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II.B4. Nutrients
Non-point source inputs, such as atmospheric deposition, are increasing recognized as
important factors with regard to surface water quality. This is especially true for macronutrients
like nitrogen and phosphorus, which are linked to excess primary production in New Jersey’s
fresh and coastal waters. Atmospheric deposition of nitrogen and phosphorus has been shown to
be a significant contributor to the total loading of nutrients to aquatic ecosystems (Eisenreich et
al., 1977; Lindberg et al., 1986; Morales et al, 2001; Manny and Owens, 1983; Delumyea, R.G.
and Petel, R.L., 1977). Due to its nature as a limiting nutrient in biological systems, excess
phosphorus can lead to enhanced biological activity resulting in premature eutrophication that
can damage aquatic systems for in-stream uses such as power generation, navigation, and
recreation. Prior to the 1960s, most detergents contained phosphates that, when discharged to
surface waters, acted as fertilizers perpetuating the growth of undesirable species, such as algae
and excess amounts of aquatic plant life. Some detergents underwent tertiary wastewater
treatment processing prior to discharge into streams and other water bodies that allowed for some
degree of control of phosphate content. However, the same was not true for primary and
secondary-treated wastewater streams, agricultural run-off of phosphates, phosphorus from bird
droppings and insects (Ahn, 1999), and the contribution from atmospheric deposition.
Introduction of nitrogen and phosphorus into water bodies can lead to the enhanced
growth of primary producer species, like algae, which play an important role in the aquatic food
chain. Algae convert carbon dioxide into biomass that is used by small aquatic organisms (i.e.
phytoplankton) as a food source. Hydrophobic organic compounds (HOCs), like PCBs, can
enter the aquatic food chain by sorption to the algae, which can then be taken up by organisms
progressively higher up the food chain. HOCs can also enter the food chain by direct passive
sorption to phytoplankton, due to the organic-carbon rich nature of phytoplankton cells. The
bioconcentrated HOCs can become incorporated into higher-level fish that can be consumed by
humans. Therefore, the bioconcentration of HOCs in aquatic ecosystems is enhanced when
phosphorus additions drive excessive algae production and subsequently, excessive growth in
higher-level organisms (Kramer, et al., 1996).
Macronutrient wet deposition into the ocean and other major bodies of water can cause
excessive growth of phytoplankton leading to dangerous blooms that affect the hierarchy of
organisms in the ocean (Migon, 1999). These blooms can also pose a danger to humans, as the
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algae can poison filter-feeding organisms, and, when consumed by humans, lead to illness and
death. Considerable effort has gone into the abatement of point sources of nitrogen and
phosphorus; however controlling non-point source additions (i.e. via agricultural runoff,
weathering/soil erosion, atmospheric deposition, incineration and biomass burning (Migon,
1999)) of these nutrients is significantly more difficult. Here we present results regarding the
atmospheric deposition of nitrate and phosphorus in NJADN, which together with a
comprehensive analysis of streamflow, surface water concentrations, and other nutrient sources,
will be useful in modeling nutrient cycling in New Jersey’s surface waters and estimating
nutrient loads to impacted waterbodies.
Nitrate in New Jersey Precipitation
Nitrate concentrations in precipitation collected in New Brunswick, Jersey City, the
Pinelands, and Camden ranged from 1.3 to 130 M, but volume-weighted mean (VWM)
concentrations at all four sites ranged from 26 to 32 µM (Table 16). The lowest VWM NO3concentrations (19 – 20 M) were measured in the winter samples at the Pinelands and New
Brunswick and the highest (38 M) in Camden in the summer. All four sites showed higher
NO3- concentrations in the spring and summer than fall and winter. The average seasonal NO3concentrations in rain collected at the NJADN sites are similar to those measured at
Washington’s Crossing (12 to 34 µM), but generally higher than those measured at the Forsythe
Reserve in southern coastal NJ (10 to 17 µM) in 1999 as part of the NADP measurements
(NADP, 2001). This spatial trend in nitrate concentrations in precipitation likely reflects greater
NOx emissions in the areas surrounding the primarily urban/suburban NJADN sites than at the
relatively pristine, coastal Forsythe Reserve location.
