20080868 Ver 2_Section II B Q2 Character 2020 PCS Creeks Report_20210701

B. Question 2-Has mining altered the geomorphic or vegetative character of
the creeks?
Geomorphology: Current geomorphology of Jacks Creek, Tooley Creek, and Huddles
Cut has not been compared to baseline geomorphology. Exact locations of the 1998 baseline
measurements were not spatially explicit, so follow-up measurements are difficult to collect in
the same place. Although effort to collect useful data at baseline was the goal, the measures
used were subjective. Replication of the effort by different biologists may indicate a "change"
driven by interpretive bias. For example, the amount of water in the system at the time of
measurement could affect two measures considerably: floodplain width and adjacent slope.
Nonetheless, baseline geomorphology was described for all the new creeks in the study in
2011, in 2013 when the last two creeks north of NC Highway 33 were brought into the study,
and in 2018 for the creeks south of Highway 33 all using the same measures as in 1998.
Vegetation: Due to transition years, discussed in Section I.A.2.0 of this report, post -Mod
Alt L years for vegetation do not match post -Mod Alt L years for other parameters. The
following impact creeks have pre- and post -Mod Alt L vegetation data: Jacks Creek, Jacobs
Creek, Drinkwater Creek, Tooley Creek, Huddles Cut, (main and western prong analyzed
separately) Porter Creek, and DCUT11.
Broomfield Swamp Creek: Monitoring for Broomfield Swamp Creek began in 2019 and
2020 was the second year of pre -Mod Alt L. No statistics were computed with only two years of
vegetation data.
SCUT1 (control): The unnamed tributary on South Creek, SCUT1, is the control for
Broomfield Swamp Creek and is monitored in conjunction with Broomfield Swamp Creek.
Jacks Creek: Approximately 150.36 acres remain of the pre -Mod Alt L —317-acre
drainage basin for Jacks Creek. Vegetation data include 12 years of pre -Mod Alt L (1998-2005
and 2011-2014) and four years of post -Mod Alt L (2017-2020); no vegetation data were
collected in transition years 2015 and 2016.
A cluster analysis based on species presence/absence data by year with a similarity
profile test (SIMPROF) showed seven clusters: A: 1998, B: 2001-2005, C: 1999-2000, D: 2011,
E: 2012, F: 2013-2014, and G: 2017-2020 (Figure II-B1). Early years clustered separately from
recent years and all post -Mod Alt L years were in the same cluster; however, an analysis of
similarities (ANOSIM) found no statistically significant difference between pre- and post -Mod Alt
L years for species presence/absence data. A similarity percentages (SIMPER) analysis based
on the Bray -Curtis similarity measure for species composition showed 35.70 percent
dissimilarity between pre- and post -Mod Alt L years. Seven species had a dissimilarity
contribution above 2 percent, one was tolerant of brackish conditions and found only after 2011.
The highest individual contributions to the dissimilarity between pre- and post -Mod Alt L data
were two species each with 2.83 percent: Alabama supplejack (Berchemia scandens), a
brackish intolerant species present in all pre -Mod Alt L years and bull -tongue arrowhead
(Sagittaria lancifolia), a brackish tolerant species present only in post -Mod Alt L years. Two of
the seven species that contributed to the dissimilarity between pre- and post -Mod Alt L data
were non -wetland species; eastern red -cedar (Juniperus virginiana) present in more recent
years (2014, 2017-2020) and Canadian black -snakeroot (Sanicula canadensis) present in 1998-
2005 and 2012.
The average percent of dominant species in the herbaceous and woody vine/shrub
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strata intolerant of brackish conditions among all transects, was higher for pre -Mod Alt L years
(50.3) than the post -Mod Alt L years (28.3) (Tables II-B1 a). A t-test of all transects combined
showed that there was a significant difference between pre- and post -Mod Alt L. Jacks Creek
showed significantly lower percentages of brackish intolerant dominants in more recent years
(2011-2014; p=<0.01 and 2020 p=0.01 than earlier years (1998-2005), which suggests a
change in vegetation before Mod -Alt L impact (Figure II-B2). When pre- and post -Mod Alt L
percentages of dominants intolerant of brackish were compared for transects individually, three
of the five transects were significantly different (JW3 p=0.02, JW5 p=0.02, and JW9 p=0.03)
(Figure II-B3). The most downstream transects, JW9 on the north prong and JW3 and JW5 on
the main prong, experienced the most notable change in the herbaceous and shrub layers in
more recent years than other transects for Jacks Creek. Common reed (Phragmites australis),
first documented at JW3 in 2012, JW5 in 2013, and JW9 in 2017, now covers nearly 100
percent of both JW3 and JW5. The influx of common reed contributed to lower percentages of
brackish intolerant dominants and decreased species richness (but not statistically significant)
over recent years. The most upstream transect on the north prong, JW7, had higher averages
for the percent of brackish intolerant dominants for post -Mod Alt L years.
To further explore potential pre- vs. post -Mod Alt L data, a t-test compared the number
of herbaceous and shrub dominants in Jacks Creek. When transects were combined there was
no significant difference for shrub dominants; however, herbaceous dominants were significantly
different (p=0.04). For the herbs, two of the five transects had significant fewer dominants post -
Mod Alt L (JW3, p=<0.01 and JW5, p=0.01) (Figure II-B4). For the shrubs, two of the five (JW3,
p=<0.01 and JW9, p=0.03) had significantly more dominants post -Mod Alt L and another (JW2,
p=<0.01) had fewer (Figure II-B5).
The total percentages of non -wetland species (species in either FACU or UPL category)
in all transects combined varied from year to year with no discernible pattern (Table II-B2). The
percent of non -wetland species for pre -Mod Alt L years ranged from 4.0 (2011) to 11.3 (2002),
with an average of 8.8; post -Mod Alt L range was 8.7 (2017) to 12.2 (2019) with an average of
10.1. The only instance of a non -wetland dominant was at one transect in 2000. Jurisdictional
wetland status of vegetation at Jacks Creek does not appear altered by the mine.
Jacobs Creek: Approximately 202.45 acres remain of the pre -Mod Alt L —524-acre
drainage basin. Vegetation data include three years of pre -Mod Alt L data (2011-2013) and four
years of post -Mod Alt L data (2017-2020) collected in one transect located between the two
Level TROLLs.
A cluster analysis based on species presence/absence data by year with a similarity
profile test (SIMPROF) showed four clusters: A: 2011, B: 2012, and C: 2013, and D: 2017-2020
(Figure II-B6). There was a significant difference between pre- and post -Mod Alt L years for
species presence/absence data when an ANOSIM was used (p=0.03). A SIMPER analysis
based on the Bray -Curtis similarity measure for species composition showed 46.03 percent
dissimilarity between pre- and post -Mod Alt L years, the second highest dissimilarity among all
creeks surveyed in 2020 with post -Mod Alt L vegetation data. The individual contributions
between pre- and post -Mod Alt L data at Jacobs Creek were three species with 7.79 percent,
one with 6.00 percent, three with —5 percent and the remaining seven species with less than 5
percent. The three species with 7.67 percent occurred only in post -Mod Alt L years; two of
which (American beautyberry, Callicarpa americana and summer grape, Vitis aestivalis) were
non -wetland species.
For all survey years, only brackish intolerant species were dominants in the herbaceous
or woody vine/shrub strata; therefore, to date there is no significant difference between
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percentages of dominant species intolerant of brackish conditions for pre- and post -Mod Alt
years (Table II-B1a). A t-test showed no statistically significant pre- vs. post -Mod Alt L
differences in the number of dominants for either the herb or shrub stratum in Jacobs Creek.
The highest percent of non -wetland species for Jacobs Creek was in 2020 (26.7),
followed closely by 2018 (23.5) (Table II-B2). Although the post -Mod Alt L average percent of
non -wetland species (22.5) was higher than pre -Mod Alt L (9.7), there was no significant
difference (p=0.06). No dominants were non -wetland species in 2011, 2017, or 2020; one-
fourth of dominants were in 2013 and 2019, one-third were in 2018, and half were in 2012
(Table II-B1a). Jurisdictional wetland status of vegetation at Jacobs Creek does not appear to
have been altered by the mine.
Drinkwater Creek: Approximately 153.32 acres remain of the pre -Mod Alt L —372-acre
drainage basin. One year of pre -Mod Alt L data (2011) and four years of post -Mod Alt L data
(2016-2019) have been collected. Since 2020 was a "skip" year, vegetation was not sampled.
Tooley Creek: Approximately 257 acres remain of the pre -Mod Alt L —571-acre drainage
basin. Pre -Mod Alt L years include 1998-2001 and 2010-2011; however, Hurricane Irene debris
prevented or limited access and only the eastern prong of Tooley Creek was surveyed in 2011
(TW1 and TW3). Post -Mod Alt L vegetation was surveyed in all transects 2015-2018 and 2020;
2019 was the first "skip" year.
Cluster analysis on Tooley Creek vegetation grouped the 11 years of data into six
clusters: A: 2011, B: 2015, C: 2016-2018, 2020, D: 1998-1999, E: 2010 and, F: 2000-2001
(Figure II-B7). Due to inaccessibility after Hurricane Irene, data were collected for two transects
out of four in 2011, which may be why that year has clustered alone every year since. A
significant difference between pre- and post -Mod Alt L years for species presence/absence data
was found when ANOSIM was used (p=0.01); fewer species were found post -Mod Alt L (Table
II-B2). A SIMPER analysis based on the Bray -Curtis similarity measure for species composition
showed 46.90 percent dissimilarity between pre- and post -Mod Alt L years, the highest
dissimilarity among all creeks surveyed in 2020 with post -Mod Alt L vegetation data. For Tooley
Creek, there were five species with a contribution greater than 2 percent. The three species
with the highest individual contribution percent (2.60) were only present during all post -Mod Alt
L years. Two of the three species, sturdy bulrush (Bolboschoenus robustus) and common reed,
were brackish tolerant and both were present at TW3; one of the three species was northern
dewberry (Rubus flagellaris), a non -wetland species. Coast cockspur (Echinochloa walteri), a
brackish tolerant species, had the next highest contribution percent (2.18) and was present in
2010 and all post -Mod Alt L years. Of the total 98 species identified within vegetation transects
at Tooley Creek, 41 were found in both pre- and post -Mod Alt years. Of the 41 species found
only in the pre -Mod Alt L years, 28 (68.3 percent) were brackish intolerant. Of the 16 species
found only in the post -Mod Alt L years, seven (43.75 percent) were brackish intolerant. Even
when 2011 species data or individuals identified only to genus were excluded from the ANOSIM
test, pre- and post -Mod Alt L species presence/absence results were significantly different.
A t-test to compare percentages for all transects of dominant herbaceous and woody
vine/shrub species intolerant of brackish conditions for pre- and post -Mod Alt L Tooley Creek
showed the two data sets were not significantly different. The percent of brackish intolerant
dominants in pre -Mod Alt L years across all transects ranged from 0 to 100, with an average of
68.5; percent of brackish intolerant dominants in post -Mod Alt L years across all transects
ranged from 0 to 100, with an average of 57.4 (Table II-B1a). For individual transects, there
was a significant difference for pre- and post -Mod Alt L percentages of dominants intolerant of
brackish conditions at TW1 and TW4 (Figure II-B8). For TW4, percentages of brackish
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intolerant species were significantly lower in post -Mod Alt L, with a weak correlation between
years and percentages (p=<0.01, r2=0.51) (Figure I I-B9). The pre -Mod Alt L average was 93.3
percent and post -Mod Alt L was 51.3 percent (Table I I-B1 a). TW4 is located on the western
prong and is the most downstream of all transects for Tooley Creek. The first occurrence of
brackish tolerant dominants was 2010, the fifth and final year of pre -Mod Alt L vegetation data
for the western prong. At TW1, the most upstream transect on the eastern prong, percentages
in post -Mod Alt L were also significantly lower, with a weak correlation between years and
percentages (p=0.02, r2=0.43) (Figure ll-B10). An increase in percent cover and number of
stems for giant cane (Arundinaria gigantea) since 2001 has led to a decrease in the number of
dominant species in the shrub layer (see Section III-E). The open canopy since Hurricane Irene
likely led to an increase in the number of dominant species in the herbaceous layer; more of
those dominants were brackish tolerant species. These two factors seem to have affected the
percentages of brackish intolerant dominants in recent years. Unlike the other transects at
Tooley Creek, TW3 has higher average percent of brackish intolerant species post -Mod Alt L
(26.3) than pre -Mod Alt L years (20.4), but not significantly (Table II-B1 a).
A t-test compared the pre- vs. post -Mod Alt L number of herbaceous and shrub
dominants in Tooley Creek on a combined and an individual transect basis. For the combined
herb stratum, there was no statistically significant difference, but one of the four transects was
significantly different post -Mod Alt L individually. Significantly fewer dominant herbs were found
post -Mod Alt L in TW6 (p=0.03) (Figure II-B11). For the shrub stratum, when combined, post -
Mod Alt L transects in Tooley Creek had significantly fewer dominants (Figure II-B12, p=0.01),
and two of the four transects individually had significant differences; TW1 (p=0.02) and TW6
(p=0.03) had significantly fewer post -Mod Alt L shrub dominants (Figure II-B13).
The percentages of non -wetland species in all transects combined for pre -Mod Alt L data
ranged from 0 (2011) to 17.8 (1999), with an average of 12.8 (Table II-B2). The percentages of
non -wetland species for post -Mod Alt L data ranged from 11.9 (2017) to 18.2 (2015), with an
average of 13.8. Tooley Creek was the only creek with UPL species every post -Mod Alt L year
while the only other instance of UPL species post -Mod Alt L was at Huddles Cut West in 2014.
The only instance of a non -wetland dominant for Tooley Creek was small dog fennel
(Eupatorium capillifolium) at TW4 in 2015. Jurisdictional wetland status of the vegetation at
Tooley Creek does not appear altered by the mine.
Long Creek (control): Vegetation data collection began at one transect for Long Creek
in 2011 and has been collected every year since. Cluster analysis for the 10 years of vegetation
data resulted in five clusters in this control creek: A: 2013-2015, B: 2020, C: 2018-2019, D:
2016-2017, and E: 2011-2012 (Figure II-B14). The percent of brackish intolerant dominants at
Long Creek in all years ranged from 33.3 to 66.7, with an average of 55.3 (Table I I-B1 b). The
percentages of non -wetland species in Long Creek ranged from 0.0 (2011, 2013, 2015, and
2020) to 12.5 (2012) with an average of 3.2 (Table II-B2). A non -wetland species has never
been a dominant at Long Creek.
Huddles Cut Main Prong: Mod Alt L activities in the Huddles Cut drainage basin ended
in 2011 and approximately 289.46 acres of the approximately 552 acres in the pre -Mod Alt L
basin remain. Pre -Mod Alt L vegetation survey years were 1998-2001, 2007-2009; post -Mod Alt
L vegetation survey years were 2013-2014 and 2016-2019; 2020 was the first "skip" year.
Huddles Cut West Prong: Drainage basin reduction and pre- and post -Mod Alt L data
collection years were the same as Huddles Cut main prong. Before the last year of pre -Mod Alt
monitoring (2009), half of the HWW2 transect and the entire transect at HWW10 were
eliminated by permitted mine activities. Then in 2012, the last of the three transition years, a
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surface depression appeared in the middle of HWW8, eliminating one of the 10 vegetation plots.
Porter Creek: Approximately 840.22 acres remain of the pre -Mod Alt L -2,438-acre
