for commercial and residential purposes, and incompatible agriculture
and forestry practices. The loss of periodic fire from the landscape
seems to be the most serious factor in its decline. Residential and
commercial development adjacent to populations can also pose a threat
since urbanization generally results in fire suppression.

SENSITIVE JOINT-VETCH

Aeschynomene virginica

Family: Fabaceae

Status: State – Threatened, Federal – Threatened

Source

  HYPERLINK "http://www.ncnhp.org/Images/107.pdf"
http://www.ncnhp.org/Images/107.pdf

Geographic Boundaries and Spatial Distribution

Sensitive joint-vetch is known from a total of 24 extant sites,
including one in Maryland, one in New Jersey, two in North Carolina, and
20 in Virginia. The species shows considerable annual fluctuation in
population numbers, varying in at least one case from approximately 50
to 2,000 individuals over a 3-year period. Although populations do
fluctuate, there is an apparent trend for large populations to remain
large and small populations to remain small. A total of 24 extant sites
are currently known to exist.

Historical Information

The Sensitive joint-vetch was first listed on May 20, 1992. It is
currently designated as Threatened in the entire range.  The historic
range for the species extended into Delaware and Pennsylvania, but the
species has not been seen in those States for more than a century.

Life History

Sensitive joint-vetch is an annual plant in the bean family native to
the eastern United States. Plants typically attain heights of 1 to 2
meters in a single growing season, although they can grow as tall as 2.4
meters. The stems are single, sometimes branching near the top, and with
stiff or bristly hairs. The leaves are even-pinnate, 2 to 12 centimeters
(cm) long, with entire, glad-dotted leaflets. Each leaf consists of 30
to 56 leaflets. Leaflets are 0.8 to 2.5 cm long and 0.2 to 0.4 cm wide.
The leaves fold slightly when touched. The yellow, irregular flowers are
1.0 to 1.5 cm across, streaked with red, and grow in racemes (elongated
inflorescence with stalked flowers). The fruit is a loment with 4 to 10
one-seeded segments, turning dark brown when ripe. Fruits are 3.0 to 7.0
cm long and shallowly scalloped along one side.

Plants flower from July through September and occasionally into October.
In Autumn, senescence may be triggered by the drop in water temperature
or by salinity intrusion due to a decrease in freshwater flow.
Bumblebees have been observed pollinating the flowers. Fruits form
shortly after the first signs of flowering in July. Although flowering
continues until late Fall, production of vigorous fruits appears to
decline significantly by mid-October. Seed maturation begins in August
and continues through October. Germination takes place from late May to
early June. Seedlings grow quickly, approximately doubling in size every
2 weeks during the first 6 weeks.

Habitat

Sensitive joint-vetch grows in the intertidal zone where plants are
flooded twice daily. The species seems to prefer the marsh edge at an
elevation near the upper limit of tidal fluctuation. It is usually found
in areas where plant diversity is high (50 species per acre) and annual
species predominate. Bare to sparsely vegetated substrates appear to be
a habitat feature of critical importance to this plant. As an annual, it
requires such microhabitats for establishment and growth. Such areas may
include accreting point bars that have not yet been colonized by
perennial species, low swales within extensive marshes, or areas where
muskrats have eaten most of the vegetation. In North Carolina, sensitive
joint-vetch appears to be a species that remains at a particular site
for a relatively short period of time, and maintains itself by
colonizing new, recently disturbed habitats where it may compete
successfully among other early-successional species. It is frequently
found in the estuarine meander zone of tidal rivers where sediments
transported from upriver settle out and extensive marshes are formed.
The substrate may be sandy, muddy, gravelly, or peaty.

Reasons for Current Status

The extirpation of sensitive joint-vetch from Delaware and Pennsylvania
and its elimination from many sites in other States can be directly
attributed to habitat destruction. Many of the marshes where it occurred
historically have been dredged and/or filled and the riverbanks
stabilized with bulkheads or riprap. Other threats include
sedimentation, competition from exotic plant species, recreational
activities, agricultural activities, mining, commercial and residential
development with associated pollution and sedimentation, impoundments,
water withdrawal projects and introduced insect pests. Sedimentation
inhibits seed germination, smothers seedlings, and promotes invasion of
competing weedy species. Herbicides, pesticides, and fertilizers from
golf courses, lawns, and gardens degrade water quality.

SWAMP PINK

Helonias bullata

Family: Liliaceae

Status: State – Threatened, Federal – Threatened

Geographic Boundaries and Spatial Distribution

New Jersey supports the largest and most numerous populations of the
species with 68 existing sites spread over 12 southern counties in the
Coastal Plain area. Most of the populations are located along the
Pinelands fringe in the Delaware River Drainage. Plant colonies are
found in the following counties: Atlantic; Burlington; Camden; Cape May;
Cumberland; Mercer; Gloucester; Middlesex; Monmouth; Morris; Ocean; and
Salem. New Jersey once supported 1OO populations; 32 of the State's
populations have been extirpated.

Besides New Jersey, six other States support populations including
Delaware; Maryland; Virginia; North Carolina; South Carolina, and
Georgia. One historic population was reported in Staten Island, New
York, near Kreislerville, but this population is believed extirpated.
Delaware's 1O existing sites are located in the Coastal Plain area of
all three counties (New Castle, Kent, and Sussex). One historic colony,
in the Piedmont, has been extirpated. In Maryland's Coastal Plain, six
plant populations are located on privately-owned lands in Anne Arundel,
Cecil, and Dorchester Counties. One other population has been
extirpated. Fifteen of the sixteen Virginia populations occur across a
1O-mile area on the western slopes of the central Blue Ridge Mountains.
The other existing population is found in the Coastal Plain. Ten of
Virginia's plant populations are located in the George Washington
National Forest, and one is on the Blue Ridge Parkway, which is owned by
the National Park Service. In North Carolina, the largest population is
found in the Pisgah National Forest in the "Pink Beds" area. Seven other
populations occur in Jackson, Henderson, and Transylvania Counties.
South Carolina and Georgia have one known population each. The South
Carolina population is located in Greenville County on South Carolina
Heritage Trust land. The privately owned, Georgia population is in Rabun
County, close to the North Carolina border.

Historical Information

The Swamp pink was first listed on September 09, 1988.  It is currently
designated as Threatened in the entire range. This species is known to
occur in: Delaware, Georgia, Maryland, North Carolina, New Jersey, New
York, South Carolina, and Virginia.

Life History

A perennial, the Swamp Pink usually is one of the first wildflowers to
bloom in the spring. The plant usually blooms from March to May. Its
fragrant flowers are pink and occur in a cluster of 3O to 5O. Its dark
evergreen, lance-shaped, and parallel-veined leaves form a basal rosette
which arises from a stout, hollow stem. This stem can grow from a height
of 2 to 9 decimeters during flowering, and to 1.5 meters during seed
maturation (U.S. Fish and Wildlife Service 199O). The plant's stout
rootstock has many fibrous rootlets. During the winter, the leaves often
turn reddish brown and will lie flat on, or slightly raised, from the
ground. These winter leaves are often hidden by leaf litter, but a
visible large button, in the center of the leaves, represents next
season's flower head. The plant produces three-lobed fruit of an
inverted heart shape. Each fruit has many ovules; each ovule opens into
six lobes that release linear shaped seeds with appendages on both ends.

Although the species can reproduce sexually, most of it's reproduction
is asexual by clonal root growth. This means plants tend to grow in
clumps, close to the parent plants, and that plant populations can be
extremely dense. Densities of up to 56 plants per square meter have been
found in southern Appalachia. Dense clusters of plants can also occur
when plants reproduce sexually because of limited seed dispersal.
Sometimes the seeds will fall out of the capsule and land beneath the
mother plant. Swamp pink seeds have appendages, and animals may
sometimes help disperse the seeds.

Habitat

Swamp Pink occurs in a variety of wetland habitats. These include
Atlantic white-cedar swamps; Blue Ridge swamps; swampy forested wetlands
that border small streams; meadows, and spring seepage areas. The plant
requires habitat that is saturated, but not flooded, with water. Swamp
Pink is commonly associated with evergreen trees such as Atlantic
white-cedar; pitch pine; American larch; and black spruce. The species
appears to be somewhat shade tolerant. In areas with less canopy cover,
deer are more likely to eat the plant's flowers, leaves, or shoots.

Reasons for Current Status

The loss of wetlands to urban and agricultural development and timbering
operations originally was the primary threat to the species. Now, State
wetland and Federal endangered species protection laws have slowed the
loss of wetlands, and the major threat to the Swamp Pink is habitat
degradation caused by off-site disturbances. Some of these impacts
include off-site water withdrawal for irrigation or crop production;
discharge from sewage treatment plants; increased siltation from the
inadequate control of soil erosion; and the introduction of excess
nutrients or chemicals into the water. Sometimes, excess nutrients will
cause an increase in natural succession, which allows the growth of
competing species such as common reed, red maple, red alder, and
mountain laurel. To alleviate the impacts of off-site disturbances,
buffer zones may be established around protected habitat. However, to be
effective in areas with difficult site topography or in overdeveloped
areas, buffer zones need to encircle over 500 feet of the area. In these
areas, smaller buffer zones tend to isolate the wetland. An isolated
wetland serves as a sink receiving all of the stormwater runoff and
pollution from the adjacent areas. The attractiveness of the Swamp Pink
makes it vulnerable to collecting by gardeners and commercial
collectors. To reduce collecting, which is illegal, people can obtain
plants cultivated from seed from some private nurseries. Even when the
plants are not collected, visitor trampling is a problem at some sites.
In the George Washington National Forest, a boardwalk has been
constructed to help save a population there.

Man-induced threats are not the only factors threatening the Swamp Pink.
It is also threatened by limited genetic variability due to its mostly
asexual reproduction, limited seed disperal and survival rates, a slow
rate of growth, and limited flowering potential. Only 0 to 6 percent of
the plants flower in any given North Carolina population. The flowering
rate is not much higher in the three Maryland populations with only 12
to 15 percent of the plants blooming in a given year.

SMALL WHORLED POGONIA

Isotria medeoloides

Family: Orchidaceae

Status: State – Threatened, Federal – Threatened

Sources

  HYPERLINK "http://www.ncnhp.org/Images/111.pdf"
http://www.ncnhp.org/Images/111.pdf

Geographic Boundaries and Spatial Distribution

This plant formerly occurred in 48 counties in 16 eastern states and
Canada, but when listed as endangered in 1982 it was known to exist in
only 16 counties in 1O states, and one county in Ontario, Canada. By
1991, a total of 86 sites in 15 states were known, and by 1993, there
was a known total of 104 sites in 15 states. Most populations are
centered in the foothills of the Appalachian Mountains in New England
and northern coastal Massachusetts The 23 populations in the Southeast
Region occur in North Carolina (5 populations); South Carolina (4
populations); Georgia (13 populations); and Tennessee (1 population).
Most Southeastern populations number less than 25 plants. South Carolina
has one population of over 25 plants, and Georgia has two populations
numbering about 100 plants. Small whorled pogonia is also known from
Virginia, Delaware, and New Jersey, Pennsylvania, Ohio, Michigan,
Illinois, and Ontario, Canada.

Historical Information

The Small whorled pogonia was first listed on September 09, 1982. It is
currently designated as Threatened in the entire range. This species is
known to occur in: Connecticut, District of Columbia, Delaware, Georgia,
Illinois, Massachusetts, Maryland, Maine, Michigan, Missouri, North
Carolina, New Hampshire, New Jersey, New York, Pennsylvania, Rhode
Island, South Carolina, Tennessee, Virginia, Vermont, West Virginia, and
Canada (Ont.).

This plant was reclassified from endangered to threatened because the
number of known populations increased from 34 in 1985 to 104 in 1993.
Also, the species' 1992 revised recovery plan stipulates that at least
25 percent of the plant's self-sustaining populations were protected
through public ownership or private landowner management agreement.
According to the October 6, 1994 Federal Register notice which
officially downlisted the species, a total of 46 small whorled pogonia
sites are currently protected rangewide, 24 of which have
self-sustaining populations. In the Southeast, North Carolina has two
protected sites, both of which are viable; South Carolina has four
protected sites, two of which are viable; and Georgia has seven
protected sites, four of which are viable.

Life History

Flowering occurs May-June. This plant may remain dormant underground for
several years. It is usually found in colonies. Indian cucumber root
(Medeola virginiana) often grows nearby. In the vegetative stage, the
two plants look very similar, thus the name medeoloides, means
“medeola like.” It may appear in any of four different states:
vegetative (nonreproductive), with an abortive flower, flowering, or
dormant. The flowering plant is tallest and has a wider whorl than the
other three with a vegetative plant being the smallest in size. Plants
that are large usually reproduce (flower) the next year unless some
event prevents them from storing adequate energy supplies. An individual
plant may retain a flower for 4-14 days. Dormancy may last from 1 to
10-20 years. Requires a symbiotic root/fungus association; seeds that
germinate become established only on substrate containing the suitable
mycorrhizal fungus.

