20080868 Ver 2_Section II B Q2 Character 2021 PCS Creeks Report_20220605

B. Question 2-Has mining altered the geomorphic or vegetative character of the
creeks?
Geomorphology: The term "geomorphic" was included in this question, but there was very
little creek -specific baseline geomorphic data collected with pre- impact conditions, and no
specific quantitative criteria for monitoring. General information on the floodplain width and
adjacent slope were characterized for all creeks but these measurements and locations were
more qualitative than quantitative. Geomorphic conditions on the new creeks (incorporated in
2011, 2013, and 2018) were characterized like those from the original study (Jacks Creek, Tooley
Creek, and Huddle Cut), but neither the original or newer creeks in the study allow for meaningful
pre -/post- comparisons.
The key parameters addressed in this section that are likely to influence geomorphic and
vegetative character of the creeks are vegetation and wetland hydrology. In addition to these two
parameters, a summary table has been compiled at the end of this section to present pre- and
post -Mod Al L differences among rainfall, vegetation, salinity, wetland hydrology, and Tar/Pamlico
River discharge.
Vegetation: 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. 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. A skip year was defined as a post -Mod Alt L year in which no
vegetation survey was conducted per the 2017 Science Panel meeting vegetation survey
clarification. The following sections discuss background conditions associated with the vegetation
data collected in each creek.
Broomfield Swamp Creek: Monitoring for Broomfield Swamp Creek occurred 2019-2021
for pre -Mod Alt L. No statistics were computed with only three 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 2015-2016 or 2021, the first skip year.
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. Since 2021 was a "skip" year, vegetation was not sampled.
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 five years of post -Mod Alt L data
(2016-2019 and 2021) have been collected.
Cluster analysis based on species presence/absence data grouped pre -Mod Alt L data
(2011) in cluster A, while post -Mod Alt L year 2016 clustered in B, 2017 in C, 2021 in D, and 2018-
2019 in E (Figure II-B1). No significant difference between pre- and post -Mod Alt L years for
species presence/absence data was found when ANOSIM was used. A SIMPER analysis based
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on the Bray -Curtis similarity measure for species composition showed 38.10 percent dissimilarity
between pre- and post -Mod Alt L years, the second lowest dissimilarity among all creeks with
post -Mod Alt L vegetation data. Drinkwater Creek had 12 species, with the highest percent of
individual contribution at 5.29 percent; the two remaining contributing species were less than or
equal to 4.17 percent. Of the 14 species, only one was not present during post -Mod Alt L years
(witchgrass; Dichanthelium commutatum & laxiflorum) and was intolerant of brackish conditions.
For all survey years, only brackish intolerant species were dominants in the herbaceous
or shrub/woody vine strata; therefore, to date there is no difference between percentages of
dominant species intolerant of brackish conditions for pre- and post -Mod Alt L years (Table II-
B1 a). The one year of pre- data had two dominant herbs and all post -Mod Alt L years had three
dominants while the shrub/vine stratum had only one dominant species for all years.
The one year of pre -Mod Alt L data (2011) had 11.8 percent non -wetland species
(indicator status of FACU or UPL) while five years of post- data averaged 14.8 percent, with 2021
being the lowest at 10.3 percent (Table II-B2). No non -wetland species have been dominants
during survey years (Table II-B1a). Jurisdictional wetland status of vegetation at Drinkwater
Creek does not appear to have been altered by the mine to date, taking into account only one
year of pre -Mod Alt L data was collected.
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 and 2021 were skip years with no survey conducted.
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 11 years of vegetation
data resulted in five clusters in this control creek: A: 2013-2015, B: 2020-2021, C: 2018-2019, D:
2016-2017, and E: 2011-2012 (Figure II-B2). The percent of brackish intolerant dominants at
Long Creek in all years ranged from 33.3 to 66.7, with an average of 53.3 (Table I I-B1 b). The
percentages of non -wetland species in Long Creek ranged from 0.0 (2011, 2013, 2015, and 2020-
2021) to 12.5 (2012) with an average of 2.9 (Table I I-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, 2016-2019, and 2021; 2020 was the first skip year and
no data were collected.
The analysis on the main prong of Huddles Cut resulted in five clusters: A: 2013, B: 2017-
2019 and 2021, C: 2014, 2016, D: 1998-2001, and E: 2007-2009 (no survey in 2015 or 2020,
Figure II-B3). A significant difference between pre- and post -Mod Alt L years for species
presence/absence data was found when ANOSIM was used (p=0.001); 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 55.60 percent dissimilarity between pre- and post -Mod Alt L years,
the second highest dissimilarity among all creeks with post -Mod Alt L vegetation data. The
highest individual contributions at the main prong of Huddles Cut were eight species with 1.73
percent, and no other species were greater than 1.50 percent. Of the eight species, four were
present in all pre -Mod Alt L years, only two of which were brackish intolerant; four were present
in all post -Mod Alt L years only, none of which were brackish intolerant. None of the eight species
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were non -wetland species.
A t-test to compare percentages for all transects of dominant herbaceous and
shrub/woody vine species intolerant of brackish conditions for pre- and post -Mod Alt L data
showed percentages were significantly lower in post -Mod Alt L years (p=<0.001) (Figure II-B4).
The percent of brackish intolerant dominants in pre -Mod Alt L years across all transects ranged
from 25.0 to 90.0, with an average of 60.0 (Table I I-B1 a). The percentages of brackish intolerant
dominants in post -Mod Alt L years across all transects ranged from 0 to 100, with an average of
42.5 (Table II-B1a). When transects were compared individually, two of the seven transects
showed a significant difference between pre- and post -Mod Alt L years with negative correlations
between years and percentages: HMW8 (p=0.008, r2=0.34) and HMW9 (p=<0.001, r2=0.52)
(Figures II-B5, II-B6, II-B7). The transects that did not show a significant difference are located
either further upstream or on smaller branches off the main prong.
A t-test to compare the number of herbaceous dominants pre- versus post -Mod Alt L for
all transects combined resulted in a significant difference post -Mod Alt L (p= <0.001 Figure II-
B8). On an individual transect basis, six of the seven transects (HMW2, p=<0.001; HMWS,
p=0.026; HMW6, p=<0.001; HMW9, p=0.044; HMW10, p=0.002; and HMW12, p=0.001) had
significantly fewer dominants post -Mod Alt L; the most downstream transect (HMW8) did not
(Figure II-B9). The most downstream transect also contained significantly more non -freshwater
species post -Mod Alt L. For the shrub stratum on the main prong, two of the seven transects
were significantly different post -Mod Alt L; HMW2 (p=0.017) had significantly fewer post -Mod Alt
L shrub dominants and HMW10 (p=0.002) had significantly more (Figure II-B10).
The percent of non -wetland species for pre -Mod Alt L data ranged from 6.6 (1999) to 15.3
(2008), with an average of 10.9 (Table II-B2). The percent of non -wetland species for post -Mod
Alt L data ranged from 3.1 (2016) to 9.4 (2013), with an average of 6.2. There was a significant
difference in the percentage of non -wetland species with higher percentages in pre -Mod Alt L
years (p=0.010). Only four dominant species have been non -wetland, with the exception of small
dog fennel (Eupatorium capillfolium); a dominant in the first year of pre -Mod Alt L), all of the
occurrences were in pre -Mod Alt L years. Jurisdictional wetland status of the vegetation on the
main prong of Huddles Cut does not appear to have been altered by the mine.
Huddles Cut West Prong: Drainage basin reduction of 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 surface
depression appeared in the middle of the HWW8 transect, altering water depth at one of the 10
vegetation quadrants.
Cluster analysis on the 14 years of vegetation data for the west prong of Huddles Cut
resulted in three clusters: A: 2013-2014, 2016-2019, 2021, B: 1998-2001, and C: 2007-2009 (no
survey occurred in 2015 or 2020 Figure II-B11). Clusters B and C contained all of the post -Mod
Alt L years. A significant difference between pre- and post -Mod Alt L years for species
presence/absence data was found when ANOSIM was used (p=0.002). A SIMPER analysis
based on the Bray -Curtis similarity measure for species composition showed 66.63 percent
dissimilarity between pre- and post -Mod Alt L years, the highest dissimilarity among all creeks
with post -Mod Alt L vegetation data. The highest individual contributions in the west prong of
Huddles Cut were 11 species with 1.66 percent; no other species were greater than 1.44 percent.
Of the 11 species, eight were present only in pre -Mod Alt L years. Of those eight, seven were
brackish intolerant species and one was Japanese honeysuckle (Lonicera japonica), a non -
wetland species. Three of the 11 species occurred only in post -Mod Alt L years and were non-
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freshwater species.
A t-test to compare percentages for all transects of dominant herbaceous and
shrub/woody vine species intolerant of brackish conditions for pre- and post -Mod Alt L data
showed percentages were significantly lower in post -Mod Alt L years (p=<0.001) (Figure II-B12).
The percent of brackish intolerant dominants in pre -Mod Alt L years across all transects (excluding
HWW10 because it was not surveyed after 2008) ranged from 33.3 to 100, with an average of
78.2 (Table II-B1 a). The percent of brackish intolerant dominants in post -Mod Alt L years across
all transects ranged from 0 to 100, with an average of 47.3. When transects were compared
individually, two of the four transects showed a significant difference between pre- and post -Mod
Alt L years with negative correlations between years and percentages: HWW2 (p=<0.001,
r2=0.60) and HWW8 (p=<0.001, r2=0.30) (Figures II-B13, II-B14, and II-B15).
A t-test to compare the number of herbaceous and shrub/woody vine dominants pre- and
post -Mod Alt L in all transects combined showed significantly fewer post -Mod Alt L dominants for
Huddles Cut west prong (Figure II-B16, p=<0.001). Individually, two of the four transects (HWW2,
p=<0.001 and HWW8, p=0.001) had significantly more herbaceous dominants in post -Mod Alt L;
the two most downstream transects (HWW4 and HWW7) were not significantly different (Figure
II-B17). Unlike the main prong, the most downstream transect in the west prong (HMW7) did not
show a significant decrease in brackish intolerant herbaceous species; being 800 feet closer to
the mouth of the creek likely means less brackish intolerant dominance in all years. In the
shrub/woody vine stratum, when combined there was no significant difference in the number of
dominant species pre- versus post -Mod Alt L; however, on an individual basis, one transect had
significantly fewer shrubs post -Mod Alt L (HWW8, p=0.004, Figure II-B18).
The percent of non -wetland species for pre -Mod Alt L data ranged from 7.4 (1998) to 13.8
(2008), with an average of 10.6 (Table II-B2). The percent of non -wetland species for post -Mod
Alt L data ranged from 0.0 (2019) to 7.4 (2013), with an average of 4.9. A t-test showed a
significant difference (p=0.001) between percentages of non -wetland species of pre -Mod Alt L
and post -Mod Alt L years. Percentages of non -wetland species for the main and western prongs
of Huddle Cut were similar all years, except 2019 when the west prong did not have any non -
wetland species. Small dog fennel was the only non -wetland species that was a dominant for the
western prong, occurring in pre- and post -Mod Alt L years. Jurisdictional wetland status of the
vegetation at the western prong of Huddles Cut does not appear to have been altered by the
mine.
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; 2019-2021 represent post -
Mod Alt L data years with five years of pre -Mod Alt L data (2011-2015). Cluster analysis based
on species presence/absence data for eight years grouped into five clusters: A: 2011, B: 2015,
C: 2012, D: 2013-2014, and E: 2019-2021 (Figure II-B19). 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