drainage basin. Mod Alt L activities began in 2016 and ended in 2018; 2019 and 2020
represent post -Mod Alt L data years with five other years of pre -Mod Alt L data (2011-2015).
The ANOSIM found no statistically significant difference between pre- and post -Mod Alt L years
for species presence/absence data. A SIMPER analysis based on the Bray -Curtis similarity
measure for species composition showed 42.87 percent dissimilarity between pre- and post -
Mod Alt L years, the third highest dissimilarity among all creeks surveyed in 2020 with post -Mod
Alt L vegetation data. Cluster analysis based on species presence/absence data for seven
years grouped into four clusters: A: 2011, B: 2012, C: 2013-2014, and D: 2015, 2019-2020
(Figure II-B15). For all survey years, percent brackish intolerant dominants ranged from 33.3 to
100.0, pre -Mod Alt L years percentages also ranged from 33.3 to 100.0 with an average of 85.0
while post -Mod Alt L years ranged from 66.7 to 100.0 with an average of 91.7 (Table I I-B1 a).
The percent of non -wetland species for pre -Mod Alt L data ranged from 0.0 (2011, 2013) to 7.4
(2014), with an average of 3.1. The post -Mod Alt L percent of non -wetland species was 7.5
(Table II-B2). Jurisdictional wetland status of vegetation at Porter Creek does not appear to
have been altered by the mine.
Duck Creek (control): Vegetation data collection began at one transect for Duck Creek
in 2011 and has been collected every year since except 2018. Cluster analysis for the nine
years of vegetation data resulted in five clusters in this control creek: A: 2011, B: 2015, C:
2012-2014, D: 2016, and E: 2017 and 2019-2020 (Figure II-B16). The percent of brackish
intolerant dominants at Duck Creek in all years ranged from 66.7 to 100.0, with an average of
95.7 (Table II-B1 b). The percentages of non -wetland species in Duck Creek ranged from 0.0
(2016) to 42.9 (2013) with an average of 5.1 (Table II-B2).
DCUT11: Approximately 81.4 acres remain of the pre -Mod Alt L -166-acre drainage
basin. Pre -Mod Alt L years include 2013-2017. Mod Alt L impacts occurred in 2018 through
January 2019 making 2020 the first year of post -Mod Alt L vegetation data collection.
Cluster analysis on the five years of pre- and one year of post -Mod Alt L vegetation data
for DCUT11 resulted in two clusters: A: 2013-2014 and B: 2015-2016 and 2020 (Figure II-B17).
The ANOSIM found no statistically significant difference between pre- and post -Mod Alt L years
for species presence/absence data. A SIMPER analysis based on the Bray -Curtis similarity
measure for species composition showed 21.01 percent dissimilarity between pre- and post -
Mod Alt L years, the lowest dissimilarity among all creeks with post -Mod Alt L vegetation data.
The pre -Mod Alt L percent of brackish intolerant dominants ranged from 71.4 to 100, with an
average of 81.9 while 2020 had 83.3 percent (Table I I-B1 a). The first year of post -Mod Alt L
(2020) was the first time a non -wetland plant (Japanese honeysuckle) was a dominant at
DCUT11 (Table I I-B1 a). Pre -Mod Alt L percent of non -wetland species at DCUT11 ranged from
0.0 (2015) to 10.0 (2017), with an average of 5.3 and 2020 had 13.0 percent (Table II-B2).
DCUT19 (control): Vegetation data collection began at one transect for DCUT19 in
2013-2017 and 2020. Cluster analysis for the six years of vegetation data resulted in two
clusters in this control creek: A: 2013-2014, B: 2015-2017 and 2020 (Figure II-B18). The
percent of brackish intolerant dominants at DCUT19 in all years ranged from 85.7 to 100.0, with
an average of 95.2 (Table II-B1 b). The percentages of non -wetland species in DCUT19 ranged
from 0.0 (2015 and 2016) to 14.3 (2013-2014 and 2020) with an average of 9.2 (Table II-B2).
The non -wetland species, Japanese honeysuckle, has been a dominant at DCUT19 for four of
the six surveys.
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Impact to Control Creek Summary Vegetation Discussion: Vegetation transects at
Jacks Creek, Tooley Creek, Huddles Cut, and Long Creek (control) are all between 3,000 and
5,000 feet (0.5 to 0.9 mile) from the mouth of their respective creek. Post -Mod Alt L averages
for percent of brackish intolerant dominants at Jacks Creek with all transects combined (28.3)
compared to Long Creek (45.8) using the post- years for Jacks Creek shows a greater change
in brackish intolerant dominant species at the impact creek. The post -Mod Alt L average for
percent of brackish intolerant dominants at Tooley Creek (57.4) for all transects combined was
nearly the same as Long Creek (54.0) using the post- years of Tooley Creek. The floodplain
width (6 to 10 feet) near the vegetation transect in Long Creek is narrower than any other creek
in the study by several factors; floodplain width in most other creeks is >25 feet and for several
creeks is greater >100 feet. The canopy cover is greater at the Long Creek transect (50
percent) than at all transects for Jacks Creek, Tooley Creek, and Huddles Cut. The vegetation
transect at Long Creek is along a small narrow prong off the main creek and elevation seems to
be also higher than either Jacks Creek or Huddles Cut, so storm surge and wind have less
influence than some transects at Jacks Creek, Tooley Creek, and Huddles Cut. The canopy at
Long Creek did not appear affected by Hurricane Irene.
To compare post -Mod Alt L data from the five impact creeks to the data from three
control creeks (Long Creek, DCUT19, and Duck Creek) for the same years, percent of species
in three wetland status categories (obligate [OBL], facultative wetland [FACW], and facultative
[FAC]) was displayed (Figure II-B19). The study included no control creek vegetation prior to
2011 and 2018 Duck Creek vegetation was not sampled. The only apparent trend with most
creeks was the FAC species were mostly in decline (Figure II-B19). Jacobs Creek decreased in
OBL species while Tooley Creek increased in OBL species. When comparing the control Long
Creek with each impact creek OBL species increased and FACW species decreased. Jacks
Creek has more transects, which might be why it showed the most variability. Jacks Creek
showed an increase of OBL species and decreased FACW species pre -Mod Alt L and
decreased OBL and increased FACW post -Mod Alt L. Pre -Mod Alt L salinity was significantly
higher than post -Mod Alt L for the upstream and downstream Aqua TROLL stations at Jacks
Creek, Jacobs Creek, Drinkwater Creek, Tooley Creek, Porter Creek, and DCUT11. The two
upstream stations at Huddles Cut, one located on each prong, had statistically significantly
lower salinity pre -Mod Alt L than post -Mod Alt L. The downstream station at Huddles Cut at the
creek mouth did not show any significant difference between pre- and post -Mod Alt L salinity.
Section III -A contains more information on salinity at the creeks.
The annual rainfall from 1998-2005 and 2007-2020 for the NOAA station Aurora 6 N
ranged from 36.16 inches (2007) to 71.10 inches (2003) and the annual average was 51.96
inches (Table I-F2). Total annual rainfall for 2020 (62.86 inches) was higher than the average
rainfall for all years by 10.9 inches. Annual rainfall data was also collected from six rain gauges
to account for spatial variability. Although annual rainfall totals from the six rain gauges have
been different from one another every year, totals typically differ by only several inches.
Because annual rainfall can affect hydrology and salinity and both strongly influence the
composition of species at the creeks, it is an important factor to consider.
Hydrology: Many wells show similar behavior in most creeks, with upstream
hydroperiods typically shorter than downstream hydroperiods. Even though many wells
occasionally record multiple wetland hydroperiods throughout the growing season, only the
longest one was used in comparisons and statistical tests. Pre- and post -Mod Alt L data sets
for hydrology data are longer than those of the vegetation data in the same creek. The creeks
with post -Mod Alt L hydrology data include Jacks Creek (six years of post- data), Jacobs Creek
(seven years of post- data), Drinkwater Creek (eight years of post- data), Tooley Creek (nine
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years of post- data), Huddles Cut (11 years of post- data), Porter Creek (five years of post -
data), and DCUT11 (three years of post- data). In 2020, there were four significant differences
between pre- and post -Mod Alt L data at impacted creeks: one well at Drinkwater Creek
recorded shorter hydroperiods post -Mod Alt L, one well at Tooley Creek recorded longer
hydroperiods post -Mod Alt L, one well at DCUT11 recorded shorter hydroperiods post -Mod Alt
L, and one well on the main prong of Huddles Cut recorded longer hydroperiods post -Mod Alt L.
Although it is not the only driver, rainfall is a key factor in hydrology analysis because it
can influence hydrology, at least to some degree, in most wetland systems, particularly in the
upper basin. Rainfall at Porter Creek (p=0.025) and DCUT11 (p=0.031) were both significantly
higher post -Mod Alt L than pre -Mod Alt L. Rainfall was not significantly different between pre -
and post -Mod Alt L years at any other creek. For impact creeks, total annual rainfall during
hydrology monitoring years was highest in 2020 at Jacks Creek, Jacobs Creek, Drinkwater
Creek, Porter Creek, and DCUT11. Tooley Creek and Huddles Cut had the highest rainfall in
2003 (Table I-F2). At all creeks, annual rainfall was higher in 2020 than 2019. From 2000-
2020, four years did not have any weeks with a drought status (2000, 2003, 2004, and 2015),
seven years had less than 25 percent of the year with a drought status (2005, 2014, 2016,
2017, and 2018-2020), and three years had more than 75 percent of the year with a drought
status (2002, 2007, and 2008) in the area surrounding South Creek (Table 1-D1).
Jacks Creek hydrology data include 10 years of pre -Mod Alt L data (2000-2005 and
2011-2014) and six years of post -Mod Alt L data (2015-2020). Post -Mod Alt L average annual
rainfall within Jacks Creek was 7.79 inches higher than pre -Mod Alt L. Of the 14 wells at Jacks
Creek, seven had a longer mean hydroperiod post -Mod Alt L and seven had a shorter mean
hydroperiod post -Mod Alt L. The mean hydroperiod for all Jacks Creek wells during pre -Mod Alt
L (144.9 days) was slightly lower than post -Mod Alt L (151.6), but not significantly different.
There was no significant difference between pre- and post -Mod Alt L hydroperiods for individual
or combined Jacks Creek well data.
Jacobs Creek hydrology data include three years of pre -Mod Alt L data (2011-2013) and
six years of post -Mod Alt L data (2014-2020). Post -Mod Alt L average annual rainfall within
Jacobs Creek was 8.45 inches higher than pre -Mod Alt L. The only year that wells recorded a
wetland hydroperiod was in 2014, which was also the first year of post -Mod Alt L data and fourth
highest total annual rainfall of all monitoring years (Table I-F2). There was no significant
difference between pre- and post -Mod Alt L hydroperiods for individual or combined Jacobs
Creek well data.
Drinkwater Creek hydrology data include two years of pre -Mod Alt L data (2011-2012)
and eight years of post -Mod Alt L data (2013-2020). Post -Mod Alt L average annual rainfall
within Drinkwater Creek was 4.09 inches higher than pre -Mod Alt L. When wells were
compared individually, post -Mod Alt L hydroperiod means were longer for two of the three wells,
including the well in the stream bed, while the other well (DWW1A) had a shorter mean
hydroperiod post -Mod Alt L (Figure II-B20). Pre- and post -Mod Alt L hydroperiods were
significantly different for DWW1A (p=0.012). When well data were combined, the post -Mod Alt
L mean hydroperiod length was higher than pre -Mod Alt L by approximately 6.6 days, though
hydroperiod length ranges were similar and not significantly different.
Tooley Creek hydrology data include four years of pre -Mod Alt L data (2000-2001 and
2010-2011) and nine years of post -Mod Alt L data (2012-2020). Post -Mod Alt L average annual
rainfall within Tooley Creek was 3.24 inches higher than pre -Mod Alt L. When wells were
compared individually, post -Mod Alt L hydroperiod means were longer for two of the three wells
on the eastern prong (TW1 and TW2 ) and two of the three wells on the western prong (TW4
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and TW5) while the other wells (TW3 and TW6) had shorter mean hydroperiods post -Mod Alt L
(Figure II-B21). Pre- and post -Mod Alt L hydroperiods were significantly different for TW5
(p=0.007). When well data were combined, the post -Mod Alt L mean hydroperiod length was
higher than pre -Mod Alt L by approximately 12.5 days, though hydroperiod length ranges were
similar and not significantly different.
Huddles Cut hydrology data include five years of pre -Mod Alt L data (2000-2001 and
2007-2009) and 11 years of post -Mod Alt L data (2010-2020). Post -Mod Alt L average annual
rainfall within Huddles Cut was 3.29 inches higher than pre -Mod Alt L. Longest combined
hydroperiods were significantly longer post -Mod Alt L in the west prong (p=<0.001) and the
main prong (p<0.001) (Figure II-B22). When wells on the main prong were compared
individually, post -Mod Alt L hydroperiod means were longer for all 12 wells, only one was
significantly longer (HMW7, p=<0.001) (Figure II-B23). The mean length of the longest
hydroperiod for all wells was 213.4 pre -Mod Alt L and 239.8 post -Mod Alt L, a difference of
approximately 26.4 days. When wells on the western prong were compared individually, post -
Mod Alt L hydroperiod means were shorter for one of the eight wells (HWW8), while the other
seven had longer mean hydroperiods post -Mod Alt L (HWW2, HWW3, HWW4, HWWS, HWW6,
HWW7, and HWW9); however, there was no significant pre- to post -Mod Alt L difference. For
HWW8, the mean length of the longest hydroperiod was 207.8 days pre -Mod Alt L and 176.5
days post -Mod Alt L; however, a t-test concluded pre- and post -Mod Alt L hydroperiods were not
significantly different (p=0.364). When all wells on the west prong were combined, hydroperiod
length was significantly different in pre- and post -Mod Alt L years (p=<0.001) (Figure II-B22).
The mean length of the longest hydroperiod for all west prong wells was 148.8 pre -Mod Alt L
and 199.2 post -Mod Alt L, approximately 50.4 days longer post -Mod Alt L. Since 2016, all wells
on the main and west prongs of Huddles Cut had a wetland hydroperiod for the entire growing
season.
Porter Creek hydrology data includes nine years of pre -Mod Alt L data (2007-2015) and
five years of post -Mod Alt L data (2016-2020). Post -Mod Alt L average annual rainfall within
Porter Creek was 11.31 inches higher than pre -Mod Alt L. For post -Mod Alt L, five of the nine
wells had longer mean hydroperiods and three had a shorter mean hydroperiod than pre -Mod
Alt L. One well located in the stream bed (PCW9B) had a hydroperiod for the entire growing
season for every year since it was installed in 2011; therefore, showed no difference between
pre- and post -Mod Alt L. There was no significant difference between pre- and post -Mod Alt L
hydroperiods for individual or combined Porter Creek well data.
DCUT11, a small tributary of Durham Creek, has five years of pre -Mod Alt L data (2013-
2017) and three years of post -Mod Alt L data (2018-2020). Post -Mod Alt L average annual
rainfall within DCUT11 was 14.21 inches higher than pre -Mod Alt L. For post -Mod Alt L, seven
of the eight wells had shorter mean hydroperiods than pre -Mod Alt L. Pre- and post -Mod Alt L
hydroperiods were significantly different for DC11W2B (p=0.036) (Figure II-B24). One well
located in the stream bed (DC11W3B), had a hydroperiod for the entire growing season for
every year since it was installed in 2013; therefore, showed no difference between pre- and
post -Mod Alt L. The mean length of the longest hydroperiod for all wells was 108.4 pre -Mod Alt
L and 84.5 post -Mod Alt L, approximately 50.4 days shorter post -Mod Alt L.
Answer: The qualitative nature of baseline measures and lack of confidence in
ability to replicate measurement locations prevent discussion of specific changes in
geomorphology; however, as reported in the 2012 report, in the case of the most
upstream areas of the western prong of Huddles Cut, a discontinuous and unstable
lithology unit called the Croatan Clay appears to have caused the formation of two
depressions as the mine operations advanced through the basin. These depressions
II-B-8