Habitat

This species typically grows in open, dry deciduous woods and areas
along streams with acid soil. Also grows in rich, mesic woods in
association with white pine (Pinus strobus) and rhododendron
(Rhododendron spp.). Prefers leaf litter and decaying material but may
be found on dry, rocky, wooded slopes, moist slopes or slope bases near
vernal streams.

Reasons for Current Status

The current status of small whorled pogonia is attributed to loss of
habitat and excessive utilization for scientific and private
collections. However, some populations observed for a number of years
have also declined for unknown reasons.

Aquatic and Aquatic-dependent Species Selected for Biological Evaluation
 TC "2.3.1  Aquatic and Aquatic-dependent Species Selected for
Biological Evaluation" \f C \l "3"

The aquatic and aquatic-dependent species that are evaluated in this
document and the rationale for their selection is given in Table 2.2;
the listed species not selected and the rationale for their exclusion is
given in Table 2.3.

Table 2.2.  New Jersey Listed Species Included in Biological Evaluation

Species	Category	Rationale

Shortnose sturgeon  	Freshwater aquatic	Wholly aquatic species

Dwarf wedge mussel 	Freshwater aquatic	Wholly aquatic species

  SEQ CHAPTER \h \r 1 Bog turtle	Freshwater aquatic-dependent	Inhabit
fens, sphagnum bogs, and wet, grassy pastures

  SEQ CHAPTER \h \r 1 Indiana bat	Freshwater aquatic-dependent	  SEQ
CHAPTER \h \r 1 Females and juveniles forage on insects in the airspace
near the foliage of riparian and floodplain trees.

  SEQ CHAPTER \h \r 1 Bald eagle	Freshwater aquatic-dependent	  SEQ
CHAPTER \h \r 1 Fish are their primary diet.

  SEQ CHAPTER \h \r 1 Northeastern beach tiger beetle	Saltwater
aquatic-dependent	  SEQ CHAPTER \h \r 1 Forages in the damp sand of the
intertidal zone; prey species include lice, fleas, and flies.  Adults
also regularly scavenge dead crabs and fish.

  SEQ CHAPTER \h \r 1 Piping plover	Saltwater aquatic-dependent	  SEQ
CHAPTER \h \r 1 The piping plover forages on intertidal beaches, wash
over areas, exposed mudflats and sandflats, wracklines, and shorelines

  SEQ CHAPTER \h \r 1 Roseate tern	Saltwater aquatic-dependent	  SEQ
CHAPTER \h \r 1 This bird forages over shallow coastal waters, inlets,
and offshore seas.

  SEQ CHAPTER \h \r 1 Hawksbill sea turtle	Saltwater aquatic-dependent
SEQ CHAPTER \h \r 1 Frequents rocky areas, coral reefs, shallow coastal
areas, lagoons or oceanic islands, and narrow creeks and passes

  SEQ CHAPTER \h \r 1 Kemp's ridley sea turtle	Saltwater
aquatic-dependent	  SEQ CHAPTER \h \r 1 Can inhabit deep or shallow
estuaries depending on their preferred diet

  SEQ CHAPTER \h \r 1 Leatherback turtle	Saltwater aquatic-dependent
SEQ CHAPTER \h \r 1 Can inhabit deep or shallow estuaries depending on
their preferred diet

  SEQ CHAPTER \h \r 1 Loggerhead turtle	Saltwater aquatic-dependent
SEQ CHAPTER \h \r 1 may be found hundreds of miles out to sea, as well
as in inshore areas such as bays, lagoons, salt marshes, creeks, ship
channels, and the mouths of large rivers

Knieskern's beaked-rush	Aquatic plant	An obligate hydrophyte, it occurs
in groundwater-influenced, constantly fluctuating, successional
environments

Sensitive joint-vetch	Aquatic plant	Grows in the intertidal zone where
plants are flooded twice daily

Swamp pink	Aquatic plant	occurs in a variety of wetland habitats

Table 2.3.  New Jersey Listed Species Not Included in Biological
Evaluation

Species	Rationale

Fin whale, Humpback whale, Right whale	These species are largely pelagic
and are expected to have limited time within New Jersey’s offshore
jurisdictional range of three miles for water quality criteria.
Critical habitat for the right whale includes portions of Cape Cod Bay
and Stellwagen Bank, the Great South Channel (each off the coast of
Massachusetts), and waters adjacent to the coasts of Georgia and the
east coast of Florida where they feed on dense populations of copepods.
The near shore waters of New Jersey are apparently not a feeding area
for the right whale.

Eastern puma	Prey species include deer, elk, occasionally domestic
livestock, and any smaller mammals which opportunity makes available.
The preferred meat is deer.

Seabeach amaranth	Seabeach amaranth occurs on barrier island beaches,
where its primary habitat consists of overwash flats at accreting ends
of islands and lower foredunes and upper strands of noneroding beaches.

American chaffseed	It is generally found in habitats described as open,
moist pine flatwoods, fire-maintained savannas, ecotonal areas between
peaty wetlands and xeric sandy soils, and other open grass-sedge
systems.

Small whorled pogonia	This species typically grows in open, dry
deciduous woods and areas along streams with acid soil.

Environmental Baseline  TC "2.4 Environmental Baseline" \f C \l "2"

  SEQ CHAPTER \h \r 1 The quality of much of New Jersey’s surface
waters, where several threatened and endangered species live and forage
for food, has been lowered by multiple human activities, such as the
release of toxic contaminants, the loss and degradation of aquatic
habitats and their surrounding vegetation.  From a total 2,151 segments
of water bodies sampled, 973 (45%) had at least one chemical or physical
parameter exceeding a water quality standard criterion.  Note:
information on impaired sites presented in this section was taken from
the New Jersey 2004 Integrated Water Quality Monitoring and Assessment
Report (NJDEP 2004b).  In 1365 segments, the water quality standard was
not attained because the waterway was impaired or threatened for one or
more designated uses by a pollutant(s).  In most cases, impairment of a
water body segment resulted from multiple contaminants.  Lead and
dissolved solids were among the causes of impairment in only 43 and 5
segments, respectively.

Some water bodies were more polluted than others.  Out of a total 2870
nontidal river miles assessed (using 457 monitoring stations) for
multiple chemical and physical parameters, 2187 (76%) did not meet the
surface water quality standard for at least one factor.  Concentrations
of metals (arsenic, lead, mercury, copper, zinc, cadmium, chromium,
thallium, selenium, nickel) were monitored in 12% of nontidal river
miles.  Violation of one or more surface water quality standards
occurred in 72% of the monitored river miles.  Again, lead and dissolved
solids represented small percentages of all criteria violations.  In
tidal rivers, fewer chemical and physical parameters were measured.
Yet, 98% of all sampled river miles (1434.5 mi) were classified as
impaired.

In many water bodies, the evidence for pollution was indirect.  The
Division of Fish and Wildlife and the New Jersey Pinelands Commission
evaluated 108 lakes (14,547 acres) for aquatic life designated use
support.  Two designated uses of New Jersey lakes, reservoirs, and ponds
were considered in this assessment: recreation and aquatic life support.
 A total of 61 lakes fully supported their designated uses.  One lake
was fully supporting, but threatened its use, and 21 lakes did not
support the designated use.  Twenty six Pineland lakes could not be
assessed because clear thresholds for biological evaluation had not yet
been developed.  The quality of waters from estuaries and coasts were
assessed only for dissolved oxygen.  Over the 616 square miles of open
estuarine waters evaluated, ranging from Newark Bay to Cape May, 48% had
dissolved oxygen concentrations sufficiently high to support a healthy
biota and 52% had periodic drops to unacceptable levels of dissolved
oxygen.  In open ocean waters, from Sandy Hook to Cape May, samples
collected at the depth of 1 meter had adequate dissolved oxygen
concentrations to support a healthy community in all evaluated areas.
In contrast, concentrations of dissolved oxygen at the ocean floor were
inadequately low in all of the 454 square miles where meter deep samples
were taken.  The impact on aquatic organisms of temporary exposure to
dissolved oxygen concentrations below 5 mg/L is unclear.  Many benthic
invertebrates can tolerate hypoxia, and many fishes can avoid areas with
low concentrations of dissolved oxygen.

Our concern here is with potential adverse effects of lead and total
dissolved solids on listed species.  As a first assessment of such
risks, maps of the distributions of endangered species were overlain
with maps identifying the river miles or sites impaired by these
contaminants.  The occurrence of impaired waters within the distribution
range of a species suggests that it may be exposed to excessively high
concentrations of lead or total dissolved solids.  Conversely, no
overlap in locations of impaired sites or river miles and the geographic
range of an endangered species indicates that lead and dissolved solids
are not likely to adversely affect it.  The available data on locations
in New Jersey of sites impaired by these     HYPERLINK
"http://www.state.nj.us/dep/wmm/sgwqt/wat/integratedlist/docs/Part%20III
%20Chapter%202.pdf"  contaminants  (pg. 44 for total dissolved solids
and pg. 80 for lead) suggest no overlap with  distributions of the
shortnose sturgeon (    HYPERLINK
"http://www.nwrc.usgs.gov/wdb/pub/0123.pdf"  Acipenser brevirostrum ,
pg. 3), dwarf wedge mussel (    HYPERLINK
"http://www.fws.gov/northeast/nyfo/es/dwm.pdf"  Alasmidonta heterodon ,
pg. 8), Kemp’s Ridley sea turtle ( HYPERLINK
"http://www.nmfs.noaa.gov/pr/readingrm/Recoverplans/kempsrid.pdf"
Lepidochelys kempii , pg. 3-4), Leatherback turtle (    HYPERLINK
"http://www.cccturtle.org/leatherback.htm"  Dermochelys coriacea ),
Loggerhead turtle (    HYPERLINK
"http://www.cccturtle.org/loggerhead.htm"  Caretta caretta ), Piping
plover (    HYPERLINK
"http://www.state.nj.us/dep/fgw/ensp/pdf/02ppfedb.pdf"  Charadrius
melodus ,    HYPERLINK
"http://www.state.nj.us/dep/fgw/ensp/pdf/02ppfedb.pdf"    pg. 16), and
Roseate tern (    HYPERLINK
"elibrary.unm.edu/sora/JFO/v055n01/p0001-p0017.pdf"  Sterna dougallii ,
pg.7).  The bog turtle (  HYPERLINK
http://pick4.pick.uga.edu/mp/20q?search=Glyptemys+muhlenbergii&guide=Tur
tles Clemmys muhlenbergii ), the Indiana bat (  HYPERLINK
http://www.fws.gov/northeast/nyfo/es/ibatdraft99.pdf Myotis sodalis ,
pg. 3), the bald eagle (  HYPERLINK
http://www.nj.gov/dep/fgw/ensp/pdf/eglrpt05.pdf Haliaeetus leucocephalus
, pg. 5), and the pink swamp (  HYPERLINK
http://plants.usda.gov/java/county?state_name=New%20Jersey&statefips=34&
symbol=HEBU Helonias bullata ) on the other hand, may be exposed to
excessively high concentrations of lead and total dissolved solids.  The
beaked-rush Knieskern’s (  HYPERLINK
http://plants.usda.gov/java/county?state_name=New%20Jersey&statefips=34&
symbol=RHKN Rhynchospora knieskernii ) and the sensitive joint-vetch (
HYPERLINK
http://plants.usda.gov/java/county?state_name=New%20Jersey&statefips=34&
symbol=AEVI3 Aeschynomene virginica ) may be exposed to excessive
concentrations of lead, yet their current distributions do not overlap
with areas where concentrations of total dissolved solids exceed the
surface water quality standard.

3.0	ASSESSING EFFECTS OF THE NEW JERSEY CRITERIA ON FEDERALLY-LISTED
SPECIES  TC "3.0	ASSESSING EFFECTS OF THE NEW JERSEY CRITERIA ON
FEDERALLY-LISTED SPECIES" \f C \l "1"

3.1  Overview  TC \l2 "3.1  Overview

See Section 3.1 of the Methods Manual.

3.2  Data Collection  TC \l2 "3.2  Data Collection

Lead

The acute and chronic lead toxicity data used in this biological
evaluation were collected from a literature search of EPA’s ECOTOX
database, EPA’s Ambient Aquatic Life Water Quality Criteria for Lead
(U.S. EPA 1984), EPA’s draft Ambient Aquatic Life Water Quality
Criteria for Lead (GLEC 1998), and Jarvinen and Ankley (1999).  To
ensure completeness and broad applicability of this biological
evaluation, data for non-North American species were included.

Total Dissolved Solids

TDS is not a searchable parameter on EPA’s ECOTOX database.
Therefore, general on-line searches were conducted to identify and
obtain information on the toxicity of TDS to freshwater organisms.
Several reviews on TDS toxicity of were obtained and used to identify
additional references.  EPA has not prepared an ambient water quality
criteria document for TDS, but there is an AWQC document for chloride
(U.S. EPA 1988), which was reviewed for acute and chronic toxicity of
chloride.

  SEQ CHAPTER \h \r 1 3.3  Toxic Effects on Aquatic Species  TC "3.3
Toxic Effects on Aquatic Species" \f C \l "2"

This section presents the results of the toxic effects assessment,
including the supporting data and analyses on Federally-listed aquatic
species, their surrogates, and their food items.  The overall process
for assessing aquatic toxicity of lead is described in detail in the
Methods Manual, Section 3.3.

