on the
Toms River (4085); the downstream station on the Assunpink Creek (4640); the stations on the
McDonalds Branch (4665), Cooper River (46715), Raccoon Creek (47712), and Cohansey River
(4128); and the upstream station on the Maurice River (4115) (figs. 22a and 23a). Trends in
dissolved oxygen concentrations during low flows are positive at the stations on the Manasquan
River (4080) and North Branch of the Pennsauken Creek (467069) (figs. 23b and 24b). Dissolved
oxygen concentrations during low flows show no trend at all stations on the Toms (4085) and
Mullica (409387) Rivers, Hammonton Creek (409416), Batsto River (4095), West Branch of the
Wading River (409815), Oswego River (4100), East Branch of the Bass River (41015), Great Egg
Harbor River (410784, 4110, and 41111), Crosswicks (4645) and Doctors (464515) Creeks,
McDonalds Branch (4665), South (46585) and North (4670) Branches of the Rancocas Creek,
South Branch of the Pennsauken Creek (467081), Raccoon (47712) and Oldmans (47751) Creeks,
and Salem (4825), Cohansey (4128), and Maurice (4115 and 4118) Rivers (figs. 22b and 23b).

Relation of load to streamflow

The range categories of regression slopes of dissolved oxygen load to streamflow are
depicted in figures 22c and 23c. The range of slopes is narrow, ranging from 0.986 at the
upstream station on the Maurice River (4115) (table 31a) to 1.342 at station 4665 on the
McDonalds Branch (table 21a), the only station with a slope in the high range. The slopes are in
the low range at the stations on the Manasquan (4080), Toms (4085), Mullica (409387), Batsto
(4095), West Branch of the Wading (409815), and Oswego (4100) Rivers; the downstream
stations on the Great Egg Harbor River (4110 and 41111); the stations on the North Branch of the
Pennsauken Creek (467069) and South Branch of the Big Timber (467329) Creek; and the
upstream station on the Maurice River (4115).

Fraction of Dissolved Oxygen at Saturation

The fraction of dissolved oxygen at saturation is the ratio of the measured DO
concentration to the maximum DO concentration possible in the water. The maximum DO
concentration possible is a function of atmospheric pressure, water temperature, and specific

96


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Table 6a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01408500, Toms River near Toms River, N.J.

(Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -,negative trend direction; NA, insufficient

data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, i 30) 2 (77) -0.708 0.290 NA NA
Hardness, mg/L as CaCO; i (29) 1 (134) 184 * 816 0) -
Total organic carbon, mg/L as C ND (0) 6.8 (65) 398 * 1.398 NA NA
Suspended sediment, mg/L 8 (30) 9 (134) 405 * 1.405 0 0
Dissolved solids, mg/L 42 (29) 44 (132) -.056 944 0 0
Dissolved sodium, mg/L as Na 6 (29) 5 (137) -234 = * 766 + 0
Dissolved chloride, mg/L as Cl 10 (30) 8 (135) -.222 778 + +
Dissolved oxygen, mg/L 9.6 (30) 95 (136) 0 * 1.013 0 0
Fraction of dissolved oxygen at 91 (29) 91 (133) -066 * ND 0 0
saturation, %
Total phosphorus, mg/L as P 02 (30) 03 (135) -324* 675 - -
Total nitrogen, mg/L as N 9 (29) 8 (127) -314 * 685 0 0
Total nitrate plus nitrite, mg/L as N 40 (29) 39 (133) 683 * 317 0 0
Total nitrite, mg/L as N 008 (18) 010 (27) 0 909 NA NA
Total ammonia plus organic nitrogen, 40 = (30) 40 (130) 0 * 1.026 0 0
mg/L as N
Total ammonia, mg/L as N -16 (25) 10 (112) -.432 568 NA NA
Total boron, ug/L as B ND 0) 30 a) =ND ND NA NA
Total lead, g/L as Pb ND (0) 7 7) 0 * 944 NA NA
Fecal coliform bacteria, MPN/100 ml ND (0) 20 (4) ND ND NA NA

Table 6b, 1993 AMNET impairment status in the vicinity of water-quality station 01408500, Toms River near Toms River, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station

At WQ-station location

Downstream from WQ station

AMNET station

Impairment status

AN0524

Non-impaired

ANO0535

Non-impaired

None

ND

37


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CONVERSION FACTORS AND ABBREVIATED WATER-QUALITY UNITS

Multiply By
Length
mile (mi) 1.609
Area
square mile (mi?) 259.0
square mile (mi?) 2.590
Volume
gallon (gal) 3.785
gallon (gal) 0.003785
cubic foot (ft?) 0.02832
Flow
cubic foot per second (ft?/s) 0.02832
pounds per day (Ib/d) 0.4536
Mass
pound, avoirdupois (Ib) 0.4536

To obtain

kilometer

hectare
square kilometer

liter
cubic meter
cubic meter

cubic meter per second
kilograms per day

kilogram

Temperature given in degrees Fahrenheit (°F) and Celsius (°C) can be converted to degrees

Celsius (°C) and Kelvin (°K) by the following equations:

°C = 5/9 x (°F-32)
°K = 273.15 +°C

Water-quality abbreviations

pm - micrometer DO
s/d - seconds per day FDO
mg/L - milligrams per liter
ng/L - micrograms per liter TP
MPN/100mL- most probable number of TN
bacteria per 100 milliliters NO32
ALK - alkalinity NO2
HARD - hardness TAON
TOC - total organic carbon
Ss - suspended sediment NH4
DS - dissolved solids B
NA - dissolved sodium PB

CL - dissolved chloride BACT

xii

- dissolved oxygen

- fraction of dissolved oxygen
at saturation

- total phosphorus

- total nitrogen

- total nitrate plus nitrite

- total nitrite

- total ammonia plus organic
nitrogen

- total ammonia

- total boron

- total lead

- fecal coliform bacteria


Comparison of results .

References cited

CONTENTS—Continued

Relation of trends in concentration to flow conditions ..........ceseeeeeeene 97
Total phosphorus
Relation of trends in concentration to flow conditions
Relation of load to streamflow ...........escscsseeeneeeeeeeee
Total nitrogen
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Total nitrate plus nitrite. .
Relation of trends i in n concentration to flow ‘conditions.
Relation of load to streamflow
Total nitrite
Relation of trends in concentration to flow conditions
Relation of load to streamflow .........s.ccecseseseeeseseeeeee
Total ammonia plus organic nitrogen
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Total ammonia
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Total boron
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Total lead... sees
Relation of trends i in n concentration to flow ‘conditions
Relation of load to streamflow .........ssesseseesseseeeeseseeenee
Fecal coliform bacteria
Relation of trends in concentration to flow conditions

Appendixes 1-18. Relations of constituent concentration and load to streamflow and trends
in concentration with time (Available on CD-ROM from U.S. Geological Survey, New Jersey
District (609-771-3900):

1.

SeEPADMAPWN

Alkalinity

Hardness

Total organic carbon

Suspended sediment

Dissolved solids

Dissolved sodium

Dissolved chloride

Dissolved oxygen

Fraction of dissolved oxygen at saturation
Total phosphorus


REFERENCES CITED

Anderson, P.W., and George, J.R., 1966, Water-quality characteristics of New Jersey streams:
U.S. Geological Survey Water-Supply Paper 1819-G, 48 p.

Anderson, P.W., and McCarthy, L.T., Jr., 1963, Chemical character of streams in the Delaware
River basin: U.S. Geological Survey Open-File Report, 11 p.

Bares, R.S.K., and Mann, K.H., eds., 1991, Fundamentals of aquatic ecology: Oxford, Blackwell
Scientific Publications, 270 p.

Bauersfeld, W.R., Moshinsky, E.W., and Gumey, C.E., 1994, Water resources data for New
Jersey—water year 1993, volume 1, surface-water data: U.S. Geological Survey Water-
Data Report NJ-93-1, 503 p.

Bauersfeld, W.R., Moshinsky, E.W., Pustay, E.A., and Jones, W.D., 1990, Water resources data
for New Jersey—water year 1989, volume 2, Delaware River Basin and Tributaries to
Delaware Bay: U.S. Geological Survey Water-Data Report NJ-89-2, 215 p.

Breidt, F.J., Boes, D.C., Wagner, J.I., and Flora, M.D., 1991, Antidegradation water quality
criteria for the Delaware River: A distribution-free statistical approach: Water Resources
Bulletin, v. 27, no.5, p. 849-858.

Buxton, D.E., and Dunne, Paul, 1993, Water-quality data for the Millstone River at Weston, New
Jersey, and the Shark River at Remsen Mill, New Jersey, March-September 1992:
U.S. Geological Survey Open-File Report 93-444, 16 p.

Buxton, D.E., Hunchak-Kariouk, Kathryn, and Hickman, R.E., 1998, Relations of surface-water
quality to streamflow in the Hackensack, Passaic, Elizabeth, and Rahway River Basins:
U.S. Geological Survey Water-Resources Investigations Report 98-4049, 102 p.

Chow, V.T., 1964, Handbook of applied hydrology: New York, McGraw Hill, Inc., 1418 p.

Cohn, T.A., 1988, Adjusted maximum estimation of the moments of lognormal populations from
type | censored samples: U.S. Geological Survey Open-File Report 88-350, 34 p.

Eaton, A.D., Clesceri, L.S., and Greenberg, A.E., eds., 1995, Standard methods for the
examination of water and wastewater (19th ed.): Washington, D.C., American Public
Health Association, 948 p.

Fishman, M.J., Raese, J.W., Gerlitz, C.N., and Husband, R.A., 1994, U.S. Geological Survey
approved inorganic and organic methods for the analysis of water and fluvial sediments,
1954-94: U.S. Geological Survey Open-File Report 94-351, 55 p.

Friedman, L.C., and Fishman, M.J., 1989, Evaluation of methods used from 1965 through 1982 to

determine inorganic constituents in water samples: U.S. Geological Survey Water-Supply
Paper 2293, 126 p.

142


The NJDEP sampling techniques and biometric assessments were modified from U.S.
Environmental Protection Agency protocols to integrate community, population, and functional
parameters into one easily understood evaluation of biological integrity (New Jersey Department
of Environmental Protection, 1996a and 1996b). The integrated assessment results at each station
were given an AMNET impairment status rating of non-impaired—the benthic community is
comparable to communities found in other undisturbed streams within the region and is
characterized by a maximum taxa richness, balanced taxa groups, and good representation of
intolerant individuals; moderately impaired—the macroinvertebrate richness and community
balance are reduced and intolerant taxa are absent because of taxa composition changes; or
severely impaired—the benthic community has dramatically changed and macroinvertebrates are
dominated by a few tolerant taxa. When used together with chemical and physical monitoring,
benthic macroinvertebrate monitoring is a good indicator of stream quality and possible sources
of impairment.

Atlantic Coastal Basin

Eleven water-quality stations are located in four subbasins in the Atlantic Coastal Basin.
One station is located on each of the Manasquan and Toms Rivers. Six stations are located in the
Mullica River Basin—one on the main stem of the Mullica and one on each of the Hammonton
Creek; Batsto River; Oswego River, West Branch of the Wading River, a tributary to the Oswego
River; and the East Branch of the Bass River. Three stations are located on the main stem of the
Great Egg Harbor River.

Manasquan River

For the one station on the Manasquan River, station 01408000 at Squankum, the 5-year
medians are smaller than the period-of-record medians for TOC, TP, TN, NO32, NO2, TAON,
NH4, and BACT; 5-year and period-of-record medians are similar for all other constituents (table
5a). The regression slopes of concentration to streamflow for DO, FDO, TP, TN, NO2, NH4, and
BACT show seasonal dependency. The regression slopes of load to streamflow are in the high
range for SS, TP, TN, and NH4, indicating greater contributions of these constituents from surface
runoff relative to that at other sites in the study area. The load slopes for SS and NH4 at this site
are the largest for these constituents in the study area. The load slopes are in the low range for
HARD, indicating smaller contributions of this constituent from storm runoff relative to that at
other sites in the study area. The load slope for HARD is the smallest for HARD in the study
area. During low flows, the trend is positive for DO and FDO and insignificant for BACT. The
trend is negative for TAON during low flow, indicating a decrease in the contributions of TAON
from point sources and ground water over time. Insufficient data are available to determine trends
for all other constituents during low fiow and for all constituents during high flows. The AMNET
impairment status is moderately impaired at, and upstream and downstream from, station
01408000 (table Sb).

34


Table 27a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01477120, Raccoon Creek near Swedesboro, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO3, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; 1g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression  Low- High-
Constituent comentaton coneemaion—cacentaon advo end)—_ trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO; 25 (27) 28 (74) 0.500 * 0.500 NA NA
Hardness, mg/L as CaCO; 63 (27) 63 (en8)) ~167  * 833 0 0
Total organic carbon, mg/L as C 3.3 (27) 3.6 (107) 163 * 1.163 - )
Suspended sediment, mg/L 12 @) 13 (17) 892 1.890 NA NA
Dissolved solids, mg/L 122 (25) 117 (105) -1220 * 878 NA +
Dissolved sodium, mg/L as Na 8 (27) 6 dll) 122 878 0 +
Dissolved chloride, mg/L as Cl 16 (27) 13 (110) -.073 927 + +
Dissolved oxygen, mg/L 93 (27) 94 (110) 102 * 1.102 0 0
Fraction of dissolved oxygen at 89 (26) 93 (101) 0 ND - 0
saturation, %
Total phosphorus, mg/L as P. cll (25) sll (100) 0 * 1.031 0) NA
Total nitrogen, mg/L as N 27 (27) 2.2 (97) .260 1.260 0 0
Total nitrate plus nitrite, mg/L as N 2.00 (27) 1.69 (99) 2520 * 1.252 0 0
Total nitrite, mg/L as N .020 (27) 018 (80) 0 * 866 NA NA
Total ammonia plus organic nitrogen, 47 (27) 50 (106) 0 * 1.141 0 0
mg/L as N
Total ammonia, mg/L as N 08 (27) 09 = (95) 0 1,093 0 NA
Total boron, pg/L as B 40 (O) 40 (17) 0 719 NA NA
Total lead, pg/L as Pb 1 (0) 2 @y 770 1.770 NA NA
Fecal coliform bacteria, MPN/100 ml 340 (25) 230 (107) 0 * ND 0 0

Table 27b. 1993 AMNET impairment status in the vicinity of water-quality station 01477120, Raccoon Creek near Swedesboro, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-siation location Downstream from WQ station
AMNET station AN0680 ANO683 AN0685
Impairment status Moderately impaired Moderately impaired Moderately impaired

65


direction along a stream would indicate an increase in the relative contribution to the instream
load from point sources and ground water and would be evident if the order of circles proceeded
from solid to hashed to quartered in the downstream direction.

Alkalinity

Alkalinity, an aggregate property of water, is a measure of the capacity of water to
neutralize acids and is the sum of all the titratable bases in solution (Eaton and others, 1995). The
carbonate contributors to alkalinity, carbonate and bicarbonate, result from the dissociation of
dissolved carbon dioxide. The important noncarbonate contributors to alkalinity include
hydroxides, silicates, borates, phosphates, and organic ligands, especially acetate and propionate.
In many surface-water bodies, alkalinity is primarily a function of carbonate, bicarbonate, and
hydroxide, and represents their combined concentrations. Alkalinity measurements are important
in the evaluation and control of potable water and wastewater processes, including chemical
coagulation, water softening, corrosion control, and buffer capacity evaluation. In surface water
that supports extensive algal blooms, consumption of carbon dioxide by algae for photosynthesis
causes an increase in pH due toa shift in the forms of alkalinity, although there is no change in the
total alkalinity (Sawyer and McCarty, 1978). Alkalinity in excess of alkaline-earth element
concentrations could make water unsuitable for irrigation. Carbonate concentrations can be
estimated from alkalinity measurements and used to compute the ion balance when checking
water analyses.

Relation of trends i ‘onto fl titi

Insufficient data are available to determine trends in alkalinity during high and low flows
at all stations in the study area (figs. 8a, 9a, 8b, and 9b).

The range categories of regression slopes of alkalinity load to streamflow are depicted in
figure 8c and 9c. The slopes range from zero at stations on the Mullica (409387) and Batsto
(4095) Rivers, East Branch of the Bass River (41015), and Great Egg Harbor (4110) River (tables
7a, 9a, 12a, and 14a, respectively) to 0.976 at station 467069 on the North Branch of the
Pennsauken River (table 23a). Slopes are in the high range at stations on the Hammonton Creek
(409416), West Branch of the Wading River (409815), Doctors Creek (464515), North Branch of
the Pennsauken (467069) Creek, Cooper River (46715), South Branch Big Timber Creek
(467329), and Salem (4825) and Cohansey (4128) Rivers. At these sites, the contributions to
instream alkalinity loads from storm runoff are larger and less influenced by point sources and
ground water than at other sites in the study area. Slopes are in the low range at stations on the
Mullica (40937), Batsto (4095), and East Branch of the Bass (41015) Rivers, and the downstream
stations on the Great Egg Harbor River (4110 and 41111). At these stations, the contributions to
instream alkalinity loads from constant sources (most likely ground water) are larger and less
influenced by storm runoff than at other sites in the study area.

14


RELATIONS OF SURFACE-WATER QUALITY TO
STREAMFLOW IN THE ATLANTIC COASTAL, LOWER
DELAWARE RIVER, AND DELAWARE BAY BASINS,
NEW JERSEY, WATER YEARS 1976-93

By Kathryn Hunchak-Kariouk, Debra E. Buxton, and R. Edward Hickman

U.S. Geological Survey
Water-Resources Investigations Report 98-4244

Prepared in cooperation with the
NEW JERSEY DEPARTMENT OF ENVIRONMENTAL PROTECTION

West Trenton, New Jersey
1999

aUSGS

science for a changing world


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CONTENTS—Continued

Mullica RiVeP oo... eeeeseeseeseesee cence sesteseesueeeeseaeeee
Great Egg Harbor River
Lower Delaware River Basin.
Assunpink Creek.
Crosswicks Creek
Rancocas Creek...
Pennsauken Creek
Cooper River
South Branch Big Timber Creek.
Raccoon Creek...
Oldmans Creek.
Salem River..
Delaware Bay Basin.
Cohansey River
Maurice River
Analysis of relations by constituent
Alkalinity
Relation of trends in concentration to flow conditions
Relation of load to streamflow ..........cccccseeeeceeneees
HardneS.........ccesceesseecssesseeeseesneesecsessessseesseeseessneeseesnees
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Total organic carbon.
Relation of trends in concentration to flow conditions
Relation of load to streamflow...
Suspended sediment... cece
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Dissolved SOldS ........c.secsecscesecseesesseeeeseeseesneseesnenteneenees
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Dissolved sodium
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Dissolved chloride
Relation of trends in concentration to flow conditions
Relation of load to streamflow
Dissolved oxygen seeseereneareneee
Relation of trends in concentration to flow conditions
Relation of load to streamflow...
Fraction of dissolved oxygen at saturation



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Steps were taken to ensure consistent data quality because of the long time period over
which the data were collected. Water-quality data for the period of record, water years 1976 to
1993, were reviewed to identify any obvious data inconsistencies (that is, data outliers) because of
changes in laboratory remark codes, reporting levels, analytical methods, project data entry
protocols, project data-quality review protocols, sample preservation, and sample processing.
Many of these factors were known to have changed over the 18-year period of record; this may
have affected the quality of the data (in this study, only data outliers were of concern). Breidt and
others (1991) reported finding similar water-quality-data anomalies in this period of record. This
review resulted in the removal from the data base of less than | percent of the original data set.
Most of the corrections (removal) were for ficld measurements made prior to 1985 and for data
that had been entered into the data base manually from paper records.

No attempt was made to identify data-biasing effects on the median values. The data
review was performed prior to statistical analysis and interpretation. Data in the 0.025 and 0.975
percentiles for cach station were candidates for being data outliers. In addition, plots of
constituent concentrations by month, as well as constituent concentrations as a function of
streamflow, were visually inspected for potential outliers. Data were evaluated by month of
sample collection to determine whether a value was a seasonal outlier, and by discharge to
determine whether the value was an outlier because it was affected by dilution during high flow.
In addition, changes in laboratory reporting remark codes and censoring limits were reviewed.
The analytical method used for the years in which the censored data were collected was
determined from tables reported by Friedman and Fishman (1989) and Fishman and others
(1994), and the analytical method lower-reporting limit was checked against those reported for
that analytical method in Skougstad and others (1979), Fishman and Friedman (1989), and
Wershaw and others (1987). The outliers were evaluated by considering:

(1) concentrations of related constituents in the same sample,

(2) the constituent concentration at sites upstream or downstream,

(3) the effects of an early or late change of season,

(4) the number of measurements for the month or season,

(5) the presence of point-source discharges upstream from the sampling site,

(6) the possibility of constituent inputs from seasonal nonpoint-source runoff,

(7) streamflow regulation,

(8) the streamflow discharge, and

(9) surrounding geology and physiographic province.

Outliers were deleted only if no plausible explanation based on the factors listed above
was found.

Streamflow Data

Instantaneous-streamflow values were used when available to calculate instream loads;
when those values were not available, an estimated daily mean was used. Continuous streamflow
records from gages were available for 18 water-quality stations and were used to determine
instantaneous streamflows. For the 10 stations with no streamflow data, a correlation with an
adjacent gaging station was developed, and a mean daily streamflow was estimated from the
correlation.

22


Branch of the Bass (41015) River; the upstream (410784) and downstream (41111) stations on the
Great Egg Harbor River; and the stations on the Crosswicks Creek (4645), Doctors Creek
(464515), South (46585) and North (4670) Branches of the Rancocas Creek, North (467069) and
South (467081) Branches of the Pennsauken Creek, Oldmans (47751) Creek, and Salem (4825)
and Cohansey (4128) Rivers.

Relation of load to streamflow

The range categories of regression slopes of TOC load to streamflow are depicted in
figures 12c and 13c. The slopes range from 0.839 at station 4825 on the Salem River (table 29a)
to 1.788 at the downstream station on the Great Egg Harbor River (41111) (table 15a). Slopes are
in the high range at the station on the East Branch of the Bass River (41015), the downstream
stations on the Great Egg Harbor River (4110 and 41111), the one station on the McDonalds
Branch (4665), and the upstream station on the Maurice River (4115). At these sites, the
contributions to instream TOC loads from storm runoff (most likely water displaced from
wetlands) are larger and less influenced by constant sources than at other sites in the study area.
Slopes are in the low range at the stations on the Hammonton Creek (409416) and West Branch of
the Wading River (409815); the upstream station on the Assunpink Creek (46362); and the
stations on the Doctors (464515), North Branch of the Pennsauken (467069), and Oldmans
(47751) Creeks and the Salem River (4825). At these sites, however, the contributions to
instream TOC loads from constant sources probably are relatively insignificant because the load-
to-streamfiow slopes are large (greater than 0.8). Storm runoff most likely is the dominant
contributor of TOC in the study area because the load-to-streamflow slopes at all stations are
large.

Suspended Sediment

Suspended sediment, an aggregate property of water, is the portion of total solids that is
retained by a filter under specified conditions; its concentration is determined by the weight of the
dry residue remaining after evaporation of the volatile portion of a sample aliquot by heating to
105 °C (Eaton and others, 1995). Large concentrations of suspended sediments in surface water
could inhibit light penetration to bottom-dwelling macrophytes and create esthetically
unsatisfactory conditions for such purposes as swimming. Some metals, nutrients, and organic
compounds can associate with the surface of the suspended sediment and be transported with the
suspended sediment in surface water. Suspended sediment concentration is the velocity-weighted
concentration of suspended sediment in the sampled zone (from the water surface to a constant
approximately 0.3 feet above the bed) (Bauersfeld and others, 1994). Generally, the primary

- source of suspended sediment in a stream is from erosion, streambed scour and overland runoff
during storm events.

ati t i tion t

Suspended sediment concentrations show no trend at the stations on the Toms River
(4085) and McDonalds Branch (4665) during high (figs. 14a and 15a) and low (figs. 14b and 15b)
flows. Sufficient data are not available for all other stations to determine trends in concentrations

81


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Approach

A river receives constituents from point and nonpoint sources within the contributing
drainage basin. Point sources are discrete, identifiable origins of constituents, such as permitted
discharges from municipal- and industrial-wastewater treatment facilities, that contribute water to
a stream at a constant rate, independent of streamflow conditions. Constituents from more
diffuse, nonpoint sources are transported to the river by storm runoff from agricultural,
residential, and urban areas and impervious surfaces (highways and parking lots), and by ground
water that could contain effluent from leaking underground-storage tanks, septic systems, and
landfills. Storm runoff, composed of overland runoff (water that flows overland when
precipitation exceeds the infiltration rate) and interflow (infiltrated water that moves in a
horizontal direction in the lower permeable subsoil), contributes to a stream intermittently,
depending on storm intensity and frequency, and only during high flows (Chow, 1964; Novotny
and Chesters, 1981). Ground-water discharge to a stream is almost constant, although it varies
slightly with season and precipitation rate. Instream concentrations of constituents are a
summation of the contributions from constant (point sources and ground-water discharge) and
intermittent (storm runoff) sources.

The magnitude, or steepness, of the regression slope for constituent loads to streamflow
indicates the relative contributions of constant and intermittent sources at a river location. The
steeper the slope, the greater the contribution from nonpoint sources during increased streamflow.
If the contributions to instream load are mainly from point sources and ground water, instream
load will remain constant with increasing streamflow, and the regression slope of load to
streamflow will be approximately zero (fig. 2). If, however, storm runoff contributes a
disproportionate amount to instream load, instream load will increase with increasing streamflow,
and the regression slope of load to streamflow will be greater than zero (fig. 2). A steep slope
does not imply that contributions from constant sources are unimportant, just that intermittent
sources contribute more to instream load during high flows than do constant sources. Price and
Schaefer (1995) used this approach (steepness of the load-to-streamflow regression line) to assess
the relative contributions of permitted and nonpermitted sources in the Musconetcong, Rockaway,
and Whippany River Basins. An idealized example of the relation of load to streamflow is shown
in figure 3. For site 01380500, the Rockaway River above the reservoir at Boonton, the slope of
the regression line is steeper (the estimated total median load from permitted point sources
upstream was approximately 100 Ibs/d) than the slope for site 01381200, Rockaway River at Pine
Brook (the estimated median load from permitted point sources was approximately 1,000 Ibs/d).
In the example, the relative importance of nonpoint sources is greater at station 01380500 than at
site 01381200, and the relative importance of point sources is greater at site 01381200 than at site
01380500.