have appeared to remain relatively stable since they formed.
Jacks Creek showed statistically significant differences pre- vs. post -Mod Alt L for
the number of dominants in the herb stratum, brackish intolerant dominants for all
transects combined, and brackish intolerant dominants on an individual basis for certain
transects. There were no significant differences when pre and post -mod Alt L data were
compared for species presence/absence, number of dominant shrubs, and percentages
of non -wetland species. For transects analyzed separately, the percentages of brackish
intolerant dominants at the two most downstream transects on the western prong and
one on the north prong were significantly lower in post -Mod Alt L years. This was likely
due to the arrival of common reed at JW3 in 2012, JW5 in 2013, and JW9 in 2017. In the
2017 report, Jacks Creek showed significantly lower percentages of brackish intolerant
dominants in more recent years (2011-2014, 2017) than earlier years (1998-2005) of data,
suggesting a change in vegetation before Mod -Alt L impacts. JW7 was the only transect
at Jacks Creek that had a higher average percentage of brackish intolerant dominants in
post -Mod Alt L years.
Jacobs Creek showed significant differences when pre and post -mod Alt L data
were compared for species presence/absence. There were no significant differences for
percentages of non -wetland species, percentages of dominant species intolerant of
brackish conditions, or number of herbaceous dominants when pre- and post -Mod Alt L
vegetation data from combined transects were compared. Jacobs Creek had 100 percent
brackish intolerant dominants for all years of monitoring, however the transect is located
farther upstream from the mouth of the creek than transects at Jacks Creek, Tooley
Creek, and Huddles Cut.
Drinkwater Creek was skipped in 2020 following five years of post -Mod Alt L data
collection. The data analyzed up to the 2019 report found no significant differences for
species presence/absence, percentages of non -wetland species, percentages of
dominant species intolerant of brackish conditions, or number of herbaceous dominants
when pre- and post -Mod Alt L vegetation data was compared.
Tooley Creek was surveyed in 2020 following four years of post -Mod Alt L data
collection to make a total of five years of post- data. The data showed significant
differences pre- vs. post -Mod Alt L for species presence/absence and number of
dominants in the shrub stratum, but no significant differences when pre and post -mod
Alt L data were compared for the number of herb dominants, percentages of non -wetland
species, and brackish intolerant dominants for all transects combined. When transects
were analyzed separately, the percentages of brackish intolerant dominants at TW1
(most upstream on eastern prong) and TW4 (most downstream on western prong) were
significantly lower in post -Mod Alt L years. The three species with the highest
contribution to pre- and post -Mod Alt L dissimilarity were absent in pre -Mod Alt L years,
but occurred in all post -Mod Alt L years. Two of the three were brackish tolerant species
and were found at TW3. The transect at TW3 was the only transect in Tooley Creek to
have a higher average percentage of brackish intolerant dominants in post -Mod Alt L
years.
Vegetation surveys for the main and west prongs of Huddles Cut were skipped in
2020 following six years of post -Mod Alt L data collection. The data analyzed up to the
2019 report showed significant differences pre- vs. post -Mod Alt L between pre- and
post -mod Alt L data for species presence/absence, percentages of brackish intolerant
dominants, and average number of herbaceous dominants for all transects combined.
II-B-9