43.22 percent dissimilarity between pre- and post -Mod Alt L years, the third highest dissimilarity
among all creeks surveyed in 2021 with post -Mod Alt L vegetation data.
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 90.3 (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 ranged from 6.3 to
8.3 with an average of 7.1 (Table II-B2). Jurisdictional wetland status of vegetation at Porter
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Creek does not appear to have been altered by the mine.
Duck Creek (control): Vegetation data collection began at four transects for Duck Creek
in 2011 and has been collected every year since except 2018. Cluster analysis for the ten years
of vegetation data resulted in seven clusters for this control creek: A: 2011, B: 2015, C: 2012-
2014, D: 2016, E: 2017, F: 2019, and G: 2020-2021 (Figure II-B20). The percent of brackish
intolerant dominants for all years ranged from 66.7 to 100, with an average of 95.7. Using pre -
and post -Mod Alt L years for the corresponding impact creek, Porter Creek, the percent of
brackish intolerant dominants at Duck Creek ranged from 80.0 to 100.0, with an average of 97.7
in pre -Mod Alt L years and ranged from 83.3 to 100.0 with an average of 97.2 in post -Mod Alt L
years (Table II-B1 b). The average percent of non -wetland species for all years of data was 4.5.
The percentage of non -wetland species in Duck Creek using the same years as Porter Creek pre -
Mod Alt L years ranged from 2.4 (2013) to 10.8 (2011) with an average of 5.8 (Table I I-B2). The
percentage of non -wetland species in Duck Creek using the same years as Porter Creek post -
Mod Alt L years ranged from 12.7 (2019 and 2021) to 14.1 (2020) with an average of 13.2.
DCUT11: Approximately 81.4 acres remain of the pre -Mod Alt L -166-acre drainage basin.
Pre -Mod Alt L years were 2013-2017; mod Alt L impacts occurred in 2018 through January 2019
and 2020-2021 were the first two years of post -Mod Alt L vegetation data collection.
Cluster analysis on the five years of pre -Mod Alt L and two years of post -Mod Alt L
vegetation data for DCUT11 resulted in two clusters: A: 2013-2014 and B: 2015-2017 and 2020-
2021 (Figure II-B21). 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 20.50 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 the two years of post -Mod Alt L averaged 83.3 percent (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. Percent of non -wetland species for the two years of post -Mod Alt
L was 13.0 (Table II-B2). Even though the two years of post- non -wetland percentage was higher
than the pre- years there was no significance statistically. This was likely due to the percent of
FACU species increasing in the last pre -Mod Alt L year; a trend also seen in the control creek
(DCUT19).
DCUT19 (control): Vegetation data collection occurred at one transect for DCUT19 in
2013-2017 and 2020-2021. Cluster analysis for the seven years of vegetation data resulted in
three clusters in this control creek: A: 2013-2014, B: 2015, and C: 2016-2017 and 2020-2021
(Figure II-B22). The percent of brackish intolerant dominants at DCUT19 using DCUT11 pre -Mod
Alt L years ranged from 85.7 to 100.0, with an average of 94.3 and the two post -Mod Alt L years
were 100 (Table II-B1 b). The percentages of non -wetland species in DCUT19 using DCUT11
pre -Mod Alt L years ranged from 0.0 (2013) to 10.7 (2017) with an average of 4.6 and the two
post -Mod Alt L years were 17.4 (Table II-B2).
Impact to Control Creek Summary Vegetation Discussion: The distance from the
Pamlico River combined with topographic differences between impact and controls creeks
presents difficulties when comparing pre- to post -Mod Alt L data. Post -Mod Alt L averages for
percent of brackish intolerant dominants at Huddles Cut (main prong: 42.5; western prong: 47.3)
were slightly lower than Long Creek (51.4) using the same post -Mod Alt L years as Huddles.
Huddles Cut is an offshoot on the Pamlico River increasing the likelihood of higher salinity than
Long Creek which is 4.0 miles from the Pamlico River. The floodplain width (6 to 10 feet) in the
vicinity of the vegetation transect in Long Creek is narrower than any other creek in the study by
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several factors; floodplain width in most other creeks is >25 feet, and for several creeks is greater
>100 feet. Canopy cover is greater at the Long Creek transect (50 percent) than all transects in
Huddles Cut and did not appear to be affected by Hurricane Irene. The vegetation transect at
Long Creek is along a small narrow prong off the main creek and elevation seems to be also
higher than Huddles Cut, so storm surge and wind have less influence. The post -Mod Alt L
average for percent of brackish intolerant dominants at Drinkwater Creek (100) was higher than
Long Creek (50.0) using the same post -Mod Alt L years. The difference in percentage between
Drinkwater Creek and Long Creek was likely due to the distance from Pamlico River. The transect
at Drinkwater Creek is 5.7 miles from the Pamlico River while Long Creek is 4.0 miles. Pre -Mod
Alt L averages for percent of brackish intolerant dominants at Porter Creek with both transects
combined was 85.0 compared to Duck Creek, using the same years as Porter Creek, with all
transects combined was 97.7. Post -Mod Alt L averages for percent of brackish intolerant
dominants at Porter Creek with both transects combined was 90.3 compared to Duck Creek with
all transects combined was 97.2. Porter Creek increased in brackish intolerant dominants from
pre- to post -Mod Alt L while Duck Creek decreased slightly in the same timeframe. Pre -Mod Alt
L averages for percent of brackish intolerant dominants at DCUT11 was 81.9 compared to
DCUT19 at 94.3. Post -Mod Alt L averages for percent of brackish intolerant dominants at
DCUT11 was 83.3 while DCUT19 was 100. While DCUT11 decreased in percent from pre- to
post -Mod Alt L, DCUT19 increased in percent for the same years.
To compare post -Mod Alt L data from three impact creeks (Huddles Cut, Porter Creek,
and DCUT11) to the data from three control creeks (Long Creek, Duck Creek, and DCUT19) for
the same years, percent of species in three wetland status categories (obligate [OBL], facultative
wetland [FACW], and facultative [FAC]) was displayed (Figure II-B23). Control creek vegetation
data was not collected prior to 2011, Huddles Cut was not sampled in 2015 and 2020, and Duck
Creek was not sampled in 2018. Several trends were apparent: most creeks showed a decline
over time in the percent of wetland species with FACW status, a slight decline in the percent of
FAC species, and an increase in the percent of OBL species (Figure II-B23). Huddles Cut on the
main prong and DCUT11 were the exceptions: Huddles Cut main prong fluctuated in FACW in
percent and DCUT11 increased then decreased in FACW percent.
Pre -Mod Alt L salinity was significantly higher than post -Mod Alt L for all upstream and
downstream Aqua TROLL stations except DCUT11, which was lower, and two Huddles Cut
Stations. The two upstream stations at Huddles Cut, one located on each prong, had significantly
lower salinity pre -Mod Alt L than post -Mod Alt L. Section III -A contains more information on
salinity at the creeks.
The annual rainfall from 1998-2005 and 2007-2020 for the Aurora plant site ranged from
36.16 inches (2007) to 71.10 inches (2003) and the annual average was 51.59 inches (Table I-
F2). Total annual rainfall for 2021 (50.36 inches) was lower than the average rainfall for all years
by 1.23 inches. Annual rainfall data were 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 (seven years of post- data), Jacobs Creek (eight years of post- data),
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Drinkwater Creek (nine years of post- data), Tooley Creek (10 years of post- data), Huddles Cut
(12 years of post- data), Porter Creek (six years of post- data), and DCUT11 (four years of post -
data). In 2021, there were seven 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, three wells at DCUT11
recorded shorter hydroperiods post -Mod Alt L, and two wells 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=0.037) was 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 lower in 2021 than 2020. 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-D 1).
Jacks Creek hydrology data include 10 years of pre -Mod Alt L data (2000-2005 and 2011-
2014) and seven years of post -Mod Alt L data (2015-2021). Post -Mod Alt L average annual
rainfall within Jacks Creek was 5.91 inches higher than pre -Mod Alt L. Of the 14 wells at Jacks
Creek, six had a longer mean hydroperiod post -Mod Alt L and eight 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 (152.7), 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
seven years of post -Mod Alt L data (2014-2021). Post -Mod Alt L average annual rainfall within
Jacobs Creek was 8.00 inches higher than pre -Mod Alt L. Wetland hydroperiods have only been
recorded in two years since monitoring began, 2014 and 2021. Total annual rainfall in 2014 was
the fourth highest for all monitoring years, while total annual rainfall in 2021 was less than one
inch below the average rainfall for all 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
nine years of post -Mod Alt L data (2013-2021). Post -Mod Alt L average annual rainfall within
Drinkwater Creek was 3.88 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-B24). Pre- and post -Mod Alt L hydroperiods were significantly different for
DWW1A (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 3.5 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 ten years of post -Mod Alt L data (2012-2021). Post -Mod Alt L average annual
rainfall within Tooley Creek was 2.66 inches higher than pre -Mod Alt L. When wells were
compared individually, post -Mod Alt L hydroperiod means were longer for one of the three wells
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on the eastern prong (TW2) and two of the three wells on the western prong (TW4 and TW5)
while the other wells (TW1, TW3 and TW6) had shorter mean hydroperiods post -Mod Alt L (Figure
II-B25). Pre- and post -Mod Alt L hydroperiods were significantly different for TW5 (p=0.002).
When well data were combined, the post -Mod Alt L mean hydroperiod length was higher than
pre -Mod Alt L by approximately 15.8 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 12 years of post -Mod Alt L data (2010-2021). Post -Mod Alt L average annual rainfall
within Huddles Cut was 3.00 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-B27). When wells on the main prong were compared individually, post -Mod
Alt L hydroperiod means were longer for all 12 wells, two wells were significantly longer (HMW1,
p=0.042 and HMW7, p=<0.006) (Figure II-B26). The mean length of the longest hydroperiod for
all wells was 213.4 pre -Mod Alt L and 241.2 post -Mod Alt L, a difference of approximately 27.8
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 183.2 days post -Mod Alt L; however,
a t-test concluded pre- and post -Mod Alt L hydroperiods were not significantly different (p=0.458).
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-B27). The mean length of the longest
hydroperiod for all west prong wells was 148.8 pre -Mod Alt L and 203.7 post -Mod Alt L,
approximately 55.0 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
six years of post -Mod Alt L data (2016-2021). Post -Mod Alt L average annual rainfall within Porter
Creek was 9.74 inches higher than pre -Mod Alt L. For post -Mod Alt L, four of the nine wells had
longer mean hydroperiods and four 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 four years of post -Mod Alt L data (2018-2021). Post -Mod Alt L average annual rainfall
within DCUT11 was 10.51 inches higher than pre -Mod Alt L. Longest combined hydroperiods
were shorter post -Mod Alt L but not significantly shorter. The mean length of the longest
hydroperiod for all wells was 108.4 pre -Mod Alt L and 82.9 post -Mod Alt L, approximately 25.5
days shorter post -Mod Alt L. For post -Mod Alt L, seven of the eight wells had shorter mean
hydroperiods than pre -Mod Alt L. One well located in the stream bed at the farthest downstream
well array (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. Pre -
and post -Mod Alt L hydroperiods were significantly dryer in the post -Mod Alt L years for three
wells at DCUT11 (DC11W1A, p=0.032, DC11W2B, p=0.015, DC11W2C p=0.0436) (Figure II-
B28). In an attempt to better understand the shorter hydroperiods that were observed at DCUT11
in the post -Mod Alt L years, the upstream, middle and downstream well arrays were evaluated
separately. The upstream -most well array (DC11 W1 A and DC11 W1 B) and the downstream most
well array (DC11W3A, DC11W3B, and DC11 W3C) each have shorter hydroperiods in the post
mod -Mod Alt L years, but not significantly shorter. The middle well array (DC11W2A, DC11W2B,
II-B-8