The annual wet depositional flux of NO3- in the NJADN ranged from 27 to 35 mmol m-2
y-1 (Table 17) compared with 20 and 15 mmol m-2 y-1 at Washington’s Crossing and the Forsythe
Reserve, respectively. Since NO3- represents roughly half of the total dissolved nitrogen in rain,
the remainder being NH4+ and dissolved organic nitrogen, total N fluxes are approximately twice
these values. Precipitation NO3- fluxes at the NJADN sites are comparable to those (22 to 26
mmol m-2 y-1) measured in other Mid-Atlantic states (Pennsylvannia, Maryland, New York;
NADN).
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Phosphate in New Jersey Precipitation
Precipitation volumes varied significantly among sampling periods at the four NJADN
sites, as shown by Figure 30. The data display no inherent seasonality in the amount of
precipitation deposited at each site with the total volume of precipitation varying by as little as a
factor of three between seasons. On an annual basis, precipitation was similar for all four sites,
on the order of 1.0 m y-1.
Concentrations of total phosphorus in New Jersey precipitation for each individual
sample ranged from 2.0 to 92 g L-1 with both the lowest (July 2000) and highest (December
2000) concentrations measured at the New Brunswick site (Figure 31). The lowest volumeweighted mean concentration (Table 16) taken across all samples occurred at Jersey City (5.9 g
L-1). The volume-weighted mean concentrations over the other three sites (NB, PL, and CC)
were of a similar magnitude to each other (7.4 g L-1, 7.7 g L-1, and 7.5 g L-1, respectively).
The Jersey City site displayed the least amount of variability in total phosphorus
concentration with a relative standard deviation of 38%. The New Brunswick, Camden and
Pinelands sites show a larger degree of variability with higher relative standard deviations: New
Brunswick (168%), Camden (78%), and Pinelands (68%). The New Brunswick and Pinelands
sites are both expected to be influenced by the localized application of phosphorus-containing
fertilizers and the re-suspension of biogenic material (soil, plant debris) subject to previous
fertilizer application. The Pinelands site may also be subject to phosphorus input from
incineration of biomass due to controlled burns initiated in the area. The Camden site is situated
in the middle of an urban center and is, therefore, not expected to be influenced by the localized
use of fertilizers. This site is influenced more by industrially associated phosphorus loadings (i.e.
incineration). Three of the samples taken at this site (May 2000, January 2000, and May 2001)
had high total phosphorus concentration, but if their influence is removed, the relative standard
deviation for Camden is 41%, and on the same order of magnitude as the Jersey City site. This
may be an indication that urbanized areas such as Jersey City and Camden are experiencing
‘background’ signals of phosphorus relative to those measured in agricultural areas. This may
suggest that agricultural use of phosphorus is more important to loading in New Jersey than
industrial sources.
Taking an average of all of the four sites in a particular season, the highest VWM
concentrations occurred in the fall and spring, although they differ from the summer and winter
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3
New Brunswick
Annual Precipitation: 0.95m/year
2
1
0
3
Camden
1.1 m/year
Sample Volumes (L/sample)
2
1
0
3
Jersey City
0.88 m/year
2
1
0
3
Pinelands
1.0 m/year
2
1
Dec
2002 Jan
Oct
Nov
Sep
Aug
Jun
2001 Jul
Apr
May
Feb
Mar
Dec
2001 Jan
Oct
Nov
Sep
Aug
Jun
2000 Jul
Apr
May
Feb
Mar
Dec
2000 Jan
Oct
Nov
Sep
Aug
1999 Jul
0
Figure 30. Precipitation volumes for each sampling period (L sample-1). Note: width of
bar corresponds to dates over which sample was integrated.