When transects were analyzed separately, two of the seven transects at the main prong
and three of the four transects on the western prong had significantly lower percentages
of brackish intolerant dominants in post -Mod Alt L years. The five transects that did not
show a significant difference are located on two smaller branches off the main prong.
On an individual basis, the number of herbaceous dominants was significantly lower
post -Mod Alt L in six main prong transects while the number of shrubs was lower in one
of those five and higher in another; in the west prong transects, two of the four had more
herbaceous dominants post -Mod Alt L and one of those two had fewer shrubs. The
transition years for Huddles Cut were 2010-2012, which coincided with Hurricane Irene
(2011). Cluster analysis based on species presence/absence similarities grouped all
post -Mod Alt L vegetation survey years separately from pre -Mod Alt L years for the main
and west prongs of Huddles Cut.
Detectable effects on vegetation from hydrologic alterations can be slow to
appear and are dependent on the degree and speed of changes in light, hydrology, and
salinity. Both prongs at Huddles Cut had significantly longer hydroperiods in post -Mod
Alt L years when all well data were combined and one well in the main prong was
significantly different from pre -Mod Alt L. Effects of longer hydroperiods in Huddles Cut
can be seen by the decreased number of non -wetland species present in the vegetation
transects and possibly by the significant difference in species presence/absence post -
Mod Alt L. The post -Mod Alt L hydroperiod length for one well at Tooley Creek (TW5)
was significantly longer from pre -Mod Alt L; however, the middle well on the western
prong, has not shown any significant changes in the number of non -wetland species
present in the vegetation transect. Even though the salinity was significantly lower post -
Mod Alt L for Tooley Creek, the percent of brackish intolerant species was significantly
lower in more recent years at the most downstream transects of Tooley Creek post -Mod
Alt L. The post -mod Alt L hydroperiod length for one well at Drinkwater Creek (DWW1A)
was significantly shorter from pre -Mod Alt L; however, when all wells are combined there
is a general increase in hydroperiods in the post -Mod Alt L years. The effects of the
shorter hydroperiod at DWW1A can be seen in the increase in the number of non -wetland
species present in the vegetation transects post -Mod Alt L. The post -mod Alt L
hydroperiod length for one well at DCUT11 (DC11W2B) was significantly different from
pre -Mod Alt L. Effects of shorter hydroperiods in DCUT11 can be seen by the increased
number of non -wetland species present in the vegetation transects and possibly by the
increase in brackish intolerant dominate species post -Mod Alt L. At the two most
upstream Huddles Cut monitors, salinity was significantly higher post -Mod Alt L and the
percent of brackish intolerant species was significantly lower.
Many wells appear to be influenced in the short-term by large rain events, or
several smaller events in a short amount of time, but some do not appear to be
influenced in the long-term and their hydroperiods do not always respond logically to
rainfall. These rainfall/hydroperiod variations make it difficult to directly correlate mine
activities to a decrease in wetland hydroperiod in all cases. Aside from rainfall,
hydrology and salinity at some wells can also be influenced by large Tar River
discharges and by wind tides, which complicates interpretation. It does not appear mine
activities have altered the vegetation or hydrology for Jacks Creek, Jacobs Creek,
Drinkwater Creek, and Tooley Creek. It is difficult to conclude if changes in vegetation,
salinity, and hydrology at Huddles Cut were due to Mod -Alt L impacts, after effects from
Hurricane Irene, a narrower creek mouth caused by a sand bar that appeared in 2008 or
2009 which contributes to periods of constricted flow, concomitant regional changes in
salinity, sea level and/or climate, or a combination of these factors.
II-B-10

In summary, Table II-B3 shows the four parameters used to illustrate changes in
the vegetative character in impact creeks and indicates with arrows those parameters
with increases or decreases (significant and non -significant) post -Mod Alt L as of 2020.
Pre- and post -Mod Alt L data sets are different among parameters for each creek and
within each creek. Many factors, alone or in combination, may contribute to differences
in vegetation or other parameters. Factors include: deeper/longer periods of standing
water, decreased canopy (no more gap -phase regeneration and fewer trees for woody
vines to climb upon), fewer tip -ups decrease microtopography, more light reduces
number of shade tolerant herbaceous species, and increase in importance of common
reed, duckweed, and cattail in some transects even though these species may not be
dominants in many.
At least one of these potential factors was obvious prior to Mod Alt L activity (e.g.,
decrease in tree canopy) and others may have begun but were less obvious (e.g.,
appearance of a persistent but somewhat migratory sand bar at the mouth of Huddles
Cut in 2008). The sand bar appeared to be coincident with a change in propulsion for the
Aurora/Bayview ferry mentioned to CZR personnel in 2008/2009 by a ferry crew member
as he observed the biological data collection at the mouth of Huddles Cut. During
previous fish and benthos collections, CZR biologists had already noticed larger bow
waves with the arrival of the ferry and in conversation, the ferry crew member agreed that
the bow wave upon docking was larger after this change in propulsion as the purpose
was to increase backing power at the dock. Eventually, the fyke nets at Huddles Cut had
to be more securely tied to the anchor poles to keep the nets in place over night as the
larger bow waves were suspected to have dislodged the nets on more than one
occasion; a situation not previously encountered during the years of overnight fyke net
deployment at Huddles Cut.
As mentioned elsewhere and in previous reports this sand bar was a geomorphic
feature that began to restrict the flow, limit the exchange of creek/river waters, deposit
sediment in the channel, and narrow the overall width of the channel; CZR has observed
a complete blockage of the channel by the sand bar several times since its formation.
Correspondence in early 2019 with Mary Willis (Business Officer, Ferry Division, NC
Dept. of Transportation) and Keith Stegall (Assistant Director, Vessel Asset Management,
Ferry Division, NC Dept. of Transportation) was initiated by CZR to determine more
details if possible. Mr. Stegall verified that the propeller on the Aurora/Bayview ferry (the
"Russell") changed in March 2012 and changed back to the original propeller type in
March 2018. One email mentioned 2008 as the year when the propeller changed but the
last correspondence only referred to 2012 and 2018. Therefore, while the presence and
observed effects of the sandbar are irrefutable, the cause(s) of its formation are not.
II-B-11