DC11W2C) has significantly shorter hydroperiods (p=0.034) in the post -Mod Alt L years. When
the two upstream well arrays are combined, post -Mod Alt L hydroperiods were significantly shorter
(p=0.011). A similar trend towards shorter hydroperiods in the post -Mod Alt L years is observed
at the two upstream -most well arrays at DCUT19 (control creek) when the same years are used
for comparison. The middle (DC19W1A and DC19W1B) and upstream (DC19W2A and
DC19W2B) well arrays are both significantly dryer (upstream, p=0.010; downstream, p=0.014) in
the post -Mod Alt L years. When the two upstream well arrays at DCUT19 are combined post -
Mod Alt L hydroperiods were also significantly shorter (p=0.001).
Answer: To address potential changes in geomorphic and vegetative character,
parameters associated with vegetation and wetland hydrology were evaluated for pre- and
post -Mod Alt L differences. In addition to these two parameters, a summary table has been
compiled at the end of this section to present pre- and post- Mod Al L differences for
rainfall, vegetation, salinity, wetland hydrology, and Tar/Pamlico discharge. 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 have appeared to remain
relatively stable since they formed.
Jacks Creek vegetation sampling was skipped in 2021 following four years of post -
Mod Alt L data. The data analyzed up to the 2020 report 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 vegetation sampling was skipped in 2021 following four years of post -
Mod Alt L data. The data analyzed up to the 2020 report 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 showed no statistical differences for species presence/absence.
The one year of pre -Mod Alt L data limits any further statistical significance; therefore,
other analyses are based on numerical changes. The percentage of non -wetland species
increased, percentages of dominant species intolerant of brackish conditions has
II-B-9