Concentrations of constituents cannot be related to streamflow in this way because
contributions from storm runoff are flow dependent, and a small concentration can represent a
large instream load during high-flow conditions. If constituents are contributed to a stream
mostly from constant sources, then instream concentrations will be diluted during periods of high
fiow. If, however, storm runoff contributes significant amounts of constituents to a stream, then


Table 13a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01410784, Great Egg Harbor River near Sicklerville, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; ig/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY

Regression Regression  Low- High-

Constituent Median Median, slope of slope of flow flow
concentration concentration concentration load to trend trend

to streamflow streamflow direction —_ direction
Alkalinity, mg/L as CaCO; 6 (27) 8 (74) -0.724 0.276 NA NA
Hardness, mg/L as CaCO, 15 (27) 19 (96) 166 * 834 NA NA
Total organic carbon, mg/L as C 10.0 (27) 8.6 (108) 427 * 1.427 0 NA
Suspended sediment, mg/L 4 (on) 6 (28) 780 * 1.777 NA NA
Dissolved solids, mg/L 59 (27) 71 (93) 0 * 986 NA NA
Dissolved sodium, mg/L as Na 5 (27) 9 (99) -214* .786 NA NA
Dissolved chloride, mg/L as Cl 9 (27) 12 (99) 0 * 910 NA NA
Dissolved oxygen, mg/L 7.8 (27) 69 (111) 102 * 1,102 tv) NA
Fraction of dissolved oxygen at 80 Q7) 67 (109) 0 * ND 0 NA
saturation, %
Total phosphorus, mg/L as P 09 (27) 31 (80) -.433 567 NA NA
Total nitrogen, mg/L as N 1 (26) 2.2 (100) 355 645 0 NA
Total nitrate plus nitrite, mg/L as N .57— (27) 1.00 (103) -.697 302 - NA
Total nitrite, mg/L as N .008 (27) O11 (88) 0 .737 NA NA
Total ammonia plus organic nitrogen, 60 (26) 82 (107) 0 1.064 0 NA
mg/L as N

Total ammonia, mg/L as N .04 (26) 1S (101) 0 1.180 0 NA
Total boron, j1g/L as B 50 (5) 80 (17) 0 1,099 NA NA
Total lead, g/L as Pb 4 (5) 4 (18) 0 1.611 NA NA
Fecal coliform bacteria, MPN/100 mi 125 (24) 80 (89) 0 * ND NA NA

Table 13b. 1993 AMNET impairment status in the vicinity of water-quality station 01410784, Great Egg Harbor River near Sicklerville, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station AN0620 AN0621 AN0623
Impairment status Moderately impaired Non-impaired Non-impaired

46


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show seasonal dependency. The regression slope of load to streamflow is in the high range for
NA, indicating a larger contribution from storm runoff relative to that at other sites in the study
area. The load slopes are in the low range for HARD, TOC, TAON, B, and PB, indicating smaller
contributions of these constituents from storm runoff relative to that at other sites in the study
area. During low flows, the trends are positive for NA and FDO, indicating an increase in the
contributions of these constituents from point sources and ground water over time. Trends are
insignificant for HARD, TOC, DS, CL, DO, TN, NO32, TAON, NH4, and BACT during low
flows. Insufficient data are available to determine trends for all other constituents during low
flows and for all constituents during high flows. The AMNET impairment status is moderately
impaired at and upstream and downstream from station 01477510 (table 28b).

Salem River

For the one station on the Salem River, station 01482500 at Woodstown, the 5-year and
period-of-record medians are similar for all constituents (table 29a). The regression slopes of
concentration to streamflow for ALK, HARD, TOC, SS, NA, CL, DO, TP, TN, NO32, NO2, and
TAON show seasonal dependency. The regression slopes of load to streamflow are in the high
range for ALK, TN, NO32, and NO2, indicating larger contributions of these constituents from
storm runoff relative to that at other sites in the study area. The load slope for NO32 at station
01482500 is the largest for NO32 in the study area. The load slopes are in the low range for TOC
and SS, indicating smaller contributions of these constituents from storm runoff relative to that at
other sites in the study area. The load slope for TOC at station 01482500 is the smallest for this
constituent in the study area. During low flows, the trend is positive for NA, CL and BACT,
indicating an increase in the contributions of these constituents from point sources and ground
water over time. Trends are insignificant for HARD, TOC, DS, DO, FDO, TN, NO32, TAON,
and NH4 during low flows. Insufficient data are available to determine trends for all other
constituents during low flows and for all constituents during high flows. The AMNET
impairment status is severely impaired at station 01482500 and moderately impaired upstream
and downstream from the station (table 29b).

Delaware Bay Basin

Three water-quality stations are located on two streams in the Delaware Bay Basin. One
station is located on the Cohansey River and two stations are located on the Maurice River.

Cohansey River

For the one station on the Cohansey River, station 01412800 at Seeley, the 5-year and
period-of-record medians are similar for all constituents (table 30a). The period-of-record median
for NO32 is the largest for NO32 at all stations in the study area. The regression slopes of
concentration to streamflow for ALK, TOC, DO, TN, NO32, NO2, and BACT show seasonal
dependency. The regression slopes of load to streamflow are in the high range for ALK, TP, NO2,
and B, indicating greater contributions of these constituents from surface runoff relative to that at
other sites in the study area. The load slopes for TP and NO2 are the largest for these constituents
in the study area. The load slopes are in the low range for DS, NA, and CL, indicating smaller

67


Table 4. Estimated detection limits for selected constituents measured in the Atlantic Coastal,
lower Delaware River, and Delaware Bay Basins, N.J., water years 1976-93

(mg/L, milligrams per liter; CaCO3, calcium carbonate; C, carbon; Na, sodium, Cl, chloride;
%, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead;
MPN/100 mL, most probable number per 100 milliliters.]

Estimated
Constituent detection limit
Alkalinity, mg/L as CaCO; 1
Hardness, mg/L as CaCO3, 10
Total organic carbon, mg/L as C 2
Suspended sediment, mg/L ‘ 1
Dissolved solids, mg/L 10
Dissolved sodium, mg/L as Na 1
Dissolved chloride, mg/L as Cl 1
Dissolved oxygen, mg/L 5
Fraction of dissolved oxygen at saturation, % 5
Total phosphorus, mg/L as P 01
Total nitrogen, mg/L as N Jl
Total nitrate plus nitrite, mg/L as N 05
Total nitrite, mg/L as N 002
Total ammonia plus total organic nitrogen, mg/L as N 03
Total ammonia, mg/L as N 01
Total boron, mg/L as B 10
Total lead, mg/L as Pb ]
Fecal coliform bacteria, MPN/100 mL 2

28


runoff relative to that at other sites in the study area. The load slopes for NA and TP at station
01409416 are the smallest for these constituents in the study area. During low flows, the trend is
positive for BACT, indicating an increase in the contributions of BACT from point sources and
ground water over time, and insignificant for TOC, NA, DO, FDO, TN, NO32, TAON, NH4, and
BACT. Insufficient data are available to determine trends for all other constituents during low
flows and for all constituents during high flows. The AMNET impairment status is severely
impaired upstream and non-impaired downstream from station 01409416 (table 8b).

For the one station on the Batsto River, station 01409500 at Batsto, the 5-year and period-
of-record medians are similar for all constituents (table 9a). The period-of-record medians for
NA, CL, and B at station 01409500 are the smallest for these constituents of all stations in the
study area. The regression slopes of concentration to streamflow for ALK, HARD, TOC, CL,
DO, and NO32 show seasonal dependency. The regression slopes of load to streamflow for
HARD, DS, NA, CL, TN, and NH4 arc in the high range, indicating greater contributions of these
constituents from storm runoff relative to that at other sites in the study area. The load slopes for
HARD and CL at station 01409416 are the largest for these constituents in the study area. Load
slope for ALK is in the low range, indicating smaller contributions of this constituent from storm
runoff relative to that at other sites in the study area, The load slope for HARD at station
01409416 is the largest for HARD in the study area. Trends are insignificant for HARD, TOC,
DS, NA, CL, DO, FDO, TN, NO32, NO2, TAON, NH4, and BACT during low flow. Insufficient
data are available to determine trends for all constituents during high flows. The AMNET
impairment status is non-impaired at station 01409500 and moderately impaired upstream from
the station (table 9b).

For the one station on the West Branch of the Wading River, station 01409815 at Maxwell,
the 5-year and period-of-record medians are similar for all constituents (table 10a). The period-
of-record medians for ALK, HARD, NA, CL, TN, NO32, and NH4 at station 01409815 are the
smallest for these constituents at all stations in the study area. The regression slopes of
concentration to streamflow for HARD, SS, DS, NA, DO, FDO, TP, TN, and TAON show
seasonal dependency. The regression slope of load to streamflow for ALK is in the high range,
indicating a greater contribution from storm runoff relative to that at other sites in the study area.
Load slopes for TOC, SS, and NH4 are in the low range, indicating a smaller contribution from
storm runoff relative to that at other sites in the study area. During low flows, the trends are
positive for NA and CL, indicating an increase in the contributions of these constituents from
point sources and ground water over time. The trends are insignificant for HARD, DS, DO, FDO,
TP, and TAON during low flow. Insufficient data are available to determine trends for all other
constituents during low flows and for all constituents during high flows. The AMNET
impairment status is non-impaired at station 01409815 (table 10b).

For the one station on the Oswego River, station 01410000 at Harrisville, the 5-year
median is greater than the period-of-record median for NO32; 5-year and period-of-record
medians are similar for all other constituents (table 11a). The period-of-record medians for ALK,
NA, CL, PB, and BACT at station 01410000 are the smallest for these constituents at all stations
in the study area. The regression slopes of concentration to streamflow for TOC, DO, TN, and
TAON show seasonal dependency. The regression slope of load to streamflow for NO2 is in the
high range, indicating a greater contribution from storm runoff relative to that at other sites in the

40


Relati tr i jon t iti

During high flows, trends in total nitrite concentrations were negative at the downstream
station on the Assunpink Creek (4640) and the one station on the Cooper River (46715),
indicating a decrease in the contributions from storm runoff over time at these sites (figs. 32a and
33a). The trends in total nitrite concentrations during low fiows are insignificant at the stations on
the Great Egg Harbor (4110) and Batsto (4095) Rivers and the downstream station on the Maurice
River (4118) (figs. 32b and 33b).

Relation of load to streamflow

The range categories of regression slopes of total nitrite load to streamflow are depicted in
figures 32c and 33c. The slopes range from 0.234 at station 467081 on the South Branch of the
Pennsauken Creek (table 24a) to 1.442 at station 4128 on the Cohansey River (table 30a).
Insufficient data were available to determine the slopes at the stations on the West Branch of the
Wading River (409815) and McDonalds Branch (4665). Slopes are in the high range at the
stations on the Oswego (4100) and East Branch of the Bass (41015) Rivers, the downstream
station on the Great Egg Harbor River (41111), the upstream station on the Assunpink Creek
(46362), and the stations on the North Branch of the Rancocas Creek (4670), and the Cooper
(46715), Salem (4825), and Cohansey (4128) Rivers. At these sites, the contributions to instream
total nitrite loads from storm runoff are larger and less influenced by constant sources than at
other sites in the study area. The slope is in the low range only at the one station on the South
Branch of the Pennsauken Creek (467081) where the contribution to instream total nitrite loads
from storm runoff is smaller and more influenced by point sources and (or) ground water than at
other sites in the study area. Slopes at stations on the Great Egg Harbor River increase in the
downstream direction, indicating an increase in the relative influence of contributions from storm
runoff along the river, whereas slopes at stations on the Assunpink Creek decrease in the
downstream direction, indicating a decrease in the relative influence of contributions from storm
runoff along the river.

Total Ammonia Plus Organic Nitrogen

Organic nitrogen is defined as organically bound nitrogen in the tri-negative oxidation
state. It includes many natural materials, such as proteins, peptides, nucleic acids, and urea, and
synthetic organic compounds, but does not include all organic nitrogen compounds. Ammonia is
produced by the deamination of organic nitrogen-containing compounds. Ammonia can enter
surface water dissolved in wastewater effluent, storm runoff, and rain. Temperature, pH, and
ionic strength control the speciation of ammonia in surface water. The un-ionized form of
ammonia, more common in low pH and low ionic strength waters, is toxic to fish. The total
ammonia plus organic nitrogen concentrations are determined together by the kjeldahl method
(Eaton and others, 1995).

109


Table 12a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01410150, East Branch Bass River near New Gretna, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO3, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 1 (27) 1 (75) 0.553 0 NA NA
Hardness, mg/L as CaCO, 4 (26) 4 (95) 0 1.069 0 NA
Total organic carbon, mg/L as C 5.0 (26) 48 (96) 602 * 1.601 0 NA
Suspended sediment, mg/L 2 (10) 2 (27) 0 1.452 NA NA
Dissolved solids, mg/L 28 (27) 29 (93) 0 1.080 0 NA
Dissolved sodium, mg/L as Na 3 (27) 3 (98) 079 1.078 0 NA
Dissolved chloride, mg/L as Cl 6 (27) 5 (97) 054 1.054 0 NA
Dissolved oxygen, mg/L 7.6 (27) Vd (97) 105 * 1.105 0 NA
Fraction of dissolved oxygen at 72 (26) 75 (93) 0 * ND 0 NA
saturation, %
Total phosphorus, mg/L as P 02 (26) 02 (64) 0 1.077 NA NA
Total nitrogen, mg/L as N 4 (27) 4 (84) 0 997 0 NA
Total nitrate plus nitrite, mg/L as N AS (27) 05 (85) 0 1.295 0 NA
Total nitrite, mg/L as N .003 (26) 003 (76) 0 1.267 NA NA
Total ammonia plus organic nitrogen, 24 (27) 27° 1) 0 1.006 0 NA
mg/L as N
Total ammonia, mg/L as N 03 (27) 05 (86) 0 666 0 NA
Total boron, j1g/L as B <10 (7) 10 (13) ND ND NA NA
Total lead, j1g/L as Pb 2 (7) 3 (16) 0 0 NA NA
Fecal coliform bacteria, MPN/100 ml 20 (25) 10 (95) 0 ND 0 NA

Table 12b. 1993 AMNET impairment status in the vicinity of water-quality station 014101 50, East Branch Bass River near New Gretna, N.J.

[AMNET, Ambient Biomonitoring Network, WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO611 None None
Impairment status Non-impaired ND ND

45


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130


Table 9a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01409500, Batsto River at Batsto, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value}

1989-93 WY 1976-93 WY
Regression Regression Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO; 2 (27) 2 (73) 0.778 * 0 NA NA
Hardness, mg/L as CaCO; 9 27) 8 (99) 305 * 1.305 0 NA
Total organic carbon, mg/L as C 5.8 (26) 55 (97) ams * 1.475 0 NA
Suspended sediment, mg/L. 2 ay 3 (30) 0 1.402 NA NA
Dissolved solids, mg/L 31 (26) 32 (93) 287 1.287 0 NA
Dissolved sodium, mg/L as Na 3 (27) 2 (99) 0 1.014 0 NA
Dissolved chloride, mg/L as Cl 5 (27) 4 (100) 128 * 1.128 0 NA
Dissolved oxygen, mg/L 90 (27) 92 (99) 0 * 1.037 0 NA
Fraction of dissolved oxygen at 87 (24) 89 (95) -.064 ND 0 NA
saturation, %
Total phosphorus, mg/L as P 03 (26) 02 (68) 0 817 NA NA
Total nitrogen, mg/L as N 6 (26) 5 (83) 336 1.336 0 NA
Total nitrate plus nitrite, mg/L as N 24 (26) 10 (85) 642 * 1.642 0 NA
Total nitrite, mg/L as N .004 (26) .004 (79) 0 1.136 0 NA
Total ammonia plus organic nitrogen, 40 (27) 36 © (95) 250 1.250 0 NA
mg/L as N
Total ammonia, mg/L as N 03 (27) 05 (88) 0 1.465 0 NA
Total boron, pg/L as B <10 () 5 (3) ND ND NA NA
Total lead, g/L as Pb 2 ©) 3 (15) 0 1.072 NA NA
Fecal coliform bacteria, MPN/100 ml 6 (25) 8 (99) 1.006 ND 0 NA

Table 9b. 1993 AMNET impairment status in the vicinity of water-quality station 01409500, Batsto River at Batsto, NJ.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-siation location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status}

Upstream from WQ station

At WQ-station location

Downstream from WQ station

AMNET station

Impairment status

AN0586

Moderately impaired

ANO0588 None

Non-impaired ND

4l


contributions of these constituents from storm runoff relative to that at other sites in the study
area. During low flows, the trend is negative for CL, indicating a decrease in the contributions of
these constituents from point sources and ground water over time. Trends during low flows are
insignificant for HARD, TOC, DS, NA, DO, FDO, TN, NO32, TAON, NH4, and BACT. During
high flows, the trend is negative for NH4, indicating a decrease in the contribution from storm
runoff over time. Trends during high flows are insignificant for HARD, TOC, DS, NA, CL, DO,
FDO, TN, NO32, TAON, and BACT. Insufficient data are available to determine trends for ALK,
SS, TP, NO2, B, and PB during low and high flows. The AMNET impairment status is
moderately impaired at and upstream from station 01412800 (table 30b).

Maurice River

The Maurice River Basin has two water-quality stations both on the Maurice River—
stations 01411500 at Norma and 01411800 near Millville. The 5-year and period-of-record
medians are similar for all constituents at both stations (tables 31a and 32a). The regression
slopes of concentration to streamflow for ALK, HARD, TOC, SS, CL, DO, FDO, TP, TN, NO32,
TAON, and BACT show seasonal dependency at station 01411500. The concentration slopes for
DO, FDO, TN, NO32, NO2, TAON, and BACT show seasonal dependency at station 01411800.

The regression slope of load to streamflow is in the high range only for TOC at station
01411500, indicating a greater contribution from storm runoff relative to that at other sites in the
study area. Load slopes are in the low range for TN and NO32 at station 01411500 and for
TAON, NH4, and PB at station 01411800, indicating smaller contributions of these constituents
from storm runoff relative to that at other sites in the study area. The load slopes for DO at station
01411500 and NH4 at station 01411800 are the smallest for these constituents in the study area.
The load slopes of TOC, NA, CL, TAON, and NH4 decrease in the downstream direction,
indicating a decrease in the contributions of these constituents from storm runoff along the
Maurice River. The load slopes of TP, TN, and NO32 increase in the downstream direction,
indicating an increase in the contributions of these constituents from storm runoff along the
Maurice River.

During low flows at station 01411500, the trend is positive for HARD and CL, indicating
an increase in the contributions of these constituents from points sources and ground water over
time, and negative for NA, indicating a decrease in the contributions of NA from points sources
and ground water over time. Trends during low flows at station 01411500 are insignificant for
DS, DO, FDO, TP, TN, NO32, and TAON. During high flows at station 01411500, the trend is
positive for HARD, indicating an increase in the contribution from storm runoff over time, and
negative for DS and TP, indicating a decrease in the contributions of these constituents from
storm runoff over time. Trends during high flows at station 01411500 are insignificant for NA,
CL, DO, FDO, TN, NO32, and TAON. Insufficient data are available at station 01411500 to
determine trends for ALK, TOC, SS, NO2, NH4, B, PB, and BACT during low and high flows.
During low flows at station 01411800, trends are insignificant for DO, FDO, TN, NO32, NO2,
TAON, NH4, and BACT. Insufficient data are available at station 01411800 to determine trends
for all other constituents during low flows and for all constituents during high flows.

70


ati f to strea

The range categories of regression slopes of hardness load to streamflow are depicted in
figures 10c and llc. The slopes range from 0.698 at station 4080 on the Manasquan River (table
5a) to 1.305 at station 4095 on the Batsto River (table 9a). The slope is in the high range only at
station 4095 on the Batsto River where the contribution to instream hardness load from storm
runoff is larger and less influenced by constant sources (most likely ground water) than at other
sites in the study area. Slopes are in the low range at the stations on the Manasquan (4080) and
Toms (4085) Rivers, the upstream station on the Great Egg Harbor River (410784), the
downstream station on the Assunpink Creck (4640), and the stations on the Crosswicks (4645),
South Branch of the Pennsauken (467081), Raccoon (47712), and Oldmans (47751) Creeks. At
these stations, the contributions to instream hardness loads from constant sources (most likely
ground water) are larger and less influenced by storm runoff than at other sites. Slopes at stations
on the Assunpink Creek decrease in the downstream direction, indicating a decrease in the
relative influence of contributions from storm runoff along the river.

Total Organic Carbon

The concentration of total organic carbon (TOC), an aggregate property of water, is a
measure of the organic compounds in various oxidation states in surface water (Eaton and others,
1995). TOC concentrations in most surface water are small compared to dissolved inorganic
solute concentrations. Although the presence of organic compounds in surface water can cause an
oxygen demand as organisms decompose the compounds, a measure of TOC does not represent a
measure of other organically bound elements, such as nitrogen and hydrogen, or inorganics that
can contribute to the oxygen demand as measured by the biochemical or chemical oxygen
demands.

The methods used to measure TOC analyze fractions of total carbon. These fractions are
defined as inorganic carbon, the carbonate, bicarbonate, and dissolved carbon dioxide removed
from solution by gas stripping under specified conditions; TOC, all carbon atoms covalently
bonded in organic molecules; dissolved organic carbon (DOC), the fraction of TOC that passes
through a 0.45 um-pore-diameter filter; particulate organic carbon (POC), the fraction of TOC
that is retained by a 0.45 um-pore-diameter filter; volatile organic carbon (VOC), the fraction of
TOC removed from an aqueous solution by gas stripping under specified conditions; and non-
purgeable organic carbon, the fraction of TOC not removed by gas stripping. In most surface
water the VOC contribution to TOC is negligible. When not measured directly, TOC
concentration is calculated as the sum of the DOC and POC concentrations.

Relation of trends i . fl lit

TOC concentrations during high flows show no trend at the stations on the Raccoon Creek
(47712) and Cohansey River (4128) (figs. 12a and 13a). The trend in TOC concentrations during
low flow is negative at the one station on the Raccoon Creek (47712), indicating a decrease in the
contributions from point sources and ground water over time at this station (figs. 12b and 13b).
TOC concentrations during low flows show no trend at the stations on the Mullica River
(409387), Hammonton Creek (409416), Batsto (4095) and Oswego (4100) Rivers, and East

80


Table Sa. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01408000, Manasquan River at Squankum, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 41 (ly 4l (i) -0.635 0.365 NA NA
Hardness, mg/L as CaCO, 80 (12) 66 (56) -302 698 NA NA
Total organic carbon, mg/L as C 18 (il) 6.8 (23) 490 1.489 NA NA
Suspended sediment, mg/L 4 rend) 16 (28) 1318 2.317 NA NA
Dissolved solids, mg/L 136 dl 128 (26) 0 923 NA NA
Dissolved sodium, mg/L as Na 8 (12) 13 (57) 0 948 NA NA
Dissolved chloride, mg/L as Cl 16 (13) 18 (62) 0 929 NA NA
Dissolved oxygen, mg/L 9.3 (21) 8.6 (119) 0 * 1.001 + NA
Fraction of dissolved oxygen at 87 (20) 82 (97) 0 * ND + NA
saturation, %
Total phosphorus, mg/L as P 05 (21) 08 (54) 447——* 1.446 NA NA
Total nitrogen, mg/L as N 1 (21) 2.6 (105) 3200 =* 1,320 NA NA
Total nitrate plus nitrite, mg/L as N .75 (21) 95 (111) 0 1.159 NA NA
Total nitrite, mg/L as N .007 (20) .032 (107) 0 * 1.049 NA NA
Total ammonia plus organic nitrogen, 27 (21) 1.68 (119) ATS 1.475 - NA
mg/L as N

Total ammonia, mg/L as N 03 (21) 80 (111) 733,—* 1.732 NA NA
Total boron, pg/L as B 25 (4) 25 (4) ND ND NA NA
Total lead, g/L as Pb <l (7) 4 (43) 1.14 2.114 NA NA
Fecal coliform bacteria, MPN/100 ml 80 (20) 490 (121) 555 * ND 0 NA

Table 5b. 1993 AMNET impairment status in the vicinity of water-quality station 01408000, Manasquan River at Squankum, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station AN0490 AN0493 AN0498
Impairment status Moderately impaired Moderately impaired Moderately impaired

35


ati ad to sti

The range categories of regression slopes of total lead to streamflow are depicted in
figures 40c and 41c. The slopes range from zero at the stations on the East Branch of the Bass
River (41015) and Oldmans Creek (47751), and the downstream station on the Maurice River
(4118) (tables 12a, 28a, and 32a, respectively) to 2.942 at station 4645 on the Crosswicks Creek
(table 18a). The slope is in the high range only at the one station on the Crosswicks Creek (4645),
where the contribution to instream total lead load from storm runoff is larger and less influenced
by point sources and ground water than at other sites in the study area. Slopes are in the low
range at the stations on the East Branch of the Bass River (41015) and Oldmans Creek (47751),
and the downstream station on the Maurice River (4118). At these stations, the contributions to
instream total lead loads are less influenced by storm runoff than at other sites in the study area.

Fecal Coliform Bacteria

Fecal coliform bacteria are present in the intestine and feces of warm-blooded animals.
The presence of high numbers of fecal coliform bacteria in surface water can indicate the recent
release of untreated wastewater or the presence of animal feces, or both. These organisms also
can indicate the presence of pathogens that are harmful to humans. High numbers of fecal
coliform bacteria can render surface water unfit for some uses, such as swimming and fishing.
Fecal coliform bacteria are often used as indicators of the sanitary quality of the water (Eaton and
others, 1995). For laboratory purposes, fecal coliform bacteria are defined as all organisms that
produce blue colonies within 24 hours when incubated at 44.5 °C £0.2 °C on M-FC medium
(nutrient medium for bacterial growth) (Bauersfeld and others, 1994).

ti i tration t ition.

The fecal coliform bacteria concentrations during high flows show no trends at the
downstream station on the Assunpink Creek (4640) and the stations on the Cooper River (46715),
Raccoon Creek (47712), and Cohansey River (4128) (figs. 42a and 43a). The trends of fecal
coliform bacteria concentrations during low flows are positive at the stations on the Hammonton
Creek (409416), Great Egg Harbor River (4110), and Salem (4825) River, indicating an increase
in the contributions from point sources and ground water over time at these sites (figs. 42b and
43b). The fecal coliform bacteria concentrations during low flows show no trends at the stations
on the Manasquan (4080), Mullica (409387), Batsto (4095), and Oswego (4100) Rivers, and East
Branch of the Bass River (41015); the downstream station on the Great Egg Harbor River
(41111); the stations on the Crosswicks Creek (4645), Doctors Creek (464515), South (46585)
and North (4670) Branches of the Rancocas Creek, the North (467069) and South (467081)
Branches of the Pennsauken Creek, Raccoon Creek (47712), Oldmans Creek (47751), and
Cohansey River (4128); and the downstream station on the Maurice River (4118).