0
0
0
N
A B
Jacks Creek Vegetation
C D E F G
CO N V N O CO t N
O O O O O O CO
W N 0 N N N N m N N
Figure II-B1. Dendrogram of hierarchical clusters of similarity of Jacks Creek vegetation survey
years based on the presence/absence of all species. Colored lines represent clusters (or single
year) that are significantly different from one another at the 5 percent level (p = 0.05). Bold
years are post -Mod Alt L.
Jacks Creek
100 -
90 -
c
80-
U
0)
0_U 70-
c
m Q 60-
c
oo50-
0 00
0 0 40-
cc
CD m 30 -
a)
a) a
D_c 20-
10-
0
TRANSITION YEARS
2°° Z67$�b 9.4467$14�7$2°
Year
Figure II-B2. Percent of dominant species intolerant of brackish conditions every year surveyed
in Jacks Creek with all transects combined. Means (dots) and ranges are shown.
II-B-12

100
90
80
70
60
50
40
30
20
10
0
Jacks Creek
JW9
p=0.026
JW5
p=0.015
UPSTREAM
JW7
p=0.364
S
JW3
p=0.024
JW2
�p=0.15'
1
1
I I
I I
Pre Post P e Post Pre Post P e Post Pre Post
Figure II-B3. Percent of dominant species intolerant of brackish conditions in each Jack Creek
transect for pre- vs post -Mod Alt L years; pre -Mod Alt L years include 1998-2005 and 2011-
2014; post -Mod Alt L years include 2017-2020. Means (dots), ranges, and p-values are shown.
Number of Herb Dominants
8
7
6
5
4
3
2
0
Jacks Creek
JW9
p=0.190
p=0.008
JW5
UPSTREAM
JW7
p=0.338
JW3
=0.004
JW2
p=0.068
}
_
•
}
I I
I
1
I
—•
I I
I I
I I
Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B4. Number of pre- vs post -Mod Alt L dominant herbs by individual transect in Jacks
Creek. Pre -Mod Alt L years include 1998-2005 and 2011-2014; post -Mod Alt L years include
2017-2020. Means (dots), ranges, and p-values are shown.
II-B-13

Number of Shrub Dominants
8
7
6
5
4
3
2
0
Jacks Creek
JW9
p=0.030
JW5
p=0.725
UPSTREAM
JW7
p=0.406
JW3
p=0.001
JW2
p=<0.001
—
}
I
1
I
, ,
,
,
, ,
, ,
,
,
Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B5. Number of pre- vs post -Mod Alt L dominant shrubs by individual transect in Jacks
Creek. Pre -Mod Alt L years include 1998-2005 and 2011-2014; post -Mod Alt L years include
2017-2020. Means (dots), ranges, and p-values are shown.
0
o —
Jacobs Creek Vegetation
A B C D
N M O
O O O O
N N N N
m cc)
O O O
N N N
Figure II-B6. Dendrogram of hierarchical clusters of similarity of Jacobs Creek vegetation
survey years based on presence/absence of all species. Colored lines represent clusters (or
single year) that are significantly different from one another at the 5 percent level (p = 0.05).
Bold years are post -Mod Alt L.
II-B-14

E
0
0
a —
0
m
O
N
Tooley Creek Vegetation
A B C
D E F
Wn m O CO n_ rn ro
N 0) O1
O O O O O O O) d7
N N N N N N 1—
Figure II-B7. Dendrogram of hierarchical clusters of similarity of Tooley Creek vegetation
survey years based on presence/absence of all species. Colored lines represent clusters (or
single year) that are significantly different from one another at the 5 percent level (p = 0.05).
Bold years are post -Mod Alt L.
Tooley Creek
100 -
90 -
(i) c
a) 80 -
U
u)U 70-
Q 60-
c
o co50-
p 0a
0 0 40 -
c
m 30 -
a)
a) o
c 20-
10 -
— TW4
p=<0.001
TW3 TW1
p=0.640
UPSTREAM
p=0.01 7
TW6 •
Pre Post
Pre Post
Pre Post
Pre Post
Figure II-B8. Percent of dominant species intolerant of brackish conditions at each transect for
Tooley Creek pre- vs post -Mod Alt L; (west prong = TW4 and TW6; east prong = TW1 and
TW3). Means (dots) and ranges are shown. TW4 and TW6 were not surveyed in 2011 due to
debris from Hurricane Irene.
II-B-15

Percent of Dominant Species
100 -
90
0
-0 80
0
0 70
t
1) 60
m 50
0 40
m 30
0
c 20
10
0
• • •
N000 N000
TW4 •
r2=0.510
•
• • •
•
O O O O O O O O O O O O
Year
Figure II-B9. Linear regression for percent of dominant brackish intolerant species every year at
TW4 in Tooley Creek; dots represent yearly values. TW4 and TW6 were not surveyed in 2011
due to Hurricane Irene debris.
Percent of Dominant Species
Intolerant of Brackish Conditions
100 -
90 -
80 -
70 -
60 -
50
40
30
20
10
0
•
TW1
r2=0.433
• • •
• •
• •
• •
•
00 0 0
°b °� r0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0 ry0
Year
Figure II-B10. Linear regression for percent of dominant brackish intolerant species every year
at TW1 in Tooley Creek; dots represent yearly values.
II-B-16

Number of Herb Dominants
Tooley Creek
4-
2-
i
Pre
TW4
p=0.115
Post
Pre
TW3
p=0.189
UPSTREAM
Post
TW1
p=0.126
•
TW6
p=0.032
Pre Post Pre Post
Figure II-B11. Number of dominant species in the herb layer in Tooley Creek pre- vs post -Mod
Alt L; pre- years include 1998-2001 and 2010-2011; post- years include 2015-2018 and 2020.
TW4 and TW6 were not surveyed in 2011 due to Hurricane Irene debris.
Number of Shrub Dominants
5
4
3-
2
0
Tooley Creek
p=0.013
T
Pre
Post
Figure II-B12. Number of dominant species in the shrub layer in Tooley Creek pre- vs post -Mod
Alt L; pre- years include 1998-2001, 2010-2011; post- years include 2015-2018 and 2020. TW4
and TW6 were not surveyed in 2011 due to Hurricane Irene debris.
II-B-17

Number of Shrub Dominants
5
4
3
2
0
Tooley Creek
UPSTREAM
TW4
p=0.310
TW3
p=0.219
TW1
p=0.017
TW6
p=0.032
•
•
•
•
—
— •
•
Pre
Post
Pre
Post Pre
Post
Pre
Post
Figure II-B13. Number of pre- vs post -Mod Alt L dominant species in the shrub layer in each
transect in Tooley Creek. Means (dots), ranges, and p-values are shown. TW4 and TW6 were
not surveyed in 2011 due to Hurricane Irene debris.
0
o
0
A
Long Creek Vegetation
B C D
O 6 07, N O N
N
O O O O O O O
N N N N N N N
Figure II-B14. Dendrogram of hierarchical clusters of similarity of Long Creek (control)
vegetation survey years based on presence/absence of all species. Colored lines represent
clusters (or single year) that are significantly different from each other at the 5 percent level (p =
0.05).
II-B-18

O
Porter Creek Vegetation
A B C D
Figure II-B15. Dendrogram of hierarchical clusters of similarity of Porter Creek vegetation
survey years based on presence/absence of all species. Colored lines represent clusters (or
single year) that are significantly different from each other at the 5 percent level (p = 0.05). Bold
years are post -Mod Alt L.
`m
E
O
Duck Creek Vegetation
B C D E
Figure II-B16. Dendrogram of hierarchical clusters of similarity of Duck Creek (control)
vegetation survey years based on presence/absence of all species. Colored lines represent
clusters (or single year) that are significantly different from each other at the 5 percent level (p =
0.05).
II-B-19

0
DCUT11 Vegetation
A B
M N N co
^ O O O O ^
N N (N N
Figure II-B17. Dendrogram of hierarchical clusters of similarity of DCUT11 vegetation survey
years based on presence/absence of all species. Colored lines represent clusters (or single
year) that are significantly different from each other at the 5 percent level (p = 0.05). Bold years
are post -Mod Alt L.
E
0
O
DCUT19 Vegetation
A B
O
0
Figure II-B18. Dendrogram of hierarchical clusters of similarity of DCUT19 (control) vegetation
survey years based on presence/absence of all species. Colored lines represent clusters (or
single year) that are significantly different from each other at the 5 percent level (p = 0.05).
II-B-20

OBL
v
a
FACW
-o
d
FAC
0
Jacks Creek (2017-2020 post)
10
20
30
40
Percent species with wetland status
50
■ 2020
■ 2019
■ 2018
■ 2017
■ 2014
■ 2013
■ 2012
■ 2011
OBL
a
a
To
FACW
c
a
FAC
Long Creek to match Jacks Creek
0 10 20 30 40 50
Jacobs Creek (2017-2020 post)
OBL
v
a
▪ FACW
-o
C
C5
d
FAC
0
20 40 60
Percent species with wetland status
80
2020
■ 2019
■ 2018
■ 2017
■ 2013
■ 2012
■ 2011
OBL
v
a
FACW
-o
C
C5
d
FAC
0
Percent species with wetland status
■ 2020
■ 2019
■ 2018
■ 2017
■ 2014
■ 2013
■ 2012
■ 2011
Long Creek to Jacobs Creek
20 40 60
Percent species with wetland status
80
■ 2020
■ 2019
■ 2018
■ 2017
■ 2013
■ 2012
■ 2011
Figure II-B19. Percent of species in three categories of wetland status (obligate [OBL], facultative wet
{FACW], and facultative [FAC]) documented in vegetation surveys in four impact creeks compared to
control creek vegetation for the same survey years as the four impact creeks (control creek vegetation was
not monitored prior to 2011). Post -Mod Alt L years for each impact creek are shown in parenthesis. Note:
Jacks Creek was not sampled in 2015-2016, Jacobs Creek was not sampled in 2014-2016, Tooley Creek
was not sampled in 2019, Porter Creek was not sampled in 2016-2018, and Duck Creek was not sampled
in 2018.
II-B-21