remained the same for all years, the number of herbaceous dominants has gone from two
in the pre- to three in the post- while the number of shrub/woody vines has remained the
same when pre- and post -Mod Alt L vegetation data were compared.
Tooley Creek vegetation sampling was skipped for 2021 with five years of post -Mod
Alt L data collection. The data analyzed up to the 2020 report 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.
The main prong of Huddles Cut showed significant differences pre- vs. post -Mod
Alt L for species presence/absence, percentages of brackish intolerant dominants, percent
of non -wetland species, and number of herbaceous dominants for all transects combined.
When transects were analyzed separately, two of the seven transects had significantly
lower percentages of brackish intolerant dominants in post -Mod Alt L years. On an
individual basis, the number of herbaceous dominants was significantly lower in six
transects and the number of shrub dominants was significantly lower in two transects
post -Mod Alt L.
The west prong of Huddles Cut showed statistically significant differences pre- vs.
post -Mod Alt L for species presence/absence, percentages of brackish intolerant
dominants, percent of non -wetland species, and number of herbaceous dominants for all
transects combined. When transects were analyzed separately, two of the four transects
had significantly lower percentages of brackish intolerant dominants in post -Mod Alt L
years. On an individual basis, the number of herbaceous dominants was significantly
lower post -Mod Alt L in two transects while the number of shrub dominants at one transect
was lower in post -Mod Alt L.
Porter Creek and DCUT11 showed no significant differences for species
presence/absence, percentages of dominant species intolerant of brackish conditions,
percentages of non -wetland species, number of herbaceous dominants, or number of
shrub/woody vine dominants when pre- and post -Mod Alt L vegetation data were
compared.
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 two wells in the main prong were 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
II-B-10

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 was 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 lengths for three
wells at DCUT11 (DC11W1A, DC11W2B, and DC11W2C) were 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 percentage
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 complicate 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.
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 2021. 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
II-B-11

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-12

E
.(
O
co
O
O —
Drinkwater Creek Vegetation
A B C D E
CO 6) W
O O O O O O
N N N N N N
Figure II-B1. Dendrogram of hierarchical clusters of similarity of Drinkwater 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). Blue
year is pre -Mod Alt L.
O —
A
Long Creek Vegetation
B C D
67 W (9 N
N N
O O O O O O O O
N N N N N N N N
Figure II-B2. Dendrogram of hierarchical clusters of similarity of Long Creek (Control) 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).
II-B-13

Dissimilaraity
A B
Huddles Cut (Main) Vegetation
C D E
N h m O M
Q)
0 0 0 N N 0 o m
N N N N r
O O r Q -
Q O O O O
0 O O N O
Figure II-B3. Dendrogram of hierarchical clusters of similarity vegetation survey years at the main
prong of Huddles Cut 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). Blue years are pre -Mod Alt L.
100 -
Cn
co
c 90 -
N .cD
a) 80
O• j 70
c
•c Y 60
E
0 • 00 50
40 -
cc
E 30 -
d
20
10 -
0-
Huddles Cut -Main Prong
•
•
p=<0.001
•
Pre -Mod Alt L
Post -Mod Alt L
Figure II-B4. Percent of dominant species intolerant of brackish conditions on the main prong of
Huddles Cut pre- vs post -Mod Alt L; pre -years include 1998-2001, 2007-2009; post -years include
2013-2014, 2016-2019, and 2021.
II-B-14

110
100
c 90
<n o
o
c — 80
o c
a o
') 0 70
-c
c • Y 60
U
oom 50
40
o
c �
30
—
• Q
c 20
10
0
Huddles Main Prong
HMW8
p=0.008
HMW9
p=<0.001
HMW6
p=0.6.0
UP`
REAM
HMW10
p=0.702
HMW5
p=0.535
C
HMW2
p=0.25
p=0.136
HMW12
•
T
lI
T
•
•
•
•
-
•
•
—
—
Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B5. Percent of dominant species intolerant of brackish conditions at each transect on
the main prong of Huddles Cut pre- vs post -Mod Alt L. Means (dots), ranges, and p-values are
shown.
• 100
w 0 Oin
w z 80
70
Q 60
Z
4v4 50
p m 40
p 30
Z z 20
w
10
W
a O
H
Z 1997
HUDDLES MAIN
HMW8
♦
= 0.24
------------------
= 0.34
•
R� = 0.29
1999 2001 2003 2005 2007 2009 2011 2013 2015 2017 2019 2021
Pre -Mod Alt L
Linear (Pre -Mod Alt L)
YEAR
• Post -Mod Alt L
— Linear { Post -Mod Alt L)
Linear {All Years)
Figure II-B6. Linear regression for percent of dominant brackish intolerant species every year at
a transect that was significantly different on the main prong of Huddles Cut pre- vs post -Mod Alt
L; pre -years include 1998-2001, 2007-2009; post -years include 2013-2014, 2016-2019, and
2021; diamond and square symbols represent yearly values.
II-B-15

HUDDLES MAIN
HMW9
N 100
Z
LI 0 90
P ❑ 80 ♦
a Z
in 8 70
1- Rz=0.004
a v=i 60 ►
Z Y
50 • ♦ - ♦ R2 = 0.52
0a m 40
LL v 30 '■'".-�,.M ■
p
E a2 20 R2=0.14
W 10
L.,.,J
a p 0 •
Z 1997 1999 2001 2003 2005 2007 2009 2011 2013 2015 2017 2019 2021
• Pre -Mod Alt L
YEAR
• Post -Mod Alt L - - - - Linear (All Years)
- linear (Pre -Mod Alt 1) - linear (Post -Mod Alt 1)
Figure II-B7. Linear regression for percent of dominant brackish intolerant species every year at
a transect that was significantly different on the main prong of Huddles Cut pre- vs post -Mod Alt
L; pre -years include 1998-2001, 2007-2009; post -years include 2013-2014, 2016-2019, and
2021; diamond and square symbols represent yearly values.
0
.) 8 -
0
lz
7-
c
6-
E
0
p 5-
2 4-
15
L
3-
2 -
m
Z
10
9-
0
Huddles Cut -Main Prong
p<0.001
•
T
•
•
•
Pre -Mod Alt L
Post -Mod Alt L
Figure II-B8. Number of dominant species in the herb layer on the main prong of Huddles Cut
pre- vs post -Mod Alt L; pre- years include 1998-2001, 2007-2009; post- years include 2013-2014,
2016-2019, and 2021.
II-B-16

Number of Herb Dominants
10
9
8
7
6
5
4
3
2
0
Huddles Main Prong
HMW8
p=0.682
HMW9
p=0.044
HMW6
p=<0.001
UPSTREAM
HMW10
p=0.002
HMW5
p=0.026
HMW2
p=<0.001
HMW12
p=0.001
>-
•
—
•
•
•
Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B9. Number of pre- vs post -Mod Alt L dominant species in the herb layer at each transect
on the main prong of Huddles Cut. Means (dots), ranges, and p-values are shown.
Number of Shrub Dominants
6
5
4
3
2
0
Huddles Main Prong
HMW8
p=0.765
HMW9
p=0.383
HMW6 HMW10
p=0.337 p=0.002
UPSTREAM
HMW5
p=0.109
HMW2
p=0.017
HMW12
p=0.598
•
t
•
Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B10. Number of pre- vs post -Mod Alt L dominant shrubs at each transect on the main
prong of Huddles Cut. Means (dots), ranges, and p-values are shown.
II-B-17