121


concentrations during low flows show no trend at all stations on the Toms (4085) and Mullica
(409387) Rivers, Hammonton Creek (409416), Batsto (4095), Oswego (4100), East Branch of the
Bass (41015), and Great Egg Harbor (410784, 4110, and 41111) Rivers, Crosswicks (4645) and
Doctors Creeks (464515), South (46585) and North (4670) Branches of the Rancocas Creek,
Raccoon (47712) and Oldmans (47751) Creeks, and Salem (4825), Cohansey (4128), and
Maurice (4115 and 4118) Rivers.

The range categories of regression slopes of total nitrogen load to streamflow are shown in
figures 28c and 29c. The slopes range from 0.645 at the upstream station on the Great Egg Harbor
River (410784) (table 13a) to 1.387 at station 4665 on McDonalds Branch (table 21a). Slopes are
in the high range at the stations on the Manasquan (4080) and Batsto (4095) Rivers, McDonalds
Branch (4665), Raccoon Creek (47712), and Salem River (4825). At these sites, the contributions
to instream total nitrogen loads from storm runoff are larger and less influenced by constant
sources than at other sites in the study area. Slopes are in the low range at the stations on the
Toms River (4085) and Hammonton Creek (409416), the upstream station on the Great Egg
Harbor River (410784), the downstream station on the Assunpink Creek (4640), the stations on
the Crosswicks (4645) and South Branch on the Pennsauken (467081) Creeks, and the upstream
station on the Maurice River (4115). At these sites, the contribution to the instream total nitrogen
load from point sources and (or) ground water is larger and less influenced by storm runoff than at _
other sites in the study area. Slopes at stations on the Great Egg Harbor River increase in the
downstream direction, indicating an increase in the relative influence of contributions from storm
runoff along the river. Slopes at stations on the Assunpink Creek decrease in the downstream
direction, indicating a decrease in the relative influence of contributions from storm runoff along
the river.

Total Nitrate Plus Nitrite

Total oxidized nitrogen concentration is the sum of the nitrate and nitrite concentrations.
Nitrite is an intermediate oxidation state of nitrogen. Nitrite is usually present in trace amounts in
surface water because it is rapidly oxidized to nitrate and is generally considered to be an
indicator of the presence of sewage or organic waste (low DO conditions). Nitrite can enter
surface water in discharge from wastewater-treatment plants and water-reuse systems in fish
culture facilities where the nitrification process to reduce ammonia concentrations is impaired
(Rand and Petrocelli, 1985). Nitrite is the etiologic agent of methemoglobinemia in humans and
fish. Under specific conditions, nitrite is involved in the formation of some carcinogenic
nitrosamines. Nitrate is an essential nutrient for many photosynthetic autotrophs and, in some
cases, has been identified as the growth-limiting nutrient. It is present generally in trace amounts
in surface water, but can attain high levels in some ground-water systems (Hem, 1985). Nitrate
fertilizers applied to agricultural and residential land, then carried to surface water by storm
runoff and ground water, can stimulate the growth of photosynthetic aquatic micro- and macro-
organisms. Nitrate is considerably less toxic to aquatic organisms than are ammonia and nitrite;
however, in excess amounts (>10 mg/L), nitrate contributes to methemoglobinemia in small
children and fish.

105


r i jon t

The trends in total ammonia plus organic nitrogen concentrations during high flows are
negative at the one station on the Cooper River (46715), indicating a decrease in the contribution
from storm runoff over time at this station (figs. 34a and 35a). The concentrations of total
ammonia plus organic nitrogen during high flows show no trends at the stations on the Toms
River (4085), Raccoon Creek (47712), and Cohansey River (4128), and the upstream station on
the Maurice River (4115). The trends in total ammonia plus organic nitrogen concentrations
during low flows are negative at the stations on the Manasquan (4080) and Oswego (4100)
Rivers, the downstream stations on the Great Egg Harbor River (4110 and 41111), the stations on
the Crosswicks Creek (4645) and North Branches of the Rancocas (4670) and Pennsauken
(467081) Creeks (figs. 34b and 35b). Contributions from point sources and ground water
decreased over time at these stations. Concentrations of total ammonia plus organic nitrogen
during low flows show no trend at the stations on the Toms (4085) and Mullica (409387) Rivers,
Hammonton Creek (409416), Batsto River (4095), West Branch of the Wading (409815) and East
Branch of the Bass (41015) Rivers; the upstream station on the Great Egg Harbor River (410784);
and all stations on the Doctors Creck (464515), South Branches of the Rancocas (46585) and
Pennsauken Creeks (467081), Raccoon Creck (47712), Oldmans Creek (47751), and Salem
(4825), Cohansey (4128), and Maurice (4115 and 4118) Rivers.

Relation of load to streamflow

The range categories of regression slopes of total ammonia plus total organic nitrogen
load to streamflow are depicted in figures 34c and 35c. The slopes range from 0.691 at station
467081 on the South Branch of the Pennsauken Creek (table 24a) to 1.752 at station 4665 on the
McDonalds Branch (table 21a). The slope is in the high range only at the station on the
McDonalds Branch (4665) where the contribution to instream loads from storm runoff is larger
and less influenced by constant sources than at other sites in the study area. Slopes are in the low
range at the stations on the Mullica River (409387) and Hammonton Creek (409416); the
downstream station on the Assunpink Creek (4640); the stations on the Doctors Creek (464515),
South (46585) and North (4670) Branches of the Rancocas Creek, North (467069) and South
(467081) Branches of the Pennsauken Creek, and Oldmans Creek (47751); and the downstream
station on the Maurice River (4118). At these sites, the contributions to instream loads from point
sources and ground water are larger and less influenced by storm runoff than at other sites in the
study area. Slopes at stations on the Assunpink Creek and Maurice River decrease in the
downstream direction, indicating a decrease in the relative influence of contributions from storm
runoff along the rivers.

Total Ammonia

Ammonia is produced largely by deamination of organic nitrogen-containing compounds
and by hydrolysis of urea. Ammonia can enter surface water by wet deposition with industrial,
municipal, and agricultural wastewater and runoff, especially from areas treated with ammonia
fertilizers. At some water-treatment plants, ammonia is added to react with chlorine to form a

114


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119


REFERENCES CITED—Continued

Fusillo, T.V., 1981, Impact of Suburban Residential Development on Water Resources in the Area
of Winslow Township, Camden County, New Jersey: U.S. Geological Survey Water-
Resources Investigations Report 81-27, 38 p.

Gillespie, B.D., and Schopp, R.D., 1982, Low-flow characteristics and flow duration of New
Jersey streams: U.S. Geological Survey Open-File Report 81-1110, 164 p.

Hay, L.E., and Campbell, J.P., 1990, Water-quality trends in New Jersey streams: U.S. Geological
Survey Water-Resources Investigations Report 90-4046, 297 p.

Helsel, D.R., and Cohn, T.A., 1988, Estimation of descriptive statistics for multiply censored
water quality data: Water Resources Research, v. 24, no. 12, p. 1997-2004.

Helsel, D.R., and Hirsch, R.M., 1992, Statistical methods in water resources: New York, Elsevier
Science Publishing Company, 522 p.

Hely, A.G., and Olmsted, F.H., 1963, Some relations between streamflow characteristics and the
environment in the Delaware River region: U.S. Geological Survey Professional Paper
417-B. p. B1-B5.

Hem, J.D., 1985, Study and interpretation of the chemical characteristics of natural water:
U.S. Geological Survey Water Supply Paper 2254, 263 p.

Hickman, R.E., 1992, Water-quality data from reconnaissance surveys of selected estuaries in
southern New Jersey, July-October 1989: U.S. Geological Survey Open-File
Report 91-491, 61 p.

Hickman, R.E., 1995, Statistical characteristics of stream discharge in tributaries of selected
estuaries in New Jersey: U.S. Geological Survey Water-Resources Investigations
Report 91-4141, 53 p.

Hirsch, R.M., 1982, A comparison of four streamflow record extension techniques: Water
Resources Research, v. 18, no. 4, p. 1081-1088.

Hirsch, R.M., Slack, J.R., and Smith, R.A., 1982, Techniques of trend analysis for monthly water
quality data: Water Resources Research, v. 18, p. 107-121.

Hochreiter, Jr., J.J., 1982, Chemical-quality reconnaissance of the water and surficial bed material
in the Delaware River estuary and adjacent New Jersey tributaries, 1980-81:
U.S. Geological Survey Water-Resources Investigations Report 82-36, 41 p.

143


CONTENTS

Page

Abstract...

Approach........
Previous studies
Acknowledgments.
Description of the study area
Atlantic Coastal Basi
Manasquan River

Toms River

Mullica River ...............

Great Egg Harbor River

Lower Delaware River Basin....
Assunpink Creek....

Crosswicks Creek

Rancocas Creek..

Pennsauken Creek

Cooper River...

Big Timber Creek

Raccoon Creek...

Oldmans Creek:

Salem River...

Delaware Bay Basin....
Cohansey Rive

Maurice River .

Methods of study...........00-.06
Selection of constituents
Data Preparation...........
Water-quality data
Streamflow data ...
Flow-duration data
Statistical methods........
Calculation of medians
Determination of relations of surface-water quality to streamflow
Relations of concentration to streamflow .

Relations of load to streamflow

Trends in concentrations during low and high flows

Relations of surface-water quality to streamflow .
Analysis of relations by basin...............
Atlantic Coastal Basin
Manasquan River

Toms River..........

, and data sources

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Table 22a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-

quality constituents at water-quality station 01467000, North Branch Rancocas Creek at Pemberton, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; jig/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
consent a a ee
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO; 1 (27) 1 (74) -0.721 0.277 NA NA
Hardness, mg/L as CaCO; 8 (27) 8 (107) -058  * 942 0 NA
Total organic carbon, mg/L as C 7.6 (27) 8.0 (108) 238 —* 1.237 0 NA
Suspended sediment, mg/L 4 (10) 5 (23) 0 1.553 NA NA
Dissolved solids, mg/L 36 (26) 36 (108) .063 1.063 0 NA
Dissolved sodium, mg/L as Na 3 (27) 3 (109) -110  * 890 + NA
Dissolved chloride, mg/L as Cl 6 (27) 5 (110) 0 * 965 + NA
Dissolved oxygen, mg/L 86 © (27) 8&1 (111) 8 * 1.118 0 NA
Fraction of dissolved oxygen at 81 Q7) 83 (111) 0 * ND 0 NA
saturation, %
Total phosphorus, mg/L as P 04 (25) 04 (79) 226 * 174 NA NA
Total nitrogen, mg/L as N 5 (27) 5 (92) 0 * 936 0 NA
Total nitrate plus nitrite, mg/L as N Jl Q7) 10 (93) 0 872 0 NA
Total nitrite, mg/L as N .006 (27) 006 (81) 0 * 1.149 NA NA
Total ammonia plus organic nitrogen, 40 (27) 46 (107) ty) * 947 - NA
mg/L as N

Total ammonia, mg/L as N .04 (27) 06 = (94) -513* 486 - NA
Total boron, pg/L as B 15 6 20 (7) s-ND 1.312 NA NA
Total lead, pig/L as Pb 6 6) 8 (18) 0 1.149 NA NA
Fecal coliform bacteria, MPN/100 ml 41 (24) 40 (107) ) * ND 0 NA

‘Table 22b. 1993 AMNET impairment status in the vicinity of water-quality station 01467000, North Branch Rancocas Creek at Pemberton, N.J.

[AMNET, Ambient Biomonitoring Net’
WOQ-station location is within 0.5 mile upstream or downstream

work; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
from the WQ station; downstream from WQ station is within 5 miles downstream

from the WQ station; ND, undetermined impairment status}

Upstream from WQ station

At WQ-station location

Downstream from WQ station

AMNET station

Impairment status

None

ND

ANO149

Non-impaired

ANOIS51

Moderately impaired

58


study area. Load slope for DO is in the low range. During low flows, the trend is negative for
TAON, indicating an increase in the contributions of TAON from point sources and ground water
over time. The trends are insignificant for HARD, TOC, DS, NA, DO, FDO, TN, NO32, NH4,
and BACT during low flows. Insufficient data are available to determine trends for all other
constituents during low flows and for all constituents during high flows. The AMNET
impairment status is non-impaired at station 01410000 and moderately impaired upstream from
the station (table 11b).

For the one station on the East Branch of the Bass River, station 01410150 near New
Gretna, the 5-year median is greater than the period-of-record median for NO32; 5-year and
period-of-record medians are similar for all other constituents (table 12a). The period-of-record
medians for SS and NO2 at station 01410150 are the smallest for these constituents at all stations
in the study area. The regression slopes of concentration to streamflow for TOC, DO, and FDO
show seasonal dependency. The regression slope of load to streamflow for TOC, NA, CL, and
NO? are in the high range, indicating a greater contribution from storm runoff relative to that at
other sites in the study area. The load slope for CL at station 01410150 is the largest for this
constituent in the study area. Load slope for ALK, NH4, and PB are in the low range, indicating
smaller contributions of these constituents from storm runoff relative to that at other sites in the
study area. During high flows, the trends are insignificant for HARD, TOC, DS, NA, CL, DO,
FDO, TN, NO32, TAON, NH4, and BACT. Insufficient data are available to determine trends for
all other constituents during low flows and for all constituents during high flows. The AMNET
impairment status is non-impaired upstream from station 01410150 (table 12b).

Great Egg Harbor River

Three water-quality stations are located on the Great Egg Harbor River—stations 0140784
near Sicklerville, 01411000 at Folsom, and 01411110 at Weymouth. The 5-year medians are
smaller than the period-of-record medians for TP, TN, NO32, NO2, TAON, and NH4 at station
01410784; 5-year and period-of-record medians are similar for all other constituents (table 13a).
The 5-year and period-of-record medians are similar for all constituents at stations 01411000 and
01411110 (tables 14a and 15a). The regression slopes of concentration to streamflow for HARD,
TOC, SS, DS, NA, CL, DO, FDO, and BACT show seasonal dependency at station 01410784.
The concentration slopes for DO, FDO, TP, NO32, and BACT show seasonal dependency at
station 01411000. The concentration slopes for ALK, TOC, NA, DO, FDO, TP, NO32, TAON,
and BACT show seasonal dependency at station 01411110.

The load slope for TOC at station 01411000 is the largest for TOC in the study area. Load
slopes are in the high range for TOC at station 01411000 and for TOC and NO2 at station
01411110, indicating greater contributions of these constituents from storm runoff relative to that
at other sites in the study area. The regression slopes of load to streamflow are in the low range
for HARD, TP, TN, and NO32 at station 01410784, for ALK, SS, DO, NO32, and NH4 at station
01411000, and for ALK, NO32, and B at station 01411110, indicating smaller contributions of
these constituents from storm runoff relative to that at other sites in the study area. The load
slopes for TN at station 01410784, ALK at station 01411000, and NO32 at station 01411110 are

44


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Almost one-half of the land use in the basin is agricultural (cropland). The remainder of
the land use is forested (woodlands), undeveloped (tidal/freshwater marshes), urban, and
agricultural (pastures) (New Jersey Department of Environmental Protection and Energy, 1993)

Delaware Bay Basin

The Delaware Bay Basin (fig.5) is in south New Jersey. The rivers in this basin—the
Cohansey and the Maurice Rivers—flow mainly in a southerly direction and into Delaware Bay.

Cohansey River

The Cohansey River is almost 30 miles long and drains an area of 105 mi’. The low relief
in this area results in many small tributaries (New Jersey Department of Environmental Protection
and Energy, 1993). Mean annual flow for water years 1951-67 is estimated to be 1.8] ft?/s at the
discontinued surface-water gaging station on the West Branch of the Cohansey River at Seeley
(01412500) (Gillespie and Schopp,1982). One water-quality station is located on the Cohansey
River at Seeley (01412800); the period of record for water-quality-data collection is water years
1975-93 (fig. 6) (Bauersfeld and others, 1994).

The main land use in the basin is agricultural. Much of the land remains forested (New
Jersey Department of Environmental Protection and Energy, 1993).

Maurice Ri

The Maurice River is about 50 miles long and drains an area of 386 mi*. Downstream
from Union Lake, the river is influenced by tides (New Jersey Department of Environmental
Protection and Energy, 1993). Mean annual flow for water years 1992-93 is estimated to be
242 ft3/s at the surface-water gaging station on the Maurice River near Millville (01411800)
(Bauersfeld and others, 1994). One water-quality station is located on the Maurice River near
Millville (01411800); the period of record for water-quality-data collection is water years
1968-93 (fig. 6) (Bauersfeld and others, 1994).

The main land use in the basin is agricultural. Much of the land remains forested (New
Jersey Department of Environmental Protection and Energy, 1993).

METHODS OF STUDY

The following section describes the methods and criteria used for the selection of
constituents, sites, and data sources. Methods for data preparation, quality assurance, and
statistical analyses are described.

18


Toms River

Toms River is 31 miles long and drains an area of 124 mi. It flows from western Ocean
and Monmouth Counties southeast to Barnegat Bay with many small tributaries feeding into it
along the way (New Jersey Department of Environmental Protection and Energy, 1993). Mean
annual flow for water years 1929-93 is estimated to be 212 ft*/s at the surface-water gaging
station on the Toms River near Toms River (01408500) (Bauersfeld and others, 1994). The only
water-quality station on the river is at Toms River (01408500) where the period of record for
water-quality data is water years 1963-93 (fig. 6) (Bauersfeld and others, 1994).

Land use in the basin is about 50 percent forested; the remaining 50 percent is residential,
military, and agricultural land use. Residential and commercial development is on the rise (New
Jersey Department of Environmental Protection and Energy, 1993).

Mullica River

The Mullica River and its tributaries drain about 561 mi2. The Mullica River is about
45 miles long. The river’s major tributaries include Hammonton Creek (9 miles long), Batsto
River (18 miles long), Wading River (30 miles long), Oswego River (21 miles long), and Bass
River (8 miles long) (New Jersey Department of Environmental Protection and Energy, 1993).
The Mullica River flows into Great Bay, which then meets the Atlantic Ocean. Mean annual flow
for water years 1928-93 is estimated to be 122 ft?/s at the surface-water gaging station on the
Mullica River at Batsto (01409500) (Bauersfeld and others, 1994). The five major tributaries and
the Mullica River each have one water-quality station (table 1). The period of record for water-
quality-data collection for each station is shown in figure 6.

Land use in the basin is mainly undeveloped State park land and forested. There are some
agricultural and developed areas (New Jersey Department of Environmental Protection and
Energy, 1993).

Great Egg Harbor River

The Great Egg Harbor River is about 49 miles long and drains an area of 304 mi?, The
river flows into Great Egg Harbor Bay, then into the Atlantic Ocean (New Jersey Department of
Environmental Protection and Energy, 1993). Mean annual flow for water years 1925-93 is
estimated to be 85.8 ft?/s at the surface-water gaging station on the Great Egg Harbor River at
Folsom (01411000) (Bauersfeld and others, 1994). Three water-quality stations are located on the
Great Egg Harbor River (table 1). The period of record for water-quality-data collection for each
station is shown in figure 6.

Land use in the basin is mainly forested; the remainder is agricultural and developed (New
Jersey Department of Environmental Protection and Energy, 1993).

14


conductance of the water sample. Values are determined from published equations. The
calculation of the fraction of dissolved oxygen at saturation removes the effect of temperature on
oxygen solubility so that the effects of photosynthesis on DO concentration are easier to evaluate.
Loads of percent dissolved oxygen saturation were not calculated.

ati nds i ration t

No trends in the fraction of dissolved oxygen at saturation during high flows are apparent
at the one station on the Toms River (4085); the downstream station on the Assunpink Creek
(4640), the stations on the McDonalds Branch (4665), Cooper River (46715), Raccoon Creek
(47712), and Cohansey River (4128); and the upstream station on the Maurice River (4115) (figs.
24a and 25a). The trends in the fraction of dissolved oxygen at saturation during low flows are
positive at stations on the Manasquan River (4080) and Oldmans Creek (47751); trends are
negative at the downstream station on the Great Egg Harbor River (41111) and stations on the
South Branch of the Rancocas (46585) and Raccoon (47712) Creeks (figs. 24a and 25a). No
trends are apparent at the stations on the Toms (4085) and Mullica (409387) Rivers, Hammonton
Creek (409416), Batsto (4095), West Branch of the Wading (409815), Oswego (4100), and East
Branch of the Bass (41015) Rivers; the upstream stations on the Great Egg Harbor River (410784
and 4110); and all stations on the Crosswicks (4645) and Doctors (464515) Creeks, McDonalds
Branch (4665), North Branch on the Rancocas Creek (4670), North (467069) and South (467081)
Branches of the Pennsauken Creek, and Salem (4825), Cohansey (4128), and Maurice (4115 and
4118) Rivers (figs. 24b and 25b).

Total Phosphorus

Phosphorus is present in surface water as orthophosphates, condensed phosphates (pyro-,
meta-, and other polyphosphates), and organically bound phosphates (Sawyer and McCarty,
1978). Phosphates are found in solution, associated with particles, detritus, and the bodies of
aquatic organisms. They are derived from a variety of sources and are relatively immobile in soils
or sediments (Hem, 1985). Phosphorus is a common element in igneous rock and is fairly
abundant in sediment. Orthophosphates applied to agricultural or residential land as fertilizers
can be carried into surface water with storm runoff. Phosphorus is an essential nutrient and can
limit the primary productivity of a water body. Primary productivity is a measure of the rate at
which new organic matter is formed and accumulated through photosynthetic and chemosynthetic
activity of producer organisms (chiefly, green plants) (Barnes and Mann, 1991). The addition of
phosphorus to surface water from storm runoff and the discharge of treated wastewater,
agricultural drainage, or certain industrial wastes to the water can stimulate the growth of
photosynthetic aquatic micro- and macro-organisms in nuisance quantities.

Relation of trends i ion tof ith

The trend in total phosphorus concentrations during high flows are negative at the one
station on the Toms River (4085) and the upstream station on the Maurice River (4115),
indicating a decrease in the contributions from storm runoff over time at these stations (figs. 26a
and 27a). The trend of total phosphorus concentrations during low flows is negative at the one
station on the Toms River (4085), indicating a decrease in the contributions from point sources

97


Determination of Relations of Surface-Water Quality to Streamflow

The processes used to determine relations between concentration and streamflow and load
and streamflow, and trends in concentrations during high and low flows are described in this
section.

Relati ncentration to strea

Water quality is strongly influenced by biological activity, which is seasonal; therefore,
relations between concentration and streamflow were developed by using (1) all measurements,
(2) growing-season measurements only, and (3) nongrowing-season measurements only. The
growing season in New Jersey is from April 1 through October 31; the nongrowing season is from
November | through March 31. The dates for the growing and nongrowing seasons were based
on the average times of the first and final frosts in New Jersey (Ruffner and Bair, 1977). All
relations take the following form:

log(CONC) = SLOPEx\og(FLOW) + INT, 7)

where

log = base-10 logarithm;

CONC = constituent concentration, in indicated units;
SLOPE = the slope of the relation;

FLOW = streamflow, in cubic feet per second; and
INT = the intercept of the relation.

These relations were developed by using Tobit regression (Cohn, 1988), which includes
less-than values. For Tobit regression in this report, greater-than values were considered to be
uncensored. Where there were no less-than values, this method resulted in the same values of
SLOPE and INT as those calculated by ordinary least-squares regression. A goodness-of-fit value
such as the correlation coefficient is not presented; the Tobit method does not result in such a
value.

A relation of water quality to streamflow at a given station was developed only if at least
nine uncensored concentration values were available. T.A. Cohn (U.S. Geological Survey,
written commun., 1995) noted that at least nine uncensored values were needed to use the Tobit
method with two unknowns. Nine uncensored values were sometimes insufficient data from
which to calculate statistically significant results.

A relation using all measurements is reported only if the value of SLOPE was different
from zero at the 0.05 level of significance; otherwise, a SLOPE of “0” is reported. A “not
determined” value of SLOPE is reported if the data were insufficient to conduct the analysis. A
value of INT was calculated only if the value of SLOPE was different from zero.

26


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COMPARISON OF RESULTS

In the Atlantic Coastal Basins, Positive trends in constituent concentrations over time
during low flows indicate increasing constant-rate source contributions for NA at two stations, for
CL at two stations, for DO at one station, for FDO at one station, and for BACT at two stations
(table 33). In the lower Delaware River and Delaware Bay Basins, increasing constant-rate
contributions are indicated for HARD at two stations, for NA at four stations, for CL at seven
stations, for DO at one station, for FDO at one station, for NO32 at one station, and for BACT at
one station (table 34).

In the Atlantic Coastal Basins, negative trends indicate decreasing constant-rate source
contributions for NA at two stations, for CL at two stations, for FDO at one station, for TP at one
station, for NO32 at one station, for NO2 at one station, and for TAON at four stations (table 33).
In the lower Delaware River and Delaware Bay Basins, decreasing constant-rate contributions are
indicated for TOC at one station, for NA at two stations, for CL at one station, for FDO at two
stations, for TN at two stations, for NO32 at one station, for TAON at three stations, for NH4 at
three stations, and for PB at one station (table 34).

Positive trends during high flows indicate increasing intermittent-source contributions for
CL at one station in the Atlantic Coastal Basins (table 35). Increasing intermittent-source
contributions are also indicated for HARD at one station and for DS, NA, and CL at one station in
the lower Delaware River and Delaware Bay Basins, respectively (table 36). Negative trends
during high flows indicate decreasing intermittent-source contributions for HARD and TP at one
Station in the Atlantic Coastal Basins (table 35). In the lower Delaware River and Delaware Bay
Basins, decreasing intermittent-source contributions are indicated for DS at one station, for TP at
one station, for TN at one station, for NO2 at two stations, for TAON at one station, and for NH4
at one station (table 36).

All water-quality stations in the Atlantic Coastal Basin and 12 stations in the lower
Delaware River and Delaware Bay Basins have sufficient data to determine trends during low
flows, but only 1 station in the Atlantic Coastal Basin and 5 stations in the lower Delaware River
and Delaware Bay Basins have sufficient data to determine trends during high flows. The
upstream station on the Assunpink Creek (46362) and the one station on the South Branch Big
Timber Creek (467329) have insufficient data to determine trends during both high and low flows.
The lack of water-quality data during low and high flows at many of the stations is due, in part, to
the conservative method used in this study. This method ensured that only data collected during
base flow and stormflow were used to determine trends. If additional data were collected or the
data-collection schedule were changed to accommodate sampling during a full range of flow
conditions, and if different flow durations were used to group the data so that more of the data
were included, a greater number of significant trends might be identified. All figures generated in
this study are available in appendixes on CD-ROM for further site-by-site comparisons of visual
trends.