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35
New Brunswick
28
55.9
VWM = 7.1 g/L
91.5
21
14
7
0
35
Camden
Total Phosphorus Concentration (ug/L)
28
VWM = 7.3 g/L
21
14
7
0
35
Liberty Science Center
28
VWM = 5.9 g/L
21
14
7
0
35
Pinelands
28
VWM = 7.6 g/L
21
14
7
Aug
Jun
2001 Jul
Apr
May
Feb
Mar
Dec
2001 Jan
Oct
Nov
Sep
Aug
2000 Jul
Jun
Apr
May
Feb
Mar
2000 Jan
Dec
Oct
Nov
Sep
Aug
1999 Jul
0
Figure 31. Concentrations of total phosphorus in precipitation (g L-1). Note: width of bar
corresponds to dates over which sample was integrated. Width of the bar corresponds to the dates
over which the sample was integrated.
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by 1.5 times (Figure 32). There is no consistent pattern for the highest and lowest seasonal
VWM concentration for any of the sites. For example, at some sites, the phosphorus
concentration is highest in fall (New Brunswick) and in other cases, it is lowest in fall (Camden).
For the individual sites, the seasonal VWM concentration varies minimally, between 4.1 ± 0.80
g L-1 and 15 ± 8.8 g L-1. This small variability suggests that the total amount of phosphorus
Total Phosphorus Volume Weighted Mean Concentration (ug/L)
loading due to wet deposition in New Jersey does not change on a spatial-scale.
25
New Brunswick
Camden
Jersey City
Pinelands
20
15
10
5
0
Summer
Fall
Winter
Spring
Figure 32. Seasonal volume-weighted mean concentrations of total phosphorus in New Jersey
precipitation (g L-1).
There are no consistent seasonal or spatial trends in total phosphorus wet-deposition, as
shown by Figure 33. The lowest wet-deposition flux occurred at the Jersey City site in fall (3.9
mg m-2 y-1). The highest occurred in the Pinelands site in the fall (14 mg m-2 y-1). There is no
statistically significant difference between the annual wet phosphorus deposition fluxes at the
four NJADN sites, as shown by Figure 34.
The data collected for New Jersey is compared to that of other studies in Table 2, which
shows that phosphorus concentrations and wet deposition fluxes in New Jersey are comparable
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to those measured elsewhere. Eisenreich et al. (1977) proposed that the dominant sources
affecting phosphorus deposition to Lake Michigan are derived from both urban/industrial
activities and agricultural sources, such as wind-blown soil and re-entrained dusts. The findings
of this study, when compared to the study of Lake Michigan, suggest that the industrial and
agricultural influences on total phosphorus loading are much greater in Michigan than in New
Jersey, by as much as a factor of four. The total phosphorus concentration in South Florida
reported by Ahn, et al (2001) is less than a factor of two higher than phosphorus concentrations
at Camden, New Brunswick, and Pinelands.
Total Phosphorus Deposition (mg/m2/year)
20
18
New Brunswick
Camden
Jersey City
Pinelands
16
14
12
10
8
6
4
2
0
Summer
Fall
Winter
Spring
Figure 33. Seasonal total phosphorus deposition flux by site (mg m-2 year-1).
Annual phosphorus wet deposition fluxes on the same order of magnitude as this study,
were reported in a recent paper by Herut et al (1999). This study sampled at two sites on the
Mediterranean coast of Israel and reported fluxes close to those in this study. The wet
depositional flux of phosphorus reported in South Florida is greater than that of Jersey City by
almost as much as an order of magnitude. This is in contrast to the similar deposition reported
from the study, suggesting many short precipitation events, rather than fewer, longer ones.
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12
Phosphorus Deposition (mg/m2/year)
10
8
6
4
2
0
NB
CC
LS
PL
Figure 34. Annual total phosphorus precipitation deposition fluxes (mg m-2 year-1).
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