.5
E
0
A
Huddles Cut (West) Vegetation
B C
• CO fCO O
CT)O O c O O
0 0 0 0 o m rn o 0 0 0
N N N N N r r N N N N
Figure II-B11. Dendrogram of hierarchical clusters of similarity of vegetation survey years for
presence/absence of all species at the west prong of Huddles Cut. 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.
100 -
0) 90 -
• c
.a
a) 73
80-
�j 70-
c
CO 0) 60-
0
O m 50 -
40-
c c
a) Es 30-
a) o
O c 20-
10 -
0
Huddles Cut -West Prong
•
p=<0.001
•
•
•
Pre -Mod Alt L
Post -Mod Alt L
Figure II-B12. Percent of dominant species intolerant of brackish conditions on the west prong of
Huddles Cut pre- vs post -Mod Alt L; pre -years include 1998-2001, 2007-2009; post -years include
2013-2014, 2016-2019, and 2021.
II-B-18

100
rn
u) • 90
o
5 80
ao
U)�j 70
_- c
N Yu)
c60
E U
50
p 00
o 5 40
N
g
C 20
10
0
30
Huddles Cut -West Prong
HWW7
p=0.48T
HWW4
p=0.079
HWW2
p=<0.001
HWW8
p=<0.001
UPSTREAM
1
1
1
1
1
Pre Post
Pre Post
Pre Post Pre Post
Figure II-B13. Percent of dominant species intolerant of brackish conditions at each transect on
the west prong of Huddles Cut pre- vs post -Mod Alt L. Means (dots), ranges, and p-values are
shown.
PERCENT OF DOMINANT SPECIES
INTOLERANCT OF BRACKISH CONDITIONS
100
90
80
70
60
50
40
30
20
10
0
1997
HUDDLES WEST
HWW2
♦
R' = 0.09
•
♦ ♦
W = 0.60
■ ■
■
W = 0.05
•
1999 2001 2003 2005 2007 2009 2011 2013 2015 2017 2019 2021
Pre -Mod Alt L
Linear (Pre -Mod Alt L)
YEAR
Post -Mod Alt L ---- Linear (All Years)
Linear (Post -Mod Alt L)
Figure II-B14. Linear regression for percent of dominant brackish intolerant species every year
at a transect that was significantly different on the west prong of Huddles Cut pre- vs post -Mod
Alt L; 1998-2001, 2007-2009; post -years include 2013-2014, 2016-2019, and 2021; diamond and
square symbols represent yearly values.
II-B-19

PERCENT OF DOMINANT SPECIES
INTOLERANCT OF BRACKISH CONDITIONS
100
90
80
70
60
50
40
30
20
10
0
1997
HUDDLES WEST
HWW8
RZ = 0.02
n R()
■
■ 1
■
R2- 0.01
1999 2001 2003 2005 2007 2009 2011 2013 2015 2017 2019 2021
• Pre -Mod Alt L
YEAR
m. Post -Mod Alt L
Linear (Pre -Mod Alt L) - Linear (Post -Mod Alt L)
Linear (All Years)
Figure II-B15. Linear regression for percent of dominant brackish intolerant species every year
at a transect that was significantly different on the west prong of Huddles Cut pre- vs post -Mod
Alt L; 1998-2001, 2007-2009; post -years include 2013-2014, 2016-2019, and 2021; diamond and
square symbols represent yearly values.
N
0
a 5 -
(0 4
E
0
3 -
0
0)
E 2 -
Z
1-
7
6-
Huddles Cut -West Prong
p=<0.001
•
0
Pre -Mod Alt L
Post -Mod Alt L
Figure II-B16. Number of dominant species on the west prong of Huddles Cut pre- vs post -Mod
Alt L; pre- years include 1998-2001, 2007-2009; post- years include 2013-2014, 2016-2019, and
2021.
II-B-20

Number of Herb Dominants
7
6
5
4
3
2
0
Huddles Cut -West Prong
HWW7
p=0.237
HWW4
p=0.902
UPSTREAM
HWW2
p=<0.001
HWW8
p=0.001
Pre
Post
Pre
Post
Pre
Post
Pre Post
Figure II-B17. Number of pre- vs post -Mod Alt L dominant herbs at each transect on the west
prong of Huddles Cut. Means (dots), ranges, and p-values are shown.
Number of Shrub Dominants
5
4
3
2
0
Huddles Cut -West Prong
HWW7
p=0.337
HWW4
p=0.218
UPSTREAM
HWW2
p=0.099
—
HWW8
p=0.004
—
>
•
•
Pre
Post
Pre
Post Pre
Post
Pre Post
Figure II-B18. Number of pre- vs post -Mod Alt L dominant shrubs at each transect on the west
prong of Huddles Cut. Means (dots), ranges, and p-values are shown.
II-B-21

a
E
o
0
Porter Creek Vegetation
A
D E
• N V
O O O O O
N N N N N
Figure II-B19. Dendrogram of hierarchical clusters of similarity of vegetation survey years based
presence/absence of all species at Porter Creek. Colored lines represent clusters (or single year)
that are significantly different from each other at the 5 percent level (p = 0.05). Blue years are pre -
Mod Alt L.
0
T
E
m
0
Duck Creek Vegetation
A 3 C DEF G
M c4 N C
N N
O O O O O O O O O O
N N N N N N N N N N
Figure II-B20. Dendrogram of hierarchical clusters of similarity of vegetation survey years based
presence/absence of all species at Duck Creek (Control). Colored lines represent clusters (or single
year) that are significantly different from each other at the 5 percent level (p = 0.05).
II-B-22

A
DCUT11 Creek Vegetation
H
Figure II-B21. Dendrogram of hierarchical clusters of similarity of vegetation survey years based
presence/absence of all species at DCUT11. 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.
a
E
N
m
0
v
c) —
O
N
O
O —
A
DCUT19 Creek Vegetation
B C
Figure II-B22. Dendrogram of hierarchical clusters of similarity of vegetation survey years
based presence/absence of all species at DCUT19 (Control). Colored lines represent clusters
(or single year) that are significantly different from each other at the 5 percent level (p = 0.05).
II-B-23

OBL
w
FACW
FAC
0
• OBL
▪ FACW
w
FAC
Huddles Main Prong (2013-2021 post)
10
20
30
Percent species with wetland status
40
■ 2021
■ 2019
■ 2018
■ 2017
■ 2016
■ 2014
■ 2013
50
OBL
m
FACW
FAC
Long Creek to match Huddles MP
10 20 30 40
Percent species with wetland status
50
■ 2021
■ 2019
■ 2018
■ 2017
■ 2016
■ 2014
■ 2013
0
OBL
7
▪ FACW
c
A
FAC
Huddles Cut West Prong (2013-2021 post)
10 20 30 40 50
Percent species with wetland status
Long Creek to match Huddles WP
0
10 20 30 40
Percent of species with wetland status
50
■ 2021
■ 2019
■ 2018
■ 2017
■ 2016
■ 2014
■ 2013
2021
■ 2019
■ 2018
■ 2017
■ 2016
■ 2014
■ 2013
Figure II-B23. Percent of species in three categories of wetland status (obligate [OBL], facultative wet {FACW], and facultative [FAC])
documented in vegetation surveys in three impact creeks compared to control creek vegetation for the same survey years as the three
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: Huddles Cut was not sampled in 2015 and 2020, Porter Creek was not sampled in 2016-2018, Duck Creek was not
sampled in 2018, and Durham Creek (DCUT11 and DCUT19) was not sampled in 2018-2019.
II-B-24

Fi•ure II-B23 concluded
Porter Creek (2019-2021 post)
OBL
cu
a
g
4-
m
n FACW
a
c
m
FAC
OBL
a
a
2
i
• FACW
c
a
a
a
FAC
0
20 40
Percent species with wetland status
60
Duck Creek to match Porter Creek
0 10 20 30 40 50
Percent species with wetland status
60
. 2021
■ 2020
• 2019
• 2015
• 2014
• 2013
• 2012
■ 2011
OBL
FAC
0
DCUT11 (2020-2021 post)
20 40 60
Percent species with wetland status
2021
■ 2020
■ 2019
■ 2015
■ 2014
■ 2013
■ 2012
■ 2011
OBL
ui
c
to
FACW
a
c
m
FAC
0
II-B-25
2021
• 2020
• 2017
• 2016
• 2015
• 2014
• 2013
DCUT19 to match DCUT11
■ 2021
■ 2020
• 2017
• 2016
■ 2015
■ 2014
• 2013
20 40 60
Percent species with wetland status