Relations of concentration to streamflow show that at most stations, concentrations
decrease with increasing flows (dilution); therefore, negative concentration slopes predominate.
Streams such as Batsto River and McDonalds Branch, which have very few or no point source
discharges and which are dominated by ground-water discharge (more than 75 percent of annual

128


Table 16a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01463620, Assunpink Creek near Clarksville, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression Low- High-
Constituent conentation cometaion—coneentaon ead wend tend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 12 (25) 14 (72) -0.276 * 0.723 NA NA
Hardness, mg/L as CaCO, 38 (25) 39 (82) -.063 937 NA NA
Total organic carbon, mg/L as C 5.8 (25) 54 (80) 0 * 924 NA NA
Suspended sediment, mg/L 9 @) i (24) 580 1.579 NA NA
Dissolved solids, mg/L 78 (24) 81 (77) 0 978 NA NA
Dissolved sodium, mg/L as Na 6 (25) 6 (82) 0 * 992 NA NA
Dissolved chloride, mg/L as Cl 14 (25) 12 (81) 0 * 993 NA NA
Dissolved oxygen, mg/L 9.0 (25) 93 (83) 1320 * 1.132 NA NA
Fraction of dissolved oxygen at 89 (25) 96 (79) 046 ND NA NA
saturation, %
Total phosphorus, mg/L as P 05 (23) 06 (54) 228 1.228 NA NA
Total nitrogen, mg/L as N 15 (25) 1.6 (79) 190 * 1.189 NA NA
Total nitrate plus nitrite, mg/L as N 63 (25) 78 (80) 414 * 1.413 NA NA
Total nitrite, mg/L as N 012 (24) 012 (63) .250 1.249 NA NA
Total ammonia plus organic nitrogen, 81 (25) 79 (82) 0 * 989 NA NA
mg/L as N
Total ammonia, mg/L asN 06 (25) 09 (78) 0 975 NA NA
Total boron, pg/L as B 20 (7) 20 (18) 1) 1.056 NA NA
Total lead, g/L as Pb 2 (1) 2 (18) 0 1,079 NA NA
Fecal coliform bacteria, MPN/100 ml 20 (23) 20 (80) 0 ND NA NA

‘Table 16b. 1993 AMNET impairment status in the vicinity of water-quality station 01463620, Assunpink Creek near Clarksville, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station

At WQ-station location

Downstream from WQ station

AMNET station

Impairment status

ANO109

Non-impaired

None

ND

ANOII6

Moderately impaired

50


and ground water over time at this station (figs. 26 and 27b). The concentrations of total
phosphorus during low flows show no trend at the stations on the West Branch of the Wading
River (409815), McDonalds Branch (4665), and Raccoon Creek (47712), and the upstream
station on the Maurice River (4115).

Relation of load to streamflow

The range categories of regression slopes of total phosphorus load to streamflow are
depicted in figures 26c and 27c. The slopes range from 0.505 at station 409416 on the
Hammonton Creek (table 8a) to 1.552 at station 4128 on the Cohansey River (table 30a), Slopes
are in the high range at stations on the Manasquan (4080) and Cohansey (4128) Rivers, where the
contributions to instream total phosphorus loads from storm runoff are larger and less influenced
by point sources and ground water than at other sites in the study area. Slopes are in the low
range at the stations on the Toms River (4085) and Hammonton Creek (409416), the upstream
station on the Great Egg Harbor River (410784), the downstream station on the Assunpink Creek
(4640), and the one station on the South Branch of the Rancocas Creek (46585). At these sites,
the contributions to instream total phosphorus from point sources and ground water are larger and
less influenced by storm runoff than at other sites in the study area. Slopes at stations on the Great
Egg Harbor River increase in the downstream direction, indicating an increase in the relative
influence of contributions from storm runoff along the river. Slopes at stations on the Assunpink
Creek decrease in the downstream direction, indicating a decrease in the relative influence of
contributions from storm runoff along the river.

Total Nitrogen

Nitrogen is an essential element for plant and animal growth; however, sufficiently large
concentrations of certain nitrogen species can adversely affect the quality of surface water by
causing excess algal growth (eutrophication) or toxicity to aquatic and terrestrial animals.
Important forms of nitrogen in surface water are, in order of decreasing oxidation state, nitrate,
nitrite, ammonia, and organic nitrogen. The cycling of nitrogen is mainly controlled by biological
processes. Nitrogen enters aquatic environments from fertilizers, agricultural wastes,
decomposition of organic matter, atmospheric deposition, biotic fixation, and ambient soils and
rocks. Ground water and storm runoff are important sources of nitrate and ammonia to surface
water. High concentrations of nitrate and nitrite can reduce the oxygen-carrying capacity of
hemoglobin in warm-blooded animals. Un-ionized ammonia can be toxic to aquatic organisms.

ati i tration to fi iti

The trend in total nitrogen concentrations during high flows is negative at the one station
on the Cooper River (46715), indicating a decrease in the contribution from storm runoff over
time at this station (figs. 28a and 29a). The concentrations of total nitrogen show no trends during
high flows at the stations on the Toms River (4085), Raccoon Creek (47712), and Cohansey River
(4128), and the upstream station on the Maurice River (4115) (figs. 28a and 29a). During low
flow, the trend in total nitrogen concentrations is negative at the stations on the North (467069)
and South (46708) Branches of the Pennsauken Creek, indicating a decrease in the contributions
from point sources and ground water over time at these station (figs. 28b and 29b). Total nitrogen

104


Table 29a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01482500, Salem River at Woodstown, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; j.g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY

Regression Regression — Low- High-

Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend

to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 28 Qn 28 (74) 0.264 * 0.736 NA NA
Hardness, mg/L as CaCO, 719 27) 78 (109) 088 * 912 0) NA
Total organic carbon, mg/L as C 8.4 (25) 7.0 (109) -160  * 839 0 NA
Suspended sediment, mg/L 28 (10) 23 (25) 0 * 1.065 NA NA
Dissolved solids, mg/L 144 (26) 143 (106) -.048 952 i) NA
Dissolved sodium, mg/L as Na 7 27) 7 (108) -088* 912 + NA
Dissolved chloride, mg/L as Cl 21 (27) 19 (109) -073* 927 + NA
Dissolved oxygen, mg/L 9.0 (27) 88 (111) 098 * 1.098 0 NA
Fraction of dissolved oxygen at 91 (26) 95 (108) 0 ND 0 NA
saturation, %
Total phosphorus, mg/L as P 16 (27) 17 (79) 0 * 918 NA NA
Total nitrogen, mg/L as N 3.8 (27) 34 (98) 351 * 1.350 0 NA
Total nitrate plus nitrite, mg/L as N 2.0 (27) 1,98 (100) 1171 * 2.171 0 NA
Total nitrite, mg/L as N 044 (26) 040 (79) 388 * 1.388 NA NA
Total ammonia plus organic nitrogen, 1.43. (27) 1.30 (108) 0 * 1.024 0 NA
mg/L as N

Total ammonia, mg/L as N +16 (27) 19 (98) 378 1.377 0 NA
Total boron, g/L as B 20 ©) 30 (9) 0 962 NA NA
Total lead, ig/L as Pb 2 () 5 9) 0 1.120 NA NA
Fecal coliform bacteria, MPN/100 ml 350 (25) 170 (107) 929 ND + NA

‘Table 29b. 1993 AMNET impairment status in the vicinity of water-quality station 01482500, Salem River at Woodstown, N.J.

{AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO0690 AN0691 AN0693
Impairment status Moderately impaired Severely impaired Moderately impaired

68


Table 2. Selected constiuents and reporting units

[mg/L, milligrams per liter, CaCO3, calcium carbonate; C, carbon; Na, sodium; Cl, chloride;
P, phosphorus; N, nitrogen; ug/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. ]

Constituent Reporting unit
Alkalinity mg/L as CaCO3
Hardness! mg/L as CaCO3
Total organic carbon! mg/L as C
Suspended sediment mg/L
Dissolved solids mg/L
Dissolved sodium mg/L as Na
Dissolved chloride mg/L as Cl
Dissolved oxygen mg/L

Fraction of dissolved oxygen at saturation! Percent

Total phosphorus mg/L as P

Total nitrogen! mg/L as N
Total nitrate plus nitrite mg/L as N
Total nitrite mg/L as N
Total ammonia plus organic nitrogen mg/L as N
Total ammonia mg/L as N
Total boron ug/L as B

Total lead ug/L as Pb
Fecal coliform bacteria MPN/100 mL.

' Values of constituent or property are calculated.

20


from IOC and residential area | A-horizon samples, at least one of the nearest neighbors must be
classified in another endmember group, because only five samples each of A-horizon soils from
1OC and from residential area 1 were collected.

Another factor that affects the strength of the IOC chemical signature in residential area |
soils is that the A-horizon soil samples contain smaller contaminant concentrations and less debris
than do some of the samples from B horizons and clays. Therefore, the IOC signature is weaker
in A-horizon soils in residential area | than in the B horizons and clays. Neither B-horizon soils
nor clays from endmember groups were found to produce models that discriminated among end-
member samples with an accuracy greater than about 60 percent, however; these models, there-
fore, could not be used to classify the residential soils. Although the residential area 1 A-horizon
soils retain an agricultural chemical signature, the debris common to IOC and residential area 1
soils indicates that materials from the Superfund site are a likely source of at least some of the
arsenic, barium, copper, and nickel in residential area | soils.

PCA did not provide the most useful group of discriminants in the modeling effort but did
identify a major discriminating factor for soils in the study area--mass loading. There are clear
differences in mass loading of the soils from different categories--that is, the mass of constituents
present in endmember A-horizon soils increases from geologic background to orchard to IOC
samples. The mass loading for soils from both residential areas is large. Some of this mass load-
ing is from anthropogenic inputs, but some is probably natural, as soils of both residential areas
are developed on clay lenses. Overall, the A-horizon soil samples from the two residential areas
contained more aluminum and more potassium than A-horizon soil samples from undeveloped
areas and most of the orchards. These larger concentrations indicate that the clay content of the
residential A-horizon soils is greater than the clay content of the background A-horizon soils and
at least some of the A-horizon orchard soils. Results of limited grain-size analyses and field
observations appear to support this assessment. Therefore, the higher clay content of the residen-
tial soils means that larger concentrations of metals in general, and of arsenic in particular, that
derive from geologic materials are present.

Although A-horizon soil samples from both residential areas | and 2 are classified by the
final model as orchard-type soils, the samples from the two residential areas are chemically dis-
tinct (figs. 26-28). When observations from the two residential areas are entered in the final model
as a two-category training set, the 13-variable, five-nearest-neighbor model separates residential
area | samples from residential area 2 samples with 100-percent accuracy. This indicates that
some of the anthropogenic effects on soil chemistry observed in samples from residential area 1
are different from those observed in samples from residential area 2.

Classification of Soil Samples by Lead-Isotope Ratios

Lead-isotope ratios for soil samples E2A, E20, and E6A, all from undeveloped forested
areas, are consistent with ratios established for atmospherically deposited gasoline lead (R. W.
Hurst, Chempet Research, written commun., 1996) and ratio/ratio plots may delineate an atmo-
spheric trend for the region (figs. 30 and 31). The atmospheric trend illustrated in figure 31 is sim-
ilar to that shown in Faure (1986, p. 333, fig. 19.11), which is defined by the average lead-isotope
ratios of galena from the Mississippi Valley, a source of lead in gasoline in pre-1940’s, and later

86


RELATIONS OF SURFACE-WATER QUALITY TO STREAMFLOW IN
THE ATLANTIC COASTAL, LOWER DELAWARE RIVER, AND
DELAWARE BAY BASINS, NEW JERSEY, WATER YEARS 1976-93

By Kathryn Hunchak-Kariouk, Debra E. Buxton, and R. Edward Hickman
ABSTRACT

Relations of water quality to streamflow were determined for 18 water-quality
constituents at 28 surface-water-quality stations within the drainage area of the Atlantic Coastal,
lower Delaware River, and Delaware Bay Basins for water years 1976-93. Surface-water-quality
and streamflow data were evaluated for trends (through time) in constituent concentrations during
high and low flows, and relations between constituent concentration and streamflow, and between
constituent load and streamflow, were determined. Median concentrations were calculated for the
entire period of study (water years 1976-93) and for the last 5 years of the period of study (water
years 1989-93) to determine whether any large variation in concentration exists between the two
periods. Medians also were used to determine the seasonal Kendall’s tau statistic, which was then
used to evaluate trends in concentrations during high and low flows.

Trends in constituent concentrations during high and low flows were evaluated to
determine whether the distribution of the observations changes through time for intermittent
(nonpoint storm runoff) and constant (point sources and ground water) sources, respectively.
High- and low-flow trends in concentrations were determined for some constituents at 26 of the
28 water-quality stations. Seasonal effects on the relations of concentration to streamflow are
evident for 10 constituents at 14 or more stations. Dissolved oxygen shows seasonal dependency
at all stations. Negative slopes of relations of concentration to streamflow, which indicate a
decrease in concentration at high flows, predominate over positive slopes because of dilution of
instream concentrations from storm runoff.

The slopes of the regression lines of load to streamflow were determined in order to show
the relative contributions to the instream load from constant (point sources and ground water) and
intermittent sources (storm runoff). Greater slope values indicate larger contributions from storm
runoff to instream load, which most likely indicate an increased relative importance of nonpoint
sources. Load-to-streamflow relations along a stream reach that tend to increase in a downstream
direction indicate the increased relative importance of contributions from storm runoff. Likewise,
load-to-streamfiow relations along a stream reach that tend to decrease in a downstream direction
indicate the increased relative importance of point sources and ground-water discharge.

The magnitudes of the load slopes for five constituents increase in the downstream
direction along the Great Egg Harbor River, indicating an increased relative importance of storm
runoff for these constituents along the river. The magnitudes of the load slopes for 11 constituents
decrease in the downstream direction along the Assunpink Creek and for 5 constituents along the
Maurice River, indicating a decreased relative importance of storm runoff for these constituents
along the rivers.


‘Table 30a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01412800, Cohansey River at Seeley, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; 1g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Consiuent coy comastaton —conentaon Tondo. tend tend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 17 (27) 14 (73) 0 * 0.871 NA NA
Hardness, mg/L as CaCO, 58 (27) 56 (110) 053 947 0 0
Total organic carbon, mg/L as C 39 (27) 3.9 (108) 344 * 1.343 0 0
Suspended sediment, mg/L 14 (9) 9 (23) 155 1.754 NA NA
Dissolved solids, mg/L 126 (26) 130 (103) -129 871 0 0
Dissolved sodium, mg/L as Na 10 (27) 12 (110) +384 616 1) 0
Dissolved chloride, mg/L as Cl 25 (27) 26 ~~ (110) -.268 731 - 0
Dissolved oxygen, mg/L 89 (27) 8.7 (110) 0) * 1.082 0 0
Fraction of dissolved oxygen at 88 (26) 89 (109) 0 ND 0 0
saturation, %
Total phosphorus, mg/L as P .08 = (27) 08 = (79) 553 1.552 NA NA
Total nitrogen, mg/L as N 49 (27) 47 (96) 0 * 996 0 0
Total nitrate plus nitrite, mg/L as N 4.35 (27) 4.08 (99) 0 * 941 0 0
Total nitrite, mg/L as N .027 (27) 027 (79) 4420 * 1.442 NA NA
Total ammonia plus organic nitrogen, 63 (27) .63 (105) 0 1.426 0) 0
mg/L asN
Total ammonia, mg/L as N 08 (27) 10 (94) 0 1.333 0 -
Total boron, pg/L as B ll (6) 20 (15) 0 1.655 NA NA
Total lead, g/L as Pb 2 (a) 3 (17) 0 1,259 NA NA
Fecal coliform bacteria, MPN/100 ml 230 (25) 230 (105) 1.382 * ND ) 0

‘Table 30b. 1993 AMNET impairment status in the vicinity of water-quality station 01412800, Cohansey River at Seeley, NJ.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO710 ANO712 ‘None
Impairment status Moderately impaired Moderately impaired ND

69


Hardness

Hardness, an aggregate property of water, is an important consideration in determining the
suitability of water for domestic and industrial uses. Hardness, historically described as a
measure of the capacity of water to precipitate soap, is commonly caused by divalent metallic
cations, namely calcium, magnesium, strontium, ferrous iron, and manganous ions (Sawyer and
McCarty, 1978). Other polyvalent cations also can precipitate soap, but they often are in complex
forms, frequently with organic constituents, and their role in water hardness may be minimal and
difficult to define (Eaton and others, 1995). Cation concentrations can be estimated from
hardness measurements and used to compute the ion balance when checking water analyses.

Calcium and magnesium, the major contributors to hardness, are often the major cations in
surface water. Calcium is the most abundant of the alkaline-earth elements and is a major
constituent of many common rock minerals; it is an essential element for plant and animal life.
Calcium geochemical behavior is governed by the availability of soluble calcium-containing
minerals, solution- and gas-phase equilibria that involve carbon dioxide species, and the
availability of sulfur in the form of sulfate (Hem, 1985). Calcium also participates in cation-
exchange equilibria at aluminosilicate and other mineral surfaces. Calcium salts used for deicing
highways can be carried to surface water with storm runoff and melting snow. Magnesium is an
alkaline-earth element and is essential in plant and animal nutrition. The water chemistry of
calcium and magnesium is similar; however, the geochemical behavior is different. The cation-
exchange behavior of magnesium is similar to that of calcium.

lati tr in ntration to fi nditions

The trend in hardness concentrations during high flows is positive at the upstream station
on the Maurice River (4115), indicating an increase in the contribution from storm runoff over
time at this station (figs. 10a and 11a). The trend in hardness concentrations during high flows is
negative at the one station on the Toms River (4085), indicating a decrease in the contribution
from storm runoff over time at this station. Hardness concentrations during high flows show no
trends at the stations on the Raccoon Creek (47712) and Cohansey River (4128). The trends in
hardness concentrations during low flows are positive at the one station on the South Branch of
the Pennsauken Creek (467081) and the upstream station on the Maurice River (4115), indicating
an increase in the contribution from point sources and ground water over time at these stations
(figs. 10b and 11b). Hardness concentrations during low flows show no trends at the stations on
the Toms River (4085), Hammonton Creek (409416), Batsto River (4095), West Branch of the
Wading River (409815), Oswego River (4100) and East Branch of the Bass (41015) River; the
downstream stations on the Great Egg Harbor River (4110 and 41111); and the stations on the
Crosswicks (4645) and Doctors (464515) Creeks, McDonalds Branch (4665), South (46585) and
North (4670) Branches of the Rancocas, North Branch of the Pennsauken (467069), Raccoon
(47712), and Oldmans (47751) Creeks, and Salem (4825) and Cohansey (4128) Rivers.

75


Figure 32.

33.

34.

35.

36.

37.

38.

39.

40.

41.

ILLUSTRATIONS—Continued

Page
Trends in total nitrite concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of total nitrite load to streamflow at
surface- ra malty 8 stations in the Atlantic Coastal Basins, N.J., water
years 1976-93... 112

Trends in total nitrite concentrations during (A) high- and 8) low-flow
conditions, and (C) relative slope of total nitrite load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .. sissesesseesteeeeestsessesssessessesseesseaeeseres LILO

Trends in total ammonia plus organic nitrogen concentrations during A) high-
and (B) low-flow conditions, and (C) relative slope of total ammonia plus
total organic nitrogen load to streamflow at surface- ater quality stations in
the Atlantic Coastal Basins, N.J., water years 1976-93... sesteteeseesesteseeseeeee L1G,

Trends in total ammonia plus organic nitrogen concentrations during (A) high-
and (B) low-flow conditions, and (C) relative slope of total ammonia plus total
organic nitrogen load to streamflow at surface-water-quality stations in the
lower Delaware River and Delaware Bay Basins, N.J., water years 1976-93.....117

Trends in total ammonia concentrations during (A) high- and\ (B) low-flow
conditions, and (C) relative slope of total ammonia load to streamflow at
surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
years 1976-93..

Trends in total ammonia concentrations during (A) high- and (B) lo low. flow
conditions, and (C) relative slope of total ammonia load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .. seeeseeseesesneeteseesseasseesessensseseeseesenee LLG

Trends in total boron concentrations during (A) high- and B) I low- flow
conditions, and (C) relative slope of total boron load to streamflow at surface-
rey stations in the Atlantic Coastal Basins, N.J., water years
1976-93 .. seseeenee a . seseessteesseetsetsneesneen 22

Trends in total boron concentrations ns during (A) high- and (B) low: flow
conditions, and (C) relative slope of total boron load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .............

Trends in total lead concentrations during (A) high- and (B) low-flow conditions,
and (C) relative slope of total lead load to streamflow relations at surface-
water-quality stations in the Atlantic Coastal Basins, N.J., water years
1976-93 .oescessccsecsessseessseseecseecsssssecsssesssecseessessuessesssssuesacssecsasecesesnecsnesaneessneeseenetees 124

Trends in total lead concentrations during (A) high- and (B) low-flow conditions,
and (C) relative slope of total lead load to streamflow relations at surface-
water-quality stations in the lower Delaware River and Delaware Bay Basins,
N.J., water years 1976-93 oo. ceccssssesssesssessescseeesesesnsnessseeeseescsessstssesssssesseeee lS

. 118

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The AMNET impairment status is non-impaired at station 01411500 and moderately
impaired upstream and downstream from the station (table 31b). The AMNET impairment status
is moderately impaired at station 01411800 and non-impaired upstream from the station (table
32b).

lati

t

Schematics of the trends in concentrations during high and low flows and the values of the
slopes of load to streamflow are shown by constituent (figs. 8-43). Trends in concentrations for
stations in the Atlantic Coastal Basin are shown separately from those for stations in the Lower
Delaware and Delaware Bay Basins because of the large number of stations in the study area.
Schematics depicting the slopes of load to streamflow are presented for each constituent except
dissolved oxygen at saturation and fecal coliform bacteria because loads were not calculated for
these two constituents. The 01 prefix and any extraneous ending zeros have been removed from
station numbers on the schematics and in the text that follows. Schematics are not drawn to scale.
Only results from stations with sufficient data for analysis are discussed. Only two of the 28
water-quality stations have insufficient data for all constituents to determine trends in
concentrations during high and low flows—the upstream station on the Assunpink Creek, station
46362, and station 467329 on the South Branch Big Timber Creek.

In the schematics showing trends of concentrations during low and high flows, symbols
are used to indicate a positive (increasing concentrations), negative (decreasing concentrations),
or no (insignificant change in concentrations) trend (figs. 8-43). Trends in concentrations during
high and low flows indicate trends in contributions from intermittent (storm runoff) and constant
(point sources and ground water) sources, respectively. Trends in concentrations during high
flows indicate changes in the relative contributions from nonpoint sources because storm runoff
contributes to a stream during high flows. Trends in concentrations during low flows indicate
changes in the relative contributions from point sources and ground water because storm runoff
does not contribute to a stream during low flows.

The steepness of the slope of load to streamflow at a site indicates the relative
contributions to the instream load from constant and intermittent sources relative to that at other
sites in the study area. The larger the contribution from storm runoff, the larger the slope will be
because the load will increase with increasing streamflow. Likewise, the larger the contribution
from constant sources, the smaller the slope will be because the instream load will be constant
with increasing streamflow. In the schematics, symbols are used to indicate the range category of
the slope at each station. Filled circles represent stations with slopes in the high range, hashed
circles represent stations with slopes in the moderate range, and quartered circles represent
stations with slopes in the low range. Open circles indicate stations for which slopes could not be
determined because of insufficient data. Only results from stations with slopes in either the high
or low range are discussed.

An increase in the magnitude of the slope in the downstream direction along a stream
would indicate an increase in the relative contribution to the instream load from the storm runoff
and would be evident if the order of circles proceeded from quartered to hashed to solid in the
downstream direction. Likewise, a decrease in the magnitude of the slope in the downstream

73


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these constituents in the study area. The load slopes for HARD, DS, NA, CL, TP, TN, NO32,
NO2, TAON, and NH4 decrease in the downstream direction, indicating a decrease in the
contributions of these constituents from storm runoff along the Assunpink Creek.

Insufficient data are available to determine trends for all constituents at station 01463620
during low and high flows. During high flows at station 01464000, trends are insignificant for
DO, FDO, NO32, and BACT; the trend is negative for NO2, indicating a decrease in the
contribution of NO2 from storm runoff over time. Insufficient data are available at station
01464000 to determine trends for all constituents during low flows.

The AMNET impairment status is non-impaired upstream from and moderately impaired
downstream from station 01463620 (table 16b). The AMNET impairment status upstream and
downstream from station 01464000 is moderately impaired (table 17b).

Crosswicks Creek

The Crosswicks Creek Basin has two water-quality stations—stations 01464500 on
Crosswicks Creek at Extonville and 01464515 on Doctors Creek at Allentown. The 5-year
medians are smaller than the period-of-record medians for TP, TN, NO32, NO2, TAON, and NH4
at station 01464500; 5-year and period-of-record medians are similar for all other constituents
(table 18a). The 5-year and period-of-record medians are similar for all constituents at station
01464515 (table 19a). At both stations, the period-of-record medians for PB are the smallest for
PB at all stations in the study area. At station 01464500, the regression slopes of concentration to
streamflow for ALK, HARD, TOC, DO, FDO, NO32, NO2, TAON, NH4, and BACT show
seasonal dependency. The concentration slopes for ALK, HARD, TOC, NA, CL, DO, FDO, TN,
NO32, NH4, and BACT show seasonal dependency at station 01464515.

The regression slopes of load to streamflow are in the high range for SS and PB at station
01464500 and for ALK at station 01464515, indicating greater contributions of these constituents
from storm runoff relative to that at other sites in the study area. Load slopes are in the low range
for HARD, DS, NA, TN, NO32, and B at station 01464500 and for TOC, TAON, NH4, and B at
station 01464515, indicating smaller contributions of these constituents from storm runoff relative
to that at other sites in the study area.

During low flows, trends are positive for CL at station 01464500 and NA at station
01464515, indicating an increase in the contributions of these constituents from point sources and
ground water over time, and negative for TAON at station 01464500 and NH4 at station
01464515, indicating a decrease in the contributions of these constituents from storm runoff over
time. Trends are insignificant during low flows for HARD, TOC, DS, DO, FDO, TN, NO32, and
BACT at both stations, for NA and NH4 at station 01464500, and for CL and TAON at station
01464515. Insufficient data are available at both stations to determine trends for all other
constituents during low flows and for all constituents during high flows.

The AMNET impairment status is severely impaired at station 01464500 and moderately

impaired downstream from the station (table 18b). The AMNET impairment status is moderately
impaired at station 01464515 and non-impaired downstream from the station (table 19b).

52


Table 15a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01411110, Great Egg Harbor River at Weymouth, N.J.