 ≈ Mg2+ > Cl- > SO4-; Na+ and Ca2+ were not significant variables in
the regression equation.

Similar to the approach given in the Methods Manual, the general
approach used to evaluate the New Jersey TDS criteria was to evaluate
the available acute and chronic toxicity data and make a conservative
estimate as to potential effects to the listed freshwater aquatic
species.

3.3.1  Aquatic Animals  tc "3.3.1  Aquatic Animals " \l 3

This section consists of the assessment results for water-column only
toxicity to aquatic animals.  The process for assessing the effects of
lead from water only exposure is described in Section 3.3.1 of the
Methods Manual.  Aquatic data for the assessment of lead are presented
in Table 3.1 as values for a given species.  These data are then used to
derive the mean and 5th percentile values for specific taxa in Table
3.2.  Several aspects of the assessment are worth noting here: (1) the
no-observed effect concentrations (NOECs) in Table 4.1 are from either
(a) chronic tests where lead in the exposure medium was measured, or (b)
are derived from acute tests through acute-to-chronic ratios for lead,
and (2) taxa in Table 3.2 are given a 5th percentile value only where
there are four or more data points for the taxon, where an Interspecies
Correlation Estimate (ICE) is available (see Appendix) for the taxon,
and/or where a 5th percentile value was derived via an alternative
approach for the taxon.

Aquatic toxicity data used toward the assessment of TDS are given in
Table 3.3.  Where more than one value was available for a species tested
with a specific component of TDS (i.e., a particular ion or a synthetic
effluent), a geometric mean was calculated.

μg/L.

Phylum	Class	Order	Family	Genus	Species	Common Name	LC50	Meas NOEC	Est
NOEC

Annelida	Clitellata	Lumbriculida	Lumbriculidae	Lumbriculus	variegatus
Oligochaete, worm	3190

228

Arthropoda	Branchiopoda	Cladocera	Moinidae	Moina	macrocopa	Water flea
546

39

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Ceriodaphnia	dubia	Water
flea	55	44

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Ceriodaphnia	reticulata
Water flea	1358

97

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Daphnia	magna	Water flea
1148	41

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Daphnia	pulex	Water flea
2311

165

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Simocephalus	vetulus
Water flea	3254

232

Arthropoda	Insecta	Diptera	Chironomidae	Chironomus	tentans	Midge	1280

91

Arthropoda	Insecta	Diptera	Chironomidae	Tanytarsus	dissimilis	Midge
161952

11568

Arthropoda	Insecta	Hemiptera	Belostomatidae	Lethocerus	sp.	Midge	983

70

Arthropoda	Malacostraca	Amphipoda	Crangonyctidae	Crangonyx
pseudogracilis	Amphipod	19955

1425

Arthropoda	Malacostraca	Amphipoda	Gammaridae	Gammarus	pseudolimnaeus
Scud	95

7

Arthropoda	Malacostraca	Amphipoda	Hyalellidae	Hyalella	azteca	Scud	18

1

Arthropoda	Malacostraca	Decapoda	Cambaridae	Orconectes	limosus	Crayfish
2386

170

Arthropoda	Malacostraca	Decapoda	Cambaridae	Procambarus	clarkii	Red
swamp crayfish	396418

28316

Chordata	Actinopterygii	Cypriniformes	Catostomidae	Xyrauchen	texanus
Razorback sucker	122910

8779

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Carassius	auratus
Goldfish	22775

1627

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Cyprinus	carpio	Common
caro	912

65

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Danio	rerio	Zebra danio
342782

24484

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Gila	elegans	Bonytail
122910

8779

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Pimephales	promelas
Fathead minnow	1709	238

	Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Ptychocheilus	lucius
Colorado squawfish	122910

8779

Chordata	Actinopterygii	Cyprinodontiformes	Poeciliidae	Gambusia	affinis
Western mosquitofish	173520

12394

Chordata	Actinopterygii	Cyprinodontiformes	Poeciliidae	Poecilia
reticulata	Guppy	14894

1064

Chordata	Actinopterygii	Perciformes	Centrarchidae	Lepomis	macrochirus
Bluegill	74155

5297

Chordata	Actinopterygii	Perciformes	Centrarchidae	Micropterus	dolomieui
Smallmouth bass	8654	293

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus	kisutch
Coho salmon,silver salmon	8352

597

Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus	mykiss
Rainbow trout,donaldson trout	16098	21

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Salvelinus	fontinalis
Brook trout	2964	60

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Thymallus	arcticus
Arctic grayling	2155

154

Chordata	Actinopterygii	Siluriformes	Heteropneustida	Heteropneustes
fossilis	Indian catfish	75915

5423

Chordata	Amphibia	Anura	Ranidae	Rana	catesbeiana	Bullfrog

565

	Ciliophora	Ciliatea	Heterotrichida	Spirostomidae	Spirostomum	ambiguum
Protozoa	1930

138

Ciliophora	Ciliatea	Heterotrichida	Spirostomidae	Spirostomum	teres
Ciliated protozoa	7794

557

Mollusca	Bivalvia	Veneroida	Corbiculidae	Corbicula	manilensis	Asiatic
clam	739795

52843

Mollusca	Bivalvia	Veneroida	Dreissenidae	Dreissena	polymorpha	Zebra
mussel

313

	Mollusca	Gastropoda	Architaenioglos	Viviparidae	Filopaludina	sp.	Snail
137980

9856

Mollusca	Gastropoda	Architaenioglos	Viviparidae	Viviparus	bengalensis
Snail	1836

131

Mollusca	Gastropoda	Basommatophora	Lymnaeidae	Lymnaea	emarginata	Pond
snail	10122

723

Mollusca	Gastropoda	Basommatophora	Lymnaeidae	Lymnaea	palustris	Marsh
snail

15

	Mollusca	Gastropoda	Basommatophora	Physidae	Aplexa	hypnorum	Snail	969

69

Mollusca	Gastropoda	Neotaenioglossa	Hydrobiidae	Amnicola	limosa	Snail
9133

652

Mollusca	Gastropoda	Neotaenioglossa	Pleuroceridae	Elimia	livescens	liver
elimia, river snail	51333

3667

Nemata	Secernentea	Rhabditida	Rhabditidae	Caenorhabditis	elegans
Nematode	78554

5611

Ochrophyta	Coscinodiscophyceae	Thalassiosirale	Stephanodiscace
Cyclotella	meneghiniana	Diatom

1617

	Cyanophycota	Cyanophyceae	Chroococcales	Chroococcaceae	Anacystis
nidulans	Blue-green algae

144600

	Cyanophycota	Cyanophyceae	Nostocales	Nostocaceae	Nostoc	muscorum
Cyanobacterium

14460

	Bacillariophyta	Bacillariophyceae	Bacillariales	Bacillariaceae
Nitzschia	obtusa	Diatom

1786

	Bacillariophyta	Bacillariophyceae	Bacillariales	Bacillariaceae
Nitzschia	palea	Diatom

2350

	Bacillariophyta	Bacillariophyceae	Naviculales	Naviculaceae	Navicula
confervacea	Diatom

1077

	Bacillariophyta	Bacillariophyceae	Naviculales	Naviculaceae	Navicula
incerta	Diatom

7924

	Charophyta	Charophyceae	Charales	Characeae	Chara	vulgaris	Stonewort

5784

	Chlorophyta	Chlorophyceae	Chlorococcales	Chlorococcaceae	Chlorococcum
sp.	Alga

1808

	Chlorophyta	Chlorophyceae	Chlorococcales	Oocystaceae	Ankistrodesmus
falcatus	Green algae

1808

	Chlorophyta	Chlorophyceae	Chlorococcales	Oocystaceae	Ankistrodesmus	sp.
Alga

723

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Scenedesmus
obliquus	Algae

12523

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Scenedesmus	sp.
Green algae

362

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Selenastrum
capricornutum	Green algae

289

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Selenastrum	sp.
Alga

362

	Chlorophyta	Trebouxiophycea	Chlorellales	Chlorellaceae	Chlorella
saccharophila	Green algae

46127

	Chlorophyta	Trebouxiophycea	Chlorellales	Chlorellaceae	Chlorella	sp.
Green algae

362

	Magnoliophyta	Liliopsida	Arales	Lemnaceae	Lemna	gibba	Inflated duckweed

144600

	Magnoliophyta	Liliopsida	Arales	Lemnaceae	Lemna	minor	Duckweed

5438

	Magnoliophyta	Magnoliopsida	Haloragales	Haloragaceae	Myriophyllum
spicatum	Eurasian watermilfoil

262449

 μg/L.*

Phylum	Class	Order	Family	Genus	Species	Common Name	LC50	Meas NOEC	Est
NOEC

Annelida	Clitellata	Lumbriculida	Lumbriculidae	Lumbriculus	variegatus
Oligochaete, worm	1442

59

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Ceriodaphnia	dubia	Water
flea	234	152

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Ceriodaphnia	reticulata
Water flea	409

17

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Daphnia	magna	Water flea
997	50

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Daphnia	pulex	Water flea
2361

97

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Simocephalus	vetulus
Water flea	11284

463

Arthropoda	Insecta	Diptera	Chironomidae	Chironomus	tentans	Midge	98449

4036

Arthropoda	Insecta	Diptera	Chironomidae	Tanytarsus	dissimilis	Midge
512012

20993

Arthropoda	Insecta	Hemiptera	Belostomatidae	Lethocerus	sp.	Midge	75644

3101

Arthropoda	Malacostraca	Amphipoda	Crangonyctidae	Crangonyx
pseudogracilis	Amphipod	59496

2439

Arthropoda	Malacostraca	Amphipoda	Gammaridae	Gammarus	pseudolimnaeus
Scud	309

13

Arthropoda	Malacostraca	Amphipoda	Hyalellidae	Hyalella	azteca	Scud	19

1

Arthropoda	Malacostraca	Decapoda	Cambaridae	Procambarus	clarkii	Red
swamp crayfish	3363308

137897

Chordata	Actinopterygii	Cypriniformes	Catostomidae	Xyrauchen	texanus
Razorback sucker	48901

2005

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Carassius	auratus
Goldfish	250635

10276

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Danio	rerio	Zebra danio
160880

6596

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Gila	elegans	Bonytail
48901

2005

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Pimephales	promelas
Fathead minnow	2443	855

	Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Ptychocheilus	lucius
Colorado squawfish	48901

2005

Chordata	Actinopterygii	Cyprinodontiformes	Poeciliidae	Poecilia
reticulata	Guppy	163907

6720

Chordata	Actinopterygii	Perciformes	Centrarchidae	Lepomis	macrochirus
Bluegill	99523

4080

Chordata	Actinopterygii	Perciformes	Centrarchidae	Micropterus	dolomieui
Smallmouth bass	5178	172

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus	kisutch
Coho salmon,silver salmon	33098

1357

Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus	mykiss
Rainbow trout,donaldson trout	24565	131

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Salvelinus	fontinalis
Brook trout	10617	213

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Thymallus	arcticus
Arctic grayling	8538

350

Chordata	Amphibia	Anura	Ranidae	Rana	catesbeiana	Bullfrog

164

	Ciliophora	Ciliatea	Heterotrichida	Spirostomidae	Spirostomum	ambiguum
Protozoa	332058

13615

Mollusca	Bivalvia	Veneroida	Corbiculidae	Corbicula	manilensis	Asiatic
clam	347214

14236

Mollusca	Bivalvia	Veneroida	Dreissenidae	Dreissena	polymorpha	Zebra
mussel

189

	Mollusca	Gastropoda	Architaenioglossa	Viviparidae	Viviparus	bengalensis
Snail	964

40

Mollusca	Gastropoda	Basommatophora	Lymnaeidae	Lymnaea	emarginata	Pond
snail	5883

Mollusca	Gastropoda	Basommatophora	Lymnaeidae	Lymnaea	palustris	Marsh
snail

10

	Mollusca	Gastropoda	Basommatophora	Physidae	Aplexa	hypnorum	Snail	2175

89

Mollusca	Gastropoda	Neotaenioglossa	Hydrobiidae	Amnicola	limosa	Snail
146734

6016

Mollusca	Gastropoda	Neotaenioglossa	Pleuroceridae	Elimia	livescens	liver
elimia, river snail	29835

1223

Ochrophyta	Coscinodiscophyceae	Thalassiosirale	Stephanodiscace
Cyclotella	meneghiniana	Diatom

1617.49

	Cyanophycota	Cyanophyceae	Chroococcales	Chroococcaceae	Anacystis
nidulans	Blue-green algae

144600

	Cyanophycota	Cyanophyceae	Nostocales	Nostocaceae	Nostoc	muscorum
Cyanobacterium

14460

	Bacillariophyta	Bacillariophyceae	Bacillariales	Bacillariaceae
Nitzschia	obtusa	Diatom

1785.8

	Bacillariophyta	Bacillariophyceae	Bacillariales	Bacillariaceae
Nitzschia	palea	Diatom

2349.8

	Bacillariophyta	Bacillariophyceae	Naviculales	Naviculaceae	Navicula
confervacea	Diatom

1077.3

	Bacillariophyta	Bacillariophyceae	Naviculales	Naviculaceae	Navicula
incerta	Diatom

7924.1

	Charophyta	Charophyceae	Charales	Characeae	Chara	vulgaris	Stonewort

5784

	Chlorophyta	Chlorophyceae	Chlorococcales	Chlorococcaceae	Chlorococcum
sp.	Alga

1807.5

	Chlorophyta	Chlorophyceae	Chlorococcales	Oocystaceae	Ankistrodesmus
falcatus	Green algae

1807.5

	Chlorophyta	Chlorophyceae	Chlorococcales	Oocystaceae	Ankistrodesmus	sp.
Alga

723

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Scenedesmus
obliquus	Algae

12522.73

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Scenedesmus	sp.
Green algae

361.5

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Selenastrum
capricornutum	Green algae

288.64

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Selenastrum	sp.
Alga

361.5

	Chlorophyta	Trebouxiophycea	Chlorellales	Chlorellaceae	Chlorella
saccharophila	Green algae

46127.4

	Chlorophyta	Trebouxiophycea	Chlorellales	Chlorellaceae	Chlorella	sp.
Green algae

361.5

	Magnoliophyta	Liliopsida	Arales	Lemnaceae	Lemna	gibba	Inflated duckweed

144600

	Magnoliophyta	Liliopsida	Arales	Lemnaceae	Lemna	minor	Duckweed

5437.83

	Magnoliophyta	Magnoliopsida	Haloragales	Haloragaceae	Myriophyllum
spicatum	Eurasian watermilfoil

262449

* The NJ Conversion Factor (0.723) was used to estimate the dissolved
value for plants (algae) because hardness was not measured, and the CF
for the current EPA criteria is hardness-dependent.