Drinkwater Creek
Longest Hydroperiod (days)
Figure II-B24. 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=2013-2021). Means (dots)
and ranges are shown.
Tooley Creek
TW4
250 -
— 200 -
>>
co -
o ▪ 150-
•= -
a) -
o -
0
100
2 -
0) 50 -
c -
o -
0-
TW3
TW2
UPSTREAM
TW1
TW5
p=0.002
TW6
Pre
Post Pre
Post Pre Post Pre Post Pre Post Pre Post
Figure II-B25. 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=2012-2021).
Means (dots) and ranges are shown.
II-B-26

Huddles Cut Main Prong
HMW8
250 -
50 -
HMW7
— •
p=0.006
III0
to 5� to 5� to 5� to 5� to 5� to 5� to 5� to 5� to 5� to 5� to 5� to 5�
Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo Q Qo
HMW9
HMW6
UPSTREAM
HMW 0 HMW5
HMW
HMW3
HMW11
HMW2
HMW12
HMW1
p=0.042
Figure II-B26. 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=2012-2021). Means (dots) and ranges are shown.
250
m 200
0
Q 150
0
2
' 100
a)
0)
0
0
J
50
0
Huddles Cut
i
•
West Prong
p=<0.001 —
•
•
Main Prong
p=<0.001
•
46
50
52
44
80
70
60
50
40 3
0
0
30 0
0)
0
20 >
10
0
Figure II-B27. Longest combined pre- and post -Mod Alt L hydroperiod and mean rainfall for
each period in Huddles Cut (pre=2000-2001, 2007-2009; post=2010-2021). Means (dots) and
ranges are shown.
II-B-27

Longest Hydroperiod (days)
DCUT11
DC11W3A
250 -
200 -
150 -
100 -
50 -
DC11 W3B
• •
DC11 W3C
DC11 W2A
DC11W2B
p=0.015
UPSTREAM
DC11 W2C
p=0.0436
I i
DC11 W1A
p=0.032
DC11 W1 B
I
0 i i i 1 1 1 1 1 1 1
Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post Pre Post
Figure II-B28. 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=2018-2021). Means (dots) and
ranges are shown.
II-B-28

C - C -
O
(6 - a)U +) Y -o
a)O C II
a) - U >,
> 0 .c £
C >+ + C)
O C
o
C
> - w
-o L)
O U (1)
Zr) N r-+ O
N (6 a)
U
C 1 C
L C (Q (Q
•C a U
u)a O2
C
Q
a)
U (6
a) -0 (13
•U Q -0
Q) 0
(/) C a)
+' L i+
C O O
(6 73 O
Q (_) C }
4 (Q
( V >
L O
Q -
O a) a)
w (6 -
a) U La) U tii_4113
QJ
> L
U) d U
- U
C O
a) (Q
E Q -c
o
a)
_ (A
8-3L (6 O
O
z La-3
-0 0 L
N C (6
)
a) •§ J
t N Q
Q 2 0
C O 0
^^to
LL
a)
as
cU
L
U a)
a)N
C -0
(6 (6
I- I
Percent of dominant non -wetland and brackish
calculations.
J
0
N
0
-o
as
Q
L
Q
a)
a)
a)
0
-o
II
a)
>
Q
Y
O
>
a)
>
O
Percent of non -wetland dominantsa/ Percent of brackish intolerant dominants"
Porter Creek
CC
rn
a
o0 0
O ci
0 O
0 0
0
6
O
0
ri co
co o
O O
0 0
oo I-- O
O co O
o \
0 O O
0 O o
o-
O O
0 0
o o
O O
O O
O
0
O
O
O
O O
g 0
O
r- O
cci O
O O O
0 0 0
O \
O O O
O N N
Jacks Creek Jacobs Drinkwater Tooley Creek DCUT11
Creek Creek
TW6 DC11 W2B
O
O
O(
0
0
O CO V O
LO r) O
I-- COI-- CO
O O O O
0 0 0 0
16.7 /83.3
0.0 / 83.3
O
0
O
O
O
O
0
O
O
O
O O
0 0
O O
O O
O O
O
0
O
O
O
Inaccessible due to
hurricane debris
O O O
0 0 0
O O O
O O O
O O O
O
0
O
O
O
0.0/33.3 0.0/0.0 0.0/100.0 0.0/100.0
TW4
0
0
O
O
d
0
0
O
O
o
0 0
0 0
O O
O O
d o
r
Cfl
CO
O
0
O O O
0 0 0
LO LO V
O O
c° 0 0
O
0
LO
O
0
TW3
O
O
LO
0
0
O
LO
N
0
0
r) r)
V r)
CO
0 0
0 0
0.0 / 0.0
0.0 / 0.0
O co O
LO r) O
N CO V
0 0 0
0 0 0
co
r)
CO
0
0
I--
CO
o
O
0
O
O
o
O
0
O O
L(i LO
O O
0 0
0.0 /66.7
0.0 /75.0
I-- O O
C0 O O
CO CO LO
O O O
0 0 0
O
O
LO
O
0
JW9 JCBW DWW1C
O
0
O
O
0
O O
0 0
O O
O O
0 0
O O
0 0
O O
O O
0 0
O
0
O
O
0
O O
O 00
0 O
o
O LO
O
00
O
6
(AO
O
00
q
O O O
O O 00
r) O
co. 6 q
CO (AO
CO
r)
r)
O
O
O
O
V
O
O
O O O
O O o
V LO N
O O O
O O O
CO
r)
CO
O
O
O
vi
N
O
O
O
O
V
O
O
O 0
0 O
(A
O O
O 0
O
0
O
O
O
0
O
O
O
0
O
O
O O O
0 0 0
O O O
O O O
JW7
O
LO
I--
O
O
O
O
CO
O
O
O I-- v
LO CO
I-- CO I--
O O O
O O O
O
O
CO
O
O
I--
CO
CO
O
O
I--
CO
CO
O
O
r rn
CO N
CO V
O O
O O
O
O
V
O
O
r
CO
CO
O
O
I--
CO
CO
O
O
O I-- I�
O CO CO
CO CO CO
O O O
O O O
JW5
r)
r)
r)
O
O
O
O
V
O
O
O CO I--
O r) CO
N CO
O O O
O O O
O
O
N
O
O
I--
CO
O
O
O
O
N
O
O
O O
LO LO
N N
O O
O O
O
O
O
O
O
O
O
O
O
O
O
O
O O O
O O O
O O O
O O O
JW3
O
O
O
0
0
V
I
o
0
LO O O
I--:LO
CO" O
L�' 0 0
0 0
CO
LO
0
0
V
0
0
V
0
0
O O
O O
O O
O 0
O
O
(A
0
0
O
O
V
0
0
O
O
O
0
O O O
O LO
O N N
O 0 0
0 0 0
BSCW1 BSCW2 JW2
O
O
O
0
O
O
0
O O O
O
OOO
O O O
0 0 0
O O O
OOO
O O O
0 0 o
O O
LL)
\ LO
O O
O O
O
LO
O
O
I-
C
CO
O
O
O
0
0
O
0
O O O
n n O
(A V\ I--
O O O
O O O
Broomfield Swamp
Creek
O O O
0 0
O\ V N
O O O
O O O
O O I�
O O CO
O o 0
0 O O
0 0 0
N
i
00
0)
—
0
T
—
0 N
0 0 0
N N N
CO
0
N
0
N
0
LO O 0 ,- N
0 co 0 0 0
N O N N N
N
CO
0
N
LO CO N.
0 0 0 0
N N N N
00 O) 0
0 0 0 0
N N N N
II-B-29