{Number in parenthesis is the number of available data values, WY, water years; mg/L, milligrams per liter, CaCO , calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; jig/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
tostreamflow streamflow direction —_ direction
Alkalinity, mg/L as CaCO, 2 (27) 3 (75) 0.790 * 0.208 NA NA
Hardness, mg/L as CaCO; 10 (27) 10 (108) 0 965 0 NA
Total organic carbon, mg/L as C 84 (27) 69 (105) 788 * 1.788 0 NA
Suspended sediment, mg/L 5 (il) 6 (9) 0 1.623 NA NA
Dissolved solids, mg/L 38 7) 43 (105) 4 1.114 0 NA
Dissolved sodium, mg/L as Na 4 (27) 5 (108) -159 0 * 841 - NA
Dissolved chloride, mg/L as Cl 8 (27) 8 (108) -052 948 - NA
Dissolved oxygen, mg/L 88 (26) 8.7 (104) 0 * 1.018 0 NA
Fraction of dissolved oxygen at 84 (26) 87 (104) 071 * ND - NA
saturation, %
Total phosphorus, mg/L as P 104 (26) 06 (78) 0 * 974 NA NA
Total nitrogen, mg/L as N 9 (7 9 (90) -.093 .907 0 NA
Total nitrate plus nitrite, mg/L as N 42 (27) 46 (94) -723 * 276 0 NA
Total nitrite, mg/L as N 007 (27) 006 (81) 330 1.330 NA NA
Total ammonia plus organic nitrogen, 4 927) AI (104) 269 * 1.269 - NA
mg/L as N
Total ammonia, mg/L as N 05 (27) 08 (95) 0 822 0 NA
Total boron, pg/L as B <5 (4) 30 (16) 0 0 NA NA
Total lead, jrg/L as Pb 4 4) 6 (16) 0 1.197 NA NA
Fecal coliform bacteria, MPN/100 ml 45 (24) 23 (100) 310 * ND 0 NA

Table 15b. 1993 AMNET impairment status in the vicinity of water-quality station 01411110, Great Egg Harbor River at Weymouth, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station. AN0625 AN0635 None
Impairment status Non-impaired Non-impaired ND

48


Acknowledgments

The authors thank Kevin Berry and Daniel VanAbs, NJDEP, Office of Environmental
Planning, for their cooperation and assistance in planning this report; William Summer, USGS,
for his extensive programing for data manipulations and schematics; and Denis Sun, USGS, for
applying his computer expertise to the design and production of the CD-ROM.

Description of the Stud

The study area is in the southern half of New Jersey and includes rivers that drain into the
Atlantic Ocean, lower Delaware River and Delaware Bay (figs. 4 and 5). Most of the study area is
in the New Jersey Coastal Plain, which consists of unconsolidated sediments of alternating layers
of sand, gravel, silt, and clay that dip gently to the southeast. This system of aquifers and
confining units can be characterized as an independent hydrologic system. In the Coastal Plain,
more than 75 percent of the streamflow is derived from ground-water discharge to stream
channels because of the physiographic, geologic, hydrologic, and climatic conditions of the
region (Vowinkel and Foster, 1981). More than 75 percent of the freshwater supply in the Coastal
Plain comes from ground water (U.S. Geological Survey, 1984). The relative contributions of
constant and intermittent sources to streams in the Coastal Plain are likely influenced by the
ground-water quality in this region of the State.

Atlantic Coastal Basin

The Atlantic Coastal Basin (fig. 4) includes rivers from the Navesink River in Monmouth
County southward to Cape May, New Jersey, that drain into the Atlantic Ocean. In this study,
surface-water-quality and streamflow data were analyzed for four smaller basins contained within
this region—Manasquan, Toms, Mullica, and Great Egg Harbor.

Manasquan River

The Manasquan River is 23 miles long and drains an area of about 81 mi2. The
headwaters start in central Monmouth County; then it flows in a southeasterly direction along the
Ocean-Monmouth County line towards the Atlantic Ocean (New Jersey Department of
Environmental Protection and Energy, 1993). One surface-water gaging and water-quality station
is located on the Manasquan River at Squankum (01408000). At this station, mean annual flow
for water years 1932-93 is estimated to be 74.7 ft*/s; water-quality data are available for the
period of record water years 1963-93 (table 1; fig. 6) (Bauersfeld and others, 1994).

Land use in the basin is about one-half agricultural-crop and pasture land and one-half
residential. Several lakes and ponds in the area are used for recreation (New Jersey Department
of Environmental Protection and Energy, 1993).

10


Table 8a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01409416, Hammonton Creek at Westcoatville, NJ.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO;, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; :g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction, NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Consent tin colts OR
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 6 (27) 6 (75) 0 0.869 NA NA
Hardness, mg/L as CaCO; 23 (27) 21 @1) 0 * 1.011 0 NA.
Total organic carbon, mg/L as C 6.9 (26) 74 (93) 0 * 955 0 NA
Suspended sediment, mg/L 6 (10) 7 Ql) 0 * 1.008 NA NA
Dissolved solids, mg/L 76 (26) 82 (93) -175  * 825 0 NA
Dissolved sodium, mg/L as Na i Q0) 12 (95) -391 * 609 0 NA
Dissolved chloride, mg/L as Cl 14 (26) 14 (94) -.223 a1 0 NA
Dissolved oxygen, mg/L 59 (27) 48 (98) 24 * 1.124 0 NA
Fraction of dissolved oxygen at 57 (25) 50 (89) 0 * ND 0 NA
saturation, %
Total phosphorus, mg/L as P 45 (27) 59 (65) -495, 505 NA NA
Total nitrogen, mg/L as N 4.0 (27) 4.8 (87) -2130«* 786 0 NA
Total nitrate plus nitrite, mg/L as N 2.60 (27) 1.80 (90) -154 0 * 846 0 NA
Total nitrite, mg/L as N 042 (26) 042 (70) -383 617 NA NA
Total ammonia plus organic nitrogen, 1.59 (27) 2.30 (92) -.168 832 0 NA
mg/L as N
Total ammonia, mg/L as N 68 (27) 1.12 (89) 0 * 759 0 NA
Total boron, pg/L as B 50 6) 60 (14) 0 884 NA NA
Total lead, g/L as Pb 4 6) 7 (18) 0) 1.110 NA NA
Fecal coliform bacteria, MPN/100 ml 60 (25) 50 (95) 0 * ND + NA

Table 8b. 1993 AMNET impairment status in the vicinity of water-quality station 01409416, Hammonton Creek at Westcoatville, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO577 None ANOS578
Impairment status Severely impaired - ND Non-impaired

39


Table 11a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01410000, Oswego River at Harrisville, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression  Low- High-
Constituent Median, Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, <l (23) <1 (69) ND ND NA NA
Hardness, mg/L as CaCO, 4 (23) 4 (93) -0.073 0.926 0 NA
Total organic carbon, mg/L as C 5.2 (22) 46 (94) 489 * 1.489 0 NA
Suspended sediment, mg/L 4 (6) 6 (23) 0 1.314 NA NA
Dissolved solids, mg/L 24 (23) 26 (93) 2 1,112 0 NA
Dissolved sodium, mg/L as Na 2 (23) 2 (96) 0 955 0 NA
Dissolved chloride, mg/L as Cl 4 (23) 4 (93) 0 975 NA NA
Dissolved oxygen, mg/L 88 (23) 9.0 (95) 0 * 1.046 0 NA
Fraction of dissolved oxygen at 92 (22) 93 (93) -.039 ND 0 NA
saturation, %
Total phosphorus, mg/L as P 03 (23) 02 (66) 0 1.088 NA NA
Total nitrogen, mg/L as N 5 (23) 4 (80) 180 * 1.180 0 NA
Total nitrate plus nitrite, mg/L as N -16 (23) 04 (84) 0 1.256 0 NA
Total nitrite, mg/L as N 004 (22) 004 (74) 335 1.335 NA NA
Total ammonia plus organic nitrogen, 30 (23) 34 (90) 216 * 1.276 - NA
mg/L as N

Total ammonia, mg/L as N 04 = (23) 05 (88) 0 1.104 0 NA
Total boron, pg/L as B <5 (4) 20 (12) ~ND ND NA NA
Total lead, pg/L as Pb 1 (5) 2 (14) ND 1.274 NA NA
Fecal coliform bacteria, MPN/100 ml 10 (21) 2 (94) 1.207 ND 0 NA

Table 11b. 1993 AMNET impairment status in the vicinity of water-quality station 01410000, Oswego River at Harrisville, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WOQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station, ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station AN0606 AN0607 None
Impairment status Moderately impaired Non-impaired ND

43


Table 32a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01411800, Maurice River near Millville, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter, CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; j1g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 1 00 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression —_Low- High-
Constituent concenaion concentaionconomtaton—tandio.=end’ end
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 9 (8) 9 (8) ND ND NA NA
Hardness, mg/L as CaCO, 24 (10) 23 (48) 0 964 NA NA
Total organic carbon, mg/L as C 5.9 (O) 64 (27) 318 1315 NA NA
Suspended sediment, mg/L 4 (8) 4 (8) ND ND NA NA
Dissolved solids, mg/L 66 (8) 69 (29) 0 1.011 NA NA
Dissolved sodium, mg/L as Na 8 (10) 9 (52) -228 772 NA NA
Dissolved chloride, mg/L as Cl 14 (10) 12 (51) -.179 821 NA NA
Dissolved oxygen, mg/L 7.7 (12) 8.2 (94) 0 * 1.027 0 NA
Fraction of dissolved oxygen at 82 a7) 84 1) 048 * ND 0 NA
saturation, %
Total phosphorus, mg/L as P 03 (16) 05 (58) 0 1.126 NA NA
Total nitrogen, mg/L as N 27 (17) 27 (84) -095 * 905 0) NA
Total nitrate plus nitrite, mg/L as N 1.88 (17) 1.70 (85) 0 * 916 0 NA
Total nitrite, mg/L as N 014 (17) O11 (85) 0 * 908 0 NA
Total ammonia plus organic nitrogen, 96 (17) 1.07 (92) -109 * 891 0 NA
mg/L as N

Total ammonia, mg/L asN 47 (17) 48 (79) -.585 AIS 0 NA
Total boron, ug/L as B 40 Q) 40 Q) = ND ND NA NA
Total lead, ug/L as Pb 2 4) 7 (24) 0 0  - NA NA
Fecal coliform bacteria, MPN/100 mL 20 (7) 33 (94) 0 * ND 0 NA

Table 32b. 1993 AMNET impairment status in the vicinity of water-quality station 01411800, Maurice River near Millville, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from W¢Q station is within 5 miles upstream from the WQ station; at
WO-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO740 ANO751 None
Impairment status : Non-impaired Moderately impaired ND

72


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127


LOAD, IN POUNDS PER DAY

STREAMFLOW, IN CUBIC FEET PER SECOND

EXPLANATION

+ Load constant with increased streamflow;
constant sources are more important

Load increases with increased streamflow;
1o; O intermittent sources are more important

Figure 2. Hypothetical logarithmic plot of expected load-to-streamflow relations
for a stream strongly affected by constant (point source and ground water) and
intermittent (nonpoint storm runoff) sources.


streamflow is base flow), generally have small concentrations, positive concentration-slope
values, and large (greater than 1.0) load-slope values. For such streams, the contributions to
instream load from storm runoff is large (tables 9 and 21). Storm runoff is composed of overland
runoff and interflow which can contain displaced shallow ground water and water from nearby
wetlands.

Significant seasonal dependency (14 or more stations) is evident for HARD, TOC, NA,
DO, FDO, TP, TN, NO32, NO2, and BACT (tables 37 and 38). Seasonal dependency is not
evident at any station for B and only at station 4085 on the Toms River for PB. DO shows
seasonal dependency at all stations, possibly because of its relation to bioactivity in surface water.
NA and HARD most likely show seasonal dependency because of road salting; however, DS,
which includes the ions sodium, calcium, and magnesium, shows seasonal dependency at only
seven stations.

A similar study was conducted in the Hackensack, Passaic, Elizabeth, and Rahway River
Basins. Buxton and others (1998) found that the minimum load-to-streamflow slopes for ALK,
HARD, TOC, DS, NA, and CL in those basins ranged from 0.56 to 0.81, and the maximum load
slopes ranged from 0.92 to 1.22. SS had the highest minimum load slope of 0.85 and the highest
maximum load slope of 1.92. For the six nutrient species, minimum load slopes ranged from 0.00
to 0.55, and maximum load slopes ranged from 1.11 to 1.24. The spread between the minimum
and maximum load slopes is smaller and the slopes tend to be of a lower magnitude for most
constituents compared to those for the Atlantic Coastal, lower Delaware River, and Delaware Bay
Basins. The slopes in the Atlantic Coastal, lower Delaware River, and Delaware Bay Basins, in
general, are greater than the slopes in the Hackensack, Passaic, Elizabeth, and Rahway River
Basins, indicating the greater relative importance of contributions from intermittent sources
(storm runoff) than from constant sources (point sources and ground water) in the ground-water-
dominated system.

Load slopes are in the low range for eight constituents at station 4640 on the Assunpink
Creek, for seven at the stations on the Hammonton Creek (409416) and South Branch of the
Pennsauken Creek (467081), and for five at station 4085 on the Toms River; all other stations
have four or less constituents with slopes in the low range. No load slopes are in the low range for
stations on the Oswego (4100) and Cooper (46715) Rivers, and South Branch Big Timber Creek
(456329). Load slopes are in the high range for six constituents at station 4095 on the Batsto
River; all other stations have four or less constituents with slopes in the high range. Stations with
no load slopes in the high range are on the Toms River (4085), Great Egg Harbor River (410784),
Assunpink Creek (4640), South Branches of the Rancocas (46585) and Pennsauken (467081)
Creeks, and Maurice River (4118).

Load slopes for each constituent can be compared at stations along the Great Egg Harbor
River, Assunpink Creek, and Maurice River. The magnitude of the load slopes for HARD, TP,
TN, NO2, and TAON increases along the Great Egg Harbor River, indicating an increase in the
relative influence of contributions from intermittent sources (storm runoff) along the river; the
period-of-record medians for these constituents decreases along the river. The magnitude of the
load slopes for ALK, HARD, DS, NA, CL, TP, TN, NO32, NO2, TAON, and NH4 decreases
along the Assunpink Creek, indicating a decrease in the relative influence of contributions from
storm runoff along the river. The magnitude of the load slopes for TOC, NA, CL, TAON, and
NH4 decreases along the Maurice River, also indicating a decrease in the relative influence of
contributions from storm runoff along the river.

129


Table 14a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01411000, Great Egg Harbor River at Folsom, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO;, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY

Regression Regression  Low- High-

Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend

to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 5 ay 5 ay -0.822 0 NA NA
Hardness, mg/L as CaCO, rT (12) 14 (65) 0 1.062 0 NA
Total organic carbon, mg/L as C 43 (1) 90 3) 653 1.652 NA NA
Suspended sediment, mg/L 5 (10) 6 (18) 0 1.035 NA NA
Dissolved solids, mg/L 39 qd 60 (35) 159 1,158 NA NA
Dissolved sodium, mg/L as Na 5 (12) 7 (67) +267 -733 - NA
Dissolved chloride, mg/L as Cl 8 (13) an (72) -.129 871 - NA
Dissolved oxygen, mg/L 8.6 (20) 88 (114) 0 * 993 0 NA
Fraction of dissolved oxygen at 80 (20) 84 (113) - 106 * ND 0 NA
saturation, Y%
Total phosphorus, mg/L as P 07 (21) 09 (63) 0 * 1.176 NA NA
Total nitrogen, mg/L as N 13. (21) 15. (94) -155 845 0 NA
Total nitrate plus nitrite, mg/L as N 73 (21) 85 (97) -613 * 387 0 NA
Total nitrite, mg/L as N 008 (20) .007 (96) 0 1.073 i) NA
Total ammonia plus organic nitrogen, ‘61 (21) 64 (111) .200 1,200 : - NA
mg/L as N

Total ammonia, mg/L as N 609 (21) 16 (96) -415 584 0 NA
Total boron, pg/L as B 40 (2) 50 (3) ND ND NA NA
Total lead, g/L as Pb 2 @) 6 (38) 0 1.149 NA NA
Fecal coliform bacteria, MPN/100 ml 27 (21) 20 (113) 907 * ND + NA

Table 14b. 1993 AMNET impairment status in the vicinity of water-quality station 01411000, Great Egg Harbor River at Folsom, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station AN0623 AN0625 AN0635
Impairment status Non-impaired Non-impaired Non-impaired

47


CONTENTS—Continued

Page

Appendixes

ll.
12.
13.
14.
15.
16.
17.
18.

Figure 1.

2.

Total nitrogen

Total nitrate plus nitrite

Total nitrite

Total ammonia plus organic nitrogen
Total ammonia

Total boron

Total lead

Fecal coliform bacteria

ILLUSTRATIONS

Map showing four watershed regions in New Jersey ...

Graph showing hypothetical logarithmic plot of expected Toad- to:
relations for a stream strongly affected by constant (point sources and ground
water) and intermittent (nonpoint storm runoff) sources... sess sessed)

. Graphs showing example plot of relation of instream load of | total nitrogen to.

instantaneous streamflow at water-quality stations in the Rockaway River
Basin, New Jersey, 1985-91.. seeseeee secseeeeeceeetseeesee O

. Map showing locations of surface- water-quality stations “and ambient

biomonitoring network stations in the Atlantic Coastal Basin, New Jersey...

. Map showing locations of surface-water-quality stations and ambient

biomonitoring network stations in the lower Delaware River and Delaware
Bay Basins, New Jersey

. Period of record of water-quality data for selected stations in the Atlantic Coastal,

lower Delaware River, and Delaware Bay Basins, New Jersey, for water
years 1976-93..

sere

. Example page from Appendix 12 of graphs showing relation of concentration to

streamflow, relation of load to streamflow, and trends in low- and high-flow
concentrations for total nitrate plus nitrite at a station on the South Branch
Rancocas Creek at Vincentown, New Jersey, water years 1976-93 ......ceeseeeend2

. Schematics showing:
. Trends in alkalinity concentrations during (A) high- and (B) low-flow conditions,

and (C) relative slope of alkalinity load to streamflow at surface-water-quality
stations in the Atlantic Coastal Basins, N.J., water years 1976-93 see Tb

. Trends in alkalinity concentrations during (A) high- and (B) low-flow conditions,

and (C) relative slope of alkalinity load to streamflow at surface-water-quality

stations in the lower Delaware River and Delaware Bay Basins, N.J., water

YOATS 1976-93 oe esceceececseescsesseesseecnesseesssccsecsnecssesessuesssssasesecsuecsecssessecssseesseaesneees 77
Trends in total hardness concentrations during (A) high- and (B) low-flow conditions,

and (C) relative slope of total hardness load to streamflow at surface-water-quality

stations in the Atlantic Coastal Basins, N.J., water years 1976-93 ........sseessesseeesee 78

vi


Table 26a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01467329, South Branch Big Timber Creek at Blackwood Terrace, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; 1g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO 25 (27) 24 (72) -0.094 0.906 NA NA
Hardness, mg/L as CaCO, 41 (27) 39 (103) -044 * 955 NA NA
Total organic carbon, mg/L as C 47 (27) 4.7 (103) 163 * 1.163 NA NA
Suspended sediment, mg/L 16 an) 18 (18) 630 1.628 NA NA
Dissolved solids, mg/L 89 (26) 83 (101) 0 * -980 NA NA
Dissolved sodium, mg/L as Na 1 (27) 8 (105) - 163 * 837 NA NA
Dissolved chloride, mg/L as Cl 17 (27) 13 (103) -155  * 845 NA NA
Dissolved oxygen, mg/L 10.0 (26) 8.2 (103) 0 * 1.018 NA NA
Fraction of dissolved oxygen at 94 (26) 85 (102) 0 * ND NA NA
saturation, %
Total phosphorus, mg/L as P 10 (27) 13 (77) 214 * 1.274 NA NA
Total nitrogen, mg/L as N 19 (27) 19 (92) 0 * 1.066 NA NA
Total nitrate plus nitrite, mg/L as N 1.13 (27) 1.12 (95) 0 * 905 NA NA
Total nitrite, mg/L as N 034 (26) 031 (77) 0 * 1.037 NA NA
Total ammonia plus organic nitrogen, 73 (27) 80 (101) 169 1.169 NA NA
mg/L as N

Total ammonia, mg/L as N 25 (27) 22 (93) 0 * 1.138 NA NA
Total boron, pg/L as B 90 (6) 50 (18) 0 788 NA NA
Total lead, pig/L as Pb 4 © 6 (18) 0 1.408 NA NA
Fecal coliform bacteria, MPN/100 ml 490 (25) 330 (100) 1.185 * ND NA NA

Table 26b. 1993 AMNET impairment status in the vicinity of water-quality station 01467329, South Branch Big Timber Creek at Blackwood
Terrace, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station None None AN0659
Impairment status ND ND Moderately impaired

64


lection of tit ites, a

Constituents were chosen on the basis of their usefulness as indicators of the quality of the
surface water and usefulness in developing effective surface-water-quality management practices.
The 18 constituents selected include aggregate water properties (properties that include
concentrations of several different chemical species), major ions, dissolved oxygen, nutrients,
metals, and bacteria (table 2).

The basins contain 25 water-quality stations (table 1) with data from water years 1976-93
that are part of the USGS/NJDEP Cooperative Ambient Surface Water Quality Network and 3
water-quality stations that are part of the National Stream Quality Accounting Network
(NASQAN). Eighteen of the stations also are operated as surface-water gaging stations. These
stations were chosen on the basis of the locations and periods of record.

Water-quality and streamflow data were retrieved from the NWIS data base. Water-
quality data for water years 1976-93 are available for 27 stations; partial records are available for
one station (fig.6). Streamflow data are available for 16 water-quality stations for water years
1976-93.

Data Preparation

Water-quality and instantaneous-streamflow data retrieved from the NWIS data base were
reviewed extensively for accuracy and were maintained in a SAS data base. Values of dissolved
nitrate plus nitrite and dissolved nitrite were substituted for values of total nitrate plus nitrite and
total nitrite where the latter were missing. This substitution is appropriate because nitrate and
nitrite are anions that are poorly absorbed to mineral surfaces, and therefore, are present in
ambient water almost exclusively as dissolved species (Hem, 1985). Where both dissolved and
total concentration values were available for nitrate plus nitrite and nitrite, little or no difference
was observed.

Water-Quality Data

Values for the fraction of dissolved oxygen at saturation and concentrations of hardness,
total organic carbon, and total nitrogen were calculated.

The fraction of dissolved oxygen at saturation is the ratio of the measured dissolved
oxygen concentration to the dissolved oxygen concentration at saturation, in percent, computed
by using the following equation:

= DO
FDO = 100 ome (a)
where

FDO = fraction of dissolved oxygen at saturation;

DO = dissolved oxygen concentration, in milligrams per liter; and

DO,q:= dissolved oxygen at saturation, in milligrams per liter.

19


Table 25a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01467150, Cooper River at Haddonfield, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction, NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression  Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO; 29 qd) 29 (11) 0.133 0.867 NA NA
Hardness, mg/L as CaCO, 56 (12) 59 (63) ~104 0 * 896 NA NA
Total organic carbon, mg/L as C 59 (10) 8.6 © (34) 0 1.110 NA NA
Suspended sediment, mg/L 26 ay 27 (20) 309 1.309 NA NA
Dissolved solids, mg/L 10 ay 155 (36) 0 941 NA NA
Dissolved sodium, mg/L as Na I (12) 21 (68) 0 969 NA NA
Dissolved chloride, mg/L as Cl 22 (13) 30 (72) 0 961 NA NA
Dissolved oxygen, mg/L 9.6 (21) 7.8 (115) 101 * 1.101 NA 0
Fraction of dissolved oxygen at 89 (21) 78 (112) 074 * ND NA 0
saturation, %
Total phosphorus, mg/L as P 28 (21) 78 (62) 0 * 1.145 NA NA
Total nitrogen, mg/L as N 14 (21) 73 (97) 0 1.064 NA -
Total nitrate plus nitrite, mg/L as N AT (21) 63 (102) 0 1.074 NA 0
Total nitrite, mg/L as N 018 (20) 070 (94) 0 sd 1.178 NA -
Total ammonia plus organic nitrogen, 89 (21) 6.80 (107) 0 1.032 NA -
mg/L as N
Total ammonia, mg/L as N 21 (2b 5.06 (100) 0 1.269 NA 0
Total boron, g/L as B 50 @) 55 (4) ND ND NA NA
Total lead, j1g/L as Pb i (5) 19 (43) 884 1.884 NA NA
Fecal coliform bacteria, MPN/100 ml 790 (21) 1300 (iis) 623 * ND NA 0

‘Table 25b. 1993 AMNET impairment status in the vicinity of water-quality station 01467150, Cooper River at Haddonfield, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status}

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station. ANO190 ANOI91 None
Impairment status Severely impaired Severely impaired ND

62


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138


Rancocas Creek

The Rancocas Creek Basin has three water-quality stations—stations 01465850 on the
South Branch of the Rancocas Creek at Vincentown, 01467000 on the North Branch of the
Rancocas Creek at Pemberton, and 01466500 on the McDonalds Branch in Lebanon State Forest.
The 5-year and period-of-record medians are similar for all constituents at all stations (tables 20a,
21a, and 22a). At station 01465850, the period-of-record median for TOC is the largest for TOC
in the study area. The period-of-record medians for ALK, HARD, SS, DS, NA, CL, DO, FDO,
TP, TN, NO32, TAON, and NH4 at station 01466500 are the smallest for these constituents at all
stations in the study area because this station on the McDonald’s Branch in Lebanon State Forest
represents a very small area (2.35 mi?) and is an undeveloped watershed. The regression slopes
of concentration to streamflow for HARD, TOC, NA, CL, DO, FDO, TP, NH4, TAON, and
BACT at stations 01465850 and 01467000, for NO32 at station 01465850, and for TN and NO2
at station 01467000 show seasonal dependency. The concentration slopes for HARD, SS, NA,
DO, FDO, and NO32 show seasonal dependency at station 01466500.

The regression slopes of load to streamflow are in the high range for B at station
01467000, indicating greater contributions of B relative to that at other sites in the study area.
The regression slopes of load to streamflow are in the high range for TOC, DS, TN, and TAON at
station 01466500 where the load slopes for all these constituents except TOC are the largest in the
study area. The load slopes for DS, TN, and TAON at station 01466500 are the largest for these
constituents in the study area. Load slopes are in the low range for SS, TP, TAON, and NH4 at
station 10465850, for TAON and NH4 at station 01467000, and for SS at station 01466500,
indicating smaller contributions of these constituents from storm runoff relative to that at other
sites in the study area.

During low flows, trends are positive for CL and NO32 at station 01465850 and for NA
and CL at station 01467000, indicating an increase in the contributions of these constituents from
point sources and ground water over time. During low flows, trends are negative for FDO at
station 01465850 and for TAON and NH4 at station 01467000, indicating a decrease in the
contributions of these constituents from storm runoff over time. Trends are insignificant during
low flows for HARD, TOC, DS, NA, DO, TN, TAON, NH4, and BACT at station 01465850, for
HARD, TOC, DS, DO, FDO, TN, NO32, and BACT at station 01467000, and for HARD, SS, DS,
NA, CL, DO, FDO, TP, and NO32 at station 01466500. Insufficient data are available to
determine trends of all other constituents at these stations during low flows. During high flows at
station 01466500, trends are insignificant for SS, DS, CL, DO, FDO, TP, and NO32. Insufficient
data are available for all other constituents at station 01466500 and for all constituents at stations
01465850 and 01467000 to determine trends during high flows.