 μg/L.

Phylum	Class	Order	Family	Genus	Species	Common Name	LC50	Meas NOEC	Est
NOEC

Annelida	Polychaeta	Aciculata	Dorvilleidae	Ophryotrocha	diadema
Polychaete	3,329

237.8

Annelida	Polychaeta	Aciculata	Dorvilleidae	Ophryotrocha	labronica
Polychaete	4,755

339.6

Annelida	Polychaeta	Aciculata	Nereididae	Neanthes	arenaceodentata
Polychaete worm	8,440

602.9

Annelida	Polychaeta	Aciculata	Nereididae	Neanthes	grubei	Polychaete
4,755

339.6

Annelida	Polychaeta	Canalipalpata	Ctenodrilidae	Ctenodrilus	serratus
Polychaete worm	5,231

373.7

Annelida	Polychaeta	Canalipalpata	Pectinariidae	Pectinaria
californiensis	Cone worm	4,755

339.6

Annelida	Polychaeta	Scolecida	Capitellidae	Capitella	capitata	Polychaete
worm	1,141

81.5

Arthropoda	Crustacea	Thoracica	Balanidae	Balanus	eburneus	Barnacle
49,547

3,539

Arthropoda	Malacostraca	Amphipoda	Ampeliscidae	Ampelisca	abdita	Amphipod
520

37.2

Arthropoda	Malacostraca	Amphipoda	Corophiidae	Corophium	insidiosum
Amphipod	4,755

339.6

Arthropoda	Malacostraca	Amphipoda	Gammaridae	Elasmopus	bampo	Amphipod
9,510

679.3

Arthropoda	Malacostraca	Amphipoda	Lysianassidae	Onisimus	litoralis
Amphipod	3,329

237.8

Arthropoda	Malacostraca	Decapoda	Cancridae	Cancer	anthonyi	Yellow rock
crab	951

67.9

Arthropoda	Malacostraca	Decapoda	Cancridae	Cancer	magister	Dungeness or
edible crab	559

39.9

Arthropoda	Malacostraca	Decapoda	Crangonidae	Crangon	sp.	Caridean shrimp
1,997

142.7

Arthropoda	Malacostraca	Decapoda	Palaemonidae	Macrobrachium	rosenbergii
Giant river prawn	951

67.9

Arthropoda	Malacostraca	Decapoda	Palaemonidae	Palaemon	elegans	Rockpool
prawn	99,917

7,137

Arthropoda	Malacostraca	Decapoda	Pandalidae	Pandalus	montagui	Aesop
shrimp	356,625

25,473

Arthropoda	Malacostraca	Decapoda	Penaeidae	Penaeus	chinensis	Fleshy
prawn	1,522

108.7

Arthropoda	Malacostraca	Mysida	Mysidae	Americamysis	bahia	Opossum shrimp
2,977	16.2

	Arthropoda	Maxillopoda	Calanoida	Acartiidae	Acartia	clausi	Copepod	635

45.4

Chordata	Actinopterygii	Acipenseriformes	Polyodontidae	Polyodon	spathula
Paddlefish	9,925

709

Chordata	Actinopterygii	Atheriniformes	Atherinidae	Menidia	beryllina
Inland silverside	2,986

213

Chordata	Actinopterygii	Atheriniformes	Atherinidae	Menidia	menidia
Atlantic silverside	9,510

679.3

Chordata	Actinopterygii	Cyprinodontiformes	Cyprinodontidae	Cyprinodon
variegatus	Sheepshead minnow	2,986

213.3

Chordata	Actinopterygii	Cyprinodontiformes	Cyprinodontidae	Fundulus
heteroclitus	Mummichog	23,106

1,650

Chordata	Actinopterygii	Perciformes	Mugilidae	Liza	vaigiensis	Square
tail mullet	129,769

9,269

Chordata	Actinopterygii	Perciformes	Serranidae	Epinephelus	sp.	Rockcod,
Grouper	16,167

1,155

Chordata	Actinopterygii	Perciformes	Terapontidae	Terapon	jarbua
Tigerfish, crescent perch	1,170

83.6

Chordata	Actinopterygii	Pleuronectiformes	Bothidae	Paralichthys
olivaceus	Hirame, flounder	28,530

2,038

Chordata	Actinopterygii	Pleuronectiformes	Soleidae	Cynoglossus	joyneri
Red Tongue Sole	713

50.9

Chordata	Actinopterygii	Scorpaeniformes	Cottidae	Scorpaenichthys
marmoratus	Cabezon	1,441

102.9

Echinodermata	Echinoidea	Echinoida	Echinidae	Paracentrotus	lividus	Sea
urchin, Echinoderm	458

32.7

Echinodermata	Echinoidea	Echinoida	Strongylocentrotidae
Strongylocentrotus	droebachiensis	Green sea urchin	9,225

658.9

Echinodermata	Echinoidea	Echinoida	Strongylocentrotidae
Strongylocentrotus	purpuratus	Purple sea urchin	9,225

658.9

Mollusca	Bivalvia	Myoida	Myidae	Mya	arenaria	soft-shell clam	25,677

1,834

Mollusca	Bivalvia	Mytiloida	Mytilidae	Mytilus	edulis	Common bay mussel
453

32.3

Mollusca	Bivalvia	Mytiloida	Mytilidae	Mytilus	galloprovincialis
Mediterranean mussel	61,815

4,415

Mollusca	Bivalvia	Mytiloida	Mytilidae	Perna	viridis	Green mussel	8,388

599

Mollusca	Bivalvia	Ostreoida	Ostreidae	Crassostrea	gigas	Pacific oyster
587

42

Mollusca	Bivalvia	Ostreoida	Ostreidae	Crassostrea	virginica	American or
virginia oyster	2,330

166.4

Mollusca	Bivalvia	Ostreoida	Pectinidae	Argopecten	irradians	Bay scallop
8,179

584.2

Mollusca	Bivalvia	Veneroida	Cardiidae	Cerastoderma	edule	Cockle	475,500

33,964

Mollusca	Bivalvia	Veneroida	Donacidae	Egeria	radiata	Freshwater Clam

208,269

	Mollusca	Bivalvia	Veneroida	Mactridae	Spisula	solidissima	Surf clam
5,135

366.8

Mollusca	Bivalvia	Veneroida	Veneridae	Mercenaria	mercenaria	Northern
quahog 	742

53.0

Mollusca	Cephalopoda	Teuthida	Loliginidae	Loligo	opalescens	California
market squid	1,988

142.0

Bacillariophyta	Coscinodiscophyceae	Lithodesmiales	Lithodesmiaceae
Ditylum	brightwellii	Diatom

38.0

	Bacillariophyta	Fragilariophyceae	Fragilariales	Fragilariaceae
Asterionella	japonica	Diatom

256.8

	Chlorophyta	Chlorophyceae	Volvocales	Dunaliellaceae	Dunaliella	salina
Green algae

855.9

	Rhodophycota	Rhodophyceae	Gigartinales	Gracilariaceae	Gracilaria
tenuistipitata	Red algae

3,804

	Rhodophycota	Rhodophyceae	Rhodymeniales	Champiaceae	Champia	parvula	Red
algae

19.3

Table 3.2a.  Lead Freshwater Toxicity Data by Taxonomic Group for New
Jersey Criteria.  The 5th percentile values are the basis for those
effects concentrations (ECAs) in Table 4.1 that rely on surrogate data.
All values are given as dissolved lead in µg/L.

Phylum	Class	Order	Family	Genus	N	Mean LC50	Mean NOEC	5th LC50	5th NOEC

Annelida

	1	3,190	227.8

	Clitellata

1	3,190	227.8

Lumbriculida

	1	3,190	227.8

	Lumbriculidae

1	3,190	227.8

Lumbriculus	1	3,190	227.8

Arthropoda

	14	1,736	140.3	14.04	1.29

	Branchiopoda

6	841	80.1	31.08	26.61

Cladocera

	1	546	39.0

	Moinidae

1	546	39.0

Moina	1	546	39.0

Diplostraca

	5	916	92.5	27.94	24.21

	Daphniidae

5	916	92.5	27.94	24.21

Ceriodaphnia	2	274	65.3

Daphnia	2	1,629	82.6

Simocephalus	1	3,254	232.4

	Insecta

3	5,885	420.4

Diptera

	2	14,396	1,028.3

	Chironomidae

2	14,396	1,028.3

Chironomus	1	1,280	91.4

Tanytarsus	1	161,952	11,568.0

Hemiptera

	1	983	70.2

	Belostomatidae

1	983	70.2

Lethocerus	1	983	70.2

	Malacostraca

5	1,993	142.4	1.69	0.12

Amphipoda

	3	322	23.0

	Crangonyctidae

1	19,955	1,425.3

Crangonyx	1	19,955	1,425.3

	Gammaridae

1	95	6.8

Gammarus	1	95	6.8

	Hyalellidae

1	18	1.3

Hyalella	1	18	1.3

Decapoda

	2	30,754	2,196.7

	Cambaridae

2	30,754	2,196.7

Orconectes	1	2,386	170.4

Procambarus	1	396,418	28,315.6

Chordata

	16	21,715	1,110.3	959.61	22.02

	Actinopterygii

16	21,715	1,110.3	959.61	22.02

Cypriniformes

	7	30,142	2,368.3	201.89	16.44

	Catostomidae

1	122,910	8,779.3

Xyrauchen	1	122,910	8,779.3

	Cyprinidae

6	23,847	1,903.7	172.49	14.19

Carassius	1	22,775	1,626.8

Cyprinus	1	912	65.2

Danio	1	342,781	24,484.4

Gila	1	122,910	8,779.3

Pimephales	1	1,709	237.9

Ptychocheilus	1	122,910	8,779.3

Cyprinodontiformes

	2	50,837	3,631.2

	Poeciliidae

2	50,837	3,631.2

Gambusia	1	173,520	12,394.3

Poecilia	1	14,894	1,063.8

Perciformes

	2	25,333	1,245.4

	Centrarchidae

2	25,333	1,245.4

Lepomis	1	74,155	5,296.8

Micropterus	1	8,654	292.8

Salmoniformes

	4	5,413	103.6	1,060.86	7.17

	Salmonidae

4	5,413	103.6	1,060.86	7.17

Oncorhynchus	2	11,595	111.6

Salvelinus	1	2,964	60.1

Thymallus	1	2,155	153.9

Siluriformes

	1	75,915	5,422.5

	Heteropneustida

1	75,915	5,422.5

Heteropneustes	1	75,915	5,422.5

Ciliophora

	2	3,879	277.1

	Ciliatea

2	3,879	277.1

Heterotrichida

	2	3,879	277.1

	Spirostomidae

2	3,879	277.1

Spirostomum	2	3,879	277.1

Mollusca

	7	18,901	1,350.1	550.23	39.30

	Bivalvia

1	739,795	52,842.5

Veneroida

	1	739,795	52,842.5

	Corbiculidae

1	739,795	52,842.5

Corbicula	1	739,795	52,842.5

	Gastropoda

6	10,258	732.7	512.35	36.60

Architaenioglos

	2	15,918	1,137.0

	Viviparidae

2	15,918	1,137.0

Filopaludina	1	137,980	9,855.7

Viviparus	1	1,836	131.2

Basommatophora

	2	3,131	223.7

	Lymnaeidae

1	10,122	723.0

Lymnaea	1	10,122	723.0

	Physidae

1	969	69.2

Aplexa	1	969	69.2

Neotaenioglossa

	2	21,652	1,546.6

	Hydrobiidae

1	9,133	652.4

Amnicola	1	9,133	652.4

	Pleuroceridae

1	51,333	3,666.6

Elimia	1	51,333	3,666.6

Nemata

	1	78,554	5,611.0

	Secernentea

1	78,554	5,611.0

Rhabditida

	1	78,554	5,611.0

	Rhabditidae

1	78,554	5,611.0

Caenorhabditis	1	78,554	5,611.0

Table 3.2b.  Lead Freshwater Toxicity Data by Taxonomic Group for
Current EPA Criteria.  The 5th percentile values are the basis for those
effects concentrations (ECAs) in Table 4.1 that rely on surrogate data.
All values are given as dissolved lead in µg/L.