Table II-B1a (concluded).
Percent of non -wetland dominantsa/ Percent of brackish intolerant dominantsb
Huddles Cut Main Prong Huddles Cut West Prong
O
j
=
O
O
O
O
O
O O
O O
O O
O O
O O
O
O
°
N..O
6
O
O
O
O
O
O
O
O
O
-O
U N
O ala)O
N_E
~ N
Transect
eliminated
-O
O )
N E
~ N
Transect
eliminated
HWW8
co
co
O
O
V O
r— CO
O O
O O
O
r
O
O
h
CO
O
O
0
CO
O
O
0
r
O
O
33.3 / 66.7
0.0 /0.0
F—• r—• 0 h
(O (O N (O
O O O O
O O O O
0.0 / 33.3
r
=
coo
( )
M
O
O
O O
N N
I� r
O O
O O
co
( )
W
O
O
O
O
CD
O
O
O
O
N
O
O
O
O
N
O
O
0.0 /0.0
0.0 / 20.0
co I- r
6 (O (O 00
co (.0 (.0(O
O O O 0
O O O O
N.
6
O
O
HWW4
O
co
O
O
N. N.
co co
O O
O O
O
r
O
O
O
CO
O
O
O
O
NN
O
coM_
O
NN
20.0 / 40.0
0.0 /20.0
M N N. r
M CD CD
O N • O O
O N O O
0.0 / 66.7
HWW2
O
ci
O
7
O
N O
0N3 O
70 O 0
O O
M
cool
O
O
M
co
O
O
O
W
O
O
ci
O
0
O
0.0 / 50.0
0.0 / 50.0
O O O O
N N N V
O O O O
O O O O
0.0/33.3 0.0/75.0
N
2
1
V
N.
O
O
h O
6g
co
O O
O o
N
N.:
co
O
O
N.
6
(O
O
O
V
1
M
a
co
(�')
co
O
O
0.0 / 0.0
0.0 / 40.0
O O O
N O O lf)
I� CO N N
O O O O
O O O O
O
1
V
V
V
O
o
N N
N N
co N
O O
0 o
O
O
(O
O
O
V•
1
O
Ln
N
O
O
O
N
N
0.0 / 33.3
0.0 / 33.3
O O M O
O O (`') O
N lf) CO (O
O O O O
O O O O
0
N
N.
O
o
HMW9
O
O
lf)
O
O
O O
O O
CO (O
O O
O 0
O
O
N
O
0
O
O
(O
O
0
O
O
N
O
0
I�
(O
(O
O
0
OD/OD
0.0 / 33.3
co co co O
() () () ui
(O (O (O N
O O O O
0 0 0 0
0.0 / 25.0
HMW8
O
LLO
O
O
O N
N CO
O O
O 0
O
L)
O
0
CO
CO
O
O
I�
(MO
O
O
N
0.0 / 16.7
0.0 / 42.9
M M O O
COCOO
O O O O
O O O O
O
O
O
O
HMW6
N
O
O
O N
0 (0
O O
O O
O
N
O
O
N.-
(0
O
O
O.
(0
O
O
N.-
(0
O
O
0.0 /0.0
0.0 / 20.0
O. O. N"'O
O
N N (0 O_
O O O 0
O O O O
0.0 / 66.7
HMW5
0)
N
V
O
O
O O
0 0
N LO
O O
O O
h
(O
(O
O
O
h
(O
(O
O
O
0
O
N
O
O
0
O
N
O
O
co
co
M
co
co
O
N
O
O
CO O h h
M O 6 6
CO N CD CD
O O O O
O O O O
0.0 / 66.7
HMW2`
N
00
O
O
O N.-
00 (D
O
O
N
W
N
O
O)
O
O
O
O
NN
O
N
s-
25.0 / 25.0
0.0 / 25.0
O O O O
N N N O
O O O O
O O O O
O
ci
0
O
O
R
U)
>-
a)
0)
7
a) O
0) O
'- N
f0
O
O N O
O No
N O N
0
N
0
O
N
0 0
O O
N N
O
N
NCO
O O
N N
.1)0 (O N.00 Cr)
N N
O O O O O O O O
N N N N N N N N
vs post- comparisons).
I I—B-30

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. Gray fill indicates no
survey (creek was not yet in the study, in transition, or a 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
2021
0.0 / 66.7
0.0 / 66.7
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
25.0/100.0
25.0/100.0
0.0 / 50.0
0.0 / 60.0
0.0 / 60.0
0.0 / 66.7
0.0 / 60.0
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
0.0/75.0
0.0/80.0
0.0/80.0
0.0/100.0
12.5/87.5
0.0/85.7
0.0/100.0
0.0/85.7
14.3/100.0
0.0/100.0
0.0 / 66.7
0.0/100.0
42.9/100.0
40.0/100.0
0.0/100.0
0.0/100.0
25.0/100.0
0.0 / 50.0
0.0/25.0
0.0/20.0
0.0/40.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
0.0/25.0
0.0/33.3
0.0/28.6
0.0/50.0
0.0/33.3
0.0/33.3
14.3/100.0
14.3/100.0
0.0/100.0
0.0/100.0
0.0/83.3
0.0/83.3
0.0/100.0
0.0/100.0
0.0/100.0
0.0/100.0
II-B-31

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 2021. 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. Gray fill indicates no survey (light gray = creek not yet in study or skip year; dark gray = transition between pre- and post -Mod Alt L). See footnote regarding Huddles Cut West.
Impact creek NWPL Pre -Mod Post -Mod
a 1998 1999 2000 2001 2002 2003 2004 2005 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016 2017 2018 2019 2020 2021
categoryAlt L avg. Alt L avg.
FAC 14 13 15 14.0
FACW 12 13 14 13.0
# of OBL 8 14 13 11.7 I NA
species FACU 0 2 4 2.0
Broomfield UPL 0 0 0 0.0
Swamp TOTAL 34 42 46 40.7 NA
Creek FAC 41.2 31 31.9 34.7
of total FACW 35.3 31 29.8 32.0
%species OBL 23.5 33.3 27.7 28.2 NA
1 FACU 0 4.8 8.5 4.4
UPL 0 0 0 0.0
Jacks
Creek
Jacobs
Creek
Drinkwater
Creek
# of
species
% of total
species
# of
species
% of total
species
# of
species
% of total
species
FAC
FACW
OBL
FACU
UPL
TOTAL
FAC
FACW
OBL
FACU
UPL
FAC
FACW
OBL
FACU
UPL
TOTAL
FAC
FACW
OBL
FACU
UPL
FAC
FACW
OBL
FACU
UPL
TOTAL
FAC
FACW
OBL
FACU
UPL
14 19 17 18 18 20 20 21 11 14 15 17
24 18 19 20 20 20 19 16 8 16 11 13
19 17 17 20 17 18 18 19 5 11 10 13
3 5 6 6 7 6 7 5 1 5 3 5
0 0 0 0 0 0 0 0_ 0 0 0 0
60 59 59 64 62 64 64 61 25 46 39 48
23.3 32.2 28.8 28.1 29.0 31.3 31.3 34.4 44.0 30.4 38.5 35.4
40.0 30.5 32.2 31.3 32.3 31.3 29.7 26.2 32.0 34.8 28.2 27.1
31.7 28.8 28.8 31.3 27.4 28.1 28.1 31.1 20.0 23.9 25.6 27.1
5.0 8.5 10.2 9.4 11.3 9.4 10.9 8.2 4.0 10.9 7.7 10.4
0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0 0.0
4 7 6
2 7 3
0 2 1
0 4 1
0 0 0
6 20 11
66.7
33.3
0.0
0.0
0.0
35.0
35.0
10.0
20.0
0.0
54.5
27.3
9.1
9.1
0.0
9
4
2
2
0
17
52.9
23.5
11.8
11.8
0.0
16 14 13 15
15 17 16 17
11 8 7 11
4 4 5 5
0 0 0 0
46 43 41 48
34.8 32.6 31.7 30.6
32.6 39.5 39.0 34.7
23.9 18.6 17.1 22.5
8.7 9.3 12.2 10.2
0.0 0.0 0.0 0.0
9 8 8 6
4 4 4 4
2 1 1 1
4 4 3 4
0 0 0 0
19 17 16 15
47.4 47.1 50.0 40.0
21.1 23.5 25.0 26.7
10.5 5.9 6.3 6.7
21.1 23.5 18.8 26.7
0.0 0.0 0.0 0.0
12 17 15 15 14
9 9 10 10 8
3 4 3 3 3
5 4 6 6 3
0 0 0 0 0
29 34 34 34 28
41.4 50.0 44.1 42.9 48.3
31.0 26.5 29.4 28.6 27.6
10.3 11.8 8.8 8.6 10.3
17.2 11.8 17.6 17.1 10.3
0.0 0.0 0.0 0.0 0.0
17.0
17.0
15.3
4.9
0.0
54.3
32.2
31.3
27.7
8.8
0.0
5.7
4.0
1.0
1.7
0.0
12.3
52.1
31.9
6.4
9.7
0.0
9.0
4.0
2.0
2.0
0.0
17.0
52.9
23.5
11.8
11.8
0.0
14.5
16.3
9.3
4.5
0.0
44.5
32.4
36.5
20.5
10.1
0.0
7.8
4.0
1.3
3.8
0.0
16.8
46.1
24.1
7.3
22.5
0.0
14.6
9.2
3.2
4.8
0.0
31.8
45.3
28.6
10.0
14.8
0.0
I I-B-32