The AMNET impairment status is severely impaired upstream from station 01465850 and
moderately impaired downstream from the station (table 20b). The AMNET impairment status is
moderately impaired at station 01466500 (table 21b). The AMNET impairment status is non-
impaired at station 01467000 and moderately impaired downstream from the station (table 22b).

35


75°30! 75° a
I I
EXPLANATION

RCER open

—— -» —— Drainage basin boundary

1464000 “NHONMOUTH
ANON18 \ Sie 0 2 babi cou

----— County boundary
01467329 U-S. Geologoical Survey surface-water-quality
v station and number

ANO179 Ambient biomonitoring network station and

v number

‘ANTGES {000s oN
‘Kia 3V- "Yo1482500,

39° |
30°
ATLANTIC COUNTY

7 DELAWARE BAY >

' &

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\

~ . 0 5 10 KILOMETERS

39° }—

A |

Base from U.S, Geological Survey digital
data, 1:100,000, 1983, Universal Transverse
Mercator projection, Zone 18

Figure 5. Locations of surface-water-quality stations and ambient biomonitoring
network stations in the lower Delaware River and Delaware Bay Basins, New Jersey.

12


Relations of load to streamflow

The relation of load to streamflow was developed by using the same procedures as those
used to develop the relation of concentration to streamflow for all measurements. Loads were not
determined for fraction of dissolved oxygen at saturation and fecal coliform bacteria. For each
constituent and station, the detection limit was sct equal to the smallest uncensored load measured
at the station. The load relation takes the following form:

log(LOAD) = SLOPE x log (FLOW) + INT, (10)
where
log = base-10 logarithm;
LOAD = constituent load, in pounds per day;
SLOPE = the slope of the relation;
FLOW = streamflow, in cubic feet per second; and
INT = the intercept of the relation.

A smoothed relation of load to streamflow is shown for a constituent at cach station at
which there were 10 or more values. This relation was determined by using the SM smoothing
routine in SAS (SAS Institute, Inc., 1990, p. 416).

t ns during low and high fi

Trends in concentrations during low and high flows were tested to determine whether the
probability distribution from which the observations come increased or decreased during water
years 1976-93. The 75-percent and 25-percent values of the flow durations were used to divide
the measurements for each station into a low- or high-flow group, respectively. Concentrations
during low flows were designated as those measured at streamflows less than or equal to the daily
mean streamflow that was exceeded 75 percent of the time; concentrations during high flows were
designated as those measured at streamflows greater than the daily mean streamflow that was
exceeded 25 percent of the time.

For both the low- and high-flow data sets, trend tests were conducted only if there was at
least one measurement in each data set consisting of not less than four of the six water years in
each one-third of the period of study (18 years). This requirement followed a recommendation
made in Helsel and Hirsch (1992) that there be no less than 20 percent of the total measurements
in each one-third of the period being tested for trends. Therefore, 12 was the minimum number of
low- or high-flow measurements used ina test. Fewer data could have been tested for trends. The
fewer the data, however, the less likely it is that the measured concentrations represent conditions
during the period tested and, therefore, the less likely that the results of the trend test are accurate.

The seasonal Kendall’s tau method (Hirsch and others, 1982) was used to examine the
data for trends. For both the low- and high-flow data sets, the test was run on the median of the
measured concentrations for each water year because of variations in sampling frequency (Hirsch
and others, 1982). The test statistic, tau, was calculated from the relative sizes of the annual

29


the smallest for these constituents in the study area. The load slopes of TOC, TN, NO2, and
TAON increase in the downstream direction, indicating an increase in the contributions of these
constituents from storm runoff along the Great Egg Harbor River.

Only BACT at station 01411000 has a positive trend during low flow, indicating an
increase in the contributions of BACT from point sources and ground water over time. During
low flows, trends are negative for NO32 at station 01410784, for NA, CL, and TAON at station
01411000, and for NA, CL, FDO, and TAON at station 01411110, indicating a decrease in the
contributions of these constituents from point sources and ground water over time. The trends are
insignificant for TOC, DO, FDO, TN, TAON, and NH4 at station 01410784, for HARD, DO,
FDO, TN, NO32, NO2, and NH4 at station 01411000, and for HARD, TOC, DS, DO, TN, NO32,
NH4, and BACT at station 01411110 during low flows. Insufficient data are available to
determine trends for all constituents during high flows at all stations on the Great Egg Harbor
River.

The AMNET impairment status is non-impaired at station 01410784 and moderately
impaired upstream and downstream from the station (table 13b). The AMNET impairment status
is non-impaired at and upstream and downstream from station 01411000 (table 14b). The
AMNET impairment status is non-impaired at and upstream from station 01411110 (table 15b).

Lower Delaware River Basin

Fourteen water-quality stations are located in nine subbasins in the lower Delaware River
Basin. Two stations are located on the Assunpink Creek, two in the Crosswicks Creek Basin,
three in the Rancocas Creek Basin, two in the Pennsauken Creek Basin, one each on the Cooper
River, South Branch Big Timber Creek, Raccoon Creek, Oldmans Creek, and Salem River.

Assunpink Creek

Two water-quality stations are located on the Assunpink Creek—stations 01463620 near
Clarksville and 01464000 at Trenton. The 5-year and period-of-record medians are similar for all
constituents at station 01463620 (table 16a). The 5-year medians are smaller for NO2, TAON,
and NH4 and greater for NO32 compared to the period-of-record medians at station 01464000
(table 17a). At station 01463620, the period-of-record median for FDO is the largest and for PB
the smallest for these constituents at all stations in the study area. At station 01464000, the
period-of-record median for ALK is the largest for this constituent at all stations in the study area.
The regression slopes of concentration to streamflow for ALK, TOC, NA, CL, DO, TN, NO32,

and TAON show seasonal dependency at station 01463620. The concentration slopes for CL,
DO, FDO, NO2, and BACT show seasonal dependency at station 01464000.

The regression slopes of load to streamflow are in the high range for NA and NO2 at
station 01463620, indicating greater contributions of these constituents from storm runoff relative
to that at other sites in the study area. Load slopes are in the low range for TOC at station
01463620 and for HARD, DS, NA, CL, TP, TN, NO32, and TAON at station 01464000,
indicating smaller contributions of these constituents from storm runoff relative to that at other
sites in the study area. The load slopes for DS and CL at station 01464000 are the smallest for

49


Lower Delaware River Basin

The lower Delaware River Basin (fig. 5) from just south of Trenton to where the river
widens into Delaware Bay contains many tributaries. In this study, surface-water-quality and
streamflow data were analyzed for nine streams that flow directly into the lower Delaware
River—Cooper and Salem Rivers, and Assunpink, Crosswicks, Rancocas, Pennsauken, South
Branch of the Big Timber, Raccoon, and Oldmans Creeks.

Assunpink Creek

Assunpink Creek is about 25 miles long and drains an area of 91 mi2, The flow begins in
Monmouth County, continues through central Mercer County, then discharges into the Delaware
River at Trenton (New Jersey Department of Environmental Protection and Energy, 1993). A
mean annual flow of 131 ft*/s is estimated for water years 1924-93 at the surface-water gaging
station on the Assunpink Creek at Trenton (01464000) (Bauersfeld and others, 1994). Two water-
quality stations are located on the Assunpink Creek (table 1). The period of record for water-
quality-data collection for each station is shown in figure 6.

Land use in the basin is varied. It ranges from undeveloped and agricultural to suburban
and urban (New Jersey Department of Environmental Protection and Energy, 1993).

Crosswicks Creek

Crosswicks Creek is about 25 miles long and drains an area of 146 mi*. It drains parts of
Mercer, Monmouth, Ocean, and Burlington Counties (New Jersey Department of Environmental
Protection and Energy, 1993). A mean annual flow of 134 ft?/s is estimated for water years
1940-93 at the surface-water gaging station on Crosswicks Creek at Extonville (01464500)
(Bauersfeld and others, 1994). The only water-quality station on the creek is at Extonville
(01464500), where the period of record for water-quality-data collection is water years 1965-93
(fig. 6) (Bauersfeld and others, 1994).

Land use in this basin is diverse. The Crosswicks Creek drainage area includes
agricultural land, forested areas, residential areas, commercial zones, and military installations
(New Jersey Department of Environmental Protection and Energy, 1993).

Rancocas Creek

Rancocas Creek basin covers about 380 mi’, making it the largest basin in south-central
New Jersey. The North Branch drains 167 mi2 of the total area, and the South Branch drains
144 mi? of the total area. The North Branch is 31 miles long and is fed by the McDonalds
Branch; the South Branch is 27 miles long. The main stem of the Rancocas Creek is about
8 miles long and drains an area of about 49 mi’. Tides influence stream levels for 15 stream miles
upstream from the Delaware River, along the entire length of the Rancocas Creek main stem to
Mount Holly on the North Branch and to Vincentown on the South Branch (New Jersey
Department of Environmental Protection and Energy, 1993). Mean annual flow for water years

15


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82


Toms River

For the one station on the Toms River, station 01408500 near Toms River, the 5-year and
period-of-record medians are similar for all constituents (table 6a). The period-of-record median
for DO at this site is the largest for DO in the study area. The regression slopes of concentration
to streamflow for HARD, TOC, SS, NA, DO, FDO, TP, TN, NO32, TAON, and PB show seasonal
dependency. The regression slopes of load to streamflow are in the low range for HARD, TP, TN,
NO32, and NH4, indicating smaller contributions of these constituents from storm runoff relative
to that at other sites in the study area. During low flows, the trend is positive for NA and CL,
indicating an increase in the contributions from point sources and ground water over time, and
negative for TP, indicating a decrease in the contributions from point sources and ground water
over time. The trends are insignificant for HARD, SS, DS, DO, FDO, TN, NO32, and TAON
during low flows. During high flows, the trend is positive for CL, indicating an increase in the
contribution of CL from storm runoff over time, and negative for HARD and TP, indicating a
decrease in the contributions of these constituents from storm runoff over time. The trends are
insignificant for SS, DS, NA, DO, FDO, TN, NO32, and TAON during high flows. Insufficient
data are available to determine trends for ALK, TOC, NO2, NH4, B, PB, and BACT during low
and high flows. The AMNET impairment status is non-impaired upstream from and at station
01408000 (table 6b).

Mullica Ri

Six water-quality stations are located in the Mullica River Basin on the Mullica River,
Hammonton Creek, Batsto River, West Branch of the Wading River, Oswego River, and Bass
River. For the one station on the Mullica River, station 01409387 at the outlet of Atsion Lake, the
5-year and period-of-record medians are similar for all constituents (table 7a). The regression
slopes of concentration to streamflow for HARD, TOC, NA, DO, NO32, NO2, and NH4 show
seasonal dependency. The regression slopes of load to streamflow for NA, CL, and B are in the
high range, indicating greater contributions of these constituents from storm runoff relative to that
at other sites in the study area. Load slopes for ALK, SS, and TAON are in the low range,
indicating smaller contributions of these constituents from storm runoff relative to that at other
sites in the study area. The load slopes for ALK and SS at station 01408500 are the smallest for
these constituents in the study area. During low flows, the trends are insignificant for TOC, NA,
DO, FDO, TN, NO32, TAON, NH4, and BACT. Insufficient data are available to determine
trends for all other constituents during low flows and for all constituents during high flows. The
AMNET impairment status is non-impaired upstream from station 01409387 and moderately
impaired downstream from the station (table 7b).

For the one station on the Hammonton Creek, station 01409416 at Westcoatville, the
5-year medians are smaller than the period-of-record medians for TP, TAON, and NH4 and larger
for NO32; 5-year and period-of-record medians are similar for all other constituents (table 8a).
The regression slopes of concentration to streamflow for HARD, TOC, SS, DS, NA, DO, FDO,
TN, NO32, NH4, and BACT show seasonal dependency. The regression slope of load to
streamflow for ALK is in the high range, indicating a greater contribution of ALK from storm
runoff relative to that at other sites in the study area. Load slopes for TOC, SS, DS, NA, TP, TN,
and TAON are in the low range, indicating smaller contributions of these constituents from storm

36


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77


Table 19a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01464515, Doctors Creek at Allentown, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY

Regression Regression — Low- High-

Constituent concenvaion concenraion concentaion lead. wend. end

to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 20 (26) 21 (73) 0.2330 * 0.767 NA NA
Hardness, mg/L as CaCO; 50 (27) 50 (107) -094 * 906 0 NA
Total organic carbon, mg/L as C 44 (27) 4.6 (103) 0 * 975 i) NA
Suspended sediment, mg/L 5 ay 6 (18) 639 1.638 NA NA
Dissolved solids, mg/L 97 (27) 99 (105) -.090 910 0 NA
Dissolved sodium, mg/L as Na 7 (27) 6 (107) -105  * 895 + NA
Dissolved chloride, mg/L as Cl 18 (27) 15 (107) -058 * 942 0 NA
Dissolved oxygen, mg/L 8.2 (26) 8.2 (106) 1630 * 1.163 0 NA
Fraction of dissolved oxygen at 91 (26) 88 (105) 094 * ND 0 NA
saturation, %
Total phosphorus, mg/L as P 14 (27) JT (80) -.190 810 NA NA
Total nitrogen, mg/L as N 19 (27) 19 (95) -069* 931 0 NA
Total nitrate plus nitrite, mg/L as N 1.08 (27) 93 (96) 0 * 1.102 0 NA
Total nitrite, mg/L as N 029 (27) 030 (79) -369 630 NA NA
Total ammonia plus organic nitrogen, 83 (27) 1.00 (106) -.220 -780 0 NA
mg/L as N

Total ammonia, mg/L as N 29° QN) 40 (97) -512* ABB - NA
Total boron, jig/L as B 30 (6) 30 (17) 803 0 NA NA
Total lead, g/L as Pb <l © 2 (18) 0 1.237 NA NA
Fecal coliform bacteria, MPN/100 ml 790 (25) 480 (104) 568 * ND 0 NA

Table 19b. 1993 AMNET impairment status in the vicinity of water-quality station 01464515, Doctors Creek at Allentown, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station None ANO129 ANO130
Impairment status ND Moderately impaired Non-impaired

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As with the water-quality data, steps were taken to ensure consistent data quality because
of the long time period over which the data were collected. Streamflow data for the period of
record, water years 1976 to 1993, were reviewed to identify any obvious data inconsistencies (that
is, data outliers), many of which were due to data entry errors. The review was performed prior to
statistical analysis and interpretation. This review resulted in the removal from the data base of
less than 2 percent of the original data set.

Streamflow data from each surface-water-quality monitoring station were regressed on
daily mean values from the NWIS data base to ensure that the values were consistent. Residuals
of plots of streamflow as a function of gage height, and streamflow at adjacent or nearby
continuous-record stations, were evaluated. Outliers were identified as those values with
studentized residuals larger than an absolute value of 2 and were further evaluated by considering:

(1) the time of sample collection,

(2) upstream flow regulation, and

(3) streamflow at nearby stations.

If no plausible explanation for the apparent inconsistency of a data point (an outlier),
based on the factors listed above, was found, the daily mean values were used. These new values
were double-checked by plotting them on a graph of field specific conductance as a function of
flow duration. Specific conductance would be expected to be inversely proportional to
streamflow, except during times of snow melt. The measurement of specific conductance is
independent of the measurement of streamflow.

Flow-Duration Data

Flow durations for each water-quality station were obtained as data from WATSTORE
(National Water Data Storage and Retrieval System), as output from computer simulation using
MOVE.1 (Maintenance of Variance Extension, Type 1) (Hirsch, 1982), and as drainage area
adjustments from nearby surface-water gaging stations (table 3).

Flow-duration tables were developed by using the Daily Value Statistics (DVSTAT)
computer program in the WATSTORE data base for 19 of the 28 surface-water-quality stations
that had continuous streamflow records. Flow-duration data show the percentage of time that a
particular discharge is exceeded, and a flow-duration point is a discharge value, in fR/s,
interpolated from a duration table for a particular percentage of time. For the purpose of this
study, the 25 percent duration point was used to determine high-flow conditions, and the 75
percent duration point was used to determine the low-flow conditions. The resulting values for
each surface-water-quality station are shown in table 3.

Base-flow relations were determined for 8 of the 28 water-quality gaging stations by
correlating instantaneous low-flow discharge at the partial-record station with the mean daily
discharge at a nearby “index” continuous-record gaging station. A streamflow record extension
technique, MOVE. 1, was used to develop the correlations (Hirsch, 1982). MOVE.1 was used
because it was adequate for the purposes of this study, in which flow duration was used only to
divide streamflow data into groups of high, moderate, and low ranges for trend analysis. The
relations are made in the following form:

23


Table

33.

34.

35.

36.

37.

38.

39.

40.

41.

42.

TABLES—Continued

Page
24. 01467081, South Branch Pennsauken Creek at Cherry Hill, N.J......e.ceeeseeseee! 61
25. 01467150, Cooper River at Haddonfield, N.J... 62

26. 01467329, South Branch Big Timber Creek at Blackwood Terrace, N.
27. 01477120, Raccoon Creek near Swedesboro, N.J. ..
28. 01477510, Oldmans Creek at Porches Mill, N.J.
29. 01482500, Salem River at Woodstown, N.
30. 01412800, Cohansey River at Seeley, N.J.
31. 01411500, Maurice River at Norma, N.J..
32. 01411800, Maurice River near Millville, N.J.
Concentration trends during low flow at surface-water-quality stations in the
Atlantic Coastal Basins, N.J., water years 1976-93 .o...eeeceeseseeseesseeseseeseeseees 130
Concentration trends during low flow at surface-water-quality stations in the
lower Delaware River and Delaware Bay Basins, N.J., water years
1976-93 .
Concentration trends during high flow at surface-water-quality stations i in n the
Atlantic Coastal Basins, N.J., water years 1976-93 .. cesses seven 132
Concentration trends during high flow at surface-water- -quality stations i in n the
lower Delaware River and Delaware Bay Basins, N.J., water years

1976-93 .. cesses seve 33
Seasonal dependency at surface: water “quality stations i in nthe ‘Atlantic Coastal

Basins, N.J., water years 1976-93 o.....cecccsccseeseesesecseesesteseeseeeseeseentecseeesneeseaee 134
Seasonal dependency at surface-water-quality stations in the lower Delaware

River and Delaware Bay Basins, N.J., water years 1976-93 ........esssssssseseseees 135

Maximum, minimum, and spread of load-to-streamflow slopes for selected

constituents at surface-water-quality stations in the Atlantic

Coastal Basins, N.J., water years 1976-93 .......cecscscesssesseseessseseeseseseseteeee | 36
Maximum, minimum, and spread of load-to-streamflow slopes for selected

constituents at surface-water-quality stations in the lower

Delaware River and Delaware Bay Basins, N.J., water years 1976-93 ..........137
Maximum, minimum, and spread of load-to-streamflow slopes for selected

nutrients at surface-water-quality stations in the Atlantic Coastal Basins,

N.J., water years 1976-93
Maximum, minimum, and spread of load-to-streamflow slopes for selected

nutrients at surface-water-quality stations in the lower Delaware River

and Delaware Bay Basins, N.J., water years 1976-93 .....ccccsesseessessecseecseeses 139

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REFERENCES CITED—Continued

Price, C.V., and Schaefer, F.L., 1995, Estimated loads of selected constituents from permitted and
nonpermitted sources at selected surface-water-quality stations in the Musconetcong,
Rockaway, and Whippany River Basins, New Jersey, 1985-90: U.S. Geological Survey
Water Resources Investigations Report 95-4040, 28 p.

Rand, G.M., and S.R. Petrocelli, 1985, Fundamentals of Aquatic Toxicity: Methods and
Applications: Washington, D.C., Hemisphere Publishing Corporation, 666 p.

Reed, T.J., and Hunchak-Kariouk, Kathryn, 1995, Surface-water temperature statistics for streams
in New Jersey and vicinity, 1955-93: U.S. Geological Survey Open-File Report 95-196,
142 p.

Robinson, K.W., and Pak, Connie, 1993, New Jersey stream water quality: U.S. Geological
Survey Water-Supply Paper 2400, p. 395-402.

Rosensteel, B.A., and Strom, P.F., 1991, River phosphorus dynamics and reservoir eutrophication
potential: Water Resources Bulletin 27:6, p. 957-965.

Ruffner, J.A., and Bair, F.E., eds., 1977, The weather almanac (2d ed.): New York, Avon Books,
35 p.

SAS Institute Inc., 1990, SAS/GRAPH software reference, version 6 (1st ed.): Cary, N.C.,
v. 1, 794 p.

Sawyer, C.N., and McCarty, P.L., 1978, Chemistry for environmental engineering: New York,
McGraw-Hill, Inc., 532 p.

Schornick, J.C., Jr., and Fishel, D.K., 1980, Effects of storm runoff on water quality in the Mill
Creek drainage basin, Willingboro, New Jersey: U.S. Geological Survey Water-Resources
Investigations Report 80-98, 111 p.

Schornick, J.C., Jr., and Ram, N.M., 1978, Nitrification in four acidic streams in southern New
Jersey: U.S. Geological Survey Water-Resources Investigations Report 77-121, 51 p.

Skougstad, M.W., Fishman, M.J., Friedman, L.C., Erdmann, D.E., and Duncan, S.S., 1979,
Methods for determination of inorganic substances in water and fluvial sediments:
U.S. Geological Survey Techniques of Water-Resources Investigations, book 5, chap. Al,
626 p.

U.S. Geological Survey, 1984, National Water Summary 1984: U.S. Geological Survey Water-
Supply Paper 2275, 467 p.

Vowinkel, E.F., and Foster, W.K., 1981, Hydrologic conditions in the Coastal Plain of New
Jersey: U.S. Geological Survey Open-File Report 81-405, 39 p.

145


Table 7a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01409387, Mullica River at outlet of Atsion Lake, at Atsion, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;
C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; 1g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction, NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression  Low- High-
Constituent Median Median slope of slope of flow flow
concentration concentration concentration load to trend trend
to streamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, 1 (27) 1 (74) -0.999 0 NA NA
Hardness, mg/L as CaCO, 7 (27) 7 7) 0 * 995 NA NA
Total organic carbon, mg/L as C 78 (27) 74 (96) 0 * 1.120 0 NA
Suspended sediment, mg/L 3 (dy 3 (21) 0 945 NA NA
Dissolved solids, mg/L 31 (27) 32 (93) .097 1.097 NA NA
Dissolved sodium, mg/L as Na 3 (27) 3 (96) 078 * 1.078 0 NA
Dissolved chloride, mg/L as Cl 6 (27) 5 (98) .089 1,089 NA NA
Dissolved oxygen, mg/L 83 (27) 9.1 (7) 075 * 1.074 0 NA
Fraction of dissolved oxygen at 87 (25) 93 (93) 0 ND 0 NA
saturation, %
Total phosphorus, mg/L as P 03 (26) 03 (69) 0 861 NA NA
Total nitrogen, mg/L as N 7 (26) 6 (85) 0 927 0 NA
Total nitrate plus nitrite, mg/L as N 21 (26) 14 (86) 0 * 1.134 0 NA
Total nitrite, mg/L as N .004 (26) 006 (82) 0 * 876 NA NA
Total ammonia plus organic nitrogen, 51 (26) 52 (95) 0 928 0 NA
mg/L asN
‘Total ammonia, mg/L as N .04 = (26) 06 (87) 0 * 855 0 NA
Total boron, pg/L as B 5 ©) 13 (5) sND 1.484 NA NA
Total lead, g/L as Pb 4 (0) 6 (19) 0 1.297 NA NA
Fecal coliform bacteria, MPN/100 ml 8 (24) 9 (94) 0 ND 0 NA

Table 7b. 1993 AMNET impairment status in the vicinity of water-quality station 01409387, Mullica River at outlet of Atsion Lake, at Atsion,
NJ.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-siation location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station AN0562 None AN0564
Impairment status Non-impaired ND Moderately impaired

38


Figure 42.

43.

Table 1.

wn

ILLUSTRATIONS—Continued
Page

Trends in fecal coliform bacteria concentrations during (A) high- and (B) low-

flow conditions at surface-water-quality stations in the Atlantic Coastal

Basins, N.J., water years 1976-93... cesses sree 26
Trends in fecal coliform bacteria concentrations during | (A) high- and (B) low-

flow conditions at surface-water-quality stations in the lower Delaware

River and Delaware Bay Basins, N.J., water years 1976-93 ........ccssesssseeeeeeee 127

TABLES

Description of, years of record for, and mean annual fiow at, selected water-
quality stations in the Atlantic Coastal, lower Delaware River, and
Delaware Bay Basins, N.J...........

Selected constituents and reporting units

Estimated flow-duration values of mean daily discharge and data source for
surface-water-quality stations in the Atlantic Coastal, lower Delaware
River, and Delaware Bay Basins, N.J.. seeseees see 2d

Estimated detection limits for selected constituents measured i in n the ‘Atlantic
Coastal, lower Delaware River, and Delaware Bay Basins, N.J., water
years 1976-93... seseee seseseeeeretene 28

Water quality and AMNET impairment status at waters -quality stations

(a) Median concentrations, relations of concentration and load to
streamflow, and directions of concentration trends for selected water-
quality constituents (at indicated station), and (b) 1993 AMNET impairment
Status (in the vicinity of indicated station):

. 01408000, Manasquan River at Squankum, N.J.

. 01408500, Toms River near Toms River, N.J. ...

. 01409387, Mullica River at outlet of Atsion Lake, at Atsion, N.J

. 01409416, Hammonton Creek at Wescoatville, N.

9. 01409500, Batsto River at Batsto, N.J.. .

10. 01409815, West Branch Wading River at Maxwell, NJ.

11. 01410000, Oswego River at Harrisville, N.J...

12. 01410150, East Branch Bass River near New Gretna, NJ.

13. 01410784, Great Egg Harbor River near Sicklerville, N.J

14. 01411000, Great Egg Harbor River at Folsom, N.J...

15. 01411110, Great Egg Harbor River at Weymouth, N.

16. 01463620, Assunpink Creek near Clarksville, N.J.

17. 01464000, Assunpink Creek at Trenton, N.J...

18. 01464500, Crosswicks Creek at Extonville, N.

19. 01464515, Doctors Creek at Allentown, N.J...

20. 01465850, South Branch Rancocas Creek at Vincentown, N. J.

21. 01466500, McDonalds Branch in Lebanon State Forest, N.J..

22. 01467000, North Branch Rancocas Creek at Pemberton, N.J.........