Phylum	Class	Order	Family	Genus	N	Mean LC50	Mean NOEC	5th LC50	5th NOEC

Annelida

	1	1,442	59.1

	Clitellata

1	1,442	59.1

Lumbriculida

	1	1,442	59.1

	Lumbriculidae

1	1,442	59.1

Lumbriculus	1	1,442	59.1

Arthropoda

	12	6,895	362.1	19.2	0.66

	Branchiopoda

5	1,205	89.5	106.4	9.40

Diplostraca

	5	1,205	89.5	106.4	9.40

	Daphniidae

5	1,205	89.5	106.4	9.40

Ceriodaphnia	2	309	50.6

Daphnia	2	1,534	69.7

Simocephalus	1	11,284	462.6

	Insecta

3	156,227	6,405

Diptera

	2	224,515	9,205

	Chironomidae

2	224,515	9,205

Chironomus	1	98,449	4,036

Tanytarsus	1	512,012	20,993

Hemiptera

	1	75,644	3,101

	Belostomatidae

1	75,644	3,101

Lethocerus	1	75,644	3,101

	Malacostraca

4	5,877	240.9	0.34	0.01

Amphipoda

	3	708	29.0

	Crangonyctidae

1	59,496	2,439

Crangonyx	1	59,496	2,439

	Gammaridae

1	309	12.7

Gammarus	1	309	12.7

	Hyalellidae

1	19.3	0.79

Hyalella	1	19.3	0.79

Decapoda

	1	3,363,309	137,897

	Cambaridae

1	3,363,309	137,897

Procambarus	1	3,363,309	137,897

Chordata

	13	33,678	1,296	2,344.5	118.64

	Actinopterygii

13	33,678	1,296	2,344.5	118.64

Cypriniformes

	6	47,522	2,785	1,745.1	776.76

	Catostomidae

1	48,901	2,005

Xyrauchen	1	48,901	2,005

	Cyprinidae

5	47,251	2,975	970.9	441.97

Carassius	1	250,635	10,276

Danio	1	160,880	6,596

Gila	1	48,901	2,005

Pimephales	1	2,443	854.8

Ptychocheilus	1	48,901	2,005

Cyprinodontiformes

	1	163,907	6,720

	Poeciliidae

1	163,907	6,720

Poecilia	1	163,907	6,720

Perciformes

	2	22,700	837.3

	Centrarchidae

2	22,700	837.3

Lepomis	1	99,523	4,080

Micropterus	1	5,178	171.8

Salmoniformes

	4	16,477	339.5	5,357.1	56.77

	Salmonidae

4	16,477	339.5	5,357.1	56.77

Oncorhynchus	2	28,514	421.9

Salvelinus	1	10,617	213.1

Thymallus	1	8,538	350.1

Ciliophora

	1	332,058	13,615

	Ciliatea

1	332,058	13,615

Heterotrichida

	1	332,058	13,615

	Spirostomidae

1	332,058	13,615

Spirostomum	1	332,058	13,615

Mollusca

	6	7,486	306.9	511.0	20.95

	Bivalvia

1	347,214	14,236

Veneroida

	1	347,214	14,236

	Corbiculidae

1	347,214	14,236

Corbicula	1	347,214	14,236

	Gastropoda

5	3,475	142.5	493.7	20.24

Architaenioglossa

	1	964	39.5

	Viviparidae

1	964	39.5

Viviparus	1	964	39.5

Basommatophora

	2	3,577	146.7

	Lymnaeidae

1	5,883	241.2

Lymnaea	1	5,883	241.2

	Physidae

1	2,175	89.2

Aplexa	1	2,175	89.2

Neotaenioglossa

	2	6,410	262.8

	Hydrobiidae

1	1,377	56.5

Amnicola	1	1,377	56.5

	Pleuroceridae

1	29,835	1,223

Elimia	1	29,835	1,223

Table 3.3.  Freshwater Toxicity Data for Total Dissolved Solids.  All
values are in mg TDS/L.

Phylum	Class	Order	Family	Genus	Species	Common Name	TDS comp’t

Mean

LC50	Mean NOEC

Platyhelminthes	Turbellaria	Tricladida	Planariidae	Dugesia	gonocephala
Flatworm	Cl-	1,230

	Annelida	Clitellata	Haplotaxida	Tubificidae	Tubifex 	tubifex
Oligochaete, worm	K+	2,000

	Annelida	Clitellata	Haplotaxida	Tubificidae	Tubifex 	tubifex
Oligochaete, worm	Ca2+	814

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Ceriodaphnia	dubia	Water
flea	Cl-	783

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Ceriodaphnia	dubia	Water
flea	HCO3-	1,077

	Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Daphnia	magna	Water flea
Cl-	1,467	372

Arthropoda	Branchiopoda	Diplostraca	Daphniidae	Daphnia	magna	Water flea
HCO3-	1,522

	Arthropoda	Maxillopoda	Cyclopoida	Cyclopidae	Cyclops	abyssorum
prealpinus	Copepod	Ca2+	7,000

	Arthropoda	Maxillopoda	Cyclopoida	Cyclopidae	Cyclops	abyssorum
prealpinus	Copepod	Mg2+	280

	Arthropoda	Malacostraca	Isopoda	Asellidae	Lirceus	fontinalis	Isopod	Cl-
2,950

	Arthropoda	Insecta	Diptera	Chironomidae	Chironomus	tentans	Midge
Synthetic effluent

1,543

Arthropoda	Insecta	Diptera	Chironomidae	Chironomus	attenuatus	Midge	Cl-
4,900

	Arthropoda	Insecta	Diptera	Chironomidae	Cricotopus 	trifascia	Midge	K+
1,567

	Arthropoda	Insecta	Diptera	Chironomidae	Cricotopus 	trifascia	Midge	Cl-
1,406

	Arthropoda	Insecta	Diptera	Culicidae	Culex	sp.	Mosquito	Cl-	6,222

	Arthropoda	Insecta	Trichoptera	Hydroptilidae	Hydroptila	angusta
Caddisfly	K+	2,316

	Arthropoda	Insecta	Trichoptera	Hydroptilidae	Hydroptila	angusta
Caddisfly	Cl-	2,077

	Mollusca	Gastropoda	Basommatophora	Physidae	Physa	gyrina	Snail	Cl-
2,540

	Mollusca	Bivalvia	Unionoida	Unionidae	Obliquaria 	reflexa	Threehorn
wartback	K+	>2,000

	Chordata	Actinopterygii	Anguilliformes	Anguillidae	Anguilla 	rostrata
American eel	Cl-	11,943

	Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus 	mykiss
Rainbow trout	Cl-	4,243	923

Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus 	mykiss
Rainbow trout	Synthetic effluent

1,348

Chordata	Actinopterygii	Salmoniformes	Salmonidae	Oncorhynchus 	keta	Chum
salmon	Synthetic effluent

300

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Pimephales	promelas
Fathead minnow	Cl-	6,570	433

Chordata	Actinopterygii	Cypriniformes	Cyprinidae	Carassius	auratus
Goldfish	Cl-	8,906

	Chordata	Actinopterygii	Perciformes	Centrarchidae	Lepomis	macrochirus
Bluegill	Cl-	5,685

	Chlorophyta	Chlorophyceae	Chlorococcales	Scenedesmaceae	Selenastrum
capricornutum	Green algae	Synthetic effluent

2,020

Besides toxicity data in which LC50 and NOEC values were reported or
estimated, other TDS data relevant to this evaluation was reviewed.
Potassium chloride, as well as other molluscicides has been found to be
effective in controlling zebra mussels.  Several researchers have been
testing the effects of these chemicals on unionid mussels for the
purpose of evaluating their safety on non-target organisms and their
effectiveness in controlling zebra mussels.  Waller et al. (1993) tested
the acute toxicity of 18 chemicals including KCl on two fish species and
the threehorn wartyback unionid mussel, Obliquaria reflexa.  An LC50
value could not be determined for the KCl test with the threehorn
wartyback mussel because of insufficient mortality at the highest
concentration tested (2000 mg/L) indicating an LC50 > 2000 mg/L.

In a separate study, Waller and Fisher (1998) tested a series of
chemicals including calcium chloride, potassium chloride and sodium
chloride on eight unionid mussels to which zebra mussels were attached.
Tests were conducted at a concentration and duration found to be lethal
to the zebra mussel.  The toxicity of the chloride salts to the unionid
mussels was varied between the eight species.  The lowest mean mortality
(6 percent) in a chloride salt treatment exposed to the unionids was
20,000 mg/L NaCl for 6 hours.  The results for these tests suggest that
acute effect levels for unionid mussels are higher than the 500 mg/L
criterion adopted by New Jersey.

A field approach to determine the effect of TDS on aquatic life was
undertaken by the Florida Department of Environmental Protection in
their study, Statistical Analysis of Surface Water Quality Specific
Conductance Data (FDEP 2005).  Quantile regression was used to predict
the effect of specific conductance on sensitive taxa found in
Florida’s streams.  Specific conductance is technically conductivity
normalized to a temperature of 25ºC and recorded in µmhos/cm.  Since
specific conductance is a measure of water’s ability to conduct
electricity, and therefore, a measure of the water’s ionic activity
and content, it is directly related to TDS.  Conversion factors relating
specific conductance to TDS range from 0.5 to 0.9 depending on the ionic
make-up.  The study evaluated the correlative relationship between
sensitive taxa and conductivity at sites determined to be “least
disturbed.”  Least disturbed sites were chosen to separate the effects
of anthropogenic impacts from those related to specific conductance.  A
total of 585 sampling events at 86 “least disturbed” sites were
evaluated with each sampling event containing both benthic community and
conductivity measurements.  The results show a statistically significant
(p<0.001) relationship at the 90th quantile with the proportion of
sensitive taxa and the proportion of sensitive individuals declining as
conductivity increases.  Specific conductance in Florida’s “least
impaired” sites ranged from approximately 20 to 600 µmhos/cm with the
concentration of ions being very dependent on the hydrogeology of the
watershed (i.e., groundwater-influenced surface waters were much higher
in conductivity than streams influenced primarily from runoff).  The
model predicts that as conductivity increases from 20 to 200 µmhos/cm,
about 50 percent of sensitive taxa are lost and 75 percent are lost by
600 µmhos/cm.  This relationship strongly suggests that the composition
of taxa in Florida as well as streams outside of Florida naturally
varies according to conductivity.  Assuming a conversion factor of 0.7,
a conductivity measurement of 600 µmhos/cm is 420 mg/L TDS a
concentration at which many of sensitive taxa found at low TDS waters
would be gone.

The Florida model suggests that there are sensitive taxa that do not
inhabit surface waters near the New Jersey criterion of 500 mg/L.  It is
important to reiterate that all the observations in the Florida study
were made at “least impaired” sites, sites which have minimal
influence from man.  Since surface waters may naturally contain TDS
levels in this range, it is important to understand the natural water
quality and specifically the TDS levels of the surface waters in which
the two aquatic species of interest (dwarf wedge mussel and shortnose
sturgeon) live.  The prime habitat of the shortnose sturgeon includes
river mouths, tidal rivers, estuaries, and bays suggesting this species
has a tolerance for higher levels of TDS.  The current and historical
record of the dwarf wedge mussel indicates this species inhabits a range
of stream types and water quality conditions from small tributaries to
large rivers (e.g., Potomac River at Washington DC) (Moser 1993).
Although limited information was found relating current populations and
TDS levels, the dwarf wedge mussel can apparently tolerate a range of
water quality conditions.

3.3.2  Comparison of New Jersey Lead Criteria with Current EPA Lead
Criteria (Freshwater Only)  TC "3.3.2  Comparison of New Jersey Lead
Criteria with Current EPA Lead Criteria (Freshwater Only)" \f C \l "3"

New Jersey derived their 2002 freshwater acute and chronic criteria
without a hardness adjustment, which is a departure from the current EPA
recommended freshwater lead criteria.  An effects analysis was also
performed on the EPA hardness-based lead criteria to assess any
potential differences in the protection of listed species.  The
estimates for acute and chronic effect concentrations of lead for the
listed species were based on LC50 and NOEC values derived using the
respective parameters New Jersey and EPA used to calculate their
criterion.  Since saltwater criteria for both New Jersey and EPA do not
adjust for hardness, this comparison was restricted to the freshwater
criteria.  The respective parameters for New Jersey and EPA were:

Parameter	New Jersey	Current EPA

	Acute	Chronic	Acute 	Chronic

Hardness adjustment	None	None	exp{1.273 [ln(hardness)]- 1.460} (CF)
exp{1.273 [ln (hardness)]-4.705} (CF)

Acute-to-chronic ratio	NA	14	NA	24.39

Conversion factor	0.723	0.723	1.46203-[(ln hardness)(0.145712)]
1.46203-[(ln hardness)(0.145712)]

  SEQ CHAPTER \h \r 1 3.3.3  Multiple Routes of Exposure  TC "3.3.3
Multiple Routes of Exposure" \f C \l "3"

Lead’s exposure through the diet is a potential additional threat to
listed species.  Therefore, the added risk factor from other exposure
routes, FR, is applied in the chronic assessment for lead, as per the
Methods Manual.  The derivation of the FR for lead is based on the data
provided in the text box below.