Figure II-B19 (concluded).
Tooley Creek (2015-2020 post)
d
FACW
c
FAC
O3L
0 10 20 30 40
Percent species with wetland status
50
■ 2020
■ 2018
■ 2017
■ 2016
■ 2015
■ 2011
a
a
n
FACW
c
m
FAC
OBL
Long Creek to Tooley Creek
0 10 20 30 40
Percent species with wetland status
50
■ 2020
■ 2018
■ 2017
■ 2016
■ 2015
■ 2011
Porter Creek (2019-2020 post)
OBL
w
FACW
a
m
3
FAC
0
20 40
Percent species with wetland status
60
■ 2020
■ 2019
■ 2015
■ 2014
■ 2013
■ 2012
■ 2011
OBL
FACW
FAC
Duck Creek to match Porter Creek
0 20 40 60
Percent species with wetland status
■ 2020
■ 2019
■ 2015
■ 2014
■ 2013
■ 2012
■ 2011
II-B-22

Longest Hydroperiod (days)
Drinkwater Creek
250
200
150
100 -
50 -
0
DWW1A
p=0.012
DWW1B
UPSTREAM
DWW1C
Pre
Post
Pre
Post
Pre
Post
Figure II-B20. Longest combined pre- and post -Mod Alt L hydroperiod for each well in
Drinkwater Creek relative to location in the creek system (pre=2011-2012; post=2013-2020).
Means (dots) and ranges are shown.
Longest Hydroperiod (days)
Tooley Creek
T W4
250 -
200 -
150 -
100 -
50 -
0-
TW3
•
TW2
UPSTREAM
TW1
TW5
p=0.004
TW6
Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B21. Longest combined pre- and post -Mod Alt L hydroperiod for each well in Tooley
Creek relative to location in the creek system (pre=2000-2001, 2010-2011; post=2012-2020).
Means (dots) and ranges are shown.
II-B-23

Huddles Cut Main Prong
250 -
>, 200 -
50 -
0 1 1 1 I I 1 1 1 1 1 1 I 1 1 I I I I I I I I I
Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo
Figure II-B22. Longest combined pre- and post -Mod Alt L hydroperiod for each well in the main
prong of Huddles Cut relative to location in the creek system (pre=2000-2001, 2010-2011;
post=2012-2020). Means (dots) and ranges are shown.
250
co 200
0
Q 150
0
100
N
ca
0
J
50
0
Huddles Cut
West Prong
— p=<0.001
—
Main Prong
— p=<0.001
—
•
•
I
T
•
Pre
Post
Pre
Post
Rainfall
80
70
60
3
50
LY
40
30 N
c6
L
20 >
10
0
Figure II-B23. Longest combined pre- and post -Mod Alt L hydroperiod and mean rainfall for
each period in Huddles Cut (pre=2000-2001, 2007-2009; post=2010-2020). Means (dots) and
ranges are shown
II-B-24

Longest Hydroperiod (days)
DCUT11
250 -
200
150
100
50
0
DC11 W3A
DC11 W3B
DC11 W3C
DC11 W2A
DC11 W2B
p=0.036
DC11 W2C
UPSTREAM I
1 i
ii
DC11W1A
fi
DC11W1B
i
i
Pre Post Pre Post Pre Post P e Post Pre Post Pre Post Pre Post Pre Post
Figure II-B24. Longest combined pre- and post -Mod Alt L hydroperiod for each well in DCUT11
relative to location in the creek system (pre=2013-2017; post=2018-2020). Means (dots) and
ranges are shown.
II-B-25

O
C
a)
U
a)
d
m
a)
Q
0
-o
a)
Ts
O
Z
�• O
C
a)
a) >
a) -
U C
U C
Q E
co
a
>
a)U
� N
c
-• o
0
(1)
C
rLi -r 6
a)
0
a)
a)
V
a)
L
0
a)
U_
aH
a)
i9
(Q
a)
O
N
s—
a)
L
L
a)
(Q
a)
U
U
O
a)
O
a)
a)
-o
O
7)
O
d
vi
O
U
U
Percent of non -wetland dominants'/ Percent of brackish intolerant dominants"
DCUT11 Porter Creek
PCW5 PCW9A
O O 0 CO I�
O 6 6 M O
Oo r r co co
p O O O O
0 O O O O
0.0 / 100.0
0.0 / 66.7
O O 0 0 0
0 0 0 0 0
0 0 0 o
© 0 0 o
0 0 o CO o
0.0 / 100.0
25.0 / 100.0
m
N
U
0
o O co V 0
p
O M O
0 0 0 0 0
0 0 0 0 0
16.7 / 83.3
Jacks Creek Jacobs Drinkwater TooleyCreek
Creek Creek
TW6
O O O O
O O O O
O O O O
O O O O
© O O O
0.0/66.7 0.0/100.0
Inaccessible due to
hurricane debris
O O O O
O O O 0
O O O O
O O O O
O O O 0
0.0/33.3 0.0/0.0 0.0/100.0 0.0/100.0
TW4
O O O O
© O O O
0 0 0 0
0 0 0 0
0 0 0 0
O o o o
O O O O
LoLC) v
O O 0
CO 0 0 0
0
© o co co
O Ln V M
N \ CON
0000
0 0 0 0
0.0 / 0.0
0.0 / 0.0
o co o co
LO M O M
CO V CO
0000
0 0 0 0
N-0 0 0
CO 0 L6 L6
0 0
0000
O O O O
0.0 / 66.7
0.0 / 75.0
N-O O 0
C0 0 0 0
CO CO O O
0000
O O O 0
JW9 JCBW DWW1C
o
O
0
0
O
0 0 0 0
O O O 0
0 0 0 0
0 0 0 0
O O O O
0 p p
0 0 0
o _ _
O O O
0 OO N
O O O 0
00 0 0 00
0 M O 0
O CO N 0
C0 O O O o C0 O O
ri 0 0 0 0 (6 L6 0
CO V V LC)N CO N V
O O O O O O O O
O O O O O O O O
0 0 0 0
0 0 0 0
N
O 0 O O
0 0 O O
0000
0 0 0 0
0000
O O O 0
JW7
0 0 0 - 0
LO 0 LO CO 0 CO CO
I� CO N--CO N--CO CO CO
O O O O O O O O
O O O O O O O O
rn 0
CO N 0 CO
co V V co
O O O O
O O O O
0
CO 0 CO CO
co co co co
O O O O
O O O O
JW5
co O O co I� O r O
M O O M CO O CO O
CO V N CON N
O O O O O O O O
O O O O O O O O
O O 0 0
Ln Ln O O
N N
O O O O
O O O O
0000
O O O 0
0000
O O O 0
JW3
O V O O CO V V
O I� OO
O r CO r O LC) N
p 0 0 p O O 0
0 O Oa O O O
0 0 O 0
O
O O N V
O 0
O O O O
0 0 O 0
O Ln
O O N N
O 0
O O O O
JW2
O O O O p O O O
O • O O 0 O O O
\ O
0 0 0 0 0 0 0 0
O O O O O O O O
0 O 0 I�
6 O O co
\ CO
O O O 0
O O O 0
O o o o
0 L(i L(i O
\ N V
0 O O 0
0 O O 0
Broomfield Swamp
Creek
CsI
N
m
0.0 / 0.0
0.0 / 40.0
U
N
m
0.0 / 100.0
0.0 / 60.0
L6
N
i
0
per) 0)) O 0 O CO Cr O N 0 0 N co V N f0 N. CO CD N
O) O) O O O O O O Cp O O O O O O O O O O O
CNN N N N N 0 N N N N N N N N N N N
0
N
II-B-26