23. 01467069, North Branch Pennsauken Creek near Moorestown, N.J.

eI



APPENDIX 12. Relations of constituent concentration and load to streamflow and trends in concentration with time
TOTAL NITRATE PLUS NITRITE
01465850 SOUTH BRANCH RANCOCAS CREEK AT VINCENTOWN, N.J
[NVALUES, number of values; LOG, base-10 logarithm; CONC, concentration in indicated units; INT, intercept; FLOW, streamflow
in cubic feet per second; NWYS, number of water years during which at least one measurement was made; a slope value of 0’
indicates that the slope is not significantly different from zero; ND, not determined; CaCO3, calcium carbonate; C, carbon;
N, nitrogen; P, phosphorus; Pb, lead; B, boron; Cl, chloride; Na, sodium; MOST PROBABLE NUMBER INDEX is per 100 milliliters]

RELATION OF CONCENTRATION TO STREAMFLOW

CONCENTRATION 1

GROWING SEASON NONGROWING SEASON
° UNCENSORED VALUE e
iv “LESS-THAN’ VALUE v
A (GREATER-THAN'VALUE Ay

RELATION: LOG(CONC) = SLOPE*LOG(FLOW) + INT
VALUES. NVALUES SLOPE _ INT.
ALL VALUES 95 0.17 -0.12
[SEASONAL RELATIONS DETERMINED;
THEY ARE DIFFERENT FROM ONE ANOTHER]
— — GROWING SEASON 65 -0.32 0.05
— = = — NONGROWING SEASON 30 0.23 0.13

CONCENTRATION.
IN MILLIGRAMS PER LITER AS N
ro)

T
°
1

' '
STREAMFLOW EXCEEDED
0.01 4 —t.

INDICATED PERCENTAGE OF TIME. 1 10 100 7,000
“* 75PERCENT = = = 25 PERCENT STREAMFLOW, IN CUBIC FEET PER SECOND

RELATION OF LOAD TO STREAMFLOW

1,000

LOAD

x UNCENSORED VALUE
v "LESS-THAN' VALUE

RELATION: LOG(LOAD) = SLOPE*LOG(FLOW) + INT
VALUES. NVALUES SLOPE _INT
ALL VALUES. 95 0.83 0.61

——— —— SMOOTHED RELATION BETWEEN LOAD AND FLOW
(SHOWN IF THERE ARE 10 OR MORE VALUES)

STREAMFLOW EXCEEDED
INDICATED PERCENTAGE OF TIME,
- = 75PERCENT = = = 25 PERCENT 1 '

LOAD, IN POUNDS PER DAY

L La
1 10 100 1,000
STREAMFLOW, IN CUBIC FEET PER SECOND

TRENDS IN LOW- AND HIGH-FLOW CONCENTRATIONS.

1.0-—— -
CONCENTRATION TTT
LOW FLOW HIGH FLOW
° UNCENSORED VALUE e 3% oat 6 d
Vv "LESS-THAN' VALUE ¥ < 7
A caReaTer-THAN'vALUE fay ° °
ga 3° oF Be
&2 o6t ° ee 4
TRENDS IN CONCENTRATION ay ° ou
VALUES __NVALUES NWYS SLOPE aS og
} _ 5
— — lowrow 36 18 0.02 22 ost % ge aD Ge eo
HIGH FLOW 15 8 ND 8s _ao o-.°8 6% °
3 Ca o 0
2 02, e 4
z ®

00 76 77 78 70 80 81 82 @S 84 BS 86 87 00 89 90 oT 82 03
WATER YEAR
Figure 7. Example page from Appendix 12 of graphs showing relation of concentration to streamflow, relation of load
to streamflow, and trends in low- and high-flow concentrations for total nitrate plus nitrite at a station on the South
Branch Rancocas Creek at Vincentown, New Jersey, for water years 1976-93. (Available on CD ROM)

32


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network stations in the Atlantic Coastal Basin, New Jersey.
11


PERCENTAGE OF TIME FLOW IS EXCEEDED
90 75 50 25 10
T TT T T

40,000 3 Estimated total median load
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reservoir at Boonton upstream
01380500 at

A
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% E ba = 100 pounds per day
a ry Y Increased relative
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importance from
point sources
100 itil "
10 100 1,000

INSTANTANEOUS STREAMFLOW,
IN CUBIC FEET PER SECOND

EXPLANATION
& Water-quality sample

Figure 3. Relation of instream load of total nitrogen to instantaneous streamflow
at water-quality stations in the Rockaway River Basin, New Jersey, 1985-91.


Figure 11.

12.

13.

14.

1S.

16.

18.

20.

ILLUSTRATIONS—Continued
Page

Trends in total hardness concentrations during (A) high- and (B) low-flow conditions,
and (C) relative slope of total hardness load to streamflow at surface-water-quality
stations in the lower Delaware River and Delaware Bay Basins, N.J., water
Years 1976-93 ooo. ecesceecseesssssssesessuessesseessesssceseesuecseeesneesnsesuecaneaseeneeseseeaesateneenseseee 79

Trends in total organic carbon concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of total organic carbon load to streamflow
at surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
years 1976-93.

Trends in total organic carbon concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of total organic carbon load to streamflow
at surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .. seeesseeseeseeseeseesnesssesseseesseesesesneeeeseess OO

Trends in suspended sediment concentrations 1s during (A) high- and ‘B) low- flow
conditions, and (C) relative slope of suspended sediment load to streamflow
at surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
OATS 1976-93 on. eeeecsecsscsseseeseestesessesesesseesesseceesuesessuesnesseeneseseessesaeeasaneenneeseeeaneeesnets 84

Trends in suspended sediment concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of suspended sediment load to streamflow
at surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93

Trends in dissolved solids concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of dissolved solids load to streamflow at
surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
years 1976-93

288

. Trends in dissolved solids concentrations during (A) high- and (B) low-flow

conditions, and (C) relative slope of dissolved solids load to streamflow at

surface-water-quality stations in the lower Delaware River and Delaware

Bay Basins, N.J., water years 1976-93 .......cecscsesesssseesecessestesesneeteseeeseeneneesneeeenee 89
Trends in dissolved sodium concentrations during (A) high- and (B) low-flow

conditions, and (C) relative slope of dissolved sodium load to streamflow at

surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
OATS 1976-93 oe cecceccececsseccesesseesesseesescssesacsseesesnceveceeeseeneeansaceneeecseeansneesueeeessnteceneee 92

. Trends in dissolved sodium concentrations during (A) high- and (B) low-flow

conditions, and (C) relative slope of dissolved sodium load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 ... seeseeneaveneenens seveeenee D3

Trends in dissolved chloride concentrations during (A) high- and ®) low-flow
conditions, and (C) relative slope of dissolved chloride load to streamflow at
surface-water-quality stations in the Atlantic Coastal Basins, N.J., water

years 1976-93. 194

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Table 24a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01467081, South Branch Pennsauken Creek at Cherry Hill, N.J.

{Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; jig/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY

Regression Regression — Low- High-

Constituent Median, Median slope of slope of flow flow
concentration concentration concentration load to trend trend

to streamflow streamflow direction _ direction
Alkalinity, mp/L as CaCO, 40 @ 39 73) -0,392 0.608 NA NA
Hardness, mg/L as CaCO, 86 (27) 85 (110) -164 0 * 836 + NA
Total organic carbon, mg/L as C 63 (25) 6.8 (105) 145 1.145 0 NA
Suspended sediment, mg/L 6 a) 14 (26) 802 1.797 NA NA
Dissolved solids, mg/L 202 (27) 205 (108) -168 * B32 0 NA
Dissolved sodium, mg/L as Na 24 (27) 24 (110) 336 * 664 C) NA
Dissolved chloride, mg/L as Cl 30 (27) 30° (110) -168 * 832 + NA
Dissolved oxygen, mg/L 63 (26) 63 (108) 214 * 1.213 0) NA
Fraction of dissolved oxygen at 68 (26) 67 ~— (107) 128 * ND ) NA
saturation, %
Total phosphorus, mg/L as P 44 (24) 65 (76) 0) 835 NA NA
Total nitrogen, mg/L as N 45 (27) 48 (95) -312 687 - NA
Total nitrate plus nitrite, mg/L as N 155 (27) 1.46 (100) =.242 758 0 NA
Total nitrite, mg/L as N 182 (26) 155. (79) ~166 * 234 NA NA
Total ammonia plus organic nitrogen, 199 (27) 330 (103) -309 691 0 NA
mg/L as N

Total ammonia, mg/L as N 143 (27) 2.20 97) -A42 558 0 NA
Total boron, ug/L as B 120 a 140 ag) -.644 355 NA NA
Total lead, pg/L as Pb 2 a 5 (22) 906 1,905 NA NA
Fecal coliform bacteria, MPN/100 ml 3300 (25) 3400 (106) 0 * ND 0 NA

Table 24b. 1993 AMNET impairment status in the vicinity of water-quality station 01467081, South Branch Pennsauken Creek at Cherry Hill,
NJ.

{AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station ANO183 None ‘ANOL84
Impairment status Severely impaired ND Severely impaired

61


1922-93 is estimated to be 171 ft?/s at the surface-water gaging station on the North Branch
Rancocas Creek at Pemberton (01467000) (Bauersfeld and others, 1994). One water-quality
station is located on each of the North and South Branches of Rancocas Creek (table 1). The one
water-quality station on McDonald’s Branch in Lebanon State Park is a hydrologic benchmark
station. The hydrology and water quality at this station are representative of that in undeveloped
areas in the New Jersey Pinelands. The period of record for water-quality-data collection for each
station is shown in figure 6.

Land use in the basin is about 50 percent forested. The remaining land use is agricultural,
urban and suburban (New Jersey Department of Environmental Protection and Energy, 1993).

Pennsauken Creek

Pennsauken Creck drains about 33 mi? of southwestern Burlington County and northern
Camden County. The main stem is 3 miles long; the North Branch is 10 miles long; and the South
Branch is 11 miles long. Tides influence stream levels along the entire main stem and for a few
miles along each of the two main branches of the river (New Jersey Department of Environmental
Protection and Energy, 1993). Mean annual flow for water years 1968-93 is estimated to be
18.7 ft°/s at the surface-water gaging station on the South Branch Pennsauken Creek at Cherry
Hill (01467081) (Bauersfeld and others, 1994). The North and South Branches of Pennsauken
Creek have one water-quality station each (table 1). Station 01467069 is on the North Branch of
Pennsauken Creek near Morristown. The period of record for water-quality-data collection for
each station is shown in figure 6.

Land use in the basin is mostly urban and suburban with some industrial areas mainly at
the mouth of Pennsauken Creek. The remainder of the land is farmland and forested land (New
Jersey Department of Environmental Protection and Energy, 1993).

Cooper River

The Cooper River is 16 miles long and covers an area of about 40 mi. It flows from
northwest Camden County to the Delaware River at Camden (New Jersey Department of
Environmental Protection and Energy, 1993). Mean annual flow for water years 1964-93 is
estimated to be 34.5 ft?/s at the surface-water gaging station on the Cooper River at Haddonfield
(01467150) (Bauersfeld and others, 1994). The only water-quality station on the river is at

Haddonfield (01467150) where the period of record for water-quality-data collection is water
years 1968-93 (fig. 6) (Bauersfeld and others, 1994).

Land use in the basin is primarily urban and suburban. There is intense development
along the main stem (New Jersey Department of Environmental Protection and Energy, 1993).

Big Timber Creek
Big Timber Creek drains an area of 63 mi. The South Branch of Timber Creek is

11 miles long; the North Branch is 10 miles long; and the main stem is less than 4 miles long
(New Jersey Department of Environmental Protection and Energy, 1993). There has never been a

16


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135


INTRODUCTION

The New Jersey Department of Environmental Protection (NJDEP) has initiated an
innovative watershed approach to water-quality management in order to attain State-mandated
goals for the quality of surface water (New Jersey Department of Environmental Protection,
1989). Water-quality will be assessed and management policies will be developed on the basis of
contributing factors, such as nonpoint source contributions, headwaters destruction, and habitat
degradation, within the watershed or basin. This approach requires evaluation of the effects of
point and nonpoint source contributions on the quality of surface water within a watershed. To
facilitate the assessment of surface-water quality, the State is divided into four regions on the
basis of watershed-management issues and hydrogeologic boundaries defined by the U.S.
Geological Survey (USGS) (fig. 1).

The USGS, in cooperation with the NJDEP, has developed a watershed-based method for
relating water quality to streamflow to assess the relative contributions of constant (point sources
and ground-water discharge) and intermittent (nonpoint sources and storm runoff) sources of
constituents to New Jersey streams in all four regions. The initial study was conducted by using a
watershed-based method for the region comprising the Hackensack, Passaic, Elizabeth, and
Rahway River Basins (Buxton and others, 1998). The other regions consist of (1) the Wallkill
River and upper Delaware River Basins; (2) the Raritan River Basin; and (3) the Atlantic Coastal,
lower Delaware River, and Delaware Bay Basins.

Pur) a

This report presents the results of analyses for 18 water-quality constituents in samples
collected at 28 surface-water-quality stations within the Atlantic Coastal, lower Delaware River,
and Delaware Bay Basins (referred to as the study area) during water years! 1976-93 (October 1,
1975, through September 30, 1993). Relations between each of the 18 constituents and
streamflow at the 28 stations over the period of record were determined by testing for trends in the
concentrations of constituents during low and high flows. Qualitative values of contributions
from constant (point sources and ground water) and intermittent (nonpoint storm runoff) sources
were estimated statistically by examining the relations between concentrations of constituents and
streamflow, and load and streamflow.

Results of analyses are presented in three ways—in tables for each station with median
concentrations, the regression slopes of concentration and load to streamflow, and the directions
of the trends in concentrations during low and high flows for all constituents; in schematics for
each constituent showing regional trends in concentration during low and high flows and the
slopes of load to streamflow; and in graphs for each constituent by station showing relations of
concentration to streamflow, load to streamflow, and trends of concentrations during low and high
flows.

1A water year is the 12-month period from October 1 through September 30 and is designated by the calendar
year in which it ends.


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133


The following evaluation by R.F. Weiss (R.J. Pickering, U.S. Geological Survey, written
commun., 1981) was used to calculate the dissolved oxygen at saturation:

100 T T T T

In DO,,, = A, +A, + +A, Ins55 + 44 Too 100 +s[B, +Boao5t B, (a) |. (2)
where

In = natural logarithm;

DOsaqr= dissolved oxygen at saturation;

A, =173.4292;

Ay = 249.6339;

Az = 143.3483;

Ag = 21.8492;

B, =0.033096;

By =0.014259;

B, =0.001700;

T = temperature, in degrees Kelvin; and
Ss = salinity, in grams per kilogram.

The concentration of total hardness, expressed as calcium carbonate in milligrams per liter
(mg/L as CaCO3), was calculated as follows:

Total hardness = 2.497 [Ca] + 4.118 [Mg], (3)

where
Ca is the dissolved calcium concentration, in milligrams per liter, and
Mg is the dissolved magnesium concentration, in milligrams per liter.

Some total organic carbon concentrations were calculated as the sum of the dissolved and
particulate organic carbon concentrations; all are expressed as carbon in milligrams per liter
(mg/L as C). The concentration of total nitrogen was calculated as the sum of the total nitrate plus
nitrite and total ammonia plus organic nitrogen concentrations; all are expressed as nitrogen in
milligrams per liter (mg/L as N).

Estimated loads were calculated for each of 16 constituents (no loads were calculated for
the fraction of dissolved oxygen at saturation or fecal coliform bacteria) by multiplying the
concentration by the instantaneous streamflow and applying unit conversions to yield an instream
load in pounds per day, as follows:

load (Ib/d) = concentration (mg/L) x streamflow (ft/s) x 2.20462 x 10° Ib/mg (4)
x 86,400 s/d x 28.316 L/ft,

When concentrations are in micrograms per liter, the conversion is

load (1b/d) = concentration (ug/L) x streamflow (ft/s) x 2.20462 x 10° Ib/ug (5)
x 86,400 s/d x 28.316 L/f?,

21


Relation of trends i . A iit

Trends in sodium concentrations during high flows are shown in figures 18a and 19a. A
positive trend at the one station on Raccoon Creek (47712) indicates an increase in the
contributions from storm runoff over time. Sodium concentrations during high flows show no
trends at the stations on the Toms (4085) and Cohansey (4128) Rivers, and the upstream station
on the Maurice River (4115). Trends in sodium concentrations during low flows are positive at
the stations on the Toms River (4085), West Branch Wading River (409815), Doctors Creek
(464515), North Branch of the Rancocas Creek (4670), Oldmans Creek (47751), and Salem River
(4825) (figs. 18b and 19b). Contributions from point sources and ground water increased over
time at these sites. Trends in sodium concentrations during low flows are negative at the
downstream stations on the Great Egg Harbor River (4110 and 41111), the station on the North
Branch of the Pennsauken Creek (467069), and the upstream station on the Maurice River (4115).
The contributions from point sources and ground water decreased over time at these sites.
Sodium concentrations during low flows show no trends at stations on the Mullica River
(409387), Hammonton Creek (409416), Batsto River (4095), Oswego River (4100), and East
Branch of the Bass River (41015), Crosswicks Creek (4645), McDonalds Branch (4665), South
Branches of the Rancocas (46585) and Pennsauken Creeks (467081), Raccoon Creek (47712),
and Cohansey River (4128).

Relation of load to streamflow

The range categories of regression slopes of dissolved sodium load to streamflow are
depicted in figures 18c and 19c. The slopes range from 0.609 at station 409416 on the
Hammonton Creek (table 8a) to 1.078 at station 41015 on the East Branch of the Bass River (table
12a). Slopes are in the high range at the stations on the Mullica (409387), Batsto (4095), and East
Branch of the Bass (41015) Rivers; the upstream station on the Assunpink Creek (46362); and the
stations on the Cooper River (46715) and Oldmans Creek (47751). At these stations, the
contributions to instream sodium loads from storm runoff are larger and less influenced by point
sources and (or) ground water than at other sites in the study area. Slopes are in the low range at
the one station on the Hammonton Creek (409416); the downstream station on the Assunpink
Creek (4640); and the stations on the Crosswicks Creek (4645), South Branch of the Pennsauken
Creek (467081), and Cohansey River (4128). At these stations, the contributions to instream
sodium loads from point sources and (or) ground water are larger and less influenced by storm
runoff than at other sites in the study area. Slopes at stations on the Assunpink Creek decrease in
the downstream direction, indicating a decrease in the relative influence of contributions from
storm runoff along the river.

Dissolved Chloride

Chloride is present in ali surface water, but usually in low (<10 mg/L) concentrations.
Chloride ions do not significantly enter into oxidation or reduction reactions, form no important
solute complexes with other ions unless the chloride concentration is extremely high, do not form
salts of low solubility, are not significantly adsorbed on mineral surfaces, and play few vital

90


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Table 21a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01466500, McDonalds Branch in Lebanon State Forest, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; j.g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
: ; Regression Regression —_Low- High-
consent concn ian coca RE
tostreamflow streamflow direction _ direction
Alkalinity, mg/L as CaCO, <l ©) <I (125) ND ND NA NA
Hardness, mg/L as CaCO, 3 (59) 3 (154) ASL * 1.150 0 NA
Total organic carbon, mg/L as C 3.7 Q) 48 (63) 696 1.696 NA NA
Suspended sediment, mg/L 3 (58) 2 (164) 0 * 1.131 0 )
Dissolved solids, mg/L 22 (59) 22 (148) 345 1.345 0 0
Dissolved sodium, mg/L as Na 2 (59) 2 (156) -073 * 927 0 NA
Dissolved chloride, mg/L as Cl 4 (58) 4 (154) 0 970 0 0
Dissolved oxygen, mg/L 3.4 (58) 3.6 (156) 342 * 1.342 0 0
Fraction of dissolved oxygen at 31 (57) 34 (152) 291 * ND 0 0
saturation, %
Total phosphorus, mg/L as P 01 (60) Ol (150) 0 1.100 0 0
Total nitrogen, mg/L as N 3 (60) 3 (126) 387 1.387 NA NA
Total nitrate plus nitrite, mg/L as N <.06 (60) 02 (148) 0 * 859 0 ft)
Total nitrite, mg/L as N <.01 (60) <01 (89) ND ND NA NA
Total ammonia plus organic nitrogen, 19 (60) 20 (132) 752 1,752 NA NA
mg/L as N
Total ammonia, mg/L as N 02 (51) 02 (103) 0 856 NA NA
Total boron, jig/L as B ND Oy ND (0) ND ND NA NA
Total lead, g/L as Pb ND (0) 4 (il) = ND 1.194 NA NA
Fecal coliform bacteria, MPN/100 ml ND (0) ND (0) ND ND NA NA

Table 21b. 1993 AMNET impairment status in the vicinity of water-quality station 01466500, McDonalds Branch in Lebanon State Forest N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station None ANO146 None
Impairment status ND Moderately impaired ND

57


constituents. During high flows, the trend is negative for TN, NO2, and TAON, indicating a
decrease in the contributions of these constituents from storm runoff over time. Also during high
flow, trends are insignificant for DO, FDO, NO32, NH4, and BACT. Insufficient data are
available to determine trends during high flows for all other constituents. The AMNET
impairment status is severely impaired at and upstream from station 01467150 (table 25b).

South Branch Big Timber Creel

For the one station on the South Branch Big Timber Creek, station 01467329 at
Blackwood Terrace, the 5-year and period-of-record medians are similar (table 26a). The
regression slopes of concentration to streamflow for HARD, TOC, DS, NA, CL, DO, FDO, TP,
TN, NO32, NO2, NH4, and BACT show seasonal dependency. The regression slope of load to
streamflow is in the high range for ALK, indicating a larger contribution from storm runoff
relative to that at other sites in the study area. The load slope is in the low range for DO.
Insufficient data are available for all constituents to determine trends during low and high flows.
The AMNET impairment status is moderately impaired downstream from station 01467329 (table
26b).

Raccoon Creek

For the one station on the Raccoon Creek, station 01477120 near Swedesboro, the 5-year
and period-of-record medians are similar (table 27a). The period-of-record medians for TOC and
PB are the smallest at station 01477120 for these constituents at all stations in the study area. The
regression slopes of concentration to streamflow for ALK, HARD, TOC, DS, DO, TP, NO32,
NO2, TAON, and BACT show seasonal dependency. The regression slope of load to streamflow
is in the high range for TN, indicating a larger contribution from storm runoff relative to that at
other sites in the study area. The load slopes are in the low range for HARD and DS, indicating
smaller contributions of these constituents from storm runoff relative to that at other sites in the
study area. During low flows, the trend is positive for CL, indicating an increase in the
contributions of these constituents from point sources and ground water over time; trends are
negative for TOC and FDO, indicating a decrease in the contributions of these constituents from
point sources and ground water over time. Trends are insignificant for HARD, NA, DO, TP, TN,
NO32, TAON, NH4, and BACT during low flows. Insufficient data are available to determine
trends during low flows for all other constituents. During high flows, trends are positive for DS,
NA, and CL, indicating an increase in the contributions of these constituents from storm runoff
over time. Trends are insignificant for HARD, TOC, DO, FDO, TN, NO32, TAON, and BACT
during high flows. Insufficient data are available for all other constituents to determine trends
during high flows. The AMNET impairment status is moderately impaired at and upstream and
downstream from station 01477120 (table 27b).

Oldmans Creek

For the one station on the Oldmans Creek, station 01477510 at Porches Mill, the 5-year
and period-of-record medians are similar for all constituents (table 28a). The regression slopes of
concentration to streamflow for ALK, TOC, NA, DO, TP, TN, NO32, NO2, TAON, and BACT

63


Table 1. Description of, years of record for, and mean annual flow at, selected water-quality stations in the
Atlantic Coastal, lower Delaware River, and Delaware Bay Basins, N.J.

IND, no data for site; mi?, square miles; ft*/s, cubic feet per second]

Daily
streamflow Mean annual flow
Station Latitude/ Drainage record in f/s
number Station name longitude area in mi? (water years) (period of record)
ic Coastal Basi
01408000 Manasquan River at Squankum 400947/740921 44.0 1932-93 74.7
201408500 Toms River near Toms River 395910/741329 123 1929-93 212
101409387 Mullica River at Outlet of Atsion Lake, at Atsion 394425/744337 26.7 ND ND
101409416 Hammonton Creek at Westcoatville 393802/744305 9.6 ND ND
01409500 Batsto River at Batsto 393833/743900 67.8 1928-93 122
201409815 West Branch Wading River at Maxwell 394030/743228 85.9 ND ND
01410000 Oswego River at Harrisville 393947/743126 = 72.5 1931-93 86.5
01410150 East Branch Bass River near New Gretna 393723/742630 8.1 1978-93 15.3
101410784 Great Egg Harbor River near Sicklerville 394402/745705 15.1 ND ND
01411000 Great Egg Harbor River at Folsom 393542/745106 57.1 1925-93 85.8
101411110 Great Egg Harbor River at Weymouth 393050/744647 154 ND ND
Delaware River Basin
01463620 Assunpink Creek near Clarksville 401611/744020 34.3 1973-93 52.3
01464000 Assunpink Creek at Trenton 401327/744458 90.6 1924-93 131
01464500 Crosswicks Creek at Extonville 400815/743602 81.5 1940-93 134
191464515 Doctors Creek at Allentown 401037/743557 17.4 ND ND
191465850 South Branch Rancocas Creek at Vincetown 395622/744550 64.5 ND ND
01466500 McDonalds Branch in Lebanon State Forest 395305/743020 24 1954-93 2.2
01467000 North Branch Rancocas Creek at Pemberton 395810/744105 118 1922-93 171
101467069 North Branch Pennsauken Creek near Moorestown 395707/745810 12.8 ND ND
01467081 South Branch Pennsauken Creek at Cherry Hill 395630/750005 8.9 1968-93 18.7
01467150 Cooper River at Haddonfield 395411/750119 17.0 1964-93 34.5
101467329 South Branch Big Timber Creek at Blackwood 394805/750427 19.1 ND ND
Terrace
01477120 Raccoon Creek near Swedesboro 394428/751533 26.9 1966-93 40.3
101477510 Oldmans Creek at Porches Mill 394157/752001 21.0 ND ND
101482500 Salem River at Woodstown 393836/751952 14.6 ND ND
Delaware Bay Basin
?01411500 Maurice River at Norma 392942/750438 112 1933-93 165
01411800 Maurice River near Millville 392652/750422 191 1992-93 242
101412800 Cohansey River at Seeley 392821/751521 28.0 ND ND

' Water-quality station only
? NASQAN (National Stream Quality Accounting Network) station


biochemical roles (Hem, 1985). Conservative constituents such as chloride move through a
stream system mainly by physical processes (water inputs and withdrawals). Chloride is present
in various rock types in concentrations lower than that of any of the other major constituents of
ambient water. In most streams, chloride concentrations are smaller than those of sulfate or
bicarbonate. Exceptions occur where streams receive inflows of ground water or industrial
wastewater containing large concentrations of chloride, or are affected by oceanic tides. Chloride
salts used for deicing highways can be carried to surface water by storm runoff and melting snow.

ati f i tratin ition:

The trends in chloride concentrations during high flows are positive at the stations on the
Toms River (4085) and Raccoon Creek (47712), indicating an increase in the contribution from
storm runoff over time at these sites (figs. 20a and 21a). Chloride concentrations during high
flows show no trends at the stations on the McDonalds Branch (4665) and Cohansey River (4128)
and the upstream station on the Maurice River (4115). The trends in chloride concentrations
during low flows are positive at the stations on the Toms River (4085), West Branch of the
Wading River (409815), Crosswicks Creek (46450), South (46585) and North (4670) Branches of
the Rancocas Creek, South Branch of the Pennsauken Creek (467081), Raccoon Creek (47712),
and Salem River (4825); and the upstream station on the Maurice River (4115) (figs. 20b and
21b). Contributions from point sources and ground water increase over time at these sites.
Trends in chloride concentrations during low flows are negative at the downstream stations on the
Great Egg Harbor River (4110 and 41111) and the one station on the Cohansey River (4128).
Contributions from constant sources (most likely ground water) decrease over time at these sites.
Chloride concentrations during low flows show no trend at the stations on Hammonton Creek
(409416), Batsto River (4095), East Branch of the Bass River (41015), Doctors Creek (464515),
McDonalds Branch (4665), North Branch of the Pennsauken Creek (467069), and Oldmans Creek
(47751).

ati to strea

The range categories of regression slopes of chloride load to streamflow are depicted in
figures 20c and 21c. The slopes range from 0.635 at the downstream station on the Assunpink
Creek (4640) (table 17a) to 1.128 at station 4095 on the Batsto River (table 9a). The slopes are in
the high range at the stations on the Mullica (409387) and Batsto (4095) Rivers, and East Branch
of the Bass River (41015). At these stations, the contributions to instream chloride loads from
storm runoff are larger and less influenced by constant sources (most likely ground water) than at
other sites in the study area. The slopes are in the low range at the downstream station on the
Assunpink Creek (4640) and the one station on the Cohansey River (4128). At these sites, the
contributions to instream chloride loads from point sources and (or) ground water are larger and
less influenced by storm runoff than at other sites in the study area. Slopes at stations on the
Assunpink Creek decrease in the downstream direction, indicating a decrease in the relative
influence of contributions from storm runoff along the river.