  SEQ CHAPTER \h \r 1 Basis for Derivation of Risk Factors for Lead -
New Jersey Criteria

Species	Aquatic NOEC, μg/ml	Diet NOEC, μg/g ww	Potency Factora	Food
Concentration Factor	Risk Factorb

Oncorhynchus mykiss	0.021c	7040d	2.98 E-6	1089e	1.0032

  SEQ CHAPTER \h \r 1 Basis for Derivation of Risk Factors for Lead -
EPA Criteria

Species	Aquatic NOEC, μg/ml	Diet NOEC, μg/g ww	Potency Factora	Food
Concentration Factor	Risk Factorb

Oncorhynchus mykiss	0.131c	7040d	1.86 E-5	1089e	1.0206

a	Potency Factor = aquatic NOEC ÷ diet NOEC

b	Risk factor = 1 + (PF x Food CF); the chronic ECA values in Table 4.1
were divided by the risk factors to obtain the ECA values.

c	Aquatic NOEC is a measured value for O. mykiss.

d	Diet NOEC is a measured value for O. mykiss.

e	Food CF is the 84th percentile of BCF/BAFs determined for
macroinvertebrate and fish.  The 84th percentile approximates one
standard deviation above the geometric mean.

Risk factors were not determined for TDS because the common constituents
in TDS ( K+, HCO3-, Mg2+, Cl-, SO4-, Na+, Ca2+) are not known to
bioaccumulate in food.  The biological evaluation for TDS assumed the
cause of toxic effects to aquatic organisms was through aqueous
exposure.

3.3.4 Aquatic Plants  TC "3.3.4 Aquatic Plants" \f C \l "3"

This section consists of the assessment results for water-column only
chronic toxicity to aquatic plants.  As indicated in the Methods Manual,
there are few existing data on acute toxicity to plants at criteria
levels for most of the 304(a) criteria pollutants, and these few data
indicate that plants do not demonstrate acute effects at criteria
levels.  Accordingly, the assessment methodology for the listed plant
species is founded on appropriate measures of chronic toxicity, where:
(1) the chronic values for plants (reported in Table 3.1 as the NOEC)
are from tests where the chemical in the exposure medium was measured,
and (2) the endpoint measured was biologically significant (e.g.,
vegetative growth or reproduction).  Because plants are rarely as
sensitive as fish and macroinvertebrates, the recovery rate for
phytoplankton is extremely rapid, and because there are few data
available on the toxicity to plants, the effects determination for
plants is based on a comparison of the chronic criterion to the most
sensitive acceptable plant value.

Toxicity data for 20 plant species, 16 algal taxa and 4 vascular plant
taxa, are available for lead.  The most sensitive are three algal taxa,
Scenedesmus sp., Selenastrum sp., and Chlorella sp., each with a
measured NOEC value of 362 µg/L.  Least sensitive taxa with measured
NOEC values exceeding 100,000 µg/L are the blue-green alga, Anacystis
nidulans, and two vascular plants, Lemna gibba and Myriophyllum
spicatum.  Because the potential chronic effect concentration exceeds
the freshwater and saltwater CCC by at least an order of magnitude, EPA
is making a “not likely to adversely affect” finding for the swamp
pink, Helonias bullata, Kneiskern’s beaked rush, Rhynchospora
knieskernii and sensitive joint vetch, Aeschynomene virginica.

Note: The EPA does not adjust lead toxicity values to plants based on
hardness; therefore the NOEC values for plants are same for both the New
Jersey and EPA data sets.

Only one test with the alga, Selenastrum capricornutum was available for
TDS.  EVS (1997) reported an NOEC for S. capricornutum of >2020 mg TDS/L
for a synthetic effluent prepared to match the overall chemical
characteristics of an effluent discharged from the a mine.  Because the
potential chronic effect concentration exceeds the freshwater CCC by
almost three orders of magnitude, EPA is making a “not likely to
adversely affect” finding for the swamp pink, Helonias bullata,
Kneiskern’s beaked rush, Rhynchospora knieskernii and sensitive joint
vetch, Aeschynomene virginica.

3.4  Aquatic-Dependent Species  TC "3.4  Aquatic-Dependent Species" \f C
\l "2"

3.4.1 Overview and Background  TC "3.4.1 Overview and Background" \f C
\l "3"

This section comprises the assessment of the 3 freshwater and 7
saltwater aquatic-dependent animal species that have more than limited
exposure to “surface waters of New Jersey,” and which may be
affected by the lead freshwater and saltwater aquatic life criteria and
the TDS freshwater criterion.  The assessment methodology for
aquatic-dependent species is in Section 3.4 of the Methods Manual.
Effects to aquatic-dependent animals from contaminants can be manifested
directly through exposure of the contaminant from food and/or water
intake and indirectly through the elimination of their prey.  This
section develops the variables needed to perform an effects assessment
to aquatic-dependent animals, namely:

bioconcentration/bioaccumulation factor (BCF/BAF) used to estimate the
concentration of the contaminant in the prey tissue living in water at
chronic criterion concentrations,

a dietary NOEC estimate for each listed aquatic-dependent animal, and

the range of effect levels for aquatic prey species of the listed
aquatic-dependent species.

The common constituents that make up TDS (K+, HCO3-, Mg2+, Cl-, SO4-,
Na+, Ca2+) do not bioaccumulate in aquatic organisms and therefore
exposure from TDS in food to aquatic-dependent animals is not included
in this biological evaluation.  Conversely, lead does bioaccumulate in
aquatic organisms over a long term exposure, albeit to levels not very
high (GLEC 1998).  Similar to other inorganic metals, the low
bioaccumulation potential of lead may be due in part to differences in
the mechanisms for chemical uptake by aquatic organisms (e.g., passive
diffusion, facilitated transport, active transport), differences in
sorption affinities to biotic and abiotic ligands, and differences in
chemical speciation in water (EPA 2000).  It is also possible that
simple lead salts are poorly absorbed in animal intestine.  An apparent
characteristic of lead, as well as for certain other metals, is that
BCF/BAFs for lead diminish up the food chain such that fish exhibit the
lowest bioconcentration potential (Varanasi and Markey, 1978).  Also,
the period of time required to reach maximum values may be in the order
of several weeks as opposed to several months (Allen, 1994, 1995).

3.4.2  Freshwater Exposure Assessment  TC "3.4.2  Freshwater Exposure
Assessment" \f C \l "3"

Bioconcentration/bioaccumulation factors (BCF/BAFs) are used to estimate
the concentration of lead in prey tissue (aquatic organisms).  BCF/BAFs
were available for 6 freshwater invertebrate species and 3 fish studies
(Table 3.4).  The geometric mean of BCF/BAFs for 9 aquatic animals is
138 L/kg with a range of 3 (Procambarus clarkia) to 3670 L/kg
(Chironomus riparius).

Given the information available for assigning appropriate food partition
coefficients, relative to natural (field) water and sediment
concentrations, the freshwater partition coefficient is set at 1089 L/kg
for invertebrates and vertebrates, which is the 84th percentile BCF
(from Table 3.4) and is roughly the equivalent of the geometric mean
BCF/BAF plus one standard deviation (the value recommended for
calculating the assessment exposure concentration in the Methods
Manual).

Table 3.4.  Lead Bioconcentration and Bioaccumulation Factorsa
(BCF/BAFs) for Freshwater Aquatic Food Organisms.  BCF/BAFs are Based on
Wet Weight.  Sources Include EPA’s ECOTOX Database, and the Ambient
Water Quality Criteria Document for Lead (GLEC 1998).

Species	Exposure duration

 (days)

g/kg fresh weight, divided by concentration measured in water
(g/L).

3.4.3  Saltwater Exposure Assessment  TC "3.4.3  Saltwater Exposure
Assessment" \f C \l "3"

Fewer studies are available to determine the bioconcentration factors
(BCFs) for lead for saltwater food items of aquatic species (Table 3.5).
 The data exist for only two classes of organisms: bivalve molluscs and
bony fish.  The BCF values reported in Table 3.5 range from a low of 1.8
L/kg for the salmonid Oncorhynchus kisutch to a high of 5,271 L/kg for
Crassostrea gigas.  The range of BCF values within this latter group of
saltwater organisms (bivalve molluscs) is quite large and spans two
orders of magnitude.  For assessments of fish-eating wildlife, the BCF
values in Table 3.5 are conservative as lead levels in the tissue of
fishes are lower than in invertebrates.

Given the information available for assigning appropriate food partition
coefficients, relative to natural (field) water and sediment
concentrations, the saltwater partition coefficient is set at 679.5 L/kg
for invertebrates and vertebrates, which is the 84th percentile BCF
(from Table 3.5).

Table 3.5.  Lead Bioconcentration Factorsa (BCFs) for Saltwater Aquatic
Food Organisms.  BCFs are Based on Wet Weight.  Sources Include EPA’s
ECOTOX Database, the Ambient Water Quality Criteria Document for Lead
(GLEC 1998), and Jarvinen and Ankley (1999).

Species	Exposure duration

 (days)

g/kg fresh weight, divided by concentration measured in water
(g/L).

b	Factor was converted from dry weight to wet weight basis by dividing
tissue concentration by 5 (assuming 80% moisture in tissue).

c	Factor based on renewal tests.

3.4.4  Toxicity Assessment - Lead  TC "3.4.4  Toxicity Assessment -
Lead" \f C \l "3"

Information on the chronic dietary effects of lead to potential
surrogate species is compiled in Table 3.6.  Data are primarily from
U.S. EPA’s ECOTOX database.

The long-term chronic dietary effects of lead have been assessed on the
endpoints: mortality, growth, reproduction and eggshell thickness using
surrogates of aquatic-dependent species (Table 3.6).  For vertebrates,
the NOECs for mortality and growth for several bird species and two
rodent species range from a low of 54 mg Pb/kg diet to 2,000 mg Pb/kg
diet.  A diet concentration of 100 mg Pb/kg did not affect egg thickness
of mallard ducks in an 85 d study (Table 3.6).  A lowest-observed effect
concentration (LOEC) based on growth was determined for juvenile shrew
fed a 371 - 423 mg Pb/kg diet in a 31 d study.  For the vertebrate data,
the chronic dietary effects concentration is set at 100 mg Pb/kg diet,
the 16th percentile of the vertebrate values in Table 3.6.  This value
is roughly the equivalent to the geometric mean chronic dietary toxicity
value minus one standard deviation (the value recommended for
calculating the assessment exposure concentration in the Methods
Manual).

New Jersey has a listed insect, the   SEQ CHAPTER \h \r 1 Northeastern
beach tiger beetle that feeds on dead and live marine organisms.  Two
chronic studies using invertebrates have assessed the effect of dietary
lead on growth and reproduction.  Denneman and Straalen (1991) reported
an NOEC of 431 mg/kg for growth and reproduction in an oribatid mite
after a 3 month exposure to lead in its diet.  Growth and cocoon
production in the compost worm was not affected by 886 mg/kg, but this
concentration did affect hatching success of exposed worms.  The chronic
dietary effects concentration is set at 431 mg Pb/kg diet for
invertebrates based on the oribatid mite study, because of the
uncertainty of the NOEC for compost worm hatching success.

Table 3.6.  Chronic Toxicity of Lead to Potential Surrogate Species
Based on Wet Weight of Oral Dose.  Data are from ECOTOX.