Table II-B2 (continued).
Impact creek
NWPL
category
1998
1999
2000
2001 2002 2003 2004 2005 2007
2008
2009 2010 2011 2012 2013
2014
2015 2016
2017
2018 2019 2020 2021
Pre -Mod
Alt L avg.
Post -Mod
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
47
45
58
48
33 41
42
45
42.5
39.8
Creekb
44 13
38
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
%species
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
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
I
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
12
17.4
11.0
FACW
24
22
20
22
17
17
15
10
13
13
14
13 12
14
19.6
12.7
# of
OBL
24
17
22
24
17
18
16
7
9
10
14
14 12
12
19.7
11.1
species
FACU
8
4
7
5
6
8
7
3
3
1
3
3 2
1
6.4
2.3
Huddles
UPL
0
0
1
0
0
1
1
0
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
39
63.6
37.1
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
30.8
27.6
29.7
of total
%species
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
35.9
30.7
34.4
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
30.8
29.7
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
2.6
10.2
6.2
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
0.0
0.7
0.0
FAC
20
17
15
20
17
16
16
10
8
9
10
10 7
11
17.3
9.3
FACW
25
22
19
26
20
22
13
9
7
7
9
7 6
6
21.0
7.3
# of
OBL
30
22
17
25
12
18
11
6
6
7
8
9 5
8
19.3
7.0
species
FACU
6
6
6
5
7
8
5
2
0
1
2
2 0
1
6.1
1.1
Huddles
UPL
0
0
0
1
0
1
1
0
1
0
0
0 0
0
0.4
0.1
Cut
TOTAL
81
67
57
77
56
65
46
27
22
24
29
28 18
26
64.1
24.9
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
42.3
27.4
37.5
of total
%species
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
23.1
32.7 29.5
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
30.8
29.3 28.1
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
3.8
9.9 4.2
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
0.0
0.7 0.6
FAC
10
13
10 10
10
11 11 10.6 11.0
FACW
3
5
4 5
5
5 5 4.4 5.0
# of
OBL
2
2
2 3
3
4 4 2.4 4.0
species
FACU
1
1
0 1
2
3 3 1.0 3.0
UPL
0
0
0
0
0
0 0 0.0
0.0
DCUT11
TOTAL
16
21
16
19
20
23 23 18.4
23.0
FAC
62.5
61.9
62.5 52.6
50.0
47.8 47.8 57.9 47.8
of total
%species
FACW
18.8
23.8
25.0 26.3
25.0
21.7 21.7 23.8 21.7
OBL
12.5
9.5
12.5 15.8
15.0
17.4 17.4 13.1 17.4
FACU
6.3
4.8
0.0 5.3
10.0
13.0 13.0 5.3 13.0
UPL
0.0
0.0
0.0 0.0
0.0
0.0 0.0 0.0 0.0
FAC
7 10 11
11
9
10 12 14
9.6
12.0
FACW
7 11 7
8
6
7 8 9
7.8
8.0
# of
OBL
0 10 6
6
5
5 8 7
5.4
6.7
species
FACU
0 1 0
2
1
2 2 2
0.8
2.0
UPL
0 0 0
0
0
0 0 0
0.0
0.0
Porter
TOTAL
14 32 24
27
21
24 30 32
23.6
28.7
Creek
FAC
50.0 31.3 45.8
40.7
42.9
41.7 40.0 43.8
42.1
41.8
of total
%species
FACW
50.0 34.4 29.2
29.6
28.6
29.2 26.7 28.1
34.3
28.0
OBL
0.0 31.3 25.0
22.2
23.8
20.8 26.7 21.9
20.5
23.1
FACU
0.0 3.1 0.0
7.4
4.8
8.3 6.7 6.3
3.1
7.1
UPL
0.0 0.0 0.0
0.0
0.0
0.0 0.0 0.0
0.0
0.0
II-B-33

Table II-B2 (concluded).
Control creek
NW PL
category
1998 1999 2000 2001 2002 2003 2004 2005 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016 2017 2018 2019 2020 2021
Control Average
SCUT1
# of
species
FAC
FACW
OBL
FACU
UPL
TOTAL
% of total
species
FAC
FACW
OBL
FACU
UPL
10 13 11
6 8 10
8 11 13
0 1 2
0 0 0
11.3
8.0
10.7
1.0
0.0
N/A
24 33 36
31.0
N/A
41.7
25.0
33.3
0.0
0.0
39.4
24.2
33.3
3.0
0.0
30.6
27.8
36.1
5.6
0.0
37.2
25.7
34.3
2.9
0.0
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 11
9 7 7 10 8 9 9 8 7 8 10
3 2 4 5 4 6 7 9 8 6 6
0 2 0 1 0 1 1 1 1 0 0
0 0 0 0 0 0 0 0 0 0 0
9.1
8.4
5.5
0.6
0.0
23 16 17 27 21 25 28 27 24 24 27
23.5
47.8 31.3 35.3 40.7 42.9 36.0 39.3 33.3 33.3 41.7 40.7
39.1 43.8 41.2 37.0 38.1 36.0 32.1 29.6 29.2 33.3 37.0
13.0 12.5 23.5 18.5 19.0 24.0 25.0 33.3 33.3 25.0 22.2
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 0.0 0.0
38.4
36.0
22.7
2.9
0.0
DCUT19
# of
species
FAC
FACW
OBL
FACU
UPL
TOTAL
% of total
species
# of
species
Duck Creek
% of total
species
FAC
FACW
OBL
FACU
UPL
FAC
FACW
OBL
FACU
UPL
TOTAL
FAC
FACW
OBL
FACU
UPL
11 11 11 14 15 10 11
7 9 7 6 6 6 5
4 4 4 4 4 3 3
0 1 1 1 3 4 4
0 0 0 0 0 0 0
22 25 23 25 28 23 23
50.0 44.0 47.8 56.0 53.6 43.5 47.8
31.8 36.0 30.4 24.0 21.4 26.1 21.7
18.2 16.0 17.4 16.0 14.3 13.0 13.0
0.0 4.0 4.3 4.0 10.7 17.4 17.4
0.0 0.0 0.0 0.0 0.0 0.0 0.0
14 15 17 20 23
16 16 17 21 14
3 3 7 9 5
3 2 1 3 2
1 0 0 0 0
37 36 42 53 44
37.8 41.7 40.5 37.7 52.3
43.2 44.4 40.5 39.6 31.8
8.1 8.3 16.7 17.0 11.4
8.1 5.6 2.4 5.7 4.5
2.7 0.0 0.0 0.0 0.0
23 27
18 18
8 13
5 8
0 0
54 66
42.6 40.9
33.3 27.3
14.8 19.7
9.3 12.1
0.0 0.0
23 27 28
19 23 23
13 11 11
8 10 9
0 0 0
63 71 71
36.5 38.0 39.4
30.2 32.4 32.4
20.6 15.5 15.5
12.7 14.1 12.7
0.0 0.0 0.0
12.4
7.0
4.0
1.2
0.0
24.6
50.3
28.7
16.4
4.6
0.0
17.8
16.8
5.4
2.2
0.2
10.5
5.5
3.0
4.0
0.0
23.0
45.7
23.9
13.0
17.4
0.0
26.0
21.7
11.7
9.0
0.0
42.4 68.3
42.0
39.9
12.3
5.3
0.5
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 -Mod Alt
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.
38.0
31.6
17.2
13.2
0.0
II-B-34

PRE- TO POST -MOD ALT L DIFFERENCES IN PARAMETERS USED TO DESCRIBE CHARACTER
DISCHARGE
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II-B-35