Table II-B1 a (concluded).
Percent of non -wetland dominants'/ Percent of brackish intolerant dominantsb
Huddles Cut Main Prong Huddles Cut West Prong
O
=
O
O
O
O
O
O
O
O
O
O
O
O
O
O
O
O
O
°
(a
O
O
O
O
O
O
O
O
O
O
-0
U
U 2
.�
H N
Transect
eliminated
-
U a.)j
a)as
N
op
=
(M
(
O
O
V
I--
O
O
O
O
(
O
0
O
6
I�
O
0
I-
6
00
O
0
O
O
00
O
0
O
6
I�
O
0
33.3 / 66.7
0.0 / 0.0
N-
(O
(O
O
0
N-
(O
(O
O
0
O
O
U7
O
0
s-
(O
(0
O
0
j
=
(.0O
(C')
O
0
N-
O
0
O
N-
O
0
(.00
00
O
0
(0
O
0
0
U7
O
0
0
U7
O
0
0.0/0.0
0.0 / 20.0
(,)
(Y)
O
0
N-
(0
O
0
N-
(0
O
0
O
O-
O
O
HWW4
O
00
O
O
I�
(0
O
O
1
(0
O
O
O
N-
O
O
O
co
O
d
O
O
NN
O
M
O
NN
20.0 / 40.0
0.0 / 20.0
co
()
O
O
Lo
M
U7
N
I-
co
O
O
N-
(O
O
O
HWW2
O
0
O
O
I�
00
O
O
O
0
O
O
M
M
00
O
O
M
((')
00
O
O
0
O
CO
O.
O
O
Si
O
O
0.0 / 50.0
0.0 / 50.0
O
In
N
O
O
O
Ili
N
O
O
O
Ili
N
O
O
O
O
V
O
O
N
2
=
V
I-
O
O
N-
60
(O
O
O
O•
O
6
U7
00
O
O
N..(-0O
6
(O
O
O
1
CO
4
M
()
O
O
0.0 / 0.0
0.0 / 40.0
6
I�
O
O
O
O
CO
O
O
O
O
U7
O
O
O
6
N
O
O
o
2
=
V
V
V
O
0
U7
N
(0
O
0
U7
6
U7
O
0
O
O
(O
O
0
V
O
4
O.
n
N
O
0
O
0
_
O
N
0.0 / 33.3
0.0 / 33.3
O
0
U7
O
0
O
0
U7
O
0
M
((')
(Y)
O
0
O
0
(0
O
0
HMW9
O
0
U7
O
0
O
0
CO
O
0
O
0
(0
O
0
O
0
U7
O
0
O
0
(0
O
0
O
O
U7
O
0
N-
(O
(0
O
0
0.0 / 0.0
0.0 / 33.3
M
r)
(n
O
0
M
r)
M
O
0
M
r)
(O
O
0
O
(n
N
O
0
HMW8
O
(n
O
0
O
U7
O
0
U7
(Y)U7
O
0
O
O
O
(Y)
(Y)
O
O
I.
(0
O
O
O
N
0.0 / 16.7
0.0 / 42.9
M
(()
O
O
M
(Y)
O
O
O
V
O
O
O
O
O
O
=
I-
U7
O
O
O
O
0
O
O
I-
6O
0U7
O
O
O
O
O
N-
6O
(0
O
O
O
(0
O
O
N-
6
(0
O
O
0.0 / 0.0
0.0 / 20.0
O
O
U7
O
O
O
O
U7
O
O
I-
60
(0
O
O
O
O
O
HMW5
O)
N
V
O
0
O
0
U7
O
0
O
O
U7
O
0
I-
(O
(0
O
0
N-
(O
(0
O
0
O
O
U7
O
0
O
O
U7
O
0
33.3 / 33.3
0.0 / 25.0
co
r)
(Y)
O
0
O
O
U7
O
0
I-
(O
(0
O
0
N-
(O
(0
O
0
N
=
(n
I,
00
O
O
0
O
00
O
O
(
N-
lf')
N
N
0
O
O
O
O
O
00
0
N
O
N
25.0 / 25.0
0.0 / 25.0
0
O
U7
O
O
0
O
U7
O
O
0
O
U7
O
O
0
O
O
-
CO a)
>-
O
O)
—
O
O)
-
O
O
N
(O
0
O N O
O N O
N 001
0
N
O
O
N
O 0
O O
N N
-
O
N
N C.,O
O O
N N
CD
O O O
N N N
h
O
N
CO
O
N
Cr)N
O O
N N
M
0
•
U
J
73
w
73
0
m
CO
U
m
73
CO
0
U1
Odum et al. (1984),Eleuterius (1990), eFloras (2008), and Weakley (2015).
° In 2009, permitted mine expansion permanently eliminated six of the 10 plots in HMW2 and entire transect at HWW10 (data from those 16 plots are not used in pre -
vs post- comparisons).
II-B-27

Table I I-B1 b. Percent of dominant non -wetland and brackish intolerant plant species (herbs,
shrubs, woody vines) in vegetation transects in four control creeks by year: SCUT1, Long
Creek, DCUT19, and Duck Creek. Dominants with no National Wetland Plant List category
and/or no brackish intolerance status were not included in the percentage calculations. Grey fill
indicates no survey (creek was not yet in the study or a transition or skip year for the associated
impact creek).
Year
Percent of non -wetland dominantsa/ Percent of brackish intolerant dominantsb
SCUT1
Long Creek
DCUT19
Duck Creek
SC1W1
SC1W2
LOCW2B
DC192A
DKCW1B
DKCW2A
DKCW3A
DKCW4B
1998-2010
2011
2012
2013
2014
2015
2016
2017
2018
2019
2020
0.0 / 25.0
0.0 / 25.0
0.0 / 20.0
0.0 / 28.6
0.0/66.7
0.0/66.7
0.0/50.0
0.0/60.0
0.0/60.0
0.0/66.7
0.0/60.0
0.0/50.0
0.0 / 40.0
0.0 / 33.3
14.3 / 85.7
14.3 / 85.7
0.0/100.0
0.0/100.0
12.5 / 100.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/75.0
0.0/80.0
0.0/100.0
0.0/100.0
0.0/80.0
0.0/100.0
12.5/87.5
0.0/85.7
0.0/100.0
0.0/100.0
0.0/100.0
0.0/85.7
14.3/100.0
0.0/100.0
0.0 / 66.7
0.0/100.0
25.0/100.0
25.0/100.0
42.9/100.0
40.0/100.0
0.0/100.0
0.0/100.0
25.0/100.0
14.3 / 100.0
0.0 / 100.0
0.0 / 100.0
0.0 / 100.0
0.0 / 83.3
0.0 / 100.0
0.0 / 100.0
0.0 / 100.0
0.0 / 100.0
aRefers to wetland rating categories as defined in Lichvaretal. (2016).
bTolerance of brackish conditions determined bya review of habitat descriptions given in Radford et al. (1968), Beal
(1977), Godfrey and Wooten (1979, 1981), Odum et al. (1984), Eleuterius (1990), eFloras (2008), and Weakley
(2015).
II-B-28

Table II-B2. Total number and percentage of species assigned a National Wetlands Plant List (NWPL) wetland rating category on an annual basis for each creek surveyed through 2020. Each survey year data are shown
(number and average) for pre- and post -Mod Alt L years in impact creeks. Gray areas are years when no survey occurred; transition years for each creek are noted; post -Mod Alt L years are to right of transition years; no
monitoring in any creek occurred in 2006. Grey fill indicates no survey (creek was not yet in the study or transition or skip year for impact creek and its associated control). See footnote regarding Huddles Cut West.
Impact creek
NWPL
categorya
1998
1999
2000
2001
2002
2003
2004
2005 2007 2008 2009 2010
2011 2012
2013 2014 2015 2016 2017
2018
2019
2020
Pre -Mod
Alt L avg.
Post -Mod
Alt L avg.
FAC
14
13
13.5
FACW
12
13
12.5
# of
OBL
8
14
11.0
NA
species
FACU
0
2
1.0
Broomfield
0
0
0.0
Swamp
_UPL _
TOTAL
34
42
38.0
NA
Creek
FAC
41.2
31
36.1
of total
%species
FACW
35.3
31
33.2
OBL
23.5
33.3
28.4
NA
FACU
0
4.8
2.4
UPL
0
0
0.0
FAC
14
19
17
18
18
20
20
21
11 14
15 17
16
14
13
15
17.0
14.5
FACW
24
18
19
20
20
20
19
16
8 16
11 13
15
17
16
17
17.0
16.3
# of
OBL
19
17
17
20
17
18
18
19
5 11
10 13
11
8
7
11
15.3
9.3
species
FACU
3
5
6
6
7
6
7
5
1 5
3 5
4
4
5
5
4.9
4.5
UPL
0
0
0
0
0
0
0
0
0 0
0 0
0
0
0
0
0.0
0.0
Jacks
-
Creek
TOTAL
60
59
59
64
62
64
64
61
25 46
39 48
46
43
41
48
54.3
44.5
FAC
23.3
32.2
28.8
28.1
29.0
31.3
31.3
34.4
44.0 30.4
38.5 35.4
34.8
32.6
31.7
30.6
32.2
32.4
of total
%species
FACW
40.0
30.5
32.2
31.3
32.3
31.3
29.7
26.2
32.0 34.8
28.2 27.1
32.6
39.5
39.0
34.7
31.3
36.5
OBL
31.7
28.8
28.8
31.3
27.4
28.1
28.1
31.1
20.0 23.9
25.6 27.1
23.9
18.6
17.1
22.5
27.7
20.5
FACU
5.0
8.5
10.2
9.4
11.3
9.4
10.9
8.2
4.0 10.9
7.7 10.4
8.7
9.3
12.2
10.2
8.8
10.1
UPL
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0 0.0
0.0 0.0
0.0
0.0
0.0
0.0
0.0
0.0
FAC
4 7
6
9
8
8
6
5.7
7.8
FACW
2 7
3
4
4
4
4
4.0
4.0
# of
OBL
0 2
1
2
1
1
1
1.0
1.3
species
FACU
0 4
1
4
4
3
4
1.7
3.8
UPL
0 0
0
0
0
0
0
0.0
0.0
Jacobs
Creek
TOTAL
6 20
11
19
17
16
15
12.3
16.8
FAC
66.7 35.0
54.5
47.4
47.1
50.0
40.0
52.1
46.1
of total
%species
FACW
33.3 35.0
27.3
21.1
23.5
25.0
26.7
31.9
24.1
OBL
0.0 10.0
9.1
10.5
5.9
6.3
6.7
6.4
7.3
FACU
0.0 20.0
9.1
21.1
23.5
18.8
26.7
9.7
22.5
UPL
0.0 0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
FAC
9
12 17
15
15
9.0
14.8
FACW
4
9 9
10
10
4.0
9.5
# of
OBL
2
3 4
3
3
2.0
3.3
species
FACU
2
5 4
6
6
2.0
5.3
UPL
0
0 0
0
0
0.0
0.0
Drinkwater
-
Creek
TOTAL
17
29 34
34
34
17.0
32.8
FAC
52.9
41.4 50.0
44.1
42.9
52.9
44.6
of total
%species
FACW
23.5
31.0 26.5
29.4
28.6
23.5
28.9
OBL
11.8
10.3 11.8
8.8
8.6
11.8
9.9
FACU
11.8
17.2 11.8
17.6
17.1
11.8
15.9
UPL
0.0
0.0 0.0
0.0
0.0
0.0
0.0
II-B-29