91


STATION NUMBERS

01408000

01408500

01409387

01409416

01409500

01409815

01410000

01410150

01410784

01411000

01411110

01411500

01411800

01412800

01463620 ;-

01464000

01464500

01464515

01465850

01466500

01467000

01467069

01467081

01467150

01467329

01477120

01477510

01482500

1976 1979 1982 1985 1988 1991 1994

WATER YEAR

Figure 6. Period of record (at least one measurement per year) of water-quality data
for selected stations in the Atlantic Coastal, lower Delaware River, and Delaware Bay
Basins, New Jersey, for water years 1976-93. (Station names are given in table 1.)

13


‘Table 10a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01409815, West Branch Wading River at Maxwell, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; g/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend diretcion; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression Low- High-
Constituent Median Median slope of slope of flow flow
concentration. concentration concentration load to trend trend
to streamflow streamflow direction —_ direction
Alkalinity, mg/L as CaCO, <l (30) <l (77) 0 0.764 NA NA
Hardness, mg/L as CaCO, 3 (30) 3 (116) 0 * 968 0 NA
Total organic carbon, mg/L as C ND (0) 6.6 (41) 0 904 NA NA
Suspended sediment, mg/L 7 (28) 8 (106) 0 * 962 NA NA
Dissolved solids, mg/L 23 (29) 25 (116) 092 * 1.092 0 NA
Dissolved sodium, mg/L as Na 2 (30) 2 (118) -046 0 * 954 + NA
Dissolved chloride, mg/L as Cl 4 (30) 4 (17) 0 S77 + NA
Dissolved oxygen, mg/L 8.8 (29) 89 = (115) 0 * -990 0 NA
Fraction of dissolved oxygen at 83 (28) 8 (114) -064 * ND 0 NA
saturation, %
‘Total phosphorus, mg/L as P 02 (30) 02 (116) -226 © 773 0 NA
Total nitrogen, mg/L as N 2 (18) 3 (60) 0 * 936 NA NA
Total nitrate plus nitrite, mg/L as N <.05 (18) 02 (63) 0 989 NA NA
Total nitrite, mg/L as N <05 (18) <.010 (21) ND ND NA NA
Total ammonia plus organic nitrogen, 20 (30) 30 (115) 0 * 993 0 NA
mg/L as N

Total ammonia, mg/L as N 03 (25) 02 (83) 344 654 NA NA
Total boron, g/L as B ND (0) <20 () ND ND NA NA
Total lead, pig/L as Pb ND (0) 6 (7) 0 963 NA NA
Fecal coliform bacteria, MPN/100 ml ND (0) 12 (9) ND ND NA NA

Table 10b. 1993 AMNET impairment status in the vicinity of water-quality station 01409815, West Branch Wading River at Maxwell, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station; at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station None AN0602 None
Impairment status ND Non-impaired ND

42


Relation of trends i : a iit

The trend in dissolved solids concentration during high flows is positive at the one station
on the Raccoon Creek (47712), indicating an increase in the contribution from storm runoff over
time at this station (figs. 16a and 17a). The trend in dissolved solids concentration during high
flows is negative at the upstream station on the Maurice River (4115), indicating a decrease in the
contribution from storm runoff over time at this station. Dissolved solids concentrations during
high flows show no trends at the stations on the Toms River (4085), McDonalds Branch (4665),
and Cohansey River (4128). Concentrations of dissolved solids during low flows show no trend
at the stations on the Toms River (4085), Hammonton Creek (409416), and Batsto (4095), West
Branch of the Wading (409815), Oswego (4100), and East Branch of the Bass (41015) Rivers; the
downstream station on the Great Egg Harbor River (41111); the stations on the Crosswicks (4645)
and Doctors (464515) Creeks, McDonalds Branch (4665), South (46585) and North (4670)
Branches of the Rancocas Creek, North (467069) and South (467081) Branches of the
Pennsauken Creek, Oldmans Creek (47751), and Salem (4825) and Cohansey (4128) Rivers; and
the upstream station on the Maurice River (4115) (figs. 16b and 17b).

ati f loa itreamfl

The range categories of regression slopes of dissolved solids load to streamflow are
depicted in figures 16c and 17c. The slopes range from 0.739 at the downstream station on the
Assunpink Creek (4640) (table 17a) to 1.345 at station 4665 on the McDonalds Branch (table
21a). Slopes are in the high range at the stations on the Batsto River (4095) and McDonalds
Branch (4665), indicating that the contributions to instream dissolved solids loads from storm
runoff are larger and less influenced by constant sources at these stations than at other sites in the
study area. Slopes are in the low range at the one station on the Hammonton Creek (409416); the
downstream station on the Assunpink Creek (4640); the stations on the Crosswicks (4645), South
Branch of the Pennsauken (467081), and Raccoon (47712) Creeks; and the station on the
Cohansey River (4128). At these sites, the contributions to instream dissolved solids loads from
constant sources are larger and less influenced by storm runoff than at other sites in the study area.
Slopes at stations on the Assunpink Creek decrease in the downstream direction, indicating a
decrease in the relative influence of contributions from storm runoff along the river.

Dissolved Sodium

Sodium is present in most surface water. The ratio of sodium to total cations is important
in agriculture and human pathology. Sodium tends to remain in solution, when dissolved from
rocks by weathering, and not form precipitates that can maintain low sodium concentrations.
Sodium is retained by adsorption on mineral surfaces, especially by minerals with high cation-
exchange capacities, such as clays. Cation exchange processes in freshwater systems tend to
extract divalent ions from solution and replace then with monovalent ions, especially sodium
(Hem, 1985). Sodium salts used for deicing highways can be carried to surface water with storm
runoff and melting snow. The reuse of water for irrigation commonly leaves a residual that is
much greater in sodium concentration than was the original water.

87


Table 3. Estimated flow-duration values of mean daily discharge and data source for surface-
water-quality stations in the Atlantic Coastal, lower Delaware River, and Delaware Bay Basins,
NJ.

[f°/s, cubic feet per second; %, percent, WATSTORE, National Water Data Storage and Retrieval
System; MOVE. 1, Maintenance of Variance Extension, Type 1; Drainage Area, adjusted on basis
of drainage area from nearby surface-water gages]

Flow duration values of mean daily discharge,

in fP/s
Station number 25% 75% Source

01408000 83.9 36.5 WATSTORE
01408500 261 131 WATSTORE
01409387 68.0 24.8 MOVE.1
01409416 26.2 9.1 MOVE.1
01409500 144 74.0 WATSTORE
01409815 177 70.3 Drainage Area
01410000 104 49.9 WATSTORE
01410150 18.9 10.2 WATSTORE
01410784 22.2 72 MOVE.1
01411000 106 50.6 WATSTORE
01411110 322 143 MOVE.1
01411500 211 96.2 WATSTORE
01411800 361 149 WATSTORE
01412800 38.0 22.5 WATSTORE
01463620 66.1 21.9 WATSTORE
01464000 155 51.6 WATSTORE
01464500 145 61.3 WATSTORE
01464515 38.3 9.8 MOVE.1
01465850 120 39.8 WATSTORE
01466500 2.7 14 WATSTORE
01467000 213 90.5 WATSTORE
01467069 46.9 8.9 MOVE.1
01467081 16.2 6.8 WATSTORE
01467150 33.4 174 WATSTORE
01467329 34.1 18.3 MOVE.1
01477120 44.0 20.3 WATSTORE
01477510 43.4 14.7 MOVE.1
01482500 19.9 72 WATSTORE

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Previous Studi

Water-quality studies have been conducted by the USGS, in cooperation with State and
local agencies, in New Jersey since the early 1960’s. Three more recent USGS studies report the
effects of nonpoint source contamination on New Jersey streams. Schornick and Fishel (1980)
reported the effect of storm runoff on the surface-water quality of the Mill Creek Basin in
Willingboro, Burlington County. Fusillo (1981) reported the effects of suburban residential
development on surface- and ground-water quality in the upper Great Egg Harbor River Basin in
Winslow Township, Camden County. Price and Schaefer (1995) reported estimated loads of
selected constituents in the Musconetcong, Rockaway, and Whippany River Basins in northern
New Jersey.

Several previous studies address surface-water issues in the river basins investigated in
this study. Anderson and George (1966) reported the results of a statewide reconnaissance study
of the water-quality characteristics of New Jersey streams. Anderson and McCarthy (1963)
described the chemical characteristics of streams in the Delaware River Basin. Hely and Olmsted
(1963) presented relations between streamflow characteristics and the environment in the
Delaware River region. Parker and others (1964) discussed the water resources of the Delaware
River Basin. Ivahnenko and Buxton (1994) discussed the presence of pesticides from agricultural
runoff in the Manasquan River, and Buxton and Dunne (1993) reported water-quality data for the
Shark River at Remsen Mill, New Jersey. Hickman (1992) presented water-quality data collected
from field reconnaissance surveys of selected estuaries in southern New Jersey, and Hickman
(1995) reported the statistical characteristics of stream discharge in tributaries of selected
estuaries in the Coastal Plain. Schornick and Ram (1978) discussed nitrification in four acidic
streams in southern New Jersey. Mansue (1972) reported the suspended-sediment yields of
streams in the Coastal Plain draining into the Delaware River estuary. Keighton (1965) studied
the water quality of the Delaware River from Bristol to Marcus Hook, Pennsylvania; Keighton
(1966) described the fresh-water discharge-salinity relations in the tidal Delaware River; and
Keighton (1969) reported water quality in the Delaware River estuary from Trenton, New Jersey,
to Reedy Island, Delaware, during the 1965-66 drought. Hochreiter (1982) reported on the
chemical quality of the water and surficial bed material in the Delaware River estuary and
adjacent New Jersey tributaries, and Hochreiter and Kozinski (1985) described the water quality
and bed material in streams in Logan Township, Gloucester County.

Several USGS studies were conducted to evaluate surface-water characteristics and water-
quality trends in New Jersey. Low-flow characteristics and flow durations of New Jersey streams
were reported by Gillespie and Schopp (1982). Hay and Campbell (1990) identified statewide
water-quality trends in New Jersey streams. Robinson and Pak (1993) summarized the water
quality of selected New Jersey streams for water years 1987-89. Statewide monthly statistical
summaries of surface-water temperatures during 1955-93 were presented by Reed and Hunchak-
Kariouk (1995). Buxton and others (1998) present relations of surface-water quality to
streamflow in the Hackensack, Passaic, Elizabeth, and Rahway River Basins for water years
1976-93.


‘able 18a. Median concentrations, relations of concentration and load to streamflow, and directions of concentration trends for selected water-
quality constituents at water-quality station 01464500, Crosswicks Creek at Extonville, N.J.

[Number in parenthesis is the number of available data values; WY, water years; mg/L, milligrams per liter; CaCO3, calcium carbonate;

C, carbon; Na, sodium; Cl, chloride; %, percent; P, phosphorus; N, nitrogen; jig/L, micrograms per liter; B, boron; Pb, lead; MPN/100 mL, most
probable number per 100 milliliters. Regression slopes and trend directions are zero when the slope is not different from zero at the 0.05
significance level; * indicates seasonal dependency (the slope and (or) intercept of growing (April through October) and non-growing (November
through March) season data were different at the 0.05 significance level); +, positive trend direction; -, negative trend direction; NA, insufficient
data for analysis; ND, undetermined value]

1989-93 WY 1976-93 WY
Regression Regression — Low- High-
Consent os
to streamflow streamflow direction —_ direction

Alkalinity, mg/L as CaCO; 19 27) 21 (75) 0391 * 0.609 NA NA
Hardness, mg/L as CaCO; 49 (26) 48 (110) -204 * .796 0 NA
Total organic carbon, mg/L as C 5.4 (26) 5.9 (108) 168 * 1.168 0 NA
Suspended sediment, mg/L 8 qd 11 (28) 1,198 2.196 NA NA
Dissolved solids, mg/L 102 (26) 102 (106) -.199 801 0 NA
Dissolved sodium, mg/L as Na 8 (27) 8 ql) -.298 -702 0 NA
Dissolved chloride, mg/L as Cl 16 27) 130 (I) 203 .797 + NA

Dissolved oxygen, mg/L 7.8 (21) 73 (108) 084 * 1.084 0 NA
Fraction of dissolved oxygen at 83 (on) 78 (108) 0) * ND 0 NA

saturation, %
Total phosphorus, mg/L as P 17 (21) 23 (106) 202 1.202 NA NA
Total nitrogen, mg/L as N 17 (27) 2.0 (101) -.170 -830 0 NA
Total nitrate plus nitrite, mg/L as N 85 (27) 1.00 (102) -3230* 677 0 NA
Total nitrite, mg/L as N 031 (27) 042 (80) -440 * 559 NA NA
Total ammonia plus organic nitrogen, 75 (2) 99 (109) 0 * 969 - NA
mg/L asN

Total ammonia, mg/L as N 18 (27) 30 (101) 0 * 986 0 NA
Total boron, g/L as B 30 () 40 (18) 0 0 NA NA
Total lead, g/L as Pb 1 (6) 2 (19) 1,942 2.942 NA NA
Fecal coliform bacteria, MPN/100 ml 330 (25) 240 (107) 687 * ND 0 NA

‘Table 18b. 1993 AMNET impairment status in the vicinity of water-quality station 01464500, Crosswicks Creek at Extonville, N.J.

[AMNET, Ambient Biomonitoring Network; WQ, water-quality. Upstream from WQ station is within 5 miles upstream from the WQ station, at
WQ-station location is within 0.5 mile upstream or downstream from the WQ station; downstream from WQ station is within 5 miles downstream
from the WQ station; ND, undetermined impairment status]

Upstream from WQ station At WQ-station location Downstream from WQ station
AMNET station None ANO125 ANO126
Impairment status ND Severely impaired Moderately impaired

53


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Relation of trends i . 4 iit

Concentrations of total nitrate plus nitrite show no trends during high flows at the one
station on the Toms River (4085); the downstream station on the Assunpink Creek (4640); the
stations on the Cooper River (46715), Raccoon Creek (47712), and Cohansey River (4128); and
the upstream station on the Maurice River (4115) (figs. 30a and 31a). The trend in total nitrate
plus nitrite concentrations during low flows is positive at the one station on the South Branch of
the Rancocas Creek (46585), indicating an increase in the contributions from point sources and
ground water over time at this site (figs. 30b and 31b). The trend in total nitrate plus nitrite
concentrations during low flows is negative at the upstream station on the Great Egg Harbor River
(410784) and the one station on the North Branch of the Pennsauken Creek (467069), indicating a
decrease in the contributions from point sources and (or) ground water over time at these sites.
Increased discharge from wastewater-treatment plants in which the organic nitrogen is almost
irely oxidized can result in increased nitrate plus nitrite concentrations in the receiving
streams. Concentrations of total nitrogen during low flows show no trends at the stations on the
Toms (4085) and Mullica (409387) Rivers, Hammonton Creek (409416), Batsto River (4095),
Oswego River (4100), and East Branch of the Bass River (41015); the downstream stations on the
Great Egg Harbor River (4110 and 41111); and all stations on the Crosswicks (4645) and Doctors
(464515) Creeks, McDonalds Branch (4665), North Branch of the Rancocas Creek (4670), South
Branch of the Pennsauken Creek (467081), Raccoon Creek (47712), Oldmans Creek (47751), and
Salem (4825), Cohansey (4128), and Maurice (4115 and 4118) Rivers.

Relation of load to st

The range categories of regression slopes of total nitrate plus nitrite load to streamflow are
depicted in figures 30c and 31c. The slopes range from 0.276 at the downstream station on the
Great Egg Harbor River (41111) (table 15a) to 2.171 at station 4825 on the Salem River (table
29a). The slope is in the high range only at the one station on the Salem River (4825) where the
contribution from storm runoff is larger and less influenced by constant sources than at other sites
in the study area. The slopes are in the low range at the one station on the Toms River (4085), all
stations on the Great Egg Harbor River (410784, 4110, and 41111), the downstream station on the
Assunpink Creek (4640), the one station on the Crosswicks Creek (4645), and the upstream
station on the Maurice River (4115). At these sites, the contributions from point sources and (or)
ground water are larger and less influenced by storm runoff than at other sites in the study area.
Slopes at stations on the Assunpink Creek decrease in the downstream direction, indicating a
decrease in the relative influence of contributions from storm runoff along the river, whereas
slopes at stations on the Maurice River increase in the downstream direction, indicating an
increase in the relative influence of contributions from storm runoff along the river.

Total Nitrite

Nitrite is an intermediate oxidation state of nitrogen, both in the oxidation of ammonia to
nitrate and in the reduction of nitrate. Nitrite species are unstable in aerated water and are
generally considered to be indicators of the presence of sewage or organic waste (low DO
conditions). Nitrite is the etiologic agent of methemoglobinemia.

108


Figure 21.

22.

23.

24.

25.

26.

27.

28.

29.

30.

31.

ILLUSTRATIONS—Continued
Page

Trends in dissolved chloride concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of dissolved chloride load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .. seseeeees seeeeeee DS

Trends in dissolved oxygen concentrations during (A) high- and @) low-flow
conditions, and (C) relative slope of dissolved oxygen load to streamflow at
surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
Years 1976-93 ooo ceccccccsecssessesssesssesssesssessuessucsssessuseseceaceaersessesuesneesneentssueeneesneess 98

Trends in dissolved oxygen concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of dissolved oxygen load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .. sesseeaee seseeseesee DD

Trends in fraction of dissolved oxygen at saturation during (A) high- ‘and
(B) low-flow conditions at surface water-quality stations in the Atlantic
Coastal Basins, N.J., water years 1976-93... sesseees seseseeeeeeee LOO

Trends in fraction of dissolved oxygen at saturation ‘during. (A) high- ‘and
(B) low-flow conditions at surface-water-quality stations in the lower
Delaware River and Delaware Bay Basins, N.J., water years 1976-93

Trends in total phosphorus concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of total phosphorus load to streamfiow at
surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
years 1976-93 sees

Trends in total phosphorus concentrations s during A ‘high- “and (B) low-flow
conditions, and (C) relative slope of total phosphorus load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware Bay
Basins, N.J., water years 1976-93... teense severeeseeree 103,

Trends in total nitrogen concentrations during (A) high- ‘and | (B) low-flow
conditions, and (C) relative slope of total nitrogen load to streamflow at
surface-water-quality stations in the Atlantic Coastal Basins, N.J., water
years 1976-93. soteeeee

Trends in total nitrogen concentrations during (A) high- and (B) low-flow
conditions, and (C) relative slope of total nitrogen load to streamflow at
surface-water-quality stations in the lower Delaware River and Delaware
Bay Basins, N.J., water years 1976-93 .. seeeesees secsseee LOT

Trends in total nitrate plus nitrite concentrations “during (A) ‘high and () low-
flow conditions, and (C) relative slope of nitrate plus nitrite load to
streamflow at surface-water- quality stations in the Atlantic Coastal Basins,

N.J., water years 1976-93 .. seeeeenes severe 110

Trends in total nitrate plus nitrite concentrations ns during (A) high- and (B) low-
flow conditions, and (C) relative slope of nitrate plus nitrite load to
streamflow at surface-water-quality stations in the lower Delaware River
and Delaware Bay Basins, N.J., water years 1976-93 ........csssessseeeeteneeeeeeeeee LIL

101

102

-106

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median concentrations, then tested to see whether it was significantly different from zero. For this
report, a trend is indicated if the value of tau was significantly different from zero at the 0.05
level. Seasonality was not included in the test.

A value of SLOPE is reported for constituent concentrations during either low or high
flows if a trend was indicated. The value of SLOPE is the median of the slopes of all pairs of
annual median concentrations. A SLOPE value of “0” is reported if sufficient data were available
for a trend test, but a trend was not indicated; a “not determined” value is reported if there were
insufficient data for a test. The units of SLOPE are units of concentration per year.

No value is reported for the intercept of the relation showing the trend of concentration
over time. An intercept value is calculated by the trend test only for the purpose of showing the
trend in a plot.

Multiple trend tests were conducted on data sets with censored values; the censored values
were set at their minimum and maximum possible values. Two tests were conducted on data sets
with less-than values but no greater-than values—one with the less-than values set to the
reporting limit and one with the less-than values set to zero. Two tests were conducted on data
sets with greater-than values but no less-than values—one with the greater-than values set to the
reporting limit and one with the greater-than values set to 107 (a value greater than all reported
uncensored values). Four tests were conducted on data sets with both less-than and greater-than
values—one with each of the permutations of the greater-than and less-than values discussed
above.

For each data set with censored values, the results are reported only for the trend relation
with the least significant value for tau. Because of the uncertainty of the censored data, a
significant trend slope is reported only if a slope is determined when the censored data are set
equal to both their minimum and maximum values.

RELATIONS OF SURFACE-WATER QUALITY TO STREAMFLOW

An understanding of the relation of surface-water quality to streamflow is important for
assessment of the relative contributions of point sources, ground water, and storm runoff to
instream loads. Point sources (permitted discharges) release constituents to a stream at a
relatively constant rate, independent of the receiving streamflow conditions. Ground-water
contributions to a stream are somewhat constant, although they vary slightly with season and
precipitation rate. Storm runoff contributions to a stream are intermittent, depending on storm
intensity and frequency, and occur only during high flows. Instream constituent concentrations
are a summation of the contributions from these constant (point source and ground water) and
intermittent (storm runoff) sources (Buxton and others, 1998).

To describe the relation of surface-water quality to streamflow, the data analyses are
presented in three ways. First, three aspects of the relation of surface-water quality to streamflow
(concentration to streamflow, load to streamflow, and trends in concentrations during low and
high flows) are presented graphically by constituent for each station in appendixes 1-18. Second,
the data analyses are presented by basin in the text; tables for each station list the median

30


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ati asi

Median concentrations, regression slopes of concentration and load to streamflow, and
directions of the trends in concentrations during low and high flows for each constituent are
presented in tables 5 through 32. Constituents that show seasonal dependency (the relations of
concentration to streamflow for the growing and nongrowing seasons are different) and the 1993
AMNET impairment status in the vicinity (at and within five miles upstream and downstream) of
the surface-water-quality station also are listed. Median concentrations were calculated for two
periods, the entire period of study (water years 1976-93) and the last five years of the period of
study (water years 1989-93) to provide a visual comparison of water quality to the AMNET
impairment status. In tables 5 through 32, the directions of trends in concentrations during low
and high flows are represented by +, -, 0, and NA symbols. Results of statistical tests are
discussed for each river basin. One- to four-letter abbreviations are used for each water-quality
constituent throughout the discussion. (See Conversions Factors and Abbreviated Water-Quality
Units, p. xii.)

Slopes of load to streamflow for each constituent are divided into three ranges in order to
describe the relative contributions of constant (point source and ground water) and intermittent
(storm runoff) sources to instream load. High-range slopes are greater than or equal to 75 percent
of the interval between the minimum and maximum slopes. For stations with slopes in the high
range, a larger contribution from storm runoff to instream load occurs than at other sites,
indicating an increased relative importance of nonpoint sources at these sites. Moderate-range
slopes are greater than 25 percent and less than 75 percent of the interval between the minimum
and maximum slopes. Low-range slopes are less than or equal to 25 percent of the interval
between the minimum and maximum slopes. For stations with slopes in the low range, a smaller
contribution from storm runoff to instream load occurs than at other sites, indicating an increased
relative importance of continuous sources at these sites. For constituents with large slopes of load
to streamflow (greater than 0.8), however, storm runoff is most likely the more significant
contributor to instream loads, even for stations with load slopes in the low range. Only load slopes
in the high and low ranges are discussed.

In 1992, the Bureau of Water Monitoring of the NJDEP reactivated the AMNET to
monitor benthic-macroinvertebrate populations at more than 700 stations in the major drainage
basins in New Jersey. The objective of this biomonitoring program is to provide long-term, basin-
wide, biological data for surface water (New Jersey Department of Environmental Protection,
1996a and 1996b). Stations will be monitored every 5 to 6 years, a realistic temporal lag between
the cessation and recovery of a biological community from a perturbation. Biomonitoring uses
instream populations of benthic macroinvertebrates as indicators of the quality of the surface
water. Species of the instream macroinvertebrate community occupy distinct niches based on
their tolerance to environmental conditions; these communities can change as environmental
conditions change. Benthic-community biological impairment is indicated by (1) the absence of
contaminant-sensitive macroinvertebrate taxa, (2) excessive dominance by certain taxon, (3) low
overall taxa richness, or (4) perceptible shifts in community structure relative to a reference
condition.

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