Species (age)	Chemical	Dose Description, Duration, and Endpoint	Acute
Toxicity

LD50

(mg/kg)	Chronic Toxicity

(mg/kg diet)	Reference

Oribatid mite

Platynothrus peltifer	Lead nitrate	Diet, 3 months, NOEC – Growth and
reproduction	-

431	Denneman and Straalen, 1991

Compost worm

Eisenia fetida	Lead nitrate	Diet, 8 weeks, NOEC – Growth, cocoon
production	-

886	Reinecke and Reinecke, 1996

Compost worm

Eisenia fetida	Lead nitrate	Diet, 8 weeks, LOEC – Hatching success	-
886	Reinecke and Reinecke, 1996

Mallard duck, Anas platyrhinchos	Lead	Diet, 85 d, NOEC - Egg thickness	-
100	Haegele et al., 1974

Mallard duck, Anas platyrhinchos

(22 wk)	Lead	Diet, 10 wk, NOEC- Growth (weight)	-

207	Heinz et al., 1999

Swan goose

Anser cygnoides (26 wk)	Acetic acid Lead (2+)salt

	Diet, 12 wk,  NOEC- Growth (wt. gain)	-	2000	Johnson and Damron, 1982

American kestrel,

Falco sparverius	Lead	Diet, 5-7 mo, NOEC -carcass weight	-	54	Franson,
et al. 1983

American kestrel,

Falco sparverius	Acetic acid Lead (2+)salt	Diet, 60 d, NOEC - Mortality
-	448.3	Custer et al., 1984

Domestic chicken

Gallus domesticus

(4 wk)	Acetic acid Lead (2+)salt	Diet, 4 wk, NOEC - Growth (wt. gain)	-
100	Damron et al., 1969

Common shrew

Sorex araneus, (<=5 mo)	Lead	Diet, 31 d, LOEC -Growth (weight)	-	371-423
Pankakoski, et al. 1994

Japanese quail

Coturnix japonica

(juvenile, 1d)	Acetic acid Lead (2+)salt	Diet, 14 d, NOEC -Growth
(weight)	-	200	Stone et al., 1981

Norway rat

Rattus norvegicus (juvenile)	Acetic acid Lead (2+)salt	Diet, 22 mo, NOEC
-  Growth (weight)

-

1000	Jessup and Shott, 1969

3.4.5  Risk Analysis  TC "3.5.5  Risk Analysis" \f C \l "3"

The exposure of lead to aquatic-dependent organisms through their food
is predicted by the “estimated residue level in diet.” This value is
determined by multiplying the CCC for lead by the bioaccumulation
potential for lead which is represented by the 84th percentile of the
BCF/BAF values.  The “estimated residue levels in diet” for the
freshwater and saltwater lead chronic criteria are:

Pb Freshwater (NJ) 		= 5.4 g/L (CCC) * 1089 L/kg (BCF) = 5.881 mg/kg

Pb Freshwater (EPA) 		= 2.5 g/L (CCC) * 1089 L/kg (BCF) = 2.722 mg/kg

Pb Saltwater 			= 24 g/L (CCC) * 679.5 L/kg (BCF) = 16.31 mg/kg

This tissue exposure concentration for each criterion (5.881, 2.722, and
16.31 mg Pb/kg prey tissue) is substantially below any potential chronic
dietary threshold for aquatic-dependent species (invertebrates: 431 mg
Pb/kg diet; vertebrates: 100 mg Pb/kg diet) and therefore, the effects
determination of lead and TDS for aquatic-dependent species is made
solely on the acute and chronic assessment effects concentration (ECA)
values for food organisms of these species listed in Tables 4.1, 4.2 and
4.3 (found in Section 4 of this document).  In each instance, the food
item effect concentration was derived from known toxicity values for
suspected food items.

3.5  Food Items of Federally-Listed Species  TC \l2 "3.5  Food Items of
Federally-Listed Species

This section consists of the assessment results for water-column only
toxicity to food items of aquatic and aquatic-dependent animals.  For a
description of the methodology to assess the effects of the New Jersey
lead and TDS aquatic life criteria on food items of such species refer
to Section 3.5 of the Methods Manual.

The aquatic toxicity data used for this assessment are presented in
Tables 3.1 (lead) and 3.3 (TDS) as acute (geometric mean LC50) and
chronic (geometric mean NOEC) values for a given species.  These data
are then grouped into common categories (e.g., oligochaetes, insects,
fish, etc.) that are relevant as food for the listed species in New
Jersey.  The range of acute and chronic ECA values for freshwater (based
on New Jersey and EPA criteria) and saltwater food items are shown in
the text boxes below.

Lead: Range of Effect Concentrations for Freshwater Food Items Used in
Tables 4.1a and 4.2a – New Jersey Freshwater Criteria Parameters

Organism Type	Acute EC (g Pb/L)	Chronic EC (g Pb/L)

Detritus, plant matter	---	289-262,449

Diatoms	---	1,077-7,924

Oligochaetes	1,405	228

Shrimp and crayfish	7.9-176,633	1-28,316

Insects	433-71,344	70-11,568

Snails	427-60,784	15

Seeds, plants and carrion	7.9-325,901	15-262,449

Fish and turtles	402-151,005	21-565

g Pb/L)	Chronic EC (g Pb/L)

Detritus, plant matter	---	289-262,249

Diatoms	---	1,077-7,924

Oligochaetes	503	59

Shrimp and crayfish	8.4-1,481,633	1-137,897

Insects	33,323-225,556	3,101-20,933

Snails	424-64,641	10

Seeds, plants and carrion	8.4-1,481,633	1-144,600

Fish and turtles	1,076-110,412	131-855

g Pb/L)	Chronic EC (g Pb/L)

Detritus, plant matter	---	2020

Diatoms	---	2020

Oligochaetes	814-2,000	372-1,543a

Shrimp and crayfish	2,950b	372-1,543a

Insects	1,406-6,222	372-1,543a

Snails	2,540	372-1,543a

Seeds, plants and carrion	N/A	2020

Fish and turtles	4,243-11,943	300-1,348

a  Range is for all invertebrates

b  Malacostraca was used as a surrogate

3.6  Effects on Glochidia Host Species  TC "3.6  Effects on Glochidia
Host Species" \f C \l "2"

EPA’s recent revision of the Methods Manual (November 2005) includes
SEQ CHAPTER \h \r 1 an evaluation of criteria concentrations that are
likely to adversely affect freshwater mussels due to toxic effect to the
host fish species of glochidia.  Glochidia are mussel larvae, which are
released by the female mussel to find a suitable fish host for
transformation into juvenile mussels.  Glochidia attach to the gills or
fins of the host fish where they encyst and eventually fall and settle
to the bottom as juveniles.  The listed species of New Jersey includes
the dwarf wedge mussel which has two host fish species to which its
glochidia attach, the tessellated darter (Etheostoma olmstedi) and the
mottled sculpin (Cottus bairdi).

EPA recommends using the toxicity information from Tables 3.1 and 3.2
from this document to estimate the sensitivity to the host species.
Because the host species are not listed species, the central tendency of
the toxicity (mean LC50 or NOEC) of the obligate host species, and not
the 5th percentile conservative estimates, is used to assess whether
there is an impact.  The mean acute and chronic ECA values of obligate
fish host species are compared to the acute and chronic criteria.  The
lead toxicity data set (Table 3.1) does not contain ECA values for
either of the host species.  The closest surrogate taxon for the mottled
sculpin (Cottus bairdi) is the family Cottidae in Table 3.2 which has a
mean LC50 of 1441 g/L (both New Jersey and EPA criteria); the mean
NOEC for this taxon is 102.9 g/L (New Jersey criteria) and 59.07
g/L (EPA criteria).  The closest surrogate taxon for the tessellated
darter (Etheostoma olmstedi) is the order Perciformes in Table 3.2,
which has a mean LC50 of 13,488 g/L (both New Jersey and EPA
criteria); the mean NOEC for this taxon is 963.4 g/L (New Jersey
criteria) and 553.0 g/L (EPA criteria).   Because all the ECA values
for the host species are well above the respective acute and chronic
criteria (both New Jersey and EPA), EPA makes a “not likely to
adversely affect” finding for the host species of the dwarf wedge
mussel.

For TDS, the closest surrogate for the two host fish species is the
bluegill sunfish in the order Perciformes.  The acute value for the
bluegill (5,685 mg Cl-/L) is well above the New Jersey’s numeric
criterion of 500 mg TDS/L.  Since no chronic values were available for
the bluegill, the chronic ECA value was estimated by calculating the
geometric mean of the four NOEC values for the class Actinopterygii (638
mg/L).  Because both the ECA values for the host species are above the
respective numeric criterion, EPA makes a “not likely to adversely
affect” finding for the host species of the dwarf wedge mussel.

4.0  EFFECTS DETERMINATIONS  TC \l1 "4.0  EFFECTS DETERMINATIONS

4.1  No Effect–Notes  TC \l2 "4.1  No Effect–Notes

EPA is making a “no effect” determination for species that have
limited exposure to “waters of New Jersey.”  See Section 2.3 of this
document for a discussion on which species were selected as aquatic or
aquatic-dependent and which species were considered to have limited
exposure.

4.2  May Effect–Notes  TC \l2 "4.2  May Effect–Notes

This section contains the effect determinations for the species
addressed in this biological evaluation, which are found in Tables 4.1,
4.2 and 4.3 below.  These effect determinations are based on the data
and analyses in Section 3 of this document and are according to the
methodology described in Section 4 of the Methods Manual.  The effect
determinations for lead and TDS rely on surrogate data and accordingly
are a conservative estimate of the assessment effect concentration
(ECA).

The effect determinations were made on aquatic and aquatic-dependent
listed species according to the following rationale as given in Section
4.2 of the Methods Manual.

Aquatic Species: Rationale for the Effect Determination in the Lead
Analysis

Type of Criterion	If the effects concentration is:	Then the effects
determination is:

New Jersey freshwater lead acute

g/L)	38 g/L

<38 g/L	Not likely to adversely affect.

Likely to adversely affecta

New Jersey freshwater lead chronic

(5.4 g/L)	5.4 g/L

<5.4 g/L	Not likely to adversely affect.

Likely to adversely affecta

New Jersey saltwater lead acute

(210 g/L)	210 g/L

<210 g/L	Not likely to adversely affect.

Likely to adversely affecta

New Jersey saltwater lead chronic

(24 g/L)	24 g/L

<24 g/L	Not likely to adversely affect.

Likely to adversely affecta

EPA freshwater lead acute

(65 g/L)	65 g/L

<65 g/L	Not likely to adversely affect.

Likely to adversely affecta

EPA freshwater lead chronic

(2.5 g/L)	2.5 g/L

<2.5 g/L	Not likely to adversely affect.

Likely to adversely affecta

New Jersey freshwater TDS

(500 g/L)	500 g/L

<500 g/L	Not likely to adversely affect.

Likely to adversely affecta

Aquatic-dependent Species: Rationale for the Effect Determination in the
Lead Analysis

Estimated Residue Level in Diet 	If the chronic dietary effects
concentration is:	Then the effects determination is:

New Jersey Freshwater

5.88 mg/kg

<5.88 mg/kg	Not likely to adversely affect.

Likely to adversely affecta

New Jersey Saltwater

(16.31 mg/kg)	16.31 mg/kg

<16.31 mg/kg	Not likely to adversely affect.

Likely to adversely affecta

EPA Freshwater

(2.72 mg/kg)	2.72 mg/kg

<2.72 mg/kg	Not likely to adversely affect.

Likely to adversely affecta

a	Unless further evaluation or best professional judgment indicates it
is reasonable to conclude not likely to adversely affect.

4.2.1  Not Likely to Adversely Affect  TC \l3 "4.2.1  Not Likely to
Adversely Affect

Lead

According to Tables 4.1, 4.2 and 4.3, a “not likely to adversely
affect” finding was determined for all aquatic and aquatic-dependent
animal species.  In making the effect determinations for the food item
component, a ‘likely to adversely affect’ determination is made
where there is toxicity to a meaningful portion of the listed species’
diet, as indicated in Section 4.2 of the Methods Manual.

The chronic effect concentration for plants (see Section 3.3.4) exceeds
the freshwater and saltwater CCC by at least an order of magnitude.
Therefore, EPA is making a “not likely to adversely affect” finding
for the swamp pink, Helonias bullata, Kneiskern’s beaked rush,
Rhynchospora knieskernii and sensitive joint vetch, Aeschynomene
virginica.  SEQ CHAPTER \h \r 1 Table 4.1a. Results of Effects Analysis
for Freshwater Aquatic Listed Species (all units in g/L)

(New Jersey Dissolved Freshwater Lead Criteria: CMC = 38 g/L, CCC =
5.4 g/L)

Scientific Name	Saltwater v. Freshwater Exposure	Order	Acute

 ECAa

(μg/L)	Chronic

 ECAb

 (μg/L)	Chronic

 ECA’

 (μg/L)	Taxon Represented

by ECA	Food Items Analysisc	Adverse Effects

Family

	Items	Acute ECA

 (μg/L)	Chronic ECA

 (μg/L)

	Dwarf Wedge Mussel

Alasmidonta heterodon	FW	Unionoida

Unionidae	242S	39.3S	39.2	Mollusca	Detritus, plant matter

diatoms

	N/A

N/A

	289-262,449

1,077-7,924

	Not likely to adversely affect

Shortnose Sturgeon

Acipenser brevirostrum	FW	Acipenseriformes

Acipenseridae	191I	31.0I	30.9	Acipenser brevirostrum	oligochaetes,

aquatic insect larvae, plants,

snails,

shrimp, and crayfish	1,405

433-71,344

N/A

427-60,784

7.9-176,633	228

70-11,568

289-262,449

15-9,856

1-28,316	Not likely to adversely affect

a	Acute assessment effects concentration derived using divisor of 2.27.

b	Chronic assessment effects concentration based on the NOEC.

c	Ranges of toxicity values for food items are provided in the order the
food items appear.  Ranges are from text box (Section 3.5 this
document).

I	Estimate derived from an ICE model (lower bound of the 95% confidence
interval) at the species, genus, or family level. All selected models
are listed in Appendix A.

S	Estimate derived from the SSD model (5% percentile).  Value taken from
Table 3.2a.

Table 4.1b. Results of Effects Analysis for Freshwater Aquatic Listed
Species (all units in g/L)

(USEPA Freshwater Dissolved Lead Criteria based on a hardness of 100
mg/L as CaCO3 : CMC = 65 g/L, CCC = 2.5 g/L)

Scientific Name	Saltwater v. Freshwater Exposure	Order	Acute

 ECAa

(μg/L)	Chronic

 ECAb

 (μg/L)	Chronic

 ECA’

 (μg/L)	Taxon Represented

by ECA	Food Items Analysisc	Adverse Effects

Family

	Items	Acute ECA

 (μg/L)	Chronic ECA

 (μg/L)

	Dwarf Wedge Mussel

Alasmidonta heterodon	FW	Unionoida

Unionidae	225S	21.0S	20.6	Mollusca	detritus

diatoms

plant matter	N/A

N/A

N/A	289-262,249

1,077-7,924

289-262,249	Not likely to adversely affect

Shortnose Sturgeon

Acipenser brevirostrum	FW	Acipenseriformes

Acipenseridae	278I	25.9I	25.4	Acipenser brevirostrum	oligochaetes,

aquatic insect larvae, plants,

snails,

shrimp, and crayfish	503

33,323-225,556

N/A

424-64,641

8.4-1,481,633	59

3,101-20,993

289-262,249

10-6,016

1-137,897	Not likely to adversely affect

a	Acute assessment effects concentration derived using divisor of 2.27.

b	Chronic assessment effects concentration based on the NOEC.

c	Ranges of toxicity values for food items are provided in the order the
food items appear.  Ranges are from text box (Section 3.5 this
document).

I	Estimate derived from an ICE model (lower bound of the 95% confidence
interval) at the species, genus, or family level. All selected models
are listed in Appendix A.

S	Estimate derived from the SSD model (5% percentile).  Value taken from
Table 3.2.

Table 4.2a.  Analysis of Effects to Freshwater Aquatic-Dependent Species
 (Concentrations Based on Wet Weight)

(New Jersey Dissolved Freshwater Lead Criteria: CMC = 38 g/L, CCC =
5.4 g/L)

Species	BAF of food organism–

Freshwatera	Estimated Residue

levels in diet– Freshwater (mg/kg)b	Chronic EC (Dietary Effects
Concentration) (mg/kg)c	Food Items Analysisd

(all units in g/L, unless noted otherwise)	Adverse Effects

Item	Acute

ECA	Chronic

ECA

	Bald eagle

Haliaeetus leucocephalus	1089	5.88	100	fish and turtles;

small mammals, waterfowl and carrion	402-151,005

N/A	21-24,484

N/A	Not likely to adversely affect

Bog Turtle

Clemmys muhlenbergii	1089	5.88	100	oligochaetes,

insects,

seeds, plant leaves, carrion	1,405

433-71,344

7.9-325,901	228

70-11,568

5,438-262,449	Not likely to adversely affect

Indiana bat

Myotis sodalis	1089	5.88	100	insects	433-71,344	70-11,568	Not likely to
adversely affect

a	BAF values were determined on a wet weight basis.  The BAF of 1089 is
the 84th percentile of 14 BCF/BAFs determined for fish and
invertebrates.  The 84th percentile approximates one standard deviation
above the geometric mean .

b	Estimated residue value is the product of the default BAF value for
lead and the freshwater CCC value, 5.4 μg/L, then divided by
1000g/L, e.g., (5.4 g/L x 1089 L/kg) x 1mg/1000 g, assuming 1L
is approximately 1 kg (see Section 3.4.5).

c	Chronic EC values are the 16th percentile of the dietary effect values
for seven bird studies, one shrew study and one rat study.

d	Ranges of toxicity values for food items are provided in the order the
food items appear.  Ranges are from text box (Section 3.5 this
document), unless indicated otherwise.

Table 4.2b.  Analysis of Effects to Freshwater Aquatic-Dependent Species
 (Concentrations Based on Wet Weight)

(USEPA Freshwater Dissolved Lead Criteria based on a hardness of 100
mg/L as CaCO3: CMC = 65 g/L, CCC = 2.5 g/L)

Species	BAF of food organism–

Freshwatera	Estimated Residue

levels in diet– Freshwater (mg/kg)b	Chronic EC (Dietary Effects
Concentration) (mg/kg)c	Food Items Analysisd

(all units in g/L, unless noted otherwise)	Adverse Effects

Item	Acute

ECA	Chronic

ECA

	Bald eagle

Haliaeetus leucocephalus	1089	2.72	100	fish and turtles;

small mammals, waterfowl and carrion	1,076-110,412

N/A	131-10,276

N/A	Not likely to adversely affect

Bog Turtle

Clemmys muhlenbergii	1089	2.72	100	oligochates,

insects,

seeds, plant leaves, carrion	503

33,323-225,556

8.4-1,481,633	59

3,101-20,993

1-144,600	Not likely to adversely affect

Indiana bat

Myotis sodalis	1089	2.72	100	insects	33,323-225,556

	3,101-20,993	Not likely to adversely affect

a	BAF values were determined on a wet weight basis.  The BAF of 1089 is
the 84th percentile of 14 BCF/BAFs determined for fish and
invertebrates.  The 84th percentile approximates one standard deviation
above the geometric mean.

the product of the default BAF value for lead and the freshwater CCC
value, 2.5 μg/L, then divided by 1000g/L, e.g., (2.5 g/L x 1089
L/kg) x 1mg/1000 g, assuming 1L is approximately 1 kg (see Section
3.4.5).

c	Chronic EC values are the 16th percentile of the dietary effect values
for seven bird studies, one shrew study and one rat study.

g/L, CCC = 24 g/L)

Species	BAF of food organism–

Freshwatera	Estimated Residue

levels in diet– Freshwater (mg/kg)b	Chronic EC (Dietary Effects
Concentration) (mg/kg)c	Food Items Analysisd

(all units in g/L, unless noted otherwise)	Adverse Effects

Item	Acute

ECA	Chronic

ECA

	Northeastern beach tiger beetle

Cicindela dorsalis dorsalis	679.5	16.31	431	beach arthropods,

dead amphipods, marine fish and crabs	229-157,104

229-157,104

	16.2 - 25,473

16.2 - 25,473	Not likely to adversely affect

Piping plover

Charadrius melodus	679.5	16.31	100	marine worms;

marine mollusks;

marine crustaceans and insects	503-3,718

200-209,471

229-157,104

	81.5 - 602.9

32.3 - 208,269

16.2 - 25,473	Not likely to adversely affect

Roseate tern

Sterna dougallii dougallii	679.5	16.31	100	fresh and marine small fish
and minnows	314-57,167	50.9 - 9,269	Not likely to adversely affect

Hawksbill sea turtle

Eretmochelys imbricata	679.5	16.31	100	jellyfish, sponges,

sessile organisms;

marine algae	202-4,064	32.7 - 658.9

19 - 3,804	Not likely to adversely affect

Kemp's ridley sea turtle

Lepidochelys kempi	679.5	16.31	100	blue crabs and other marine
crustaceans	229-157,104

	16.2 - 25,473	Not likely to adversely affect

Leatherback turtle

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愀Ĥ؀fish and 'soft-bodied' sea animals	202-4,064	32.7 - 658.9	Not
likely to adversely affect

Loggerhead turtle

Caretta caretta	679.5	16.31	100	marine sponges;

mollusks;

horseshoe crabs	202-4,064

200-209,471

229-157,104	32.7 - 658.9

32.3 - 208,269

16.2 - 25,473	Not likely to adversely affect

a  BAF values were determined on a wet weight basis.  The BAF of 679.5
is the 84th percentile of BCF/BAFs determined for fish and
invertebrates.  The 84th percentile approximates one standard deviation
above the geometric mean.

b  Estimated residue value is the product of the BAF value for lead and
the freshwater CCC value, 24 μg/L, then divided by 1000g/L, e.g.,
(24 g/L x 679.5 L/kg) x 1mg/1000 g, assuming 1 L is approximately
1 kg (see Section 3.4.5).

c   Several chronic dietary toxicity values exist for surrogate
aquatic-dependent species where the dose has been expressed in the
desired units of mg Pb/kg food (prey item).  The 16th percentile value
of 100 mg/kg food was selected as the NOEC value for the analysis.

d  Ranges of toxicity values for food items are provided in the order
the food items appear.  Ranges are from text box (Section 3.5 this
document), unless indicated otherwise.

Total Dissolved Solids

The two listed freshwater species that are the focus of the biological
evaluation for TDS are the dwarf wedge mussel and the shortnose
sturgeon.  The closest taxonomic grouping in Table 3.3 for the shortnose
sturgeon is Class Actinopterygii which has five mean LC50 values ranging
from 4,243 to 8,906 mg/L; and four mean NOECs (range, 300 to 1,348
mg/L).  The prime habitat areas for shortnose sturgeon are river mouths,
tidal rivers, estuaries, and bays suggesting this species is tolerant to
high levels of TDS.  Shortnose sturgeon do migrate upstream to spawn to
waters most likely with lower TDS levels.  TDS has been associated with
effects on egg hardening in salmonids, but in a review of TDS effects on
salmonids as well as other aquatic life by Scannell and Jacobs (2001),
the authors noted fertilization and hatching rates in coho and chum
salmon are significantly reduced beginning in the range of 750 mg/L.
Although little is known of the spawning requirements of the shortnose
sturgeon, a criterion of 500 mg/L should be protective of young
production based on the response of sensitive salmonid species.  Based
on the toxicity data for Class Actinopterygii in Table 3.3 and its
preference for high TDS waters, EPA is making a “not likely to
adversely affect” finding for New Jersey’s TDS criteria on the
shortnose sturgeon.

Regarding the dwarf wedge mussel, Table 3.3 lists an LC50 of >2000 mg
KCl/L for a mussel in the same family (Unionidae), the threehorn
wartyback.  Since no chronic data are available for mollusks, the
surrogate NOECs for invertebrates are 372 mg/L (Daphnia magna) and 1,543
mg/L (Chironomus tentans).  Daphnids appear to be one of the more
sensitive groups to TDS with D. magna and Ceriodaphnia dubia all having
mean LC50 values less than 2000 mg/L (Table 3.3).  This latter
observation is relevant to the New Jersey TDS criteria in that C. dubia
is a test species in New Jersey’s whole effluent toxicity (WET)
program and part of the TDS criterion requires compliance with WET
limitations (see Section 2.2.1).  Based on the ability of the WET
program to control TDS and the apparent lack of sensitivity of Unionid
mussels to TDS, EPA is making a “not likely to adversely affect”
finding for New Jersey’s TDS criteria on the dwarf wedge mussel.

For the plants that may be exposed to TDS, the potential chronic effect
concentration exceeds the freshwater CCC by almost three orders of
magnitude.  Therefore, EPA is making a “not likely to adversely
affect” finding for the swamp pink, Helonias bullata, Kneiskern’s
beaked rush, Rhynchospora knieskernii and sensitive joint vetch,
Aeschynomene virginica.

4.2.2 Species Requiring Further Evaluation  TC \l3 "4.2.2 Species
Requiring Further Evaluation

Lead

None.  No particular group of organisms as a whole appears to be most
sensitive, such that further evaluation would be needed.

Total Dissolved Solids

None.  Neither the dwarf wedge mussel nor the shortnose sturgeon appear
to be sensitive to TDS, such that further evaluation would be needed.

5.0	ASSESSING EFFECTS OF THE NEW JERSEY LEAD AND TOTAL DISSOLVED SOLIDS
CRITERIA ON DESIGNATED CRITICAL HABITAT  TC "5.0	ASSESSING EFFECTS OF
THE NEW JERSEY PROPOSED LEAD AND TOTAL DISSOLVED SOLIDS CRITERIA ON
DESIGNATED CRITICAL HABITAT" \f C \l "1"

None of the listed species addressed in this biological evaluation have
a critical habitat designated in New Jersey.  Accordingly, where EPA has
made a “not likely to adversely affect” for a listed species, EPA
will similarly make a “not likely to adversely affect” determination
for its critical habitat.

REFERENCES  TC \l1 "REFERENCES

Allen, P. 1994. Accumulation profiles of lead and the influence of
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exposure.  Toxicol. Environ. Chem. 44(1-2):101-112.

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Amiard, J.C., H. Ettajani, A.Y. Jeantet, C. Ballan-Dufrancais and C.
Amiard-Triquet. 1995. Bioavailability and toxicity of sediment-bound
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Atchinson, G.J., et al. 1977.  Trace metal contamination of bluegill
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Borgmann, Kramar, and Loveridge, 1978.  Rates of mortality, growth, and
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Custer, T.W., J.C. Franson, and O.H. Pattee. 1984. Tissue Lead
Distribution and Hematologic Effects in American Kestrels (Falco
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Damron, B.L., C.F. Simpson, and R.H. Harms. 1969. The Effect of Feeding
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Denneman, C.A.J. and N.M. van Straalen 1991.  The toxicity of lead and
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Biochem.
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