Table II-B2 (continued).
NWPL
Pre -Mod Post -Mod
impact creeK
category
999if
1999
ZUUU
ZUU1 ZUUZ ZUU3 ZUU4 ZUU0 ZUU/
ZUUS
ZUU9 ZU1U
ZU99 ZUIZ ZU93
ZU14
ZU10
ZU1b
ZU1 /
ZU1S
ZU19 ZUZU
Alt L avg.
Alt L avg.
FAC 18
17
21
18
21
6
12
15
16
17
13 16.8
14.6
FACW 13
12
17
14
12
5
10
12
13
13
11 12.2
11.8
# of
OBL 10
8
12
8
4
2
5
9
8
9
9 7.3
8.0
species
FACU 6
8
8
8
7
0
5
4
4
5
4 6.2
4.4
Tooley
UPL
0
0
0
0
0
0
1
1
1
1
1
0.0
1.0
TOTAL
45
58
38
42.5
39.8
Creek
47
48
44
13
33
41
42
45
FAC
38.3
37.8
36.2
37.5
47.7
46.2
36.4
36.6
38.1
37.8
34.2
40.6
36.6
%of total
FACW
27.7
26.7
29.3
29.2
27.3
38.5
30.3
29.3
31.0
28.9
28.9
29.8
29.7
species
OBL
21.3
17.8
20.7
16.7
9.1
15.4
15.2
22.0
19.0
20.0
23.7
16.8
20.0
FACU
12.8
17.8
13.8
16.7
15.9
0.0
15.2
9.8
9.5
11.1
10.5
12.8
11.2
UPL
0.0
0.0
0.0
0.0
0.0
0.0
3.0
2.4
2.4
2.2
2.6 0.0
2.5
FAC
17
18
20
18
16
15
18
12
11
8
12
12
10 17.4 10.8
FACW
24
22
20
22
17
17
15
10
13
13
14
13
12 19.6 12.5
# of
OBL
24
17
22
24
17
18
16
7
9
10
14
14
12 19.7 11.0
species
FACU
8
4
7
5
6
8
7
3
3
1
3
3
2
6.4 2.5
Huddles
UPL
0
0
1
0
0
1
1
0
0
0
0
0
0
0.4 0.0
Cut
TOTAL
73
61
70
69
56
59
57
32
36
32
43
42
36
63.6 36.8
Main
FAC
23.3
29.5
28.6
26.1
28.6
25.4
31.6
37.5
30.6
25.0
27.9
28.6
27.8
27.6 I 29.6
%of total
FACW
32.9
36.1
28.6
31.9
30.4
28.8
26.3
31.3
36.1
40.6
32.6
31.0
33.3
30.7 34.1
species
OBL
32.9
27.9
31.4
34.8
30.4
30.5
28.1
21.9
25.0
31.3
32.6
33.3
33.3
30.8 29.6
FACU
11.0
6.6
10.0
7.2
10.7
13.6
12.3
9.4
8.3
3.1
7.0
7.1
5.6
10.2 6.8
UPL
0.0
0.0
1.4
0.0
0.0
1.7
1.8
0.0
0.0
0.0
0.0
0.0
0.0 0.7 0.0
FAC
20
17
15
20
17
16
16
10
8
9
10
10
7 17.3 9.0
FACW
25
22
19
26
20
22
13
9
7
7
9
7
6 21.0 7.5
# of
OBL
30
22
17
25
12
18
11
6
6
7
8
9
5 19.3 6.8
species
FACU
6
6
6
5
7
8
5
2
0
1
2
2
0 6.1 1.2
Huddles
UPL
0
0
0
1
0
1
1
0
1
0
0
0
0
0.4
0.2
Cut
TOTAL
81
67
57
77
56
65
46
27
22
24
29
28
18
64.1
24.7
West°
FAC
24.7
25.4
26.3
26.0
30.4
24.6
34.8
37.0
36.4
37.5
34.5
35.7
38.9
27.4 36.7
%of total
FACW
30.9
32.8
33.3
33.8
35.7
33.8
28.3
33.3
31.8
29.2
31.0
25.0
33.3
32.7 30.6
species
OBL
37.0
32.8
29.8
32.5
21.4
27.7
23.9
22.2
27.3
29.2
27.6
32.1
27.8
29.3 27.7
FACU
7.4
9.0
10.5
6.5
12.5
12.3
10.9
7.4
0.0
4.2
6.9
7.1
0.0
9.9 4.3
UPL
0.0
0.0
0.0
1.3
0.0
1.5
2.2
0.0
4.5
0.0
0.0
0.0
0.0
0.7 0.8
FAC
10
13
10
10
10
11
10.6 11.0
FACW
3
5
4
5
5
5
4.4 5.0
# of
OBL
2
2
2
3
3
4
2.4 4.0
species
FACU
1
1
0
1
2
3 1.0 3.0
UPL
0
0
0
0
0
0 0.0
0.0
DCUT11
TOTAL
16
21
16
19
20
23 18.4
23.0
FAC
62.5
61.9
62.5
52.6
50.0
47.8 57.9 47.8
%of total
FACW
18.8
23.8
25.0
26.3
25.0
21.7 23.8 21.7
species
OBL
12.5
9.5
12.5
15.8
15.0
17.4 13.1 17.4
FACU
6.3
4.8
0.0
5.3
10.0
13.0 5.3 13.0
UPL
0.0
0.0
0.0
0.0
0.0
0.0 0.0 0.0
FAC
7 10 11
11
9
10 12
9.6
11.0
FACW
7 11 7
8
6
7 8
7.8
7.5
# of
OBL
0 10 6
6
5
5 8
5.4
6.5
species
FACU
0 1 0
2
1
2 2
0.8
2.0
UPL
0 0 0
0
0
0 0
0.0
0.0
Porter
TOTAL
14 32 24
27
21
24 30
23.6
27.0
Creek
FAC
50.0 31.3 45.8
40.7
42.9
41.7 40.0
42.1
40.8
%of total
FACW
50.0 34.4 29.2
29.6
28.6
29.2 26.7
34.3
27.9
species
OBL
0.0 31.3 25.0
22.2
23.8
20.8 26.7
20.5
23.8
FACU
0.0 3.1 0.0
7.4
4.8
8.3 6.7
3.1
7.5
UPL
0.0 0.0 0.0
0.0
0.0
0.0 0.0
0.0
0.0
II-B-30

Table II-B2 (concluded).
Control creek
NW PL 1998 1999 2000 2001 2002 2003 2004 2005 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016 2017 2018 2019 2020
category
Control Average
SCUT1
# of
species
FAC
FACW
OBL
FACU
UPL
TOTAL
%of total
species
FAC
FACW
OBL
FACU
UPL
10 13
6 8
8 11
0 1
0 0
24 33
41.7 39.4
25.0 24.2
33.3 33.3
0.0 3.0
0.0 0.0
11.5
7.0
9.5
0.5
0.0
28.5
40.5
24.6
33.3
1.5
0.0
N/A
N/A
N/A
Long Creek
# of
species
FAC
FACW
OBL
FACU
UPL
TOTAL
%of total
species
FAC
FACW
OBL
FACU
UPL
11 5 6 11 9 9 11 9 8 10
9 7 7 10 8 9 9 8 7 8
3 2 4 5 4 6 7 9 8 6
0 2 0 1 0 1 1 1 1 0
0 0 0 0 0 0 0 0 0 0
8.9
8.2
5.4
0.7
0.0
23 16 17 27 21 25 28 27 24 24
23.2
47.8 31.3 35.3 40.7 42.9 36.0 39.3 33.3 33.3 41.7
39.1 43.8 41.2 37.0 38.1 36.0 32.1 29.6 29.2 33.3
13.0 12.5 23.5 18.5 19.0 24.0 25.0 33.3 33.3 25.0
0.0 12.5 0.0 3.7 0.0 4.0 3.6 3.7 4.2 0.0
0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0
38.2
35.9
22.7
3.2
0.0
DCUT19
# of
species
FAC
FACW
OBL
FACU
UPL
TOTAL
%of total
species
FAC
FACW
OBL
FACU
UPL
11 11 11 14 15 10
7 9 7 6 6 6
4 4 4 4 4 3
0 1 1 1 3 4
0 0 0 0 0 0
22 25 23 25 28 23
50.0 44.0 47.8 56.0 53.6 43.5
31.8 36.0 30.4 24.0 21.4 26.1
18.2 16.0 17.4 16.0 14.3 13.0
0.0 4.0 4.3 4.0 10.7 17.4
0.0 0.0 0.0 0.0 0.0 0.0
12.4
7.0
4.0
1.2
0.0
10.0
6.0
3.0
4.0
0.0
23.0
43.5
26.1
13.0
17.4
0.0
24.6
50.3
28.7
16.4
4.6
0.0
Duck Creek
# of
species
FAC
FACW
OBL
FACU
UPL
TOTAL
%of total
species
FAC
FACW
OBL
FACU
UPL
14 15 17 20 23 23 27 23 27
16 16 17 21 14 18 18 19 23
3 3 7 9 5 8 13 13 11
3 2 1 3 2 5 8 8 10
1 0 0 0 0 0 0 0 0
21.0
18.0
8.0
4.7
0.1
37 36 42 53 44 54 66 63.0 71.0
51.8
37.8 41.7 40.5 37.7 52.3 42.6 40.9 36.5 38.0
43.2 44.4 40.5 39.6 31.8 33.3 27.3 30.2 32.4
8.1 8.3 16.7 17.0 11.4 14.8 19.7 20.6 15.5
8.1 5.6 2.4 5.7 4.5 9.3 12.1 12.7 14.1
2.7 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0
40.9
35.9
14.7
8.3
0.3
a National Wetland Plant List (2018)
b Due to inaccessibility after Hurricane Irene in 2011, the western prong of Tooley Creek was not sampled, therefore only data from the eastern prong of Tooley Creek are shown for 2011. The data for 2011 was included in the pre-
` In 2009, permitted mine activies eliminated six plots in HWW2 and the entire transect at HWW10. Data from those plots prior to 2009 are shown in this table and included in the pre- and post -Mod Alt L averages, but are not
used in the statistical comparisons for pre- vs post -Mod Alt L species richness, percent brackish intolerants, number of dominants, or percent non -wetland dominants.
II-B-31

character for each
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PRE- TO POST -MOD ALT L DIFFERENCES IN PARAMETERS USED TO DESCRIBE CHARACTER
DISCHARGE
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HYDROLOGY
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Individual Well
uee w
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VEGETATION
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data through 2019.
II